DSHW-1992-004061 - 0901a068803194a2

lip-0010 i>\
INSTALLATION RESTORATION PROGRAM (IRP)
STAGE 2
U.S. AIR FORCE PLANT 78
BRIGHAM CITY, UTAH
RI/FS
VOLUME I
ENVIRONMENTAL SCIENCE & ENGINEERING, INC.
2 INVERNESS DRIVE EAST, SUITE 201
ENGLEWOOD, COLORADO 80112
FEBRUARY 1992
DRAFT FINAL
USAF Contract No. F33615-87-D-4016
ESE Contract No. 89946
Delivery Order No. 0008
Delivery Order No. 0008
Sam A Taffinder
AFCEE MAJCOM Coordinator
Brooks Air Force Base, Texas 78235-5501
U.S. AIR FORCE
AFCEE
Brooks Air Force Base, Texas 78235-5501
P78-921/P78TOCJ
02/18/92
TABLE OF CONTENTS
VOLUME 1
Section Page
1.0 INTRODUCTION 1-1
1.1 PURPOSE 1-1
1.2 TIME PERIOD AND STAGES OF THE IRP AT PLANT 78 1-1
1.3 INSTALLATION HISTORY 1-2
1.3.1 DESCRIPTION OF INSTALLATION 1-3
1.3.2 PAST WASTE MANAGEMENT PRACTICES 1-3
1.3.2.1 Industrial Operations fShops^) 1-3
1.3.2.2 Fuels Management 1-6
1.3.2.3 Pesticide Utilization 1-6
1.3.2.4 Waste Storage Areas 1-6
1.3.2.5 SpiUs 1-6
1.4 IDENTIFICATION OF SITES 1-8
1.5 DESCRIPTION AND STAGE 1 CHARACTERIZATION OF SITES 1-8
1.5.1 NORTH DRAINAGE DITCH 1-8
1.5.2 E-512 DRAINAGE DITCH 1-13
1.5.3 FAUST VALLEY DRAINAGE COURSE 1-13
1.5.4 M-585 FRENCH DRAIN SITE 1-14
1.5.5 BLUE CREEK 1-14
1.5.6 SANITARY SEWAGE TREATMENT EVAPORATION POND 1-17
1.6 CATEGORIZATION OF SITES 1-17
1.6.1 NORTH DRAINAGE DITCH 1-19
1.6.2 E-512 DRAINAGE DITCH 1-19
1.6.3 FAUST VALLEY DRAINAGE COURSE 1-19
1.6.4 M-585 FRENCH DRAIN SITE 1-19
1.6.5 BLUE CREEK 1-20
1.6.6 SANITARY SEWER TREATMENT EVAPORATION POND 1-20
1.6.7 E-515 AND E-519 ACID DRAINS 1-20
1.7 IDENTIFICATION OF THE FIELD TEAM 1-20
2.0 ENVIRONMENTAL SETTING 2-1
2.1 GEOGRAPHIC SETTING 2-1
2.1.1 PHYSICAL GEOGRAPHY 2-1
2.1.2 CULTURAL GEOGRAPHY 2-1
2.2 GEOLOGY 2-4
2.2.1 GEOLOGIC SETTING 2-4
2.2.2 BEDROCK GEOLOGY 2-4
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TABLE OF CONTENTS
VOLUME 1 (Continued)
Section Page
2.2.3 SURFICIAL GEOLOGY 2-7
2.2.3.1 Surficial Sediments 2-7
2.2.3.2 Soils 2-15
2.3 HYDROGEOLOGY 2-15
2.3.1 GROUNDWATER 2-20
2.3.1.1 Occurrence and Movement 2-20
2.3.1.2 Groundwater Oualitv 2-20
2.3.1.3 Groundwater Uses 2-20
2.3.1.4 Well Inventory 2-26
2.3.2 SURFACE WATER 2-26
2.3.2.1 Occurrence and Flow 2-26
2.3.2.2 Surface Water Oualitv 2-29
2.4 NATURAL RESOURCES 2-31
2.5 CULTURAL RESOURCES 2-31
2.6 BIOLOGY AND ECOLOGY 2-31
2.7 CLIMATOLOGY/METEOROLOGY 2-31
3.0 FIELD INVESTIGATION PROGRAM 3-1
3.1 ORGANIZATION AND DEVELOPMENT OF FIELD PROGRAM 3-1
3.1.1 REMEDIAL INVESTIGATION HELD PROGRAM 3-1
3.1.1.1 Soil Gas Surveys 3-5
3.1.1.1.1 M-585 3-5
3.1.1.1.2 NDD, E-512, E-515, and E-519 3-5
3.1.1.2 Drilling Activities 3-5
3.1.1.3 Monitoring WeUs 3-6
3.1.1.4 Aquifer Tests 3-6
3.1.1.5 Sampling Activities 3-6
3.1.1.6 Surveying 3-7
3.1.1.7 Evaluation and Screening nf Data 3-7
3.1.2 RISK ASSESSMENT FIELD PROGRAM 3-8
3.1.2.1 Applicable or Relevant and Appropriate Requirements 3-8
3.1.2.2 Contaminant Identification 3-8
3.1.2.3 Exposure Assessment 3-9
3.1.2.4 Toxicity Assessment 3-9
3.1.2.5 Risk Characterization 3-9
ii
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TABLE OF CONTENTS
VOLUME 1 (Continued)
Section Page
3.1.2.6 Evaluation of Data 3-10
3.1.3 FEASIBILITY STUDY PROGRAM 3-10
3.2 DATA QUALITY OBJECTIVES 3-11
3.2.1 INTRODUCTION 3-11
3.2.2 PHASE II STAGE 2 OBJECTIVES AND DQO APPROACH 3-12
3.2.2.1 Surface and Vadose Zone Soils 3-21
3.2.2.2 Groundwater 3-21
3.2.2.3 Hydrogeology 3-21
3.2.2.4 Surface Water and Sediment 3-21
3.2.2.5 Biological Sampling 3-21
3.2.2.6 Deep Stratigraphic Soil Borings 3-21
3.2.2.7 Soil Gas 3-22
3.3 IMPLEMENTATION OF FIELD PROGRAM AND SUMMARY OF FIELD
WORK 3-22
3.3.1 TIME SEQUENCE OF WORK PERFORMED 3-22
3.3.2 IDENTIFICATION AND ROLE OF SUBCONTRACTORS 3-22
3.4 INVESTIGATION METHODS AND SURVEYS CONDUCTED 3-23
3.4.1 GEOPHYSICAL INVESTIGATION 3-23
3.4.2 SOIL GAS INVESTIGATIONS 3-23
3.4.2.1 M-585 Soil Gas Survev 1 3-23
3.4.2.2 NDD. E-515. E-519. and E-512 Soil Gas Survev 3-25
3.4.3 SURVEYING AND PERMANENT FIELD IDENTIFICATION OF
MONITORING WELLS 3-25
3.5 DRILLING AND BOREHOLE PROGRAM 3-29
3.5.1 SHALLOW SOIL BORINGS AND DEEP STRATIGRAPHIC BORINGS . . 3-29
3.5.1.1 Shallow Soil Borings 3-29
3.5.1.2 Deep Stratigraphic Borings and Monitoring Wells 3-29
3.5.2 FOOTAGE SUMMARY 3-29
3.5.3 GEOTECHNICAL DRILLING PROGRAM 3-29
3.5.3.1 Shallow Soil Borings . 3-29
3.5.3.2 Deep Stratigraphic Borings and Monitoring Wells 3-29
3.5.4 MONITORING WELL DESIGN AND CONSTRUCTION 3-39
3.5.5 MONITORING WELL DEVELOPMENT 3-40
iii
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TABLE OF CONTENTS
VOLUME 1 (Continued)
Section Page
3.5.6 AQUIFER TESTING 3-40
3.5.6.1 Data Analysis 3-42
3.5.6.2 Additional Data Analysis 3-43
3.5.7 MONITORING WELL ABANDONMENT 3-44
3.5.8 WATER LEVEL MEASUREMENTS 3-44
3.6 SAMPLING PROGRAM FOR PHASE II STAGE 2 USAF PLANT 78 IRP 3-45
3.6.1 TYPES AND NUMBERS OF SAMPLES TAKEN 3-45
3.6.1.1 Soil Gas Survev 3-45
3.6.1.2 Surface Sediment and Surface Water Samples 3-45
1 3.6.1.2.1 North Drainage Ditch 3-45
2 3.6.1.2.2 E-512 3-45
3 3.6.1.2.3 Faust Valley Drainage 3-45
M 3.6.1.2.4 Blue Creek 3-50
3.6.1.3 ShaUow Borings 3-50
1 3.6.1.3.1 North Drainage Ditch 3-50
2 3.6.1.3.2 E-512 3-50
3 3.6.1.3.3 Faust VaUey Drainage 3-50
M 3.6.1.3.4 Blue Creek 3-50
3.6.1.4 Deep Borings 3-50
S 3.6.1.4.1 M-585 3-56
I 3.6.1.4.2 North Drainage Ditch 3-56
T. 3.6.1.4.3 E-512 3-56
^ 3.6.1.4.4 E-519 3-56
1 3.6.1.4.5 E-515 3-56
3.6.1.5 Groundwater Samples 3-56
3.6.1.6 Biological Sampling 3-56
3.6.1.6.1 Sampling of Plant Communities 3-56
3.6.1.6.2 Sampling of Aquatic Ecosystems 3-64
3.6.1.6.3 Small Mammal Trapping 3-64
3.7 LABORATORY OA/OC PROGRAM. SUMMARY OF QAPP 3-64
4.0 RESULTS AND SIGNIFICANT FINDINGS 4-1
4.1 DISCUSSION OF RESULTS 4-1
iv
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TABLE OF CONTENTS
VOLUME 1 (Continued)
Section Page
4.1.1 DISCUSSION OF NON SITE-SPECIFIC ECOLOGICAL
CHARACTERIZATION STUDIES 4-1
4.1.1.1 Terrestrial Vegetation 4-1
4.1.1.2 Terrestrial Vertebrates 4-1
4.1.1.2.1 Birds 4-1
4.1.1.2.2 Mammals 4-4
4.1.2 DISCUSSION OF NON SITE-SPECIFIC HYDROGEOLOGY RESULTS . 4-4
4.1.2.1 Upper Shallow Groundwater Zone 4-7
4.1.2.2 Deeper Shallow Groundwater Zone 4-11
4.1.3 DISCUSSION OF RESULTS FOR THE NORTH DRAINAGE DITCH
AND E-519 SITES 4-14
4.1.3.1 North Drainage Ditch and E-519 Geology 4-14
4.1.3.2 North Drainage Ditch and E-591 Hydrogeology 4-17
4.1.3.2.1 Aquifer Testing 4-17
4.1.3.3 Analvtical Results 4-18
4.1.3.3.1 Surface Water Samples 4-18
4.1.3.3.2 Surface Sediment Samples 4-18
4.1.3.3.3 Shallow Soil Boring Samples 4-18
4.1.3.3.4 Deep Stratigraphic Boring Samples 4-18
4.1.3.3.5 Groundwater Samples 4-18
4.1.3.3.6 Soil Gas Samples 4-18
4.1.3.4 Discussion of Analvtical Results for NDD 4-28
4.1.3.4.1 Significance of Findings 4-28
4.1.3.4.2 Zone(s) of Contamination 4-38
4.1.3.4.3 Contamination Migration 4-38
4.1.4 DISCUSSION OF RESULTS FOR THE E-512 DRAINAGE DITCH 4-38
4.1.4.1 E-512 Drainage Ditch Geology 4-38
4.1.4.2 E-512 Drainage Ditch Hydrogeology 4-40
4.1.4.2.1 Aquifer Testing 4-40
4.1.4.3 Analytical Results 4-40
4.1.4.3.1 Surface Water Samples 4-40
4.1.4.3.2 Surface Sediment Samples 4-40
4.1.4.3.3 Shallow Soil Boring Samples 4-40
v
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TABLE OF CONTENTS
VOLUME 1 (Continued)
Section Page
4.1.4.3.4 Deep Stratigraphic Boring Samples 4-44
4.1.4.3.5 Groimdwater Sample 4-44
4.1.4.3.6 Soil Gas Samples 4-44
4.1.4.4 Discussion of Analytical Results for E-512 Drainage Ditch Site .... 4-44
4.1.4.4.1 Significance of Findings 4-44
4.1.4.4.2 Zone(s) of Contamination 4-50
4.1.4.4.3 Contamination Migration 4-50
4.1.5 DISCUSSION OF RESULTS FOR THE FAUST VALLEY DRAINAGE
COURSE AND E-515 SITES 4-51
4.1.5.1 Faust Vallev Drainage Course Geology 4-51
4.1.5.2 Faust Vallev Drainage Course and E-515 Hydrogeology 4-51
4.1.5.2.1 Aquifer Testing 4-52
4.1.5.3 Analvtical Results 4-52
4.1.5.3.1 Surface Sediment Samples 4-52
4.1.5.3.2 Shallow Borings 4-52
4.1.5.3.3 Deep Boring Samples 4-57
4.1.5.3.4 Groundwater Samples 4-57
4.1.5.3.5 Soil Gas Samples 4-57
4.1.5.4 Discussion of Results for FVD and E-515 4-57
4.1.5.4.1 Significance of Findings 4-57
4.1.5.4.2 Zone(s) of Contamination 4-65
4.1.5.4.3 Contamination Migration 4-66
4.1.6 DISCUSSION OF RESULTS FOR THE M-585 FRENCH DRAIN SITE .. 4-67
4.1.6.1 M-585 French Drain Geology 4-67
4.1.6.2 M-585 French Drain Hydrogeology 4-67
4.1.6.2.1 Aquifer Testing 4-69
4.1.6.3 Analvtical Results 4-69
4.1.6.3.1 Deep Stratigraphic Boring Samples 4-69
4.1.6.3.2 Groundwater Samples 4-69
4.1.6.3.3 Soil Gas Samples 4-75
4.1.6.4 Discussion of Analvtical Results for M-585 4-75
4.1.6.4.1 Significance of Findings 4-75
4.1.6.4.2 Zone(s) of Contamination 4-84
vi
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TABLE OF CONTENTS
VOLUME 1 (Continued)
Section Page
4.1.6.4.3 Contamination Migration 4-86
4.1.7 DISCUSSION OF THE RESULTS FOR BLUE CREEK 4-86
4.1.7.1 Blue Creek Geology 4-86
4.1.7.2 Blue Creek Hydrogeology 4-86
4.1.7.3 Analvtical Results 4-86
4.1.7.3.1 Surface Water Samples 4-86
4.1.7.3.2 Surface Sediment Samples 4-92
4.1.7.3.3 Shallow Boring Samples 4-92
4.1.7.3.4 Aquatic Ecosystem Sampling 4-92
4.1.7.4 Discussion of Analvtical Results for Blue Creek 4-92
4.1.7.4.1 Significance of Findings 4-100
4.1.7.4.2 Zone(s) of Contamination 4-104
4.1.7.4.3 Contamination Migration 4-104
4.2 BASELINE RISK ASSESSMENT 4-105
4.2.1 WASTE CHARACTERIZATION 4-114
4.2.1.1 Chloroform 4-114
4.2.1.1.1 Ambient Levels 4-114
4.2.1.1.2 Health Effects 4-114
4.2.1.1.3 Enviromnental Fate 4-119
4.2.1.2 1.2-Pichloroethane 4-120
4.2.1.2.1 Ambient Levels 4-120
4.2.1.2.2 Health Effects 4-120
4.2.1.2.3 Environmental Fate 4-123
4.2.1.3 1.1.1-Trichloroethane 4-124
4.2.1.3.1 Ambient Levels 4-124
4.2.1.3.2 Health Effects 4-124
4.2.1.3.3 Environmental Fate 4-127
4.2.1.4 Trichloroethylene 4-127
4.2.1.4.1 Ambient Levels 4-127
4.2.1.4.2 Health Effects 4-127
4.2.1.4.3 Environmental Fate 4-130
4.2.2 SOURCE AND RELEASE CHARACTERIZATION 4-131
vii
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TABLE OF CONTENTS
VOLUME 1 (Continued)
Section Page
4.2.2.1 Contaminant Sources 4-131
4.2.2.1.1 Faust Valley Drainage Course 4-131
4.2.2.1.2 North Drainage Ditch 4-131
4.2.2.1.3 E-512 Drainage Ditch 4-134
4.2.2.1.4 M-585 French Drain 4-134
4.2.2.1.5 Blue Creek 4-135
4.2.2.2 Quantitation of Potential Release Mechanisms 4-135
4.2.2.2.1 Particulate Release 4-135
4.2.2.2.2 Volatilization from Soil or Sediments 4-135
4.2.2.2.3 Volatilization from Surface Water to Air 4-140
4.2.2.2.4 Volatilization from Groundwater to Air 4-143
4.2.2.2.5 Leaching from Surface Water to Groundwater 4-143
4.2.2.2.6 Release to Groundwater (Leaching) 4-146
4.2.3 TRANSPORT AND FATE OF CONTAMINATION 4-153
4.2.3.1 Surface Water Fate 4-153
4.2.3.2 Groundwater Fate 4-160
4.2.3.3 Atmospheric Fate 4-169
4.2.3.3.1 Volatilization from Surface Water 4-171
4.2.3.3.2 Volatilization from Soil or Sediment 4-172
4.2.3.4 Uncertainty Analvsis 4-176
4.2.4 EXPOSURE PATHWAYS 4-180
4.2.4.1 Direct Contact 4-180
4.2.4.2 Inhalation of Vapors and Dusts 4-185
4.2.4.3 Ingestion of Water and Soil 4-185
4.2.4.4 Ingestion of Crops and Livestock 4-186
4.2.4.5 Ingestion nf Game Species and Aquatic Organisms 4-187
4.2.4.6 Comparison to Requirements. Standards, and Criteria 4-187
4.2.4.6.1 Established Criteria 4-187
4.2.4.6.2 Estimated Criteria 4-190
4.2.4.7 Wildlife and Domestic Livestock 4-191
4.2.4.7.1 Surface Water Ingestion by Nonhuman Biota 4-191
4.2.4.7.2 Inhalation 4-192
4.2.4.7.3 Sediment/Soil Ingestion 4-192
4.2.4.7.4 Dermal Exposure for Nonhuman Biota 4-193
4.2.5 IDENTIFICATION OF RECEPTORS 4-193
4.2.6 THREAT TO HUMAN HEALTH > 4-198
viii
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TABLE OF CONTENTS
VOLUME 1 (Continued)
Section Page
4.2.6.1 Inhalation 4-198
4.2.6.2 Ingestion 4-199
4.2.6.3 Dermal 4-201
4.2.7 CARCINOGENIC RISKS 4-208
4.2.8 THREAT TO WILDLIFE 4-208
4.2.9 NO THREAT TO HEALTH 4-211
5.0 ALTERNATE REMEDIAL MEASURES 5-1
6.0 RECOMMENDATIONS 6-1
6.1 DIRECTION AND APPROACH OF FUTURE IRP EFFORTS 6-1
6.2 RECOMMENDATIONS FOR EACH SITE AND/OR OPERABLE UNIT 6-1
7.0 REFERENCES 7-1
PLATE 1 STAGE 1 AND STAGE 2 SAMPLING LOCATIONS
ix
TABLE OF CONTENTS
VOLUME n
APPENDIX A USAF STATEMENT OF WORK PLANT 78 PHASE II STAGE 2
APPENDIX B RESUMES OF KEY PROJECT STAFF
APPENDIX C LITHOLOGIC, GEOPHYSICAL, AND BORING LOGS; STREAM
DISCHARGE LOGS; WELL DEVELOPMENT AND SAMPLING FORMS
NORTH DRAINAGE DITCH
E-512 DRAINAGE DITCH
FAUST VALLEY DRAINAGE COURSE
BLUE CREEK DRAINAGE
M-585 FRENCH DRAIN SITE
BOREHOLE GAMMA RAY AND DENSITY LOGS
APPENDIX D AQUIFER TEST PLOTS
P78-921/P78TOCJO
02/18/92
TABLE OF CONTENTS
VOLUME IIIA
APPENDIX E ANALYTICAL LABORATORY DATA
ANALYTICAL LABORATORY DATA REPORTED IN APRIL 1989 ITIR
SAMPLE IDENTIFICATION CROSS REFERENCE TABLES
ANALYTICAL DATA
Soil Analvsis Results
8010/8020, Total Hydrocarbons Soil Analysis
8010/8020, Total Hydrocarbons Soil Confirmation Analysis
Base/Neutral Acids Soil Analysis
TCLP Soil Analysis
Herbicides Soil Analysis
Water Analvsis Results
8010/8020, Total Hydrocarbons Water Analysis
8010/8020, Total Hydrocarbons Water Confirmation Analysis
8010/8020 Trip Blanks
8010/8020 Rinse Water Blanks
8010/8020 Rinse Water Blanks Confirmation
Base Neutral Acids Water Analysis
Base/Neutral Acids Rinse Water Blanks
SAMPLE DATE REPORTS
Soil Methods and Holding Times
Water Methods and Holding Times
QA/QC SUMMARY SHEETS
Soil
8010/8020 Standard Matrix Spike Recovery & Replicate Summary
TRPH Standard Matrix Spike Recovery & Replicate Summary
Soil Leachates, TLP, Standard Matrix Spike Recovery & Replicate Summary
BNA Standard Matrix Spike Recovery & Replicate Summary
Method Blank Summary
Water
8010/8020 Standaard Matrix Spike Recovery & Replicate Summary
BNA Standard Matrix Spike Recovery & Replicate Summary
Method Blank Summary
Surrogate Spike Recoveries for Soil and Water
Discussion of Analytical Problems and Corrective Actions
xi
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TABLE OF CONTENTS
VOLUME UTA
(Continued)
ANALYTICAL LABORATORY DATA REPORTED IN APRIL 1989 ITIR
CHAIN-OF-CUSTODY FORMS
Soil
Water
xii
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02/18/92
TABLE OF CONTENTS
VOLUME mB
APPENDIX E ANALYTICAL LABORATORY DATA (Continued)
ANALYTICAL LABORATORY DATA REPORTED IN DECEMBER 1989 ITIR
SAMPLE IDENTIFICATION CROSS REFERENCE TABLES
ANALYTICAL DATA
Soil Analysis Results
Water Analvsis Results
SAMPLE DATE REPORTS
Soil Methods and Holding Times
Water Methods and Holding Times
QA/QC SUMMARY SHEETS
Soil
Method Blank Sample Summary
Standard Matrix Spike Recovery and Replicate Summary
Sample Matrix Spike Recovery Summary
Surrogate Spike Recovery Summary
Water
Method Blank Sample Summary
Standard Matrix Spike Recovery and Replicate Summary
Sample Matrix Spike Recovery Summary
Surrogate Spike Recovery Summary
Table Definitions and Footnotes for QC Summaries
CHAIN-OF-CUSTODY FORMS
ANALYTICAL LABORATORY DATA REPORTED IN JULY 1990 ITIR
SAMPLE IDENTIFICATION CROSS REFERENCE TABLES
ANALYTICAL DATA
Soil Analvsis Results
Water Analysis Results
SAMPLE DATE REPORTS
Soil Methods and Holding Times
Water Methods and Holding Times
xui
TABLE OF CONTENTS
VOLUME IHB
(Continued)
QA/QC SUMMARY SHEETS
Soil
Method Blank Sample Summary
Standard Matrix Spike Recovery and Replicate Summary
Sample Matrix Spike Recovery Summary
Water
Method Blank Sample Summary
Standard Matrix Spike Recovery and Replicate Summary
Sample Matrix Spike Recovery Summary
Table Definitions and Footnotes for OC Summaries
CHAIN-OF-CUSTODY FORMS
GLOSSARY OF TERMS AND SYMBOLS
xiv
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02/18/92
LIST OF TABLES
Table Page
E-1 Compound Detection by Medium and Investigation Site xii
E-2 Summary of Risks Relevant to Plant 78 bdi
E-3 Comparison of EPA Groundwater Classifications, Federal Drinking Water
Water Rules, State of Utah Proposed Groundwater Regulations, and State
of Utah Drinking Water Rules briv
1-1 Principle Pesticides Used on USAF Plant 78 1-7
1-2 Phase II Stage 1 Field Program for Plant 78 1-10
1-3 Summary of Phase II Stage 1 Recommendations, Plant 78 1-18
1- 4 Current Stage 2 Key Project Staff 1-21
2- 1 USAF Plant 78 Soils 2-17
2-2 Hydrogeologic Units and Their Water-Bearing Characteristics in the
Vicinity of USAF Plant 78 2-19
2-3 Historical Groundwater Quality Data for USAF Plant 78 Vicinity 2-23
2-4 Well Data for USAF Plant 78 and Vicinity 2-25
2- 5 Climatic Data for USAF Plant 78 2-32
3- 1 Field Activities and Rationale Used to Select These Activities for
Phase II Stage 2 Program at Plant 78 3-2
3-2 Number of Water Analyses by Site at USAF Plant 78 Phase II Stage 2 3-3
3-3 Number of Soil Analyses by Site at USAF Plant 78 Phase II Stage 2 3-4
3-4 Summary of Data Needs for RI/FS at Plant 78 3-14
3-5 Soil Analyses: DQO Analytical Levels 3-15
3-6 Water Analyses: DQO Analytical Levels 3-16
3-7 Summary of Precision and Accuracy for Non-Metallic Inorganics
and Petroleum Hydrocarbons 3-17
3-8 Summary of Precision and Accuracy for Metals 3-18
3-9 Summary of Precision and Accuracy for Matrix Spike Compounds, Quality
Control Check Samples, and Surrogates for Organic Analysis 3-19
3-10 Matrix Spikes and MSD's SW846, Method 8270 Semi-Volatile Organic
Analytes in Water and Soils 3-20
xv
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LIST OF TABLES
(Continued)
Table Page
3- 11 Map Coordinates and Surveyed Elevations, Stage 2 Groundwater
Monitoring Wells 3-28
4- 1 Flora Observed on Plant 78; Frequencies and Floristic Composition 4-3
4-2 Bird species observed on or near Plant 78 4-5
4-3 Mammals observed or expected near Plant 78 4-6
4-4 Groundwater Measurements, Stage 1 and Stage 2, Plant 78 4-10
4-5 Stage 2 Analytical Results for Surface and Groundwater Samples,
North Drainage Ditch and E-519 4-20
4-6 Stage 2 Analytical Results for Surface Sediment Samples,
North Drainage Ditch 4-21
4-7 Stage 2 Analytical Results for Shallow Boring Soil Samples,
North Drainage Ditch 4-23
4-8 Stage 2 Analytical Results for Deep Boring Soil Samples,
North Drainage Ditch and Building E-519 4-25
4-9 Detectable Constituents in Onsite Water, Plant 78 4-30
4-10 Relevant Water Quality Criteria for USAF Plant 78 Based on EPA
1986 and 1988 Criteria and Current Standards (1991) 4-32
4-11 Stage 2 Analytical Results for Surface and Groundwater Samples,
E-512 Drainage Ditch 4-42
4-12 Stage 2 Analytical Results for Surface Sediment Samples,
E-512 Drainage Ditch 4-43
4-13 Stage 2 Analytical Results for Deep Boring Soil Samples,
E-512 Drainage Ditch 4-43
4-14 Stage 2 Analytical Results for Surface Sediment Samples,
Faust Valley Drainage 4-54
4-15 Stage 2 Analytical Results for Deep Stratigraphic Boring Samples,
E-515 4-59
4-16 Stage 2 Analytical Results for Groundwater Samples,
Faust Valley Drainage and Building E-515 4-61
4-17 Summary of Stage 1 Inorganic Analytical Results in Soil Borings and
Sediments, Faust Valley Drainage Course 4-62
xvi
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LIST OF TABLES
(Continued)
Table Page
4-18 Stage 2 Analytical Results for Deep Stratigraphic Boring Samples,
M-585 French Drain Site 4-71
4-19 Stage 2 Analytical Results for Groundwater Samples,
M-585 French Drain Site 4-73
4-20 Stage 2 Analytical Results for Surface Water Samples, Blue Creek 4-90
4-21 Stage 2 Analytical Results for Surface Water Samples,
Blue Creek Drainage 4-91
4-22 Stage 2 Analytical Results for Surface Sediment Samples,
Blue Creek Drainage 4-93
4-23 Stage 2 Analytical Results for Surface Sediment Samples,
Blue Creek Drainage 4-94
4-24 Stage 2 Analytical Results for Shallow Boring Soil Samples,
Blue Creek Drainage 4-96
4-25 Stage 2 Species and Total Numbers of Aquatic Invertebrates,
Shannon-Wiener Diversity Index, and Evenness in Blue Creek 4-98
4-26 Screening Process for Selection of Indicator Chemicals
Stage 1 Sampling Program 4-106
4-27 Screening Process for Selection of Indicator Chemicals
Stage 2 Sampling Program 4-107
4-28 Maximum Observed Concentrations in each Media by Location-Stage 1 4-108
4-29 Maximum Observed Concentrations in each Media by Location-Stage 2 4-109
4-30 Plant 78 Contaminants Detected in Groundwater at
Concentrations Exceeding EPA MCLs 4-112
4-31 Physical, Chemical, and Toxicological Properties of the
Indicator Chemicals at USAF Plant 78 4-115
4-32 Summary of Toxicity Values for Potential Noncarcinogenic Effects 4-116
4-33 Summary of Toxicity Values for Potential Carcinogenic Effects 4-117
4-34 Concentrations of the Indicator Chemicals in each Media by
Area of Concern - Stage 1 Sampling Data 4-132
4-35 Concentrations of the Indicator Chemicals in each Media by
Area of Concern - Stage 2 Sampling Data 4-133
xvii
P78-921/P78TOCxviii
02/18/92
LIST OF TABLES
(Continued)
Table Page
4-36 Parameters Used in the Estimation of Volatilization Fluxes
of Contaminants From Soils or Sediments 4-137
4-37 Volatilization Flux Rates of Contaminants in Soil or Sediment 4-139
4-38 Environmental Parameters Used in the Estimation of Contaminant
Volatilization Flux From NDD and E-512 Surface Water 4-141
4-39 Volatilization Rate Constants and Mass Transfer Coefficients of
the Contaminants From NDD and E-512 Areas 4-144
4-40 Contaminant Volatilization Fluxes From Surface Waters in
NDD and E-512 Drainage Ditches 4-145
4-41 Release Rates from Surface Water to Groundwater 4-147
4-42 Summary of Release Mechanisms and Releases by Area 4-152
4-43 Concentrations of the Indicator Chemicals in Blue Creek
Sediments and Surface Water 4-155
4-44 Average Values of the Environmental Parameters Used in the
Estimation of Contaminant Volatilization Fluxes From Blue Creek 4-158
4-45 Summary of Fate of Contaminants of Concern in Abiotic Media 4-159
4-46 Volatilization Rate Constants and Mass Transfer Coefficients
for Contaminants From Blue Creek 4-161
4-47 Summary of Release Mechanisms and Flux Rates for Blue Creek 4-162
4-48 Retardation Factors of the Four Indicator Chemicals Used
in the Contaminant Migration Analysis 4-164
4-49 Contaminant Transport Velocities and Travel Times From
M-585 to Site Boundary and Blue Creek 4-166
4-50 Contaminant Transport Velocities and Travel Times From the
Northern Plume to Site Boundary and Blue Creek 4-167
4-51 Concentrations of the Contaminants in Groundwater at the
Site Boundary and Blue Creek 4-170
4-52 Air Exposure Concentrations at the Source Onsite or
Blue Creek Resulting from Volatilization from Surface Water 4-173
4-53 Air Exposure Concentrations at the Source Resulting From
Volatilization From Contaminated Soil or Sediments 4-174
xviii
P78-921/P78TOCxix
02/18/92
LIST OF TABLES
(Continued)
Table Page
4-54 Air Exposure Concentrations at Site Boundary Downwind
of Source Area 4-177
4-55 Summary of Estimated Exposure Point Concentrations at a
Source Onsite 4-178
4-56 Estimated Exposure Point Concentrations Downwind or
Downgradient at the Boundary (or Blue Creek) by
Area of Concern 4-179
4-57 Conceptual Exposure Model for Plant 78 4-181
4-58 Summary of Potential Exposure Pathways 4-182
4-59 Summary of Potential ARARs 4-188
4-60 Summary of EPA Health Advisories for 1,2-DCA and 1,1,1-TCA 4-189
4-61 Summary of Exposure Intakes for Current and Future Land Uses 4-205
4-62 Chronic Hazard Index Estimates 4-207
4-63 Summary of Chemical Specific Carcinogenic Risks for Each
Exposure Pathway and Total Carcinogenic Risk 4-209
xix
P78-92l/P78TOCja
02/18/92
LIST OF FIGURES
Figure Page
E-1 PLANT 78 SITE LOCATION xxviii
E-2 FACILITY SITE PLAN xxix
E-3 PLANT 78 GENERAL SITE LOCATION MAP xxx
E-4 STAGE 1 AND STAGE 2 SAMPLING LOCATIONS
NORTH DRAINAGE DITCH xxxiii
E-5 STAGE 1 AND STAGE 2 SAMPLING LOCATIONS
E-512 DRAINAGE DITCH xxxiv
E-6 STAGE 1 AND STAGE 2 SAMPLING LOCATIONS
FAUST VALLEY DRAINAGE xxxvi
E-7 STAGE 1 AND STAGE 2 SAMPLING LOCATIONS,
M-585 FRENCH DRAIN xxxvii
E-8 STAGE 1 AND STAGE 2 SAMPLING LOCATIONS,
BLUE CREEK NORTH xxxviii
E-9 STAGE 1 AND STAGE 2 SAMPLING LOCATIONS,
BLUE CREEK SOUTH xxxix
E-10 STAGE 2 VEGETATION TRANSECT LOCATIONS xliv
E-ll STAGE 2 SMALL MAMMAL TRAPPING LOCATIONS xlvi
E-12a UPPER SHALLOW GROUNDWATER ZONE, WATER TABLE MAP, 1989 xlvii
E-12b UPPER SHALLOW GROUNDWATER ZONE, WATER TABLE MAP, 1991 xlviii
E-13a DEEPER SHALLOW GROUNDWATER ZONE, WATER TABLE MAP, 1989 1
E-13b DEEPER SHALLOW GROUNDWATER ZONE, WATER TABLE MAP, 1991 li
1-1 AREA LOCATION 1-4
1-2 FAdLITY SITE PLAN 1-5
1-3 PLANT 78 GENERAL LOCATION MAP 1-9
1-4 PHASE H STAGE 1 NORTH DRAINAGE DITCH/E-512
DRAINAGE DITCH 1-12
1-5 M-585 SITE AND STAGE 1 BORING LOCATIONS 1-15
1- 6 BLUE CREEK STAGE 1 SAMPLING AND SURFACE WATER
FLOW LOCATIONS 1-16
2- 1 REGIONAL PHYSIOGRAPHIC FEATURES 2-2
xx
P78-921/P78TOCjm
02/18/92
LIST OF FIGURES
(Continued)
Figure Page
2-2 LOCAL PHYSIOGRAPHIC FEATURES 2-3
2-3 GEOLOGIC MAP 2-5
2-4 GEOLOGIC CROSS-SECTION D-D' 2-6
2-5 MAP SHOWING PLEISTOCENE PLUVIAL LAKES IN
WESTERN UNITED STATES 2-8
2-6 SCHEMATIC BLOCK DIAGRAM SHOWING THE VERTICAL AND
LATERAL RELATIONSHIPS OF FACIES AND DEPOSITIONAL
ENVIRONMENTS DURING DEPOSITION OF THE LAKE CLAYS
AND GRAVELS 2-9
2-7 BORING LOG E-519B1 AND WELL CONSTRUCTION DIAGRAM FOR P-8 2-10
2-8 LOCATION OF TEST BORINGS AND GEOLOGIC CROSS-SECTIONS 2-11
2-9 GEOLOGIC CROSS-SECTION A-A' 2-12
2-10 GEOLOGIC CROSS-SECTION B-B' 2-13
2-11 GEOLOGIC CROSS-SECTION C-C 2-14
2-12 SOILS MAP 2-16
2-13 POTENTIOMETRIC SURFACE MAP OF BLUE CREEK VALLEY AREA, 1970 . . 2-21
2-14 LOCATION OF WELLS AND SPRINGS 2-22
2-15 BLUE CREEK VALLEY WATERSHED 2-27
2- 16 USAF PLANT 78 SURFACE DRAINAGE MAP 2-30
3- 1 DATA QUALITY OBJECTIVES THREE STAGE PROCESS 3-13
3-2 SOIL GAS SAMPLE LOCATIONS M-585 FRENCH DRAIN 3-24
3-3 M-585 SOIL GAS SURVEY NUMBER 2 GRID 3-26
3-4 LOCATIONS OF SOIL GAS SAMPLES, NDD, E-519, E-515 AND E-512 3-27
3-5 STAGE 2 SHALLOW SOIL BORING LOCATIONS 3-30
3-6 STAGE 2 DEEP STRATIGRAPHIC BORINGS AND GROUNDWATER
MONITORrNG WELLS 3-31
3-7 BORING LOG NDD-B1 AND WELL CONSTRUCTION DIAGRAM FOR P-4 3-32
xxi
P78-921/P78TOCjaril
02/18/92
LIST OF FIGURES
(Continued)
Figure Page
3-8 BORING LOG E-512B1 AND WELL CONSTRUCTION DIAGRAM FOR P-5 3-33
3-9 BORING LOG M-585B1 AND WELL CONSTRUCTION DIAGRAM FOR P-6 3-34
3-10 BORING LOG M-585B-2 AND WELL CONSTRUCTION DIAGRAM FOR P-7 ... 3-35
3-11 BORING LOG E-515B1 3-36
3-12 BORING LOG E-519B1 AND WELL CONSTRUCTION DIAGRAM FOR P-8 3-37
3-13 BORING LOG E-515B-2 AND WELL CONSTRUCTION DIAGRAM FOR P-9 3-38
3-14 COMBINED SOIL GAS SURVEYS 1 AND 2, M-585 FRENCH DRAIN SITE 3-46
3-15 STAGE 2 SURFACE WATER AND SEDIMENT SAMPLING LOCATIONS,
NORTH DRAINAGE DITCH 3-47
3-16 STAGE 2 SHALLOW SOIL BORING LOCATIONS E-512 SITE 3-48
3-17 STAGE 2 SHALLOW SOIL BORING LOCATION, FAUST VALLEY
DRAINAGE SITE 3-49
3-18 STAGE 2 SURFACE SEDIMENT AND WATER SAMPLE LOCATIONS,
BLUE CREEK 3-51
3-19 STAGE 2 SHALLOW SOIL BORING LOCATIONS, NORTH
DRAINAGE DITCH 3-52
3-20 STAGE 2 SHALLOW SOIL BORING LOCATIONS E-512 SITE 3-53
3-21 STAGE 2 SHALLOW SOIL BORING LOCATIONS, FAUST
VALLEY DRAINAGE SITE 3-54
3-22 STAGE 2 SHALLOW SOIL BORING LOCATIONS, BLUE CREEK 3-55
3-23 DEEP STRATIGRAPHIC BORING LOCATIONS, M-585 SITE 3-57
3-24 STAGE 2 DEEP STRATIGRAPHIC BORING LOCATION, NORTH
DRAINAGE DITCH 3-58
3-25 STAGE 2 DEEP STRATIGRAPHIC BORING LOCATION, E-512 SITE 3-59
3-26 STAGE 2 DEEP STRATIGRAPHIC BORING, E-519 SITE 3-60
3-27 STAGE 2 DEEP STRATIGRAPHIC BORINGS, E-515 SITE 3-61
3-28 GROUNDWATER MONITORING WELLS, USAF PLANT 78 3-62
3-29 STAGE 2 VEGETATION TRANSECT LOCATIONS 3-63
xxii
P7M21/P78TOCJOQ11
02/18/92
LIST OF FIGURES
(Continued)
Figure Page
3-30 STAGE 2 AQUATIC SAMPLE LOCATIONS 3-65
3- 31 STAGE 2 SMALL MAMMAL TRAPPING LOCATIONS 3-66
4- 1 VEGETATION TRANSECT LOCATIONS 4-2
4-2a UPPER SHALLOW GROUNDWATER ZONE, WATER TABLE MAP, 1989 4-8
4-2b UPPER SHALLOW GROUNDWATER ZONE, WATER TABLE MAP, 1991 4-9
4-3a DEEPER SHALLOW GROUNDWATER ZONE, WATER TABLE MAP, 1989 4-12
4-3b DEEPER SHALLOW GROUNDWATER ZONE, WATER TABLE MAP, 1991 4-13
4-4 LOCATION OF HYDROGEOLOGIC CROSS-SECTIONS D-D' & E-E' 4-15
4-5 HYDROGEOLOGIC CROSS-SECTION D-D' NORTH DRAINAGE DITCH E-512,
E-519, AND E-515 4-16
4-6 STAGE 2 SURFACE WATER AND SEDIMENT SAMPLE RESULTS,
NORTH DRAINAGE DITCH 4-19
4-7 STAGE 2 SHALLOW SOIL BORING SAMPLE RESULTS,
NORTH DRAINAGE DITCH 4-22
4-8 STAGE 2 DEEP STRATIGRAPHIC BORING SAMPLE LOCATIONS AND
RESULTS, NORTH DRAINAGE DITCH AND BUILDING E-519 4-24
4-9 STAGE 2 GROUNDWATER SAMPLE RESULTS,
NORTH DRAINAGE DITCH AND BUILDING E-519 4-26
4-10 LOCATION OF SOIL GAS SAMPLES, NDD, E-519,
E-515, AND E-512 4-27
4-11 TRICHLOROETHANE ION FLUX MAP, SOIL GAS SURVEY,
NORTH DRAINAGE DITCH 4-34
4-12 TRICHLOROETHYLENE ION FLUX MAP, SOIL GAS SURVEY,
NORTH DRAINAGE DITCH 4-35
4-13 TETRACHLOROETHENE ION FLUX MAP, SOIL GAS SURVEY,
NORTH DRAINAGE DITCH 4-36
4-14 HYDROCARBONS ION FLUX MAP, SOIL GAS SURVEY,
NORTH DRAINAGE DITCH 4-37
4-15 LOCATION OF THE NORTH PLANT 78 GROUNDWATER CONTAMINANT
PLUME 4-39
4-16 STAGE 2 SURFACE SEDIMENT AND WATER SAMPLE RESULTS,
E-512 DRAINAGE DITCH 4-41
xxiii
P78-921/P7STOCJOOV
02/18/92
LIST OF FIGURES
(Continued)
Figure Page
4-17 STAGE 2 DEEP STRATIGRAPHIC BORING SAMPLE RESULTS
E-512 DRAINAGE DITCH 4-45
4-18 STAGE 2 GROUNDWATER SAMPLE RESULTS
E-512 DRAINAGE DITCH 4-47
4-19 STAGE 2 SURFACE SEDIMENT SAMPLE ANALYTICAL RESULTS,
FAUST VALLEY DRAINAGE 4-53
4-20 STAGE 2 SHALLOW SOIL BORING LOCATION,
FAUST VALLEY DRAINAGE 4-56
4-21 STAGE 2 DEEP BORING SAMPLE RESULTS,
FAUST VALLEY DRAINAGE 4-58
4-22 STAGE 2 GROUNDWATER SAMPLE RESULTS,
FAUST VALLEY DRAINAGE AND BUILDING E-515 4-60
4-23 GEOLOGIC/HYDROGEOLOGIC CROSS-SECTIONS E-E',
M-585 FRENCH DRAIN SITE 4-68
4-24 STAGE 2 DEEP STRATIGRAPHIC BORING RESULTS,
M-585 FRENCH DRAIN 4-70
4-25 STAGE 2 GROUNDWATER ANALYTICAL RESULTS,
M-585 FRENCH DRAIN 4-72
4-26 SOIL GAS SAMPLE LOCATION M-585 FRENCH DRAIN 4-76
4-27 M-585 SOIL GAS SURVEY NUMBER 2 GRID 4-77
4-28 SOIL GAS SURVEY, TRICHLOROETHYLENE (TCE) ION FLUX,
M-585 FRENCH DRAIN SITE 4-79
4-29 SOIL GAS SURVEY, TRICHLOROETHANE (TCA) ION FLUX,
M-585 FRENCH DRAIN SITE 4-81
4-30 SOIL GAS SURVEY, TETRACHLOROETHYLENE (PCE) ION FLUX,
M-585 FRENCH DRAIN SITE 4-82
4-31 SOIL GAS SURVEY, CHLOROFORM ION FLUX,
M-585 FRENCH DRAIN SITE 4-83
4-32 STAGE 2 SOIL GAS SURVEY RESULTS M-585 FRENCH DRAIN SITE 4-85
4-33 LOCATION OF THE GROUNDWATER CONTAMINANT PLUME, M-585 4-87
4-34 STAGE 2 SURFACE SAMPLE RESULTS, BLUE CREEK NORTH 4-88
xxiv
P78-921/P78TOCJOK
02/18/92
LIST OF FIGURES
(Continued)
Figure Page
4-35 STAGE 2 SURFACE SAMPLE RESULTS, BLUE CREEK SOUTH 4-89
4-36 STAGE 2 SHALLOW SOIL BORING LOCATIONS, BLUE CREEK 4-95
4-37 STAGE 2 AQUATIC SAMPLE LOCATIONS BLUE CREEK 4-97
4-38 STAGE 1 AND STAGE 2 SAMPLE RESULTS, BLUE CREEK NORTH 4-156
4-39 STAGE 1 AND STAGE 2 SAMPLE RESULTS, BLUE CREEK SOUTH 4-157
4-40 POTENTIAL HUMAN AND LIVESTOCK RECEPTORS; SPRING 1989 4-194
4-41 SURFACE WIND ROSES FOR 8:00 AM AND 4:00 PM AT
THIOKOL PLANTSITE 4-195
4-42 LAND USE MAP USAF PLANT 78 AND VICINITY 4-196
XXV
LIST OF ACRONYMS
ac-ft/yr acre feet/yr
AFESC Air Force Engineering and Services Center
ARAR Applicable or Relevant and Appropriate Requirements
C-4 designation for Trident 1 missile
CERCLA Comprehensive Environmental Response, Compensation and Liability Act
cfs cubic foot/second
DEQ ' Defense Environmental Quality Program Policy Memorandum
DOD Department of Defense
E-512 E-512 Drainage Ditch
EM electromagnetic
EPA United States Environmental Protection Agency
ES Engineering Science, Inc.
ESE Environmental Science & Engineering, Inc.
FS Feasibility Study
ff foot/feet
FVD Faust Valley Drainage Course
IRP Installation Restoration Program
L liter
M-508 M-508 X-O-MAT Discharge Area
M-585 M-585 French Drain Site
M-636 M-636 X-O-Mat Discharge Area
mg/L mg/liter
MCL maximum containment levels
MCLGs maximum containment level guidelines
MX Peacekeeper missile
NDD North Drainage Ditch
NGVD National Geodetic Vertical Datum
NIPDWR National Interior Primary Drinking Water Regulations
NOAA National Oceanographic and Atmospheric Agency
NSDWR National Secondary Drinking Water Regulations
PID photoionization detector
Plant 78 USAF Plant 78
ppb parts per billion
ppm parts per million
RA Risk Assessment
RCRA Resource Conservation and Recovery Act
RI Remedial Investigation
SARA Superfund Amendments Reauthorization Act
SCS Soil Conservation Service
SSTEP Sanitary Sewage Treatment Evaporation Pond
TDS total dissolved solids
Thiokol Thiokol Corporation
Toe top of casing
U.S. United States
USAF United States Air Force
/tg microgram
xxvi
P78-921/P78TOCjBmi
02/13/92
EXECUTIVE SUMMARY
INTRODUCTION
U.S. Air Force (USAF) Plant 78 (Plant 78) is located in Box Elder County, Utah, approximately 35 miles west
of Brigham City (Plate 1) (Figure E-1). The plant site is part of a complex of facilities operated by The Thiokol
Corporation (Thiokol) (Figure E-2). USAF Plant 78, constructed in 1962, is engaged in the mixing, casting, and
final assembly of solid propellant chemicals into rocket motors. As a part of the solid propellant rocket motor
production, components, such as nozzles and motor housings, have also been fabricated at Plant 78. The plant
site encompasses 1,550 acres and is characterized by open areas between the production buildings, with the
greatest concentration of facilities located around Buildings 508 and 517. The area surrounding the plant is
mostly ranch land and unoccupied natural terrain.
PHASE I INSTALLATION RESTORATION PROGRAM
Engineering Science, Inc. (ES) was retained by the Air Force Engineering and Services Center (AFESC) to
conduct the Phase I records search under the USAF Installation Restoration Program (IRP). This records search
began in December 1983, and was completed in March 1984, resulting in the identification of three disposal sites
and a drainage ditch with potential for contaminant migration. These four sites were prioritized for Stage 1 field
work conducted under Phase II of the IRP.
PHASE n STAGE 1 INSTALLATION RESTORATION PROGRAM
During a Phase II pre-survey meeting and site inspection (September 26,1985), four additional areas of concern
were identified. The Plant 78 Stage 1 work by Environmental Science & Engineering, Inc. (ESE) began in the
fall of 1986. The eight individual sites were investigated to assess potential occurrence and extent of
contamination, (Figure E-3). After the imtial evaluation, two prioritized Stage 1 sites became Resource
Conservation and Recovery Act (RCRA) sites. These sites were prioritized in the Spring of 1987 prior to the
completion of the Stage 1 investigation. These two RCRA sites are currently being investigated by Thiokol.
Surface water and surface sediment samples were collected and analyzed, momtoring wells were installed and
sampled, soil borings were drilled, sampled, and analyzed, and an EM-31 geophysical survey was conducted.
Additional soil borings (resampling) and another monitoring well (P-3) was installed during the winter of 1988
under an extended Stage 1 effort. The results of all Stage 1 work were presented in the final report submitted
by ESE to the USAF in September 1989. The Stage 1 work resulted in the assignment of each site mto one of
three categories: (1) requiring no further action; (2) requiring further Phase II investigation; or (3) requiring
remedial action. As a result of the Phase II Stage 1 investigations, six of the eight sites were selected for
additional investigation under the Phase II Stage 2 of the IRP program.
xxvii
xxviii
t
Tho Thiokol Corporation
Wasatch Operations
B
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AIR FORCE PLANT 78
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Figure E-2
FACILITY SITE PLAN
SOURCE: THIOKOL FACILITY DOCUMENT
INSTALLATION RESTORATION
PROGRAM USAF .PLANT 78
700 1400 Feet
APPROX. SCALE IN FEET
Figure E-3
PLANT 78 GENERAL LOCATION MAP
SOURCE FACILITY DOCUMENTS; ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
XXX
P78-921/P78TOCJraa
02/13/92
PHASE II STAGE 2 INSTALLATION RESTORATION PROGRAM
The IRP objectives of the Phase II Stage 2 investigation were to conduct field investigations to verify Stage 1
results, define the magnitude and migration potential of contaminants, perform a baseline risk assessment, and
develop preliminary and detailed alternatives for remedial action. ESE conducted the Phase II Stage 2 effort.
The six sites selected for Phase II investigation were:
1. North Drainage Ditch (NDD); e ' ^
2. E-512 Drainage Ditch (E-512);
3. Faust Valley Drainage Course (FVD); f ^
4. M-585 French Drain Site (M-585); y
5. Blue Creek (BC); and ^ \ Or-
6. Sanitary Sewage Treatment Evaporation Pond (SSTEP). sj \, (r; ^ e'
The SSTEP was eliminated from Stage 2 due to the low levels of contamination detected in Stage 1, the low
probability of industrial contamination, and the decision to concentrate investigation resources on sites with
higher contamination probabilities.
In December 1988, two additional sites, E-515 and E-519, were added to the Stage 2 investigation. E-519 is
included within the NDD site and E-515 is included in the FVD site. Although E-519 and E-515 are separate
sites, shallow groundwater found at both sites is probably interconnected. Neither of these sites were investigated
under Stage 1. Both sites contain "acid drains" which received laboratory wastewater in past operations. Drilling
and sampling of a deep soil boring and installation of a groundwater monitoring well was recommended for each
site.
Stage 2 work began in December 1988 and continued through March 1990. Six groundwater monitoring wells
were installed and a number of surface, shallow soil, surface water, and groundwater samples were collected.
SUMMARY OF STAGE 1 AND STAGE 2 INVESTIGATIONS
North Drainage Ditch
Petroleum hydrocarbon wastes, solvents, and wastewater have been discharged into the surface drainage ditches
(collectively called the North Drainage Ditch) surrounding Buildings E-512, E-516, E-517, and M-508. The
Stage 1 investigation involved the collection of surface water and sediment samples and shallow (25 foot) soil
boring samples. Petroleum hydrocarbons, halomethanes, volatile organohalogens, and metals were detected in
NDD surface water and petroleum hydrocarbons and metals were detected in surface sediments. Soil boring
samples contained detectable levels of petroleum hydrocarbons and methylene chloride. After the initial Stage 1
field work for the NDD was completed, one momtoring well, P-3, was installed but not sampled under an
extended Stage 1 field effort. The NDD was recommended as a category 2 site requiring additional monitoring
under a Stage 2 investigation.
xxxi
P78-921 /rarOCjccrii
02/13/92
Stage 2 investigations included a soil gas survey of the site area; two surface water and sediment samples; seven
shallow borings (NDD-SB1 through NDD-SB7) drilled to depth of 8 feet and sampled at two intervals; four soil
samples collected from deep boring NDD-B1 (NDD-B1A through NDD-B1D); six soil samples collected from
deep boring E-519B1 (E-519B1A through E-519B1F); groundwater samples collected from momtoring wells Pj3_
and P-8; and aquifer testing to determine aquifer characteristics for momtoring wells P-3 and P-8. Figure E-4
shows Stage 1 and Stage 2 sampling locations for NDD.
E-512 Drainage Ditch
This ditch was used for disposing paint booth water and chromated rust inhibitor prior to 1980. Metals and
petroleum hydrocarbons were detected in a composite sediment sample and 1,1-dichloroethane
1,1,1-trichloroethane, 1,1-dichloroethene, trichloroethylene, tetrachlorethene, bromoform, and chloroform were
detected in a E-512 surface water sample under Stage 1 investigations. E-512 was recommended as a category 2
site requiring additional study under a Stage 2 investigation.
Stage 2 investigations included: a soil gas survey of the site area; one composite surface sediment and surface
water sample (E-512SS1 and E-512SWS1) collected from the E-512 ditch; three shallow borings (E-512SB1,
E-512SB2, and E-512SB3) to depths of approximately 8 feet with two samples each; one deep boring (E-512B1)
with five soil samples (E-512B1A through E-512B1E); one groundwater sample from momtoring well P-5; and
aquifer testing to determine aquifer characteristics for monitoring well P-5. Figure E-5 shows Stage 1 and
Stage 2 sampling locations for E-512.
Faust Valley Drainage Course
The FVD is a major surface drainage feature on Plant 78. Phase 1 IRP reported that the FVD received paint
booth water and chromated rust inhibitor disposed in the smaller E-512 tributary (ES, 1984). Field observations
conducted under Stage 1 revealed that the E-512 ditch does not discharge into the FVD.
During the Stage 1 investigation, monitoring well P-1 was constructed in boring 200B and a water sample was
collected for chemical analysis. Organic contaminants were not detected in groundwater from this sample.
Upgradient and downgradient sediment samples and soil samples collected from boring 200B at the FVD
contained petroleum hydrocarbons. The FVD was recommended as a category 2 site requiring additional study
under a Stage 2 investigation.
Stage 2 investigations included: a soil gas survey of the site area; the sampling of six surface sediment sites
(FVD-SS1, FVD-SS2, FVD-SS3, FVD-SS5, FVD-SS6, and FVD-SS8) (surface water samples were not coUected
at FVD, because of lack of discharge); one shaUow boring (FVD-SB1) driUed to a depth of 8 feet and sampled
at two intervals; drilling and sampling of two deep borings (E-515B1 and E-515B2); groundwater samples
xxxii
P78 STAGE 2 02/91
NDD-SB5
50 G
25 A & AR
NDD-SB6
NDD-SB4
NDD-SS2
N0D-SW2
25 C
NDD-517
25 CR
NDD-516
WELL P-3
(bor« 200C)
NDD-SB3
NDD-SB2
ND0-SS1
NDD-SW1
SANITARY SEWAGE TREATMENT
AND EVAPORATION POND
NDDIB
NDD-SB1
NDD-B1 (WELL P-4)
25 B & BR R AVE.
8C-5WS15 LOCATED ONE MILE
UP GRADIENT
ON BLUE CREEK
,BC-SWSl4
BC/ND
NDD-SB7
BC-SWS13
ND/BC
>v, Co^Oc ^
•7-0 S^il.
LEGEND
A STAGE 1 BORING LOCATIONS
• STAGE 1 SOIL AND/OR SURFACE WATER SAMPLES
• STAGE 1 GROUND WATER SAMPLES
A STAGE 2 BORING LOCATIONS
• STAGE 2 SOIL AND/OR SURFACE WATER SAMPLES
• STAGE 2 GROUND WATER MONITORING WELLS
• STAGE 1 AND 2 SOIL AND/OR SURFACE WATER SAMPLES
STAGE 2 VEGETATION TRANSECTS
+ AQUATIC SAMPLING
(fa\ ' N
0 100 200 300 400 500
Figure E-4
LOCATION OF STAGE 1 AND
STAGE 2 SAMPLE LOCATIONS
NORTH DRAINAGE DITCH
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF .PLANT 78
xxxiii
P78 STAGE 2 07/91
E-512-SB3 E-5I2-SW1 E-512-SS1 E-512-SB2 E-512 E-512-SB1
WELL P-5 (bor« E-512-B1)
SANITARY SEWAOC TREATMENT
ANO EVAPORATION PONO
R AVE.
LEGEND
A STAGE 1 BORING LOCATIONS
• STAGE 1 SOIL AND/OR SURFACE WATER SAMPLES
• STAGE 1 GROUND WATER SAMPLES
A STAGE 2 BORING LOCATIONS
• STAGE 2 SOIL AND/OR SURFACE WATER SAMPLES
• STAGE 2 GROUND WATER MONITORING WELLS
• STAGE 1 AND 2 SOIL AND/OR SURFACE WATER SAMPLES
STAGE 2 VEGETATION TRANSECTS
+ AQUATIC SAMPLING
N
0 100 200 SOO 400 SOO
Figure E-5
STAGE 1 AND STAGE 2
SAMPLE LOCATIONS
E-512 DRAINAGE DITCH
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
xxxiv
P78-921/P78TOCJODIV
02/13/92
collected from momtoring wells P-1 and P-9; and aquifer testing to determine aquifer characteristics for
monitoring wells P-1 and P-9. Figure E-6 shows Stage 1 and Stage 2 sampling locations for the FVD.
M-585 French Drain
The French Drain (M-585) site includes the french drain and surrounding area. The french drain consists of
a 4-inch diameter gravity flow line leading westward from Building M-585 and draining into a subsurface pit.
M-585 has received laboratory rinsewater containing waste propellants, acids, alkalies, and various solvents,
including acetone, methyl ethyl ketone, and benzene. Use of this drain was discontinued in 1973.
Detectable levels of petroleum hydrocarbons and methylene chloride were reported in Stage 1 soil boring
samples collected at M-585. Chloroform, methylene chloride, 1,1,1-trichloroethane, and toluene were detected
at low concentrations in groundwater from momtoring well P-2. M-585 was recommended as a category 2 site
requiring additional study under a Stage 2 investigation.
Stage 2 investigations included: a soil gas survey of the site area; the drilling of deep borings (M-585B1 and
M-585B2) with four soil samples (M-585B1A through M-585B1D) collected from M-585B1 and three soil
samples (M-585B2A through M-585B2C) collected from M-585B2; groundwater sampling of momtoring wells
P-2, P-6, and P-7; and aquifer testing to determine aquifer characteristics for momtoring wells P-2, P-6, and P-7.
Figure E-7 shows Stage 1 and Stage 2 sampling locations for the M-585 site.
Blue Creek
Blue Creek, a perennial stream, flows adjacent to the western boundary of Plant 78. Sampling under Stage 1
involved both surface water and sediment samples. Petroleum hydrocarbons were detected in all the Blue Creek
surface sediment samples. Surface water samples contained detectable concentrations of petroleum
hydrocarbons, bromoform, chloromethane, methylene chloride, trichloroethylene, and benzene. Blue Creek was
recommended as a category 2 site requiring additional study under a Stage 2 investigation.
Stage 2 investigations included: 2 rounds of surface water and sediment sampling conducted (15 sites for surface
water [BC-SWS1 through BC-SWS15], 7 sites for surface sediment [BC-SS1 through BC-SS7] during Round 1
and 9 sites for surface water [BC-SW3 through BC-SW10], 9 sites for surface sediment [BC-SS3 through
BC-SS10] during Round 2); 6 shallow borings (BC-SB1 through BC-SB6) drilled to a depth of 8 feet with two
samples collected from each boring; and sampling of the invertebrate aquatic ecosystem at tliree Blue Creek sites
(to estimate diversity and populations). Figures E-8 and E-9 show Stage 1 and Stage 2 sampling locations along
Blue Creek.
xxxv
P78 STAGE 2 7/91
WELL P-1
(bora 200B)
FVD-SS8
FVO/NE
BLUE CREEK
LEGEND
A STAGE 1 BORING LOCATIONS
• STAGE 1 SOIL AND/OR SURFACE WATER SAMPLES
• STAGE 1 GROUNO WATER SAMPLES
• STAGE 2 BORING LOCATIONS
• STAGE 2 SOIL ANO/OR SURFACE WATER SAMPLES
• STAGE 2 GROUNO WATER MONITORING WELLS
• STAGE 1 ANO 2 SOIL AND/OR SURFACE WATER SAMPLES
"~ STAGE 2 VEGETATION TRANSECTS
O 100 100 300 400 900
[] M-E89
Figure E-6
STAGE 1 AND STAGE 2
SAMPLE LOCATIONS
FAUST VALLEY DRAINAGE
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
xxxvi
P78 STAGE 2 7/91
LEGEND
A STAGE 1 BORING LOCATIONS
• STAGE 1 SOIL AND/OR SURFACE WATER SAMPLES
• STAGE 1 GROUND WATER SAMPLES
• STAGE 2 BORING LOCATIONS
Q STAGE 2 SOIL AND/OR SURFACE WATER SAMPLES
• STAGE 2 GROUNO WATER MONITORING WELLS
• STAGE 1 AND 2 SOIL AND/OR SURFACE WATER SAMPLES
N
W
0 100 200 300 400 500 1000 fMt
Figure E-7
STAGE 1 AND STAGE 2 SAMPLE
LOCATIONS
M-585 FRENCH DRAIN:
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
xxxvii
P78 STAGE 2 7/91
K-SWS1S LOCArco ONE MLE
ur CRADICNT
OH BLUE CHEEK
_BC-SWSM
BC/ND
LEGEND
STACC 1 tORINC LOCATIONS
3TAQC I SOU. AND/OR SURFACE WATER SAMPLES
STACC 1 CROUNO WATER SAMPLES
STAGE 2 IORINS LOCATIONS
STACC 2 SOIL AND/OR JURfACC WATCR SAMPLES
STACC 2 GROUND WATER UOMTORINS WILLS
STAOC 1 AND 2 SOL AHD/OR SURFACE WATCR SAMPLES
STACC 2 VEGETATIOH TRANSCCTS
-|- AOUATIC SAUPUNS
Figure E—8
STAGE 1 AND STAGE
BLUE CREEK, NORTH
2 SAMPLE LOCATIONS INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
SOURCE: ESE, 1991.
P78 STAGE 3 7/91
Figure E-9
STAGE 1 AND STAGE 2
BLUE CREEK, SOUTH
SAMPLE LOCATIONS INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
SOURCE: ESE, 1991.
P78-921/P7OTOC.X1
02/13/92
Sanitary Sewage Treatment Evaporation Pond
Domestic sewage from administrative and manufacturing facilities at the north end of Plant 78 is collected and
treated at the SSTEP. No industrial wastes were reported to have been disposed in the sanitary sewer.
Petroleum hydrocarbons were detected in a surface sediment sample collected during Stage 1. No other
compounds were detected.
The SSTEP site was deleted from Stage 2 due to the low levels of contamination detected in Stage 1, the low
probability of industrial chemical contamination, and the decision to concentrate investigative resources on sites
with higher contamination probabilities.
SIGNIFICANCE OF FINDINGS
To evaluate the quality of groundwater and surface water at Plant 78, federal (EPA, 1991) and State of Utah
(1990, 1991) water quahty standards (e.g. maximum contaminant levels [MCLs]) are used to indicate the quality
of the water relative to drinking water. These drinking water standards are not, however, directly applicable to
the samples collected at Plant 78. Groundwater in the vicinity of Plant 78 is unsuitable for use as drinking water
either at the installation or within the immediate vicinity due to a naturally high dissolved solids content.
Shallow groundwater and surface water at Plant 78 and in Blue Creek are non-potable due to high naturally
occuring TDS. Results of the groundwater investigations have concluded that there appears to be no connection
between the shallow groundwater aquifer(s) at the site and any usable groundwater aquifers. Sodium, potassium,
and chloride ions that make up the naturally occurring TDS concentrations are not removed by conventional
water treatment (Clark, Viessman, and Hammer, 1971). The shallow groundwater at the site, therefore, meets
EPA requirements for a Class IIIB groundwater (EPA, 1986d and 1988d). For Class III groundwaters, drinking
water standards are not applicable or relevant and appropriate (Code of Federal Regulations 55FR page 8732).
Table E-1 lists compound detections by sample media at each site investigation.
Non Site-specific Ecological Findings
Vegetative cover was measured with ten 50-meter (m) transects across Plant 78 (Figure E-10). Total herbaceous
cover for Plant 78 was estimated at 32 percent of the surface area, a relatively low total cover in comparison to
the surrounding area. Because of ongoing activities at the plant and for fire prevention, vegetation must be cut
to a low height. This, in combination with the low precipitation and use of herbicides, has resulted in a low
percentage of herbaceous cover and low species diversity at Plant 78.
A great number of waterfowl and water associated bird species are potential visitors to Plant 78. This is due
to its proximity to Bear River Migratory Bird Refuge, managed by the U.S. Fish and WUdlife Service (USFWS)
and the State of Utah Waterfowl Management areas that are located within five to ten miles south of Plant 78.
xl
P78/P78TB-1.1
02/14/92
Table E-1. Compound Detection by Medium and Investigation Site, Stage 1 and/or 2 (Page 1 of 3).
SAMPLE MEDIA
Site (compound) Surface Water Surface Sediment Soils Groundwater
Stage 1 Stage 2 Stage 1 Stage 2 Stage 1 Stage 2 Stage 1 Stage 2
NDD (includes E-519)
Petroleum Hydrocarbons XX X X X X X
Bromodichloromethane X
Bromoethane X
Chlorobenzene X
Chloroform XX X
Chloromethane X X
Dibromochloromethane X
Dichlorobenzene X
1,1-Dichloroethane XX X
1.1- Dichloroethylene XX X
1,1,1-Trichloroethane XX X
1.2- Dichloroethane X X
1,2-Dichloropropane X
Methylene Chloride XX X
Tetrachloroethene XX X
Trichloroethylene X X
Bromoform
Diethylphthalate X
Di-N-Butylphthalate X
Bis (2-ethylhexyl) phthalate X
Butyl Benzylphthalate X
Methyl Chloride X
E-512
Chloroform XX X
1,1-Dichloroethane X X
1.1- Dichloroethylene X X
1.2- Dichloroethane X
1,1,1-Trichloroethane XX X
Petroleum Hydrocarbons X XX X
Bromoform X
Trichloroethylene X
FVD (includes E-515)
1,1,1-Trichloroethane X X
Methyl Chloride X
Petroleum Hydrocarbons X X
Trichloroethylene X
Vinyl Chloride X
Chlorobenzene X
xii
P78/P78TE-1.2
02/14/92
Table E-1. Compound Detection by Medium and Investigation Site, Stage 1 and/or 2 (Page 2 of 3).
SAMPLE MEDIA
Site (compound) Surface Water Surface Sediment Soils Groundwater
Stage 1 Stage 2 Stage 1 Stage 2 Stage 1 Stage 2 Stage 1 Stage 2
FVD (includes E-515)
(Continued)
Chloroform X
Chloromethane X
Dichlorobenzene X
1,1-Dichloroethane X
1.1- Dichloroethylene X
1.2- Dichloroethane X
1,2-Dichloropropane X
Tetrachloroethene X
Acetophenone X
Bis (2-ethylhexyl) phthalate X
Butyl Benzylphthalate X
M-585
Trichloroethylene X X
Benzene X
Toluene X X
Chlorobenzene X
Chloroform X X
1,1-Dichloroethane X
1.1- Dichloroethylene X
1.2- Dichloroethane X
t,l,2-Dichloroethene X
1,1,1-Trichloroethane X X
Trichlorofluromethane X
Vinyl Chloride X
Petroleum Hydrocarbons X
Methylene Chloride X X
Tetrachloroethene X
BLUE CREEK
Xylenes X
2-Chloroethylvinyl Ether X
Chloroform X
Chloromethane X X
1,2-Dichloropropane X
Tetrachloroethene X
1.1.1- Trichloroethane X XX
1.1.2- Trichloroethane X
Vinyl Chloride X
xlii
P78/P78TE-13
02/14/92
Table E-1. Compound Detection by Medium and Investigation Site, Stage 1 and/or 2 (Page 3 of 3).
SAMPLE MEDIA
Site (compound) Surface Water Surface Sediment Soils Groundwater
Stage 1 Stage 2 Stage 1 Stage 2 Stage 1 Stage 2 Stage 1 Stage 2
BLUE CREEK
(Continued)
Petroleum Hydrocarbons X XX
Bromoform X
Benzene X
Trichloroethylene X
Methylene Chloride X
1,2-Dichloroethane X
Source: ESE, 1991.
xliii
P78 STAGE 2 05/91 PFIG 3-29
VEGETATION
TRANSECT #9 VEGETATION
TRANSECT #10
Figure E—10
STAGE 2 VEGETATION TRANSECT LOCATIONS
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P7M21/P78TOCjdv
02/13/92
However, the low, monotypic vegetation on the plant limits the probable resident species to scavengers, such as
gulls, ravens, and crows. Notable exceptions to the rule may be cliff swallows and bank swallows.
The same factors limiting the diversity of resident birds on Plant 78 also restrict the number and variety of
mammals on base. Four nights of small mammal trapping yielded only two species of small mammal, the deer
mouse and the brush mouse (Figure E-ll).
Non Site-specific Hydrogeology Results
Shallow groundwater at Plant 78 is probably dependent upon facUity input, which maybe responsible for the
upper shaUow groundwater zones monitored by wells P-3, P-5, P-6, and P-7. Water in aU of these momtoring
wells occurs at depths less than the reported 150 foot depth for the regional aquifer in Blue Creek VaUey (ES,
1984).
Upper shaUow groundwater flow at Plant 78 is in the west-southwest direction at M-585 with an estimated
hydrauhc gradient of 0.026 foot/foot between monitoring wells P-6 and P-7 (Figure E-12a and E-12b).
Figure E-12a shows groundwater elevation contours based on 1989 groundwater measurements. Figure E-12b
shows groundwater contours based on 1991 groundwater measurements.
Figure E-12b was constructed with groundwater elevations measured by Thiokol in November 1991 for weU P-3
and P-5. Both of these monitoring weUs indicate substantial decreases in water elevation for the upper shaUow
groundwater zone over 1989 measurements. Monitoring weU P-3 shows a decrease ot^LMeet. Monitoring
well P-5 shows a decrease offl0.17 feet. As discussed above, the upper shaUow groundwater zone at Plant 78
shows a possible influence between facUity waste-water disposal and possible groundwater mounding. Since
construction of the Plant 78 waste-water treatment facility in 1989, waste-water previously disposed into surface
drainage ditches and subsurface dry weUs is now coUected, treated, and released (under state permit) to Blue
Creek. Groundwater elevations measured in 1991 indicate that the possible groundwater mound at the facUity
is decreasing. The estimated hydrauhc gradient for the NDD and E-512 area is from 0.00525 foot/foot at
monitoring weU P-5 to 0.018 foot/foot at monitoring weU P-3. These gradients were calculated measuring the
weU point perpendicular to the groundwater contour interval. This variance in hydraulic gradient across the plant
is indicative of the heterogeneous nature of the upper shaUow groundwater zone at Plant 78.
The deeper shaUow groundwater zone at Plant 78 is unconfined, heterogeneous, and transversely isotropic.
Monitoring wells P-1, P-8, and P-9 are aU completed in this deeper shaUow groundwater zone, which may be part
of the regional Blue Creek VaUey aquifer. However, monitoring weU P-2 may be completed in an isolated
perched water zone above the level of the deeper shaUow groundwater zone. Monitoring weUs P-1, P-8, and P-9
(FVD and NDD sites) iUustrate water depths that decrease from monitoring weU P-1 (upgradient) to
xiv
P78 STAGE 2 05/91
Figure E-1 1
STAGE 2 SMALL MAMMAL TRAPPING LOCATIONS
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P7B STAGE 2 05/91 PFIG4-2
0100 300 500 1000 f..t
LEGEND
A*1° GROUNDWATER CONTOUR
INFERRED WHERE DASHED
Figure E-1 2a
UPPER SHALLOW GROUNDWATER
ZONE, WATER TABLE MAP, 1989
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
xlvii
P78 STAGE 2 05/91 PrtG4-2b
0100 300 300 1000
LEGEND
A*"10 GROUNDWATER CONTOUR
INFERRED WHERE DASHED
Figure E-1 2b
UPPER SHALLOW GROUNDWATER
ZONE, WATER TABLE MAP, 1991
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
xlviii
P78-921/P78TOCjllix
02/13/92
groundwater monitoring well P-8 (downgradient), which is counter to the regional trend, and may be influenced
by facUity wastewater disposal.
The deeper shaUow groundwater flow at Plant 78 is to the east at momtoring wells P-8, P-9, and P-1
(Figure E-13a). The flow direction at momtoring weU P-2 is unknown; however, based upon water elevations,
if it is in the same water bearing zone as P-1, P-8, and P-9, the suggested direction of flow would be toward the
northeast. Both of these flow directions in the deeper shaUow water zone are localized reversals to the
predominately west-southwest flow direction observed for the upper shaUow water zone. This reversal is possibly
due to mounding caused by wastewater disposal. The estimated hydrauhc gradient between momtoring wells
P-8 and P-9 is 0.0043 foot/foot and between momtoring wells P-9 and P-1 0.0129 foot/foot.
Figure E-13b shows groundwater elevation contours based on 1991 groundwater measurements. The most
striking difference between the 1989 (Figure E-13a) and 1991 measurements is the large decrease in the
suspected groundwater mound associated with the Plant 78 facilities. WeU P-1 shows an increase of 34.83 feet
since instaUation in 1988. WeU P-9 shows a decrease of 5.20 feet and WeU P-8 shows a decrease of 4.23 feet
since instaUation in 1989.
The 1989 measurements (Figure E-13a) indicates a localized eastward reversal in the predominately west regional
groundwater flow direction, the 1991 measurements indicate that this local reversal has greatly diminished
(Figure E-13b). Hydrauhc gradient calculations of the 1991 data indicate that hydraulic gradients associated with
the possible groundwater mound have also decreased.
The possible groundwater mounding observed at Plant 78 and the aparent local eastward reversal in the regional
west groundwater flow direction observed in the deeper shaUow groundwater zone, are suspected to be caused
by Plant 78 wastewater disposal. The 1991 groundwater elevation measurments indicate that this possible mound
is decreasing. Although weU P-1 static water level is increasing, the net effect of this water level rise along with
the decreases in static water levels observed in weU P-9 and P-8 is to counter the aparent local reversal in
groundwater flow observed in the deeper shaUow groundwater zone at Plant 78 (Figure E-13b).
In 1989, Plant 78 industrial wastewater surface discharges along the Northern end of Plant 78 were routed to a
wastewater treatment plant located near the intersection of R Avenue and 200 Street. The plumbing of these
surface water discharges may have resulted in a decreased water levels in momtoring wells observed during 1991.
Wastewater is now treated to acceptable discharge standards and released to Blue Creek under State of Utah
Authorization to Discharge Permit No. UT0024805.
xlix
P76 STAGE 2 05/91 PFIG4-3
GROUNDWATER FLOW
DIRECTION
0 ICO MO 500 1000 (••! — 4360 — GROUNDWATER CONTOUR
INFERRED WHERE DASHED
Figure E-13a
DEEPER SHALLOW GROUNDWATER
ZONE, WATER TABLE MAP, 1989
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
l
P7B STAGE 2 05/«1 PFIC4-JB
WELL P-1
4346.15 ft MSL'
LEGEND
GROUNDWATER CONTOUR
INFERRED WHERE DASHED
Figure E— 1 3b
DEEPER SHALLOW GROUNDWATER
ZONE, WATER TABLE MAP, 1991
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
li
P78-921/P78TOC.LU
02/13/92
SITE SPECIFIC RESULTS
NORTH DRAINAGE DITCH SITE
Soil Samples
Methylene chloride was detected sporadically in Stage 1 soil samples collected from borings adjacent to Buildings
E-516 and E-517. Methylene chloride was detected at low concentrations in two soil samples collected from
shallow borings NDD-SB1 and NDD-SB2, and from a soil sample collected at 36 feet in boring E-519B1 during
Stage 2 sampling.
Bis (2-ethylhexyl) phthalate was detected at 137 feet, 17 feet, and in the method blank in E-519B1. Butyl
benzylphthalate, diethylphthalate and di-n-butylphthalate were also detected in E-519B1. These constituents are
commonly laboratory or field contaminants.
Trichloroethylene was detected sporadically in Stage 1 soil samples collected at the NDD. Trichloroethylene was
detected only at 171 feet in E-519B1 during Stage 2 sampling.
Surface Sediment
Relatively high levels of petroleum hydrocarbons detected by Stage 1 sampling in surface sediment samples near
Buildings E-516 and E-517 suggest contaminant contribution from either or both of these potential sources.
Petroleum hydrocarbons were only detected in one sample during Stage 2 (NDD-SS2) and review of the method
blank for this analysis reveals that the concentration observed is not reliable and could be due to laboratory
contamination.
The conflict between Stage 1 and Stage 2 sampling results may be due to individual sample variability between
the two sampling periods. Stage 1 sampling may have detected a specific contaminant release event which had
passed through the site prior to Stage 2 samplings, or the decrease in observed contaminant concentrations may
be due to natural degradation.
Surface Water
Chloroform, bromoform, bromodichloromethane, dichloromethane, and petroleum hydrocarbons were observed
at low concentrations during Stage 1 investigations. Chloromethane, chloroform, 1,2-dichloroethane,
1,1,1-trichloroethane, 1,1-dichloroethane, 1,1-dichloroethene, trichloroethylene, and 1,2-dichloropropane were
observed at low concentrations during Stage 2.
Chloroform, bromoform, bromodichloromethane, and chloromethane were observed in a sample of the Plant 78
approved (onsite) water collected during Stage 1. At the time of both the Stage 1 and Stage 2 sampling, the
approved water contributed to the flow of the NDD and the majority of the halomethanes (especially chloroform)
detected at low concentrations in water sampling at Plant 78 can be attributed to chlorination of the approved
lii
P78-921/P78TOC.lui
02/13/92
water for drinking purposes. The presence of chloroform and petroleum hydrocarbons are, however, consistent
with the NDD site disposal history.
Concentrations of bromodichloromethane, bromoform, and bromomethane in the Plant 78 water supply (sampled
during Stage 1) are at concentrations exceeding either EPA 10"* Human Health Risk Criteria (HHRC) or MCLs.
Purgable halocarbons were also detected at low concentrations in Stage 1 surface water samples. Stage 2 sample
results show 1,2-dichloroethane, chloromethane, 1,1-dichloroethene, and chloroform at concentrations exceeding
EPA 10-6 HHRC. Concentrations of 1,1,1-trichloroethane, trichloroethene, and 1,2-dichloropropane do not
exceed EPA 10"6 HHRC or MCLs. There are no EPA 10"6 HHRC or MCLs for 1,1-dichloroethane.
Groundwater
Chloroform, tetrachloroethylene, 1,1-dichloroethane, 1,2-dichloroethane, 1,1,1-trichloroethane, and
trichloroethylene were observed in Stage 2 water quahty analysis conducted on groundwater from monitoring
well P-3. Petroleum hydrocarbons, detected in surface water and sediment sampling of the NDD under Stage 1,
were not detected in P-3 groundwater. The concentrations for trichloroethylene and 1,1,1-trichloroethane are
much higher in P-3 groundwater than concentrations of these analytes in NDD surface water. Concentrations
of chloroform, trichloroethylene, and 1,1,1-trichloroethane exceed MCLs. 1,2-Dichloroethane exceeds EPA 10"6
HHRC but does not exceed the MCL of 5 jtg/L.
Chloroform, chlorobenzene, methylene chloride, tetrachloroethene, 1,2-dichloroethane, 1,1-dichloroethene,
dichlorobenzene, 1,1,1-trichloroethane, 1,1-dichloroethane, and trichloroethylene were detected in water quality
analyses on groundwater from monitoring well P-8. The concentrations of trichloroethylene,
1,1,1-trichloroethane, 1,1-dichloroethene, and 1,2-dichloroethane from groundwater monitoring well P-8 are
higher than all other surface and groundwater samples at Plant 78. Concentrations of 1,1,1-trichloroethane,
1,2-dichloroethane, 1,1-dichloroethene, tetrachloroethene, and trichloroethylene exceed MCLs. Concentrations
of chloroform and methylene chloride exceed EPA 10"* HHRC.
Soil Gas Survey
Trichloroethane and trichloroethylene were detected over the majority of the NDD and E-519 areas.
Tetrachloroethene and petroleum hydrocarbons were only observed near Buildings E-516 and E-517.
E-512 DRAINAGE DITCH SITE
Surface Sediment
Petroleum hydrocarbons were the only analyte detected in surface sediment sample E-512DD during Stage 1.
Stage 2 verified this detection in sample E-512SS1. Petroleum hydrocarbons were detected at 1,320 mg/kg. The
presence of petroleum hydrocarbons is consistent with the site history.
Iiii
P78-921/P78TOCJiv
02/13/92
Deep Stratigraphic Boring
Petroleum hydrocarbons were detected in samples collected at 50 feet (36.8 mg/kg) and 126 feet (18.5 mg/kg)
in boring E-512B1. A duplicate sample collected at 50 feet contained no detections. No duplicate sample was
collected at 126 feet.
Surface Water
Petroleum hydrocarbons were detected in a surface water sample collected during Stage 1. Bromoform,
chloroform, 1,1-dichloroethane, 1,1,1-trichloroethane, and 1,1-dichloroethene were detected at low concentrations
in a surface water sample.
Stage 2 surface water samples did not contain any petroleum hydrocarbons. One sample did contain low
concentrations of chloroform and 1,1,1-trichloroethane. The chloroform detection exceeds the EPA 10"* HHRC.
Groundwater
Chloroform, 1,2-dichloroethane, 1,1-dichloroethene, 1,1-dichloroethane, 1,1,1-trichloroethane, and
trichloroethylene were observed in groundwater from groundwater monitoring well P-5. Chloroform,
1,2-dichloroethane, and 1,1-dichloroethene exceeded the EPA 10"* HHRC. Chloroform, 1,2-Dichloroethene and
1,1-dichloroethane do not, however, exceed MCLs. 1,1,1-Trichloroethane does not have a 10"6 HHRC but does
have a MCL. The concentration is well below the MCL. Trichloroethylene exceeded the MCL.
The similarity of chloroform concentrations between surface and groundwater suggests that the chloroform
present in shallow groundwater at E-512 may not be due to site disposal activities. Chloroform is present in the
Plant 78 water supply which directly supplies the water present in the E-512 ditch and indirectly recharges the
shallow groundwater aquifer monitored by momtoring well P-5.
Soil Gas Survev
Trichloroethane and trichloroethylene were detected in the majority of the E-512 soil gas collectors. The
predominate area of contamination is associated with the Hazardous Waste Storage Yard located due south of
Building E-512. Additional areas of trichloroethane contamination exist both south and east of Building E-512.
The distributions for tetrachloroethene and petroleum hydrocarbons detected were more limited than the
distributions for trichloroethylene and trichloroethane.
FAUST VALLEY DRAINAGE SITE
Sediment Sampling
The relatively uniform petroleum hydrocarbon concentrations detected under Stage 1 sampling suggested a
non-point source. Lack of confirmation under Stage 2 sampling, however, indicates that the petroleum
Uv
P78-921/P7STOCJV
02/13/92
hydrocarbons detected may not be due to non-point source activities. This lack of contamination may be due
to individual sample variability between the two sampling periods, the detection of a petroleum hydrocarbon
release event which has since dissipated, or the decrease in petroleum hydrocarbon concentration may be due
to natural degradation.
Stage 2 sampling indicated the widespread occurrence of low levels of 1,1,1-trichloroethane.
1,1,1-Trichloroethane is widely used as an industrial solvent at Plant 78. The FVD, however, does not serve as
a drain for any of the Plant 78 drainage ditches. Any surface flow within the FVD would arise from either offsite
drainage into the FVD upgradient of Plant 78 or from localized, non-channeled surface run-off originating on
Plant 78. The source for the 1,1,1-trichloroethane observed in FVD samples is unknown.
Boring Samples
Boring E-515B1 had low concentrations of methyl chloride in samples collected from 20 feet, 35 feet, and 50 feet.
Samples from boring E-515B2 did not have any detections for methyl chloride.
Low concentrations of acetophenone, bis (2-ethylhexyl) phthalate, and butyl benzylphthalate were also detected
in samples from both borings, however, review of the method blank analyses indicates that these compounds may
be due to laboratory contamination.
Very low concentrations of vinyl chloride were detected in soil samples collected at 97 and 135 feet in boring
Surface Water
During both Stage 1 and Stage 2 sampling, the FVD was dry. No surface water samples were collected.
Groundwater
One groundwater sample was collected from momtoring well P-1 under Stage 1 and contained no detectable
well P-9, were collected under Stage 2. The sample from momtoring well P-1 contained low concentrations of
chloroform, chloromethane, 1,2-dichloroethane, 1,1,1-trichloroethane, and trichloroethylene. 7 ^
Until 1989, wastewater disposal practices at Plant 78 consisted of disposal into surface ditches, subsurface dry
wells, and into a surface holding and evaporation pond (SSTEP) which may have resulted in the development
of a groundwater mound. Over an approximately 30 year time period (since 1962), this groundwater mound
would have probably reached a maximum many years before the installation of groundwater momtoring well P-1.
Well P-1 did not have any evidence of organic compound contamination when sampled under Stage 1. It is
unlikely that contaminated groundwater identified at wells P-8 and P-9 in conjunction with the groundwater
E-515B2.
organic compounds. Three groundwater samples, one from monitoring well P-1 and two from momtoring
lv
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P78-921/P78TOCJvi
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mounding would migrate upgradient into the well P-1 area of Plant 78 within the two year period between
Stage 1 and Stage 2 sampling and not within the previous 28 years. The groundwater sample collected for
considered to be unusable foT site evaluations. Monitoring well P-9 contained high concentrations of
1,1,1-trichloroethane, trichloroethylene, 1,1-dichloroethane, 1,1-dichloroethene, 1,2-dichloroethane,
tetrachloroethene, chloroform, dichlorobenzene, chlorobenzene, and chloromethane.
Concentrations of chloroform, chloromethane, 1,2-dichloroethane, and tetrachloroethene from momtoring
well P-9 exceed EPA 10"6 HHRC. Concentrations of 1,1-dichloroethylene, 1,1,1-trichloroethane, trichloroethylene
exceed MCLs.
Soil Gas Survev
Trichloroethane was detected in the area surrounding Building E-515. Additional areas of minor
tetrachloroethane contamination exists to the south and southeast of Building E-515.
Trichloroethylene was detected only in the proximity of the "acid drain", and tetrachloroethene and hydrocarbons
were not detected in the soil gas survey at Building E-515.
M-585 FRENCH DRAIN SITE
Deep Stratigraphic Borings
Determination of organic analytes in soil samples collected during Stage 1 indicated the presence of low
concentrations of petroleum hydrocarbons. Methylene chloride was also observed in three samples. Under
Stage 2, two soil samples taken from boring M-585B1 (M-585B1-D and duplicate) at 89 feet contained low
concentrations of trichloroethylene. All other soil samples collected at M-585 contained no detectable organic
analytes. The low levels of petroleum hydrocarbons detected in Stage 1 boring samples were not confirmed by
Stage 2 sampling.
Soil Gas Surveys
Trichloroethylene, trichloroethane, and tetrachloroethylene are present in three anomalies. The main anomaly
is centered around the French Drain. A second anomaly is present due north of the French Drain and appears
to be related to a septic sewer leach field for wastewater from Building M-585. The third anomaly is located
at the southwest end of the M-585 soil gas survey area and suggests that trichloroethylene contamination may
be increasing to the southwest. Chloroform, however, is present only in the anomaly centered around and
directly southwest of the French Drain.
believed to be cross-contaminated. Thus, analytical results from this sample are
The results of Soil Gas Survey 1 led to the identification of two areas of possible contamination other than the
French Drain, one located north of the French Drain, and one located to the southwest. Groundwater sampling
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02/13/92
at these two locations (monitoring wells P-6 and P-7) confinned this contamination. The investigations indicate
that contaminant levels increase at the survey boundaries. Therefore, a second soil gas survey was conducted
to investigate the aerial extent of this contamination.
In the area of the north anomaly, identified by Soil Gas Survey 1, subsequent groundwater sampling (momtoring
well P-6) confirmed chlorinated solvent contamination. Organic vapor detections extend approximately 100 feet
to the north of momtoring well P-6 where soil gas readings drop to background levels. Organic vapor detection
also extended eastward toward Building M-585. Relatively high levels of organic vapors were detected along the
western side of Building M-585.
In the area of the west anomaly, identified by Soil Gas Survey 1, sampling of monitoring well P-7 confirmed
chlorinated solvent contamination in groundwater. Organic vapor detections extend in a linear fashion
approximately 300 feet to the southwest of monitoring well P-7.
Groundwater Samples
Groundwater chemical analyses from momtoring well P-2 under Stage 1 contained low concentrations of
chloroform, methylene chloride, 1,1,1-trichloroethane, and toluene. Chloroform, 1,2-dichloroethane, and
1,1,1-trichloroethane were detected at low concentrations in momtoring well P-2 under Stage 2. Only chloroform
exceeded the EPA 10"* HHRC.
Tetrachloroethene, trichlorofluromethane, benzene, chlorobenzene, 1,2-dichloroethane, 1,1-dichloroethene,
1,1,1-trichloroethane, vinyl chloride, t-l,2-dichloroethene, toluene, 1,1-dichloroethane, and trichloroethylene were
detected in momtoring well P-6. Benzene, 1,1-dichloroethene, 1,2-dichloroethane, 1,1,1-trichloroethane, and
trichloroethylene, exceed MCLs. Chlorobenzene, tetrachloroethene, and trichlorofluromethane exceed EPA 10"6
HHRC. 1,1-Dichloroethane was also detected at a high concentration, however, there is no MCL or 10"6 Human
Health Risk Criterion for this compound.
Benzene, chlorobenzene, 1,1-dichloroethene, 1,2-dichloroethane, 1,1-dichloroethane, trichloroethylene,
chloroform, and 1,1,1-trichloroethane were detected in momtoring well P-7. Concentrations of
1,1-dichloroethene, 1,2-dichloroethene, 1,1,1-trichloroethane, and trichloroethylene exceed MCLs. Benzene and
chloroform were detected at concentrations which exceed EPA 10"6 HHRC.
BLUE CREEK
Stage 1 results for organic analytes in Blue Creek surface water contained low concentrations of bromoform,
chloromethane, methylene chloride, trichloroethylene, benzene, and petroleum hydrocarbons. Two sampling
episodes were conducted during Stage 2 to verify the results of Stage 1 sampling.
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Stage 1 sampling of Blue Creek surface sediment determined the presence of low concentrations of petroleum
hydrocarbons.
Sampling Episode One
Surface Water Samples
Two background surface water samples collected from Blue Creek, taken 1 mile (BC-SWS15) and one-half mile
upgradient of Plant 78 (BC-SWS14) contained 1,2-dichloroethane. The source of 1,2-dichloroethane is unknown.
It may be related to a contamination event, or agricultural or industrial activity(s) on farm land along Blue Creek
upstream of Plant 78.
1,2-Dichloroethane was detected in 11 out of the 14 Blue Creek surface water samples. Although an upstream
source of 1,2-dichloroethane was indicated by the Stage 2 sampling, Plant 78 is a contributing factor to the
1,2-dichloroethane present in Blue Creek as evidenced by the increase of 1,2-dichloroethane concentrations from
samples taken at BC-SWS11 (near Building M-624) and BC-SWS6 (near Buildings M-696 and M-697).
1,2-Dichloroethane concentrations exceeded the MCL at sample locations BC-SWS6, BC-SWS7, BC-SWS8,
BC-SWS10, BC-SWS11, and BC-SWS13. The remaining detections except for BC-SWS2 and BC-SWS3 exceeded
EPA 10'6 HHRC.
Chloromethane was detected at low concentrations in 6 of the 14 samples collected from Blue Creek. Several
potential sources exist on Plant 78 that could contribute to this contamination. However, the low concentrations
of chloromethane detected indicate that the chloromethane in Blue Creek is probably due to chlorination of the
Plant 78 water supply. All samples collected which contained concentrations of chloromethane exceed the EPA
10'6 HHRC. There is no MCL for chloromethane.
1,2-Dichloropropane was detected in 4 out of the 14 samples collected from Blue Creek. The detection of
1,2-dichloropropane is not inconsistent with Plant 78 site history. However, 1,2-dichloropropane is also used as
an agricultural soil fumigant to control nematodes. The concentrations detected at Blue Creek are low and
because Blue Creek drains an extensive agricultural area above Plant 78, the presence of 1,2-dichloropropane
may be due to offsite agricultural application(s). None of the observed 1,2-dichloropropane concentrations
exceed the MCL of 5 jtg/L.
1.1.1- Trichloroethane was only detected in sample BC-SWS13 (located at the NDD intersection of NDD and
Blue Creek but not actually on Blue Creek). The concentration is near the method detection limit for the
analysis and does not exceed the MCL of 200 /ig/L.
1.1.2- Trichloroethane was only detected in sample BC-SWS6 (near Building M-628) at a concentration that just
exceeds the EPA IO"6 HHRC of 0.6 jig/L.
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P78-921/P78TOCJix
02/13/92
Vinyl chloride was detected in sample BC-SWS13 at a concentration of 0.229 /tg/L. This concentration is below
the EPA IO-6 HHRC of 2 pg/L. There is no MCL for vinyl chloride.
Tetrachloroethene was detected in only 3 of the 14 Blue Creek samples. Samples BC-SWS6, BC-SWS9, and
BC-SWS13 were at 0.352 /tg/L, 1.43 /tg/L, and 0.473 /tg/L, respectively. The concentrations observed in
BC-SWS6 and BC-SWS13 are below the EPA 10"* HHRC of 0.8 /tg/L. The concentration in sample BC-SWS9
exceeds the EPA 10"6 HHRC. None of these samples exceed the MCL of 5 /tg/L.
Total Xylenes were only detected in sample BC-SWS9 at a concentration of 3.62 /tg/L. There is no water quahty
criterion for total xylenes.
Surface Sediment Samples
Petroleum hydrocarbons were detected in 2 of the 7 surface sediment samples collected. Sampling verified that
minor petroleum hydrocarbon contamination (observed under Stage 1) does exist around Buildings M-627 and
M-697, however, the widespread occurrence observed during Stage 1 sampling was not confirmed.
1,1,1-Trichloroethane was detected in low concentrations in 3 of the 7 samples collected. Sample BC-SS5 is
located near Building M-627 where minor petroleum hydrocarbon contamination was detected in Stage 1 and
Stage 2 sampling. Sample BC-SS7 was collected one-half mile upgradient of Plant 78. Detection of
1,1,1-trichloroethane in surface sediment samples yielded no consistent pattern.
Sampling Episode Two
Surface Water Samples
Nine surface water samples (eight samples and one duplicate sample) were collected from Blue Creek during
sampling episode 2. This sampling had no detections.
Surface Sediment Samples
Nine surface sediment samples (eight samples and one duplicate sample) were collected from Blue Creek during
sampling episode 2. There were no detections in these samples.
Shallow Boring Samples
Six shallow soil borings were installed along Blue Creek. Two samples were collected from each boring at 4-
and 8-foot depths. Only shallow boring BC-SB4, located at the intersection of Thiokol Road and 1500 Street,
contained contamination, where low concentrations of 1,1,1-Trichloroethane were detected in both samples.
lix
P7M21/P78TOC.1X
02/13/92
Aquatic Ecosystem Sampling
Blue Creek was sampled at three locations: upstream from Plant 78, near the center of the drainage on Plant 78,
and downstream from Plant 78. Tliree sediment samples were collected from each location and the benthic
invertebrates in the sediment identified and counted.
A statistical comparison of the three sites for evenness, diversity index, and number of taxa was completed using
a Kruskal-Wallace nonparametric procedure. No significant differences were found for any comparison between
the three sites. All nine samples collected from Blue Creek were above 0.5 in evenness (evenness below 0.5
indicates a stressed ecosystem), and the mean Shannon-Wiener index for each sample site was above 2.0 (a value
below 2.0 is an indicator of stress). While Blue Creek does have low numbers of taxa and low diversity, this
situation is probably due to the inconsistency of water flow and width of the stream. There is no evidence of
contaminant related adverse effects on the benthic invertebrate community.
The presence of organic compounds such as 1,1,1-trichloroethane and petroleum hydrocarbons in Blue Creek
samples is not inconsistent with the site history, however, the low levels of occurrence and lack of clear
verification by Stage 2 samplings suggests that the different compounds detected during Stage 1 sampling may
be due to sampling variability, that both Stage 1 and episode 1 of the Stage 2 samplings may have delineated a
specific contamination event(s) that passed through the site, or natural degradation (i.e., photolysis,
biodegradation, etc.) may have removed these compounds.
Some of the compounds detected in Blue Creek surface water may be attributed to chlorination of the onsite
water for drinking purposes (halomethanes) or to offsite usage or disposal not related to Plant 78 (i.e.,
1,2-dichloropropane).
RISK ASSESSMENT SUMMARY
A baseline risk assessment is a component of the Stage 2 IRP at USAF Plant 78. The purpose of the risk
assessment is to evaluate the IRP results, identify contaminant transport pathways and receptors, and evaluate
actual or potential risks on pubhc health and the environment from hazardous materials present at the site.
IRP investigations have defined four sites that serve as major sources of contamination at Plant 78: NDD, E-512,
FVD, and M-585. These areas, and the media impacted by contaminants originating there, are the focus of the
risk assessment.
The chemicals of concern (COCs) at Plant 78 are chloroform, 1,2-dichloroethane, 1,1,1-trichloroethane, and
trichloroethylene. These compounds, volatile chlorinated hydrocarbons, represent the most mobile, toxic, and
widespread contaminants detected at Plant 78.
Ix
P78-921/P7STOC.ba
02/13/92
The potential for each indicator chemical to migrate from source areas was determined through a fate and
transport evaluation that predicted an estimation of exposure point concentrations in air, surface water,
groundwater, and soil for both onsite and offsite locations. Key exposure routes evaluated include inhalation of
vapors, ingestion of water and soil, and dermal absorption of chemicals associated with water, sediment, and soil.
Ingestion of water was only evaluated for surface water because natural groundwater at Plant 78 is not potable
due to high TDS.
Ingestion of crops, livestock, game species, and aquatic organisms were exposure pathways excluded from analysis
due to very low bioaccumulation factors for the COCs. Current exposures were evaluated for both workers at
the plant and residents offsite. Future exposures onsite were not evaluated because access to Plant 78 is highly
restricted for security and safety reasons and because it is likely that the site will remain industrial for the future.
However, future exposure to offsite residents was evaluated.
The summary of risks relevant to Plant 78 are present in Table E-2. Risks relevant to contaminated surface
water were evaluated for both workers and residents. These risks include dermal absorption and inhalation of
contaminants volatilized from surface water for workers onsite, and incidental ingestion, dermal absorption, and
inhalation of contaminants volatilized from surface water for residents offsite. The total carcinogenic risk
estimate to workers from dermal exposure to surface water is 1.6 x 10'9. The total current carcinogenic risk
estimate due to incidental ingestion of surface water by children is 1.2 x 10"7. Carcinogenic risk estimates
associated with inhalation exposure to surface water for future residential populations is 4.4 x 10"6. This estimate
includes exposure via inhalation to chemicals associated with soil and sediment transported to the installation
boundary, as well as inhalation of vapor at Blue Creek.
The total noncarcinogenic risk estimate (Hazard Index as defined in RAGS [EPA, 1989]) posed to current
worker and residential populations exposed to contaminants are 2.0 x 10^ and 4.7 x IO"5, respectively. The total
noncarcinogenic risk associated with contamination in surface water, soil, and sediment through inhalation
exposure to future populations of residents is 6.4 x 10^.
Risks relevant of contaminated soils and sediments in the Plant 78 area were evaluated only for onsite workers.
Exposures and risks were quantified for incidental soil/sediment ingestion, dermal absorption, and inhalation
of contaminants volatilized from soil. The total carcinogenic risk estimate due to all soil/sediment related worker
exposures (dermal and incidental ingestion) at Plant 78 is 1.6 x 10"12. The total noncarcinogenic risk estimate
due to all soil/sediment related worker exposures (dermal and incidental ingestion) is 1.2 x 10 s. Risks associated
with future exposure to sediment are summarized in conjunction with soil and surface water in the previous
paragraph.
lxi
P78-914/P78TE-2.1
02/14/92
Table E-2. Summary of Risks Relevant to Plant 78.
Pathway
Risk Estimate
Carcinogenic Noncarcinogenic
Risk Level Hazard Index
Current Pathways
Worker Inhalation of Volatiles at Source
Worker Dermal Absorption of Surface Water at Source
Worker Ingestion of Soil/Sediment at Source
Worker Dermal Absorption of Soil/Sediment at Source
Total Worker
1.2 x ICV7
1.6 x 1CT9
2.4 x 10'13
1.4 x 10'12
1.2 x 10"7
1.9 x 10"*
1.6 x ICV6
1.8 x IO"6
1.0 x IO"5
2.0 x W
Resident Dermal Absorption of Surface Water at Blue Creek 2.5 x 10"'
Resident Dermal Absorption of Sediment at Blue Creek —
Resident Ingestion of Surface Water at Blue Creek 1.2 x 10"7
Total Resident 1.2 x 10"7
Total Current 2.4 x Iff7
6.7 x IO"7
1.4 x 10"5
3.2 x Iff5
4.7 x 10"5
2.5 x W4
Future Pathways
Resident Inhalation of Vapors at Boundary
Resident Inhalation of Vapors at Blue Creek
9.5 x Iff7
3.4 x Iff*
4.1 x Iff1
2.3 x 10^
Total Future
TOTAL
4.4 x 10"*
4.6 x 10-6
6.4 x 10A
8.9 x 10"*
lxii
P78-921/P78TOCJxiii
02/13/92
Total noncarcinogenic risks to current worker population associated with inhalation exposure to chemicals at the
source is 1.9 x IO"4. Total carcinogenic risks posed to current workers exposed via inhalation is 1.2 x 10"7.
The cancer risk for the potential exposure pathways do not exceed the EPA recommended 10"6 risk level (risks
for current workers and residents combined is 2.4 x 10"7). The noncarcinogenic hazard indices are less than unity
(total hazard indices for current workers and residents combined is 2.5 x ICV4). The total combined cancer and
noncancer risk to future residential populations due to inhalation exposure is 4.4 x IO"6 and 6.4 x 10"*, respectively.
There are no observed ecological health effects and none expected to occur in the future. These results indicate
that there is no current or potential future threat to human health or environment associated with Plant 78.
CONCLUSIONS
The Stage 2 investigation at Plant 78 has determined that the levels of site-related constituents detected in
environmental media at the site do not pose an unacceptable current or future risk to human health and the
environment. The results of the investigation support the implementation of a no-action or limited action
alternative and as such, the perfonnance of a Feasibility Study (FS) is not necessary or appropriate.
Implementation of the no-action or limited action alternative is consistent with current EPA guidance (EPA,
1988). In situations where the results of the baseline risk assessment may indicate that the site poses little or
no threat to human health or the environment, the feasibility study should be either scaled down as appropriate
to that site and its potential hazard, or eliminated altogether (EPA, 1988). The results of the remedial
investigation and baseline risk assessment will serve as the primary means to documenting a no-action decision
(EPA, 1988). In addition, Section 104(a)(1) of CERCLA authorizes response actions only if a release or
threatened release may present an imminent or substantial endangerment to the pubhc health or welfare. The
remote location of Plant 78 and the unique geological and hydrogeological characteristics of the site supports
the appropriateness of the no-action or limited action alternative.
In the evaluation of the quahty of the surface and groundwater at Plant 78, federal and state water quahty
standards (e.g., maximum contaminant levels [MCLs]) have been used to indicate the quahty of the water relative
to drinking water. These drinking water standards are not, however, directly apphcable to the samples collected
at Plant 78. The waters collected at Plant 78 are unsuitable for use as a chinking water source either at the
installation or within the immediate vicinity due to naturally high dissolved solids content.
Site-related constituents are present in the shallow groundwater beneath Plant 78 where site constituents may
leach from soil to groundwater. This shallow groundwater and surface water meets the State of Utah Class III
groundwater classification. Table E-3 summarizes apphcable state and federal rules and guidelines utilized in
review of Stage 2 groundwater data at Plant 78. TDS concentrations from both shallow groundwater and surface
water at the site range from 644 mg/L to greater than 3,000 mg/L, and salinity as high as 1,400 mg/L. For non-
lxiii
P78/P78TE-3.1
12/20/91
Table E-3. Comparison of EPA Groundwater Classifications, Federal Drinking Water Rules, State of Utah Proposed Groundwater Regulations, and State of Utah
Drinking Water Rules (Page 1 of 2).
EPA Groundwater Protection Strategy*1'
Federal Drinking
Water Rules'2'
State of Utah
Drinking Water Rules(3)
Class I Class II Class III Primary Primary
Special Groundwaters
Special groundwaters are those that are:
(1) Highly vulnerable to contamination
because of the hydrological characteristics
of the area where they occur, and
(2) Characterized by either of the
following factors:
- Groundwater is irreplaceable in that no
reasonable alternative source of drinking
water is available to substantial
populations.
- The groundwater is ecologically vital, in
that the aquifer provides the base flow
for a particularly sensitive ecological
system that, if polluted would destroy a
unique habitat.
Current (IIA) and potential (IIB)
sources of drinking water and waters
having other beneficial uses.
This class includes all other
groundwaters that are currently used
or are potentially available for drinking
water or other beneficial use.
Groundwater not considered a potential
source of drinking water and of limited
beneficial use.
Class IIIA and IIIB is saline, i.e., has,
TDS levels over 10,000 mg/L, or is otherwise
contaminated by naturally occurring
constituents or human activity that is not
associated with a particular waste disposal
activity or another site beyond levels that
allow remediation using methods reasonably
employed in public water treatment systems.
Class III also includes groundwater that is
not available in sufficient quantity at any
depth to meet the needs of an average
household.
Class IIIA includes groundwater that is
interconnected to surface water or adjacent
groundwater that potentially could be used
for drinking water.
No primary. Total dissolved solids (TDS) not to
exceed 2,000 mg/L. If TDS is greater
than 1,000 mg/L, the supplier must
demonstrate that no better water is
available.
Secondary Secondary
TDS 500 mg/L. TDS 500 mg/L. Concentration above
which usually results in consumer
complaint.
Class IIIB includes groundwater that has no
interconnection to surface water and no
potential to migrate to Class I or II
groundwaters.
P78/P78TE-3.2
12/20/91
Table E-3. Comparison of EPA Groundwater Classifications, Federal Drinking Water Rules, State of Utah Proposed Groundwater Regulations, and State of Utah
Drinking Water Rules (Page 2 of 2).
State of Utah Proposed Groundwater Regulations'4'
Class IA Class II Class III Class IV
TDS less than 500 mg/L.
TDS may not increase 1.1 times background,
but not more than 500 mg/L.
Other Contaminants
Not Detectable
May not exceed 0.1 times standard or detection
limit.
Detectable
May not exceed 0.1 times standard, or 1.1 times
background, whichever is greater.
Class IB
Same as Class IA except TDS may not exceed
2,000 mg/L.
Other Contaminants
Not Detectable
Same as Class IA.
Detectable
Same as Class IA.
Class IC
Case by case.
TDS between 500 and 3,000 mg/L. May not
increase over 1.25 times background.
Other Contaminants
Not Detectable
May not exceed 0.25 times standard, or
detection limit, whichever is greater.
Detectable
May not exceed 0.25 times standard, or 1.25
times background, whichever is greater.
TDS between 3,000 to 10,000 mg/L. TDS may
not increase above 1.25 times background.
Other Contaminants
Not Detectable
May not exceed 0.5 times standard, or detection
limit, whichever is greater.
Detectable
May not exceed 0.5 times standard, or 1.5 times
background, whichever is greater.
TDS greater than 10,000 mg/L.
Other Contaminants
Not Detectable
Case by case.
Detectable
Case by case.
Source: (1)EPA, 1986d and 1988b.
"'EPA, 1991.
'"State of Utah, 1990.
(4)State of Utah, 1991.
P78^21/P7aTOCJltvi
02/14/92
potable groundwaters, drinking water standards are not applicable, relevant, or appropriate and will not be used
to determine preliminary remediation goals. EPA criteria suggests that resources can be better spent cleaning
up sites and groundwaters that do pose a threat to human health and the environment (Code of Federal
Regulations 55 FR, pages 8,732 and 8,733).
Shallow groundwater and surface water at the site generally fails to meet the State of Utah Drinking Water Rules
for primary water, which states that if TDS are greater than 1,000 mg/L, the supplier must demonstrate that no
better water is available and that TDS are not to exceed 2,000 mg/L.
TDS concentrations in shallow groundwater and surface water at the site exceed the EPA's secondary maximum
contaminant levels (SMCL) for drinking water of 500 mg/L.
Due to the poor quahty of groundwater beneath Plant 78, water for the plant complex is supplied from wells and
springs 3 to 10 miles from the plant. Thiokol installed several wells for potential groundwater use during the
early 1980's and found the water nonpotable. In general, historical data reflects the poor quahty of the deeper
aquifer in the area of the site.
Results of the baseline risk assessment indicate that there is no threat to human health and that the apparent
human health risks at the site appear to be minimal, despite the levels of groundwater contamination observed.
This is due to the following reasons:
• Groundwater is nonpotable without prior treatment due to naturally occurring high TDS (Sections
2.3.1.2 and 2.3.1.3),
• Distance to the nearest homes ( Section 4.2.5),
• Distance to the nearest surface water drainage (Blue Creek) (Section 4.2.3.2),
• Length of time for plume to reach Blue Creek (Section 4.2.3.2),
• Low population density in the surrounding area (Section 4.2.5), and
• The lack of bioaccumulative properties for the contaminants in the area (Section 4.2.1, Environmental
Fate).
The combined cancer risks for the potential exposure pathways are 4.6 x 10"* risk level, and the weight of
evidence is B2. The noncancer hazard quotients are all less than unity, predicting minimal threat to health, based
on noncarcinogenic effects. There are no observed ecological health effects due to observed contamination at
Plant 78.
There is little potential for direct human contact at Plant 78 because the area is closed to the pubhc and
extensive measures are taken at the site to ensure that trespassing does not occur for security and safety reasons.
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Because soil contamination is not widespread and contaminant concentrations are very low, direct contact with
contaminated soil is considered a rare event (even by workers at the source).
Surface water from Blue Creek is not utilized immediately downgradient of Plant 78 for drinking water or
irrigation purposes. However, livestock and wildlife may access Blue Creek and consume surface water. It is
unlikely that children or other human receptors will contact Blue Creek and ingest water due to the low
population density in the area, the distance to the nearest residences, the high TDS of the water, and the lack
of game fish that would attract fisherman.
RECOMMENDATIONS
For purposes of simplifying future discussion of investigation sites at Plant 78, the NDD (including Building
E-519), E-512, and FVD (including Building E-515) are grouped into Operable Unit (OU) No. 1. The M-585
site and Blue Creek will remain as separate sites.
OU No. 1 is classified as a Category 1 site where no further IRP action (including remedial actions) is required.
The M-585 French Drain Site is classified as a Category 1 site where no further IRP action (including remedial
actions) is required.
Blue Creek is classified as a Category 1 site where no further IRP action (including remedial actions) is required.
Ixvii
1.0 INTRODUCTION
P78-921/P781.1
02/13/92
1.0 INTRODUCTION
1.1 PURPOSE
The Installation Restoration Program (IRP) was developed by the Department of Defense (DOD) to ensure that
its facilities comply with legislation governing disposal of hazardous waste. DOD IRP policy, as contained in
Defense Environmental Quahty Program Policy Memorandum (DEQ PPM) 8-15, dated December 11, 1981, is
to identify and fully evaluate suspected problems associated with past contamination and to control resulting
hazards to health, welfare, and the environment. The IRP is the basis for response actions on United States Air
Force (USAF) installations under provisions ofthe Comprehensive Environmental Response, Compensation, and
Liability Act (CERCLA) of 1980, as clarified by Executive Order 12316, and the Superfund Amendments
Reauthorization Act (SARA) of 1986, as clarified by Executive Order 12580.
The objectives of the IRP are to identify and evaluate suspected problems at past hazardous material disposal
sites, to control the migration of hazardous contaminants, to control resulting hazards to health, welfare and the
environment, and to consider feasible mitigation actions. The four phases of the original IRP include:
Phase I Records Search - to identify and prioritize past disposal sites that may pose a hazard to pubhc
health;
Phase II Confirmation and Quantification - to define and quantify the presence or absence of contamination
by the design and implementation of environmental surveys;
Phase III Technical Base Development - to implement research and technology development for
environmental assessments; and
Phase IV Remedial Actions - to select and implement appropriate control measures.
In November 1986, the USAF modified the IRP to provide for an integrated Remedial Investigation/FeasibUity
Study (RI/FS) program in response to SARA and Environmental Protection Agency (EPA) guidance. The IRP
was thus expanded to incorporate elements of Phases IT and IV to conduct the RI/FS in parallel instead of serial
fashion. The program is now oriented to include determination of Apphcable or Relevant and Appropriate
Requirements (ARARs), identification and screening of technologies, and development of alternatives in
Phase II.
1.2 TIME PERIOD AND STAGES OF THE IRP AT PLANT 78
Engineering Science, Inc. (ES) was retained by the Air Force Engineering and Services Center (AFESC) to
conduct the Phase I records search. This records search began in December 1983 and was completed in March
1984, resulting in the identification of three disposal sites and a drainage ditch with a potential for contaminant
migration. These four sites were prioritized for Stage 1 field work conducted under Phase II of the IRP.
1-1
P78-921/P781.2
02/13/92
During the Phase II pre-survey meeting and site inspection, several additional areas of concern were identified.
The Plant 78 Stage 1 work by Environmental Science & Engineering, Inc. (ESE) began in the fall of 1986. Eight
individual sites were investigated to assess potential occurrence and extent of contamination. Surface
water/surface sediment samples were collected and analyzed, momtoring wells were installed and sampled. Soil
borings were instaUed, sampled, and analyzed and an EM-31 geophysical survey was conducted to accomplish
the contamination assessment. Additional soU borings (resamples) and another momtoring weU (P-3) were
instaUed during the winter of 1988 under an extended Stage 1 effort. The results of aU Stage 1 work were
presented in the final report submitted by ESE to the USAF in August 1989. As a result of the Phase II Stage 1
investigations, five of the eight sites were selected for additional investigation under the Phase II Stage 2 of the
IRP program.
The IRP objectives of the Phase II Stage 2 investigation were to conduct field investigations to verify Stage 1
results, define the magnitude and migration potential of contaminants, perform a baseline risk assessment, and
develop preliminary and detailed alternatives for remedial action. The Phase II Stage 2 effort was conducted
by ESE. The USAF Statement of Work for the Phase II Stage 2 investigation is provided in Appendix A.
Stage 2 work began in December 1988 and continued through March 1990. Six groundwater monitoring wells
were instaUed and surface, shaUow soil, surface water, and groundwater samples were coUected. These data have
been assessed and this summary technical report assembled.
A Risk Assessment (RA) was also conducted under the Stage 2 investigation. No FS was conducted based on
the results of the RA.
1.3 INSTALLATION HISTORY
The information in this section was taken, in part, from the IRP Phase I - Records Search Report (ES, 1984).
The Thiokol Corporation (Thiokol) constructed a complex of sohd propeUant technology development facilities
in 1957. USAF Plant 78 (Plant 78) was constructed in 1962. Plant 78 is separated from the Thiokol facilities
by approximately five miles. From 1962 to 1979, Plant 78 was engaged in the mixing, casting, and final
assembling of sohd propeUant chemicals into rocket motors for the Minuteman I MissUe Program. Beginning
in 1972, rocket motor production activities were expanded to include the first stage of the Trident-I (C-4) missUe.
In 1980, fuU production of the first stage rocket motor for the Peacekeeper (MX) missUe began. As a part of
the sohd propeUant rocket motor production, components such as nozzles and motor housings have been
fabricated at Plant 78.
1-2
P7W21/P7813
02/13/92
1.3.1 DESCRIPTION OF INSTALLATION
Plant 78 is located in Box Elder County, Utah, approximately 35 miles west of Brigham City (Figure 1-1). The
plant site is part of a complex of facilities operated by Thiokol. The area surrounding the plant is mostly ranch
land and unoccupied natural terrain. The plant site encompasses 1,550 acres and the facUity site plan is shown
in Figure 1-2. The plant site is characterized by open areas between the production buUdings, with the greatest
concentration of facilities located around BuUdings 508 and 517.
1.3.2 PAST WASTE MANAGEMENT PRACTICES
A study of current and past waste generation and management methods was conducted to identify those activities
that resulted in the generation of hazardous waste. After a review of information obtained from files, records,
interviews with current and former plant employees, and site inspections, it was assessed that the sources of waste
can be associated with the foUowing activities:
• Industrial operations (shops),
• Fuels management,
• Pesticide utilization,
• Waste storage areas, and
• Spills.
The foUowing discussion emphasizes those wastes generated at Plant 78 that are either hazardous or potentiaUy
hazardous. In this discussion, a hazardous substance is defined as hazardous by CERCLA, and a potentiaUy
hazardous waste is one which is suspected of being hazardous, although insufficient data are available to fully
characterize the waste material.
1.3.2.1 Industrial Operations (Shops)
Industrial operations at Plant 78 have been conducted by Thiokol since 1962. Plant 78 has been involved in
providing rocket motors for various systems such as the C-4, MX, Minuteman missUes, and Space Shuttle
boosters. Operations at the plant have involved producing rocket motor nozzles, preparing and casting the
propeUants, and analyzing the casts for imperfections. The rocket motor fabrication process involves mixing,
casting, curing, tooling, and painting. The specific processes performed onsite include macliining aluminum,
plastics, and titanium; degreasing; anodizing; plastics molding; casting/curing; cast cleaning; painting; propeUant
mixing; and ingredient preparation (drying and grinding). AdditionaUy, rocket motors are radiographicaUy
inspected onsite and test-fired on Thiokol property.
Wastes generated have included chlorinated and nonchlorinated organic solvents, waste propeUants, and oxidizers.
Waste management practices at Plant 78 include drum storage, drum treatment, tank treatment, and resource
recovery. Since 1962, aU wastes have been transported from Plant 78 property to Thiokol property for ultimate
disposal. Waste materials not disposed through treatment or burning are disposed through outside contractors.
1-3
f
The Thiokol Corporation
Wasatch Operations
13 14 15 16
AIR FORCE PLANT 78
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Figure 1 — 2
FACILITY SITE PLAN
SOURCE: THIOKOL FACILITY DOCUMENT
INSTALLATION RESTORATION
PROGRAM USAF .PLANT 78
1-5
P78-921/P781.6
02/13/92
Temporary accumulation points for hazardous wastes are located throughout the industrial areas. Up through
1989, sumps and tanks were used to collect contaminated wastewater, which was then pumped into a tank truck
and disposed at the Thiokol facilities off Plant 78 property. In 1989, Plant 78 wastewater discharges, previously
collected by these sumps and tanks, were connected to a newly constructed wastewater treatment plant located
near the intersection of R Avenue and 200 Street. Wastewater is now treated to acceptable discharge standards
and released to Blue Creek under State of Utah Authorization to Discharge Permit No. UT0024805.
1.3.2.2 Fuels Management
The fuels used at Plant 78 consist of gasoline and diesel fuel to service the plant vehicles. The fuel is stored at,
Building E-516 in three 5,000-gallon underground tanks (gasoline) and one 3,200-gallon aboveground tank (diesel
fuel). The tanks were precision tested in 1979 and gave no indications of leakage. There have been no known
spills greater than five-gallons in conjunction with refueling activities.
As reported to the Bureau of Environmental Response and Remediation on November 14, 1990, Thiokol
conducted a tank removal and an overexcavation project at the E-516 facihty. Approximately 580 cubic yards
of soil were removed from the dispenser island area to approximately 22 feet. Five soil samples were taken in
the excavation and analytical test results indicated that no further work was necessary.
1.3.2.3 Pesticide Utilization
The pesticide and herbicide utilization program for Plant 78 has been managed by Thiokol personnel since 1962.
All chemical storage, mixing, and equipment cleaning is done off plant property. The types and approximate
quantities of pesticides used on Plant 78 are shown in Table 1-1. Pesticides are used primarily for mosquito
control (spring, summer, and fall) and herbicides for weed control (spring and fall).
1.3.2.4 Waste Storage Areas
Since 1980, storage of hazardous wastes at Plant 78 has occurred at Building E-501. This facihty serves as a
storage area for several items and is used to store recoverable 1,1,1-trichloroethane waste solvent. The
recoverable solvent is sold to a contractor for reuse. Prior to 1980, the recoverable 1,1,1-trichloroethane was
stored off Plant 78 property awaiting sale to a contractor. All nonrecoverable hazardous chemical wastes had
been taken offsite by Thiokol for disposal prior to completion of the 1984 ES report.
1.3.2.5 Spills
Available information indicates that there have been no major spill incidents reported on Plant 78 since
operations began in 1962. Minor spillage of fuel oil may occur on the ground area at the boiler house (M-576)
during unloading operations (ES, 1984).
1-6
P7M14/P78T1-1.1
02/14/92
Table 1-1. Principle Pesticides Used on USAF Plant 78.
Approximate
Name Quantity
Malathion (91 percent) 100 gals/yr
Atrazine1 1,200 lbs/yr
Kovar n 1,000 lbs/yr
Oust 500 lbs/yr
Round-up 5 gals/yr
1 Discontinued in 1981.
Source: Engineering Science, 1984.
1-7
P78-921/P781.8
02/13/92
1.4 IDENTIFICATION OF SITES
Four sites were recommended for Phase II investigation as a result of the Phase I records search. Discussions
held during a presurvey meeting and site tour (September 26, 1985) resulted in four additional areas added to
the Phase II work effort (Stage 1). The eight sites originally selected for investigation were:
1. North Drainage Ditch (NDD),
2. E-512 Drainage Ditch (E-512),
3. Faust Valley Drainage Course (FVD),
4. M-585 French Drain Site (M-585),
5. Blue Creek,
6. Sanitary Sewage Treatment Evaporation Pond (SSTEP),
8. M-636 X-O-MAT Discharge Area (M-636). J
After initiation of the IRP Phase II Stage 1 field program, investigations at M-636 and M-508 were suspended.
These two areas are being investigated by Thiokol as part of a Resource Conservation and Recovery Act
(RCRA) Closure Plan. Figure 1-3 identifies the locations of these sites.
1.5 DESCRIPTION AND STAGE 1 CHARACTERIZATION OF SITES
Field activities conducted under Phase II Stage 1 are summarized in Table 1-2 and are discussed in the Plant 78
IRP, Phase II Confirmation/Quantification, Stage 1 Report (ESE, 1989). The results of the Stage 1
investigations for each site are summarized below.
1.5.1 NORTH DRAINAGE DITCH
Since the 1960's, petroleum hydrocarbon wastes, solvents, and wastewater have been discharged into the surface
drainage ditches surrounding Buildings E-512, E-516, and M-508. The Stage 1 field activities consisted of the
coUection of surface water and surface sediment samples from three locations in the NDD (Figure 1-4). Six
surface sediment and six surface water sample couplets were coUected and analyzed. In addition, six shaUow
(25 foot) soU borings were driUed and sampled at 5 to 8 feet, 15 to 16 feet, and 25 to 26.5 feet, next to the three
surface water and sediment samples (Figure 1-4). Twenty soU samples were coUected and analyzed from the
shaUow borings. After the imtial field work for the NDD, one groundwater momtoring weU P-3 was instaUed
under extended Stage 1 field work.
Stage 1 analytical results indicate that the surface water in the NDD contains detectable levels of petroleum
hydrocarbons, halomethanes, volatUe organohalogens, and metals. None of the organic contaminants occurred
above the maximum contaminant levels (MCLs) estabhshed by the EPA, although many of the concentrations
do exceed the EPA recommended 10"* human health risk level. /AU metal concentrations were found to be within £cf*&\\
the reported ranges of representative United States (U.S.) concentrations in surface water (ESE, 1989).
7. M-508 X-O-MAT Discharge Area (M-508), and
1-8
700 1400 Feet
APPROX. SCALE IN FEET
Figure 1-3
PLANT 78 GENERAL LOCATION MAP
SOURCE: FACILITY DOCUMENTS; ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
1-9
P7S-914/P78T1-2.1
02/14/92
Table 1-2. Phase II Stage 1 Field Program for Plant 78 (Page 1 of 2).
Site Name Field Activities Rationale
North Drainage Ditch Collected surface water and composite
sediment samples at the conduit near E-516,
near the confluence with E-517 ditch, and at
the instaUation boundary. Performed stream
flow measurements. InstaUed three soil
borings to a depth of 25 feet. CoUected three
split-spoon soU samples per boring for
chemical analysis. DupUcate samples were
coUected in the first interval of borings 25A
and 25C.
Characterize potential contamination by oUs,
solvents, metals, and propeUants, and potential
for migration to Blue Creek.
E-512 Drainage Ditch Collected surface water and composite
sediment sample.
Characterize potential contamination by oUs,
solvents, and metals.
Faust Valley Drainage Ditch CoUected composite sediment samples at
confluence of Faust VaUey Drainage Ditch
and Faust VaUey Road, and Faust VaUey
Drainage Ditch and R Avenue. One deep
boring, 200B (260 feet), was completed in the
VaUey FiU Aquifer as a ground water
monitoring weU and sampled. Eight split-
spoon soU samples were coUected from Boring
200B.
Characterize potential contamination by oils,
solvents, and metals. EstabUsh background
conditions and define VaUey FU1 stratigraphy.
P78-914/P78T1-2.2
02/14/92
Table 1-2. Phase II Stage 1 Field Program for Plant 78 (Page 2 of 2).
Site Name Field Activities Rationale
M-585 French Drain Performed a geophysical survey to determine
drain location and subsurface contamination.
Installed seven soil borings for collection of
split-spoon soil samples and evaluation of
stratigraphy. Three borings were drilled to a
maximum depth of 50 feet and monitored in
the field for organic vapors. One deep
(180 feet) boring was completed in the Valley
Fill Aquifer as a monitoring well and sampled.
Three additional 50 feet borings were drilled
foUowing field detection of organic vapors
from previous borings. DupUcate samples
were coUected in the first interval of borings
50A, 50C, and 50F, as weU as in the first
interval of deep weU 200A.
Estimate and characterize lateral extent of
potential contamination by acids, alkalies, and
organic solvents. Define VaUey FU1
stratigraphy and investigate potential
groundwater contamination in perched VaUey
FU1 Aquifer.
Blue Creek
Sanitary Sewer Treatment
Evaporation Pond
Performed stream flow measurements
upstream and downstream of plant adjacent to
Thiokol landfiU, and at tributary inflows where
possible. CoUected surface water and
composite sediment samples upstream and
downstream of plant, near Thiokol landfiU and
potential tributaries leading from Plant 78.
CoUected one composite sediment sample
from evaporation pond.
Determine influent/effluent conditions.
Evaluate background conditions and potential
for offsite migration.
Verify presence or absence of contaminants in
sanitary sewer system.
M-508 X-O-Mat Performed a geophysical survey to estimate
extent of subsurface contamination.
Evaluate extent of potential sUver and heavy
metal contamination.
Source: ESE, 1989.
TO HOWELL
Shallow (Max. Depth 25 Feet)
Soil Boring
Extended Phase II Stage 1
Deep Boring Well
Extended Phase II Stage 1
Shallow Borings (50 Feet)
300 600 Feet
SCALE IN FEET
Figure 1-4
PHASE II STAGE I NORTH DRAINAGE DITCH / E-512 DRAINAGE DITCH
SOURCE: FACILITY DOCUMENTS; ESE, 1989
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-921/P781.13
02/13/92
Analytical results indicate surface sediments in the NDD were found to contain detectable levels of petroleum
hydrocarbons and metals. Other organic analytes were not detected in the NDD surface sediments. All metal
concentrations were found to be within the reported ranges of representative U.S. concentrations in surface
sediment.
Soil borings, sampled in the NDD during the Stage 1 study, contained detectable levels of petroleum
hydrocarbons and methylene chloride. Groundwater samples were not taken from monitoring well P-3 under
This ditch was used for the disposal of paint booth water and chromated rust inhibitor prior to 1980. Metals
and petroleum hydrocarbons were detected in a composite sediment sample.
Concentrations of all inorganic constituents, measured in the surface water sample in the Stage 1 study, did not
exceed the National Interior Primary Drinking Water Regulations (NIPDWR) or National Secondary Drinking
Water Regulations (NSDWR) recommended levels. Major and minor element chemistry, including sulfate,
chloride, nitrogen, and phosphorous, were comparable to the onsite water supply that indirectly supplies the
ditch. Volatile organohalogens; including 1,1-dichloroethane, 1,1,1-trichloroethane, 1,1-dichloroethene,
trichloroethylene, tetrachloroethene, bromoform, and chloroform; were detected in the E-512 surface water
sample. None of the compounds detected exceeded the MCLs established by the EPA. Both bromoform and
1,1-dichoroethene exceeded the EPA recommended 10"* human health risk level.
1.5.3 FAUST VALLEY DRAINAGE COURSE
FVD is a major surface drainage feature on Plant 78, and has reportedly received paint booth water and
chromated rust inhibitor disposed in a smaller tributary, the E-512 Drainage Ditch (ES, 1984). Field
observations revealed, however, that the E-512 ditch does not discharge into the FVD.
Analysis conducted on all surface sediment and soil samples revealed that concentrations of metal analytes were
within representative ranges of those elements in soils and surficial sediments in the western U.S. (ESE, 1989).
Concentrations of beryllium, copper, chromium, lead, nickel and zinc appear to increase slightly between
upgradient and downgradient surface sediment samples. Petroleum hydrocarbons were detected in all the FVD
surface sediment and soil samples.
To estabUsh background chemical conditions at Plant 78, a deep boring (200B) was driUed upgradient of the
plant near the northeast instaUation boundary and Faust VaUey Road and soU samples were coUected.
Groundwater momtoring weU P-1 was constructed in this boring and a water sample was coUected for chemical
Stage 1 field activities. \
1.5.2 E-512 DRAINAGE DITCH
1-13
P78-921/P781.14
02/13/92
analysis. These samples estabhshed background groundwater and soil chemical parameters for Plant 78. Organic
contaminants were not detected in soil samples from boring 200B or in groundwater from monitoring well P-1.
Concentrations of all inorganic constituents measured were within Utah State drinking water standards, MCLs,
and EPA recommended 10"6 Human Health Risk Criteria.
Momtoring well P-1 and boring 200B are included in the FVD site based upon their geographic location.
1.5.4 M-585 FRENCH DRAIN SITE
M-585 consists of a 4-inch diameter gravity flow line leading westward from Building M-585 and drains into a
subsurface pit (Figure 1-5). The drain has received laboratory rinsewater containing waste propeUants, acids,
alkalies, and various solvents, including acetone, methyl ethyl ketone, and benzene. Disposal of solvents into this
drain was discontinued in 1973. The drain is still used for disposal of nonhazardous wastewater.
A geophysical survey (EM-31 profiling) conducted under Stage 1 indicated an anomalous conductive trend
starting at the French Drain and continuing to the southwest. These results are consistent with a possible
contamination plume originating from the French Drain and moving downgradient to the southwest.
Detectable levels of metals, ammonia, petroleum hydrocarbons, and methylene chloride were reported in some
or aU soU boring samples coUected at M-585. Metal concentrations in samples from the French Drain were
consistent with values observed in the FVD background soU boring, and are compatible with values reported as
average environmental concentrations in U.S. sous. Ammonium concentrations were higher than those observed
at FVD. SoU boring samples at M-585 contained detectable levels of petroleum hydrocarbons and methylene
chloride.
Chloroform, methylene chloride, 1,1,1-trichloroethane, and toluene were detected at low concentrations in
groundwater from momtoring weU P-2. None of these compound concentrations occurred above the MCLs
established by the EPA. However, both chloroform and methylene chloride concentrations exceeded the EPA
recommended 10'6 human health risk level.
1.5.5 BLUE CREEK
Blue Creek, a perennial stream, flows adjacent to the western boundary of Plant 78 (Figure 1-6). Past water
quahty sampling by Thiokol indicates that Blue Creek surface water has elevated levels of iron and copper and
also detectable levels of ammonium perchlorate, a propeUant ingredient.
Detectable levels of metals were found in the Stage 1 surface sediment samples. Samples taken both upgradient
and downgradient of Plant 78 are comparable to the range of environmental concentrations of metals in U.S.
sous and surficial sediments (ESE, 1989). The Blue Creek tributary ditches, with the exception of the 1400 Street
1-14
EXPLANATION-
PHASE II STAGE 1 SURVEY
O Soil Boring
® Deep Stratigraphic Boring (Well)
50 100 Feet
SCALE IN FEET
Figure 1-5
M-585 SITE AND STAGE I
BORING LOCATIONS
SOURCE: FACILITY DOCUMENTS; ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
1-15
NORTH
DRAINAGE
DITCH
FAUST VALLEY
DRAINAGE COURSE
Intermittent Stream
Perennial Stream
Ditch
Figure 1-6
BLUE CREEK STAGE I SAMPLING AND
SURFACE WATER FLOW LOCATIONS
SOURCE: FACILITY DOCUMENTS: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
1-16
P78-921/P781.17
02/13/92
ditch, exhibited metal concentrations comparable to those observed in Blue Creek. The 1400 Street ditch sample
contained higher concentrations of beryllium, copper, chromium, lead, nickel, and zinc than did the other Blue
Creek surface sediment samples.
Ammoma was also detected in the sediment samples from Blue Creek. The highest concentration occurred in
the 1400 Street ditch sample. Petroleum hydrocarbons were the only organic contaminant detected in all the
Blue Creek surface sediment samples. The concentration of petroleum hydrocarbons increased in a
downgradient direction within the creek.
Surface water samples from Blue Creek indicated the presence of detectable concentrations of petroleum
hydrocarbons, bromoform, chloromethane, methylene chloride, trichloroethylene, and benzene. None of these
compounds occurred above the MCLs or maximum contaminant level* guidelines (MCLGs) estabhshed by the
EPA. Concentrations of chloromethane, methylene chloride, and benzene, however, did exceed the EPA
recommended 10'5 Human Health Risk Criteria.
1.5.6 SANITARY SEWAGE TREATMENT EVAPORATION POND
Domestic sewage from administrative and manufacturing facilities at the north end of Plant 78 is collected and
treated at the SSTEP (Figure 1-4). No industrial wastes were reported to have been disposed in the sanitary
sewer.
Petroleum hydrocarbons were detected in a surface sediment sample. None of the other analyte concentrations
measured in the sample from SSTEP under Stage 1 were above analytical detection limits.
1.6 CATEGORIZATION OF SITES
Based on results of the Phase II Stage 1 IRP investigation, the sites investigated were assigned to one of three
categories:
1. Requiring no further action,
2. Requiring further Phase II investigation, or
3. Requiring remedial action.
Six of the eight sites investigated were assigned to Category 2. The remaining two sites (M-508 and M-636) weie
removed from the IRP investigation prior to the completion of the Stage 1 investigation. These two sites are
currently being investigated by Thiokol as part of a RCRA Closure Plan. None of the sites investigated were
considered suitable for Category 1 or Category 3 classification. Table 1-3 summarizes classification of sites and
recommendations for additional evaluations.
1-17
P78-921/P78T1-3.1
02/14/92
Table 1-3. Summary of Phase II Stage 1 Recommendations, Plant 78.
Site Classification Recommendations
North Drainage Ditch Category 2
E-512 Drainage Ditch Category 2
Faust VaUey Drainage Course Category 2
M-585 French Drain Category 2
Blue Creek
Sanitary Sewer Treatment
and Evaporation Pond
M-508 X-O-MAT
M-636 X-O-MAT
Category 2
Category 2
Not Classified
Not Classified
Resampling surface water in ditch
SampUng ditch sediments at depth to determine contaminant distribution
Install monitoring weUs to determine water quahty and hydrauhc gradient
CoUect soU samples to verify presence of contaminants and determine subsurface distribution
Perform aquifer testing
Resample surface water to verify presence of contaminants
Sample ditch sediments at depth to determine contaminant distribution
Collect soU samples to determine subsurface contaminant distribution
Install monitoring weU to determine water quahty and hydrauhc gradient
Perform aquifer testing
Sample ditch sediments at depth to determine contaminant distribution
Resample groundwater to provide background comparison
Perform aquifer testing
Perform soU gas investigation
Install two monitoring weUs to verify water quaUty and determine hydrauhc gradient
Resample existing monitoring weU to verify presence of contaminants
CoUect soU samples to verify subsurface distribution of contaminants
Perform aquifer testing
Resample Blue Creek sediment and surface water to verify the presence of
contaminants and estabUsh background conditions
Sample pond sediments to verify presence of contaminants
RCRA Investigation assigned to Thiokol
RCRA Investigation assigned to Thiokol
Source: ESE, 1989.
P7&921/P781.19
02/13/92
1.6.1 NORTH DRAINAGE DITCH
The NDD was assigned a Category 2 classification requiring further Phase II investigation. Detectable levels
of petroleum hydrocarbons, halomethanes, and volatile organohalogens were observed in surface sediment and
surface water under Stage 1 sampling. Additional sampling of soil, surface sediment and water, and groundwater
sampling of momtoring well P-3 was recommended to verify the presence of contaminants observed under
Stage 1. Aquifer testing, to determine aquifer characteristics, was also recommended for monitoring well P-3.
1.6.2 E-512 DRAINAGE DITCH
E-512 was assigned a Category 2 classification requiring further Phase II investigation. Petroleum hydrocarbons
were detected in the surface sediment sample and purgable organohalogens were detected in the corresponding
surface water sample. As a result, additional sampling of E-512 surface water, surface sediments, and shaUow
soU borings was recommended to verify the presence and extent of contamination at E-512. In addition,
instaUation of a groundwater momtoring weU was recommended at E-512 to first water. Analysis of the soU
samples from the instaUation of the monitoring weU, as weU as a groundwater sample, was recommended to
detect surface contaminants. Aquifer testing of the momtoring weU was recommended to determine aquifer
characteristics.
1.6.3 FAUST VALLEY DRAINAGE COURSE
The FVD was assigned a Category 2 classification requiring further Phase II investigation. Additional sampling
of surface sediments along the length of the ditch was proposed to investigate the presence of petroleum
hydrocarbons identified in surface sediments and in deep boring 200A. SampUng of groundwater from
momtoring weU P-1 was recommended to provide a comparison to background conditions determined in Stage 1.
Aquifer testing of momtoring weU P-2 was also recommended to determine aquifer characteristics.
1.6.4 M-585 FRENCH DRAIN SITE
M-585 site was assigned a Category 2 classification requiring further Phase II investigation. Stage 1 sampling
detected petroleum hydrocarbons, ammoma, and methylene chloride in soU samples coUected in the vicinity of
the French Drain. In addition, a groundwater sample coUected from momtoring weU P-2 indicated the presence
of low concentrations of methylene chloride, chloroform, 1,1,1-trichloroethane, and toluene. A soU gas survey
was recommended to identify the extent of subsurface contamination indicated by the electromagnetic (EM)
geophysical survey. Any resulting geophysical anomalies detected were to be investigated and at least one
additional momtoring weU instaUed downgradient of monitoring weU P-2. A recommendation was made to
sample and analyze groundwater from both the proposed new momtoring weU and existing momtoring weU P-2
for organic parameters identified in Stage 1. Aquifer testing of aU the groundwater momtoring wells was
recommended to determine local hydrogeologic characteristics.
1-19
P78-921/P781.20
02/13/92
1.6.5 BLUE CREEK
Blue Creek and its associated tributaries were classified as a Category 2 site requiring further Phase II
investigation. During Stage 1 investigations, petroleum hydrocarbons, ammoma, and elevated levels of metals
were detected in Blue Creek surface sediment samples. Surface water samples indicated detectable levels of
petroleum hydrocarbons, volatile organohalogens, and volatile aromatics. It was recommended that surface water
and sediments be resampled to verify the presence of contaminants detected during Stage 1 investigations. In
addition, several shallow soil borings and samples were recommended for the 1400 Street ditch and the
1500 Street ditch to further investigate elevated levels of contaminants detected during Stage 1.
1.6.6 SANITARY SEWER TREATMENT EVAPORATION POND
As a result of the Stage 1 investigations, the SSTEP site was selected for Stage 2 investigation; however, it was
later eliminated from Stage 2 due to the low levels of contamination detected in Stage 1, the low probability of
industrial chemical contamination and the decision to concentrate investigation resources on sites with higher
contamination probabilities.
1.6.7 E-515 AND E-519 ACID DRAINS
In December 1988, two additional sites, E-515 and E-519, were added to the Stage 2 investigation. Neither of
these sites were investigated under Stage 1. Both sites contain "acid drains" that reportedly received laboratory
wastewater in past operations. Neither of these two sites is currently used as a laboratory facihty. In order to
investigate possible surface and subsurface contamination resulting from laboratory disposal practices, drilling
and sampling of a deep boring and instaUation of a groundwater momtoring weU were recommended for each
site.
1.7 IDENTIFICATION OF THE FIELD TEAM
The Phase II Stage 2 effort was active between October 1988 and March 1990. Personnel key to the Stage 2
effort are hsted in Table 1-4 and their resumes are included in Appendix B.
1-20
P78-921/P781.21
02/13/92
Table 1-4. Current Stage 2 Key Project Staff.
Name Title
Lou Bilello (John Bonds)
Robert Chesson (Wendy Howell)
Ken Dahlin
Deborah McKinley
Carolyn Fordham (James Kountzman)
Project Director, Phase JJ
Project Manager, Stage 2 Phase JJ
Project QA Supervisor
Feasibility Study Task Manager
Risk Assessment Task Manager
NOTE: Parentheses ( ) indicate a change in personnel.
Source: ESE, 1991.
1-21
2.0 ENVIRONMENTAL SETTING
P7M14/P782.1
2/13/92
2.0 ENVIRONMENTAL SETTING
2.1 GEOGRAPHIC SETTING
The geographic setting, or physical landscape, is a function of both physiography and topography. Significant
features of both will be used to describe the appearance of the landscape in the vicinity of Plant 78.
2.1.1 PHYSICAL GEOGRAPHY
Plant 78 is located within the Basin and Range Physiographic Province of northern Utah (Figure 2-1). This
province is characterized by broad valleys trending north and south, bounded by relatively low mountains on
either side of the valleys. Two major physiographic features of the general area are the Great Salt Lake, located
south of the plant, and the Wasatch Mountain Front, located east of the plant.
The topography of Plant 78 is typical of the general province topography. The plant is on the eastern side of
Blue Creek Valley. The North Promontory Mountains are located on the western side of Blue Creek VaUey,
and the Blue Spring HiUs are located on the eastern side of the vaUey (Figure 2-2). Engineer Mountain, located
southwest of the plant, has elevations approximately 600 feet above the vaUey floor. The highest peak on
Engineer Mountain is 5,263 feet above the National Geodetic Vertical Datum (NGVD) of 1929. Blue Creek,
which flows south through the lower elevations of the Blue Creek VaUey, has cut a relatively deep (40 feet)
meandering path through the soU and the lalce clays and gravel deposits. Blue Creek flows near the western
property boundary of Plant 78 and empties into the northern section of the Great Salt Lake.
Elevations on the plant vary from a high of 5,020 feet above NGVD on the western edge of the Blue Spring Hills
to a low of 4,444 feet above NGVD near Blue Creek. The plant relief is low to moderate, with slopes of
approximately 2 percent in the northern section of the plant and approximately 13 percent in the southeastern
section of the plant.
The areas immediately surrounding Plant 78 include agricultural lands to the north and west, mountains to the
east, and industrial development (Thiokol) to the south.
2.1.2 CULTURAL GEOGRAPHY
Plant 78 is located approximately 35 mUes west of Brigham City, Utah (Figure 1-1). Land surrounding the plant
is used primarily for farming and ranching. Brigham City is the closest major population center to the plant,
although the smaU town of Conine is located approximately 25 mUes east of the facihty. Additional information
regarding pubhc health and welfare are included in the Risk Assessment, Section 4.2.
2-1
HANZEL MOUNTAINS -
WEST HILLS
USAF
PLANT 78
MIDDLE
ROCKY
MOUNTAINS
JBASIN AND RANGE-!
COLORADO
\
/
COLORADO
PLATEAU
TRANSITION
PLATEAU
EXPLANATION
Major Physiographic
Province Boundary
I
N
Physiographic Subdivision
Boundary
«- State Boundary
0 20 40 Miles
SCALE IN MILES
Figure 2-1
REGIONAL PHYSIOGRAPHIC FEATURES
SOURCE: STOKES, 1977; ES, 1984; ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
2-2
ANDERSON
HILL
NORTH
PROMONTORY
MOUNTAINS
SCALE IN MILES
Figure 2-2
LOCAL PHYSIOGRAPHIC FEATURES
SOURCE: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
2-3
P78-914/P782.4
2/13/92
2.2 GEOLOGY
Plant 78 is located in the outcrop areas of the lake clays and gravel units of Quaternary Age and is surrounded
by outcrops of Paleozoic, Mesozoic, and Tertiary sedimentary bedrock units (Figure 2-3). The lake clays are
composed of clay and silt, while the lake gravels are composed of gravel with minor amounts of sand, silt, and
clay. The geology in the area of the plant is complex and involves both unconsolidated and consolidated
sediments. No major folds or faults are present on the plant, although some minor faults do exist within the
area.
2.2.1 GEOLOGIC SETTING
Plant 78 occurs in an area of Quaternary lake clays and gravels, and is flanked on the east and west by
outcropping Mississippian-age bedrock (Figure 2-3). General geomorphologic characteristics of the area are
discussed in Section 2.1.1. Tectonic and seismic history are discussed below.
Plant 78 has been affected by two moderately large earthquakes in recent years. On March 28, 1975, an
earthquake ranking 6.0 on the Richter Scale was felt by employees of the plant. The epicenter of this earthquake
was in Pocatello Valley, Idaho, approximately 30 miles north of the plant (Richens, 1984). According to the
Richter Scale, an earthquake ranked between 6.0 and 7.0 is potentially destructive. As a result of this
earthquake, Blue Creek changed from an intermittent stream to a perennial stream. A second earthquake, also
felt by plant employees, occurred on October 28,1983, and was ranked 7.3 on the Richter Scale. The epicenter
of this earthquake was in MacKay, Idaho, approximately 175 miles north of the plant. According to the Richter
Scale, an earthquake ranking between 7.0 and 7.7 is a major earthquake. There have been no observable effects
from either earthquake at Plant 78. Numerous smaller earthquakes, ranking between 2.0 and 3.0 on the Richter
Scale, have occurred within 50 miles of Blue Creek Valley throughout historical time (Richens, 1984).
2.2.2 BEDROCK GEOLOGY
Bedrock in the Plant 78 area consists of Tertiary, Permian, Pennsylvanian, and Mississippian age units
(Figure 2-3). These include the volcaniclastic-rich sandstones, conglomerates, and limestones of the Tertiary Salt
Lake Group (Tsi), and the calcareous sand and orthoquartzite of the Permian Diamond Creek Sandstone (Pdc).
Bedrock near Plant 78 also includes the Manning Canyon Shale (MPPmc) that consists of shales and siltstones,
as well as the Great Blue Formation (Mgb), which is comprised of massive limestone. Hydrolgeologic
characteristics of these formations are discussed in Section 2.3.
Plant 78 occurs in a structural graben in which the Plant 78 area has been downfaulted relative to surrounding
bedrock (Figure 2-4). Quaternary sediments were either deposited in or preserved in the graben (lake clays and
gravels). This type of tectonic activity may have produce fracturing within bedrock units, and the Engineering
Science report (1984) implies that fracturing may be present in bedrock outcrops in the southeast corner of
Plant 78.
2-4
-PPPo
EXPLANATION
<=>'(\<X
•
Qlc - Lake Clays
Qas - Alluvium
Qg - Gravel
Qs - Sandy Deposits
Tsl - Salt Lake Group
Pdc - Sandstone
Diamond Creek
PPPo - Oquirrh Formation,
Undifferentiated
0 ^
MPPmc - Shale
Manning Canyon
Mgb-
Great Blue Formation
Contact, Surficial Where Dashed
Fault, Dashed Where Inferred;
U, Upthrown Side; D, Downthrown Side
Thrust Fault Dashed Where Inferred;
Saw-Teeth On Upper Plate Side
N
2 Miles
SCALE IN MILES
Figure 2-3
GEOLOGIC MAP
SOURCE: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
2-5
WEST
5400 -
5200
5000 -
4800 -
Q > O
z
UJ > o m <
|jj 4600
LL
z
O 4400
w 4200 -
4000 -
3800 -
EXPLANATION
Water-Bearing Zones
Arrow Indicates Direction
of Fault Movement
Gravel Zones
NOTE: SEE FIGURE 3-6 FOFTCROSS SECTION LOCATION
1000 2000 Feet
APPROX. SCALE IN FEET
Figure 2-4
GEOLOGIC CROSS-SECTION
SOURCE: FACILITY DOCUMENTS; ESE, 1091
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-914/P782.7
2/13/92
2.2.3 SURFICIAL GEOLOGY
2.2.3.1 Surficial Sediments
The surficial sediments of Plant 78 consist of the Quaternary lake clays and gravels, deposited while Pleistocene
Lake Bonneville covered the valley. During the Pleistocene, Lake Bonneville, a very large, pluvial, fresh water
lake, existed throughout large areas of northern Utah (Flint, 1971) (Figure 2-5). The remnant of Lake
Bonneville is the Great Salt Lake, now rendered too salty by evaporation to be usable for irrigation or drinking.
Bonneville Lake levels in the Plant 78 areas were several hundred feet above the present ground surface as
evidenced by wave-cut benches observable on the flanks of the North Promontory, Promontory, Engineer
Mountains, and the Blue Spring Hills. These wave cut benches are clearly visible at many places along the
margins of the Blue Creek Valley, especially near the highest level (5,200 feet) reached by the lake (Bolke and
Price, 1972).
The lake clays consist of thinly bedded dark grey to red, organic rich, silty clays interbedded with medium- to
fine-grained clay rich sands. The lake gravels consists of discontinuous, lobate and sheet shaped pebble
conglomerate, usually less than five meters thick, and are generally poorly sorted, ranging from clast to matrix
supported. The gravel clasts are subrounded to subangular and are composed predominantly of limestone,
sandstone, and rare chert.
The lake clays and gravels were deposited in a shaUow lacustrine environment. The Basin and Range Province
of block uplifts and grabens provided an environment of rapid erosion and deposition of sediments. The
stratigraphic relationships of the sedimentary features, observed at Plant 78, indicate that these sediments
accumulated in a mixture of shaUow to deep, humid aUuvial fans, restricted to open lake and lake margin
environments.
Organic rich fine-grained clay, sUts, and sands present in the lake clays and gravels represent the low-energy
depositional environment of the lake. Gravels represent flood derived sediments washed down off the uplifts
in the form of sheet floods, mud flows, and subaqueous aUuvial fan deposits. A generalized reconstruction of
the paleogeography for the lake clay and gravels deposits at Plant 78 is shown in Figure 2-6.
The surficial sediments at Plant 78 have been penetrated by numerous borings. One deep boring (E-519B1;
180 feet deep) encountered numerous layers of sUt and gravel, with varying compositions of clay and sand
(Figure 2-7). This sequence of varying compositions is typical of the lake clays and gravels sediments. Cross
section and test boring locations are shown on Figure 2-8. The cross sections shown on Figures 2-9, 2-10,
and 2-11 iUustrate the stratigraphy of surficial geologic material underlying the plant. Cross sections A-A' and
B-B' shown in Figures 2-9 and 2-10, respectively, iUustrate the shaUow stratigraphy in the northern and central
sections of the plant. Sandy sUt dominates the northern section, and clayey sUt is dominant in the central section.
2-7
Figure 17-3 Sketch map showing pleistocene lakes in Westem United States.
(From Flint, 1971)
Figure 2-5
MAP SHOWING PLEISTOCENE PLUVIAL LAKES
IN WESTERN,UNITED STATES
SOURCE: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
2-8
1 j ' ! i I Pre-Quatemary Rocks
Figure 2-6
SCHEMATIC BLOCK DIAGRAM SHOWING THE VERTICAL AND LATERAL
RELATIONSHIPS OF FACIES AND DEPOSITIONAL ENVIRONMENTS DURING
DEPOSITION OF THE LAKE CLAYS AND GRAVELS
SOURCES: Modified from Hildebrand and Newman, 1985; ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
CO/P7B/P.8/E518/B-1
4" Rise Of Pad To Allow For
Proposed Asphalt Pavement
Ground Elevation:
4517.80 ft
15
30
45
60
75
90
105
120
135
150.
165.
180.
Rebar P-8
/
Limited Access Water-Tight
Manhole Cover (Flush Installation)
t-W
•W
%
w
w
•w •w •w w •w w w •w
ass w w w w
to:
159.10' 7/89
— (4358.7'MSL)
$
w
Lw to" •w •v. v.
••>«
•w •w •w v w
es
E-519/B-1
'#."#.*#.*#.*#.
• . a. y.y.y.y.y.
y. y. y. y. y. y. *<
*#. >- *#*. V. V. >
179.64 ft
Poorly graded gravel, clayey, poorly graded und, low plasticity, dense
slightly moist. (GP) dark grayish brawn 10 YR 4/2.
Very silty, day. low plasticity, moist, firm. (CL) brown 10 YR 5/3.
Silt, low pUsttoSy. slightly candy, gravelly with vary fine-grained aand. moist Soma Iron
oxide staining. (ML) ight gray 10 YR 7/2. Clayey, grading downward into alts. Lightly
motet, non-plastic Pebbles up to 1 1/2", mottled taxtura. (ML) Light gray to brown 10
YR7/2-10YRS3. Sampla P7B-S*8 coBected at 20-21.5 laat TIP-23.2 ppm.
Silts, clayey, slightly gravely with vwy fite-grained sand, non-plastic.
(GP) Light gray to brown grading down Into gravadO YR 0(2.
Silts, gravally, and fina-grainad sand, noo-ptasSc to low plasticity, slightly moist.
Pebbles 1M--1/7 kl diameter. (ML) Yellowish brown 10YRSV8. Brownish yellow 10 YR
616. Sample P78-S*7 taken at 36 - 37 laat Clayey, minor lenses ol poorly sorted,
slightly moist sandstone, low plasticity. (ML) yelowtsh brown 10 YR 5/8.
Sand, sightly slty, clayey, sightly moist, poorly sorted, low plasttoty.
(SM) yellowish brown 10 YR 578.
Gravel poorly gradad, loose pebbles and cobbles up te 2* in diameter, sandy, minor
sit grading downward Into gravel up to 1/2* ki diameter. Moderately sorted.
(GP) yelowlsh brown 10 YR SI6.
Coarse gravel slty. day, poorly sorted and graded, dry. Pebbles of dark gray
days tone, color variegated. (QM)
GravaL sightly slty and clayey Increasing towards bottom, slightly plastb.lncreaslngly
moist (GM)yelcwtehbrown10YR3/4.
Gravel with thin lenses of slty daystone. moderately plastic (GM) yellowish brown 10
YR5/8.
Gravel with minor ciayey^tty matrix, sag r^ (GM)yeSowish
brawn 10YR5/8. Sample P7B-S*8 takan at 97-87.4 feet.
Poorly gradad gravel wtth tMn lenses of slty daystone, slightly moist, tow plasticity.
(GM) yetawMi brown 10 YR S/B.
Silt, sandy, minor gravel, very tow moisture, tow plasticity.
(ML) brownish yellow 10 YR 6/8.
Clayey, dry, norvpiastic
Silt, very fine-grained sand, minor gravel, no moisture, tow to non-plastic
(ML) yelowlsh brawn 10YR5/8. Sampla P78-S*9 takan at 137-138 feat
Minor Interbedded sltstona, sTIghtry moist
Minor sK wth thin lenses of day, low moisture, slightly plastic
(ML) yelowlsh brown 10 YR 678.
SDt. vary dayay, minor gravel, poorly sorted, moist, moderate plasticity, moderately
danse.
(ML) dark yeOcwUt brown 10 YR 3*8.
Ctay, minor gravel, traoe of sit, moderately dense, moist, moderately plastic
(ML) dark yellowish brown 10 YR 5/B.
SampleP78-SM0taken at 171/*-1713leaL
Sarnple P78-S-11 taken at 171 J-173Jfaet
TD: 180.40 ft
Vertical Scale In Feet
11nch = 30 Feet
Figure 2-7
BORING LOG E-519B1 AND WELL
CONSTRUCTION DIAGRAM FOR P-8
SOURCE: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
2-10
E-9 E-8
STATE HIG\<WAY «V
NDD/B1-
APPROX. SCALE IN FEET
Figure 2-8
LOCATION OF TEST BORINGS AND
GEOLOGIC CROSS-SECTIONS
SOURCE: FACILITY DOCUMENTS; ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
2-11
A
WEST
4550'-,
>
m <
£ 4500-
—i
4450-
4400-1
200B
E-6
E-5I2/BI
•-3
NOD/BI
M-34
TD K00.2
EXPLANATION
HD Sand
EZ-3 Gravel
CEI Clayey Silt
EB Sandy Slit
•ROUND
SURFACE
TDI27' TD260*
NOTE: SEE FIGURE 3-6 FOR CROSS-SECTION LOCATION
-4500
A"
EAST
r-4550'
-4450
250
•-4400'
500
SCALE IN FEET
Figure 2-9
GEOLOGIC CROSS-SECTION A - A'
SOURCE: FACILITY DOCUMENTS; ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
B
WEST
4600' -i
4550'-
> o z
LU
o 4500'
CO <
r-
Z
o
2
y 4450'-^
4400v
B'
M-16 EAST
t
-GROUND r4600
SURFACE
-4550
EXPLANATION
Sandy Clay EES Clayey Silt
Gravel El Sandy Silt
TD 178' 400 800'
-4500
-4450
L-4400
SCALE IN FEET
NOTE: SEE FIGURE 3-6 FOR CROSS-SECTION LOCATION
Figure 2-10
GEOLOGIC CROSS-SECTION B - B'
SOURCE: FACILITY DOCUMENTS; ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
Figure 2-11
GEOLOGIC CROSS-SECTION C - C
SOURCE: FACILITY DOCUMENTS; ESE, 1001
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-914/P782.15
2/13/92
Cross section C-C, shown on Figure 2-11, illustrates the stratigraphy in the southern section of the plant. Sandy
silt with some gravel is dominant in the western portion of this cross section, but sand with gravel and fractured
sandstone is most abundant in the eastern portion. The eastern portion of Plant 78 is in the area identified by
the Soil Conservation Service (SCS) as having cobbly silt loam soils with shallow fractured rock. This portion
is also in the same area identified by Doelling (1980) as having gravel outcrops. Monitoring well 8A, drilled as
a water supply test well for Thiokol encountered 445 feet of lake and valley fill sediments and 165 feet of
partially fractured and faulted limestone.
2.2.3.2 Soils
The soils of Plant 78 are typically silty loam with combinations of clayey, cobbly, and gravelly loam. Loam is a
soil with varying proportions of sand, silt, clay, and organic matter. The three most extensive soil types are
Hansel silt loam, Hupp gravelly silt loam, and Thiokol silt loam (Figure 2-12). Hansel and Thiokol soil types
developed as a result of the deposit of silty material on lake terraces of Lake Bonneville (Chadwick, et al., 1975).
Hupp soil types developed as a result of the deposit of cobbly and gravelly material in alluvial fans on the slopes
of foothills. Soil descriptions and the engineering properties for all soil types on Plant 78 are summarized in
Table 2-1.
In assessing the potential for surface water infiltration, permeability is the soil property of concern. The vertical
permeabiUty values for the soils on the plant range from 4.2 x 10 s centimeters per second (cm/sec) to
1.4 x 10'3 cm/sec (Chadwick, et al., 1975). These values indicate that surface water wiU infiltrate slowly to
moderately. SCS has ranked the soU types on the plant as having slight, moderate, and severe use limitations
for septic tank absorption fields. Hupp and Thiokol soU types have slight to moderate use limitations, wlule ah
other soU types have moderate to severe use limitations. The SCS has noted slow permeabiUty, land slopes, and
shaUow bedrock as reasons for the use limitations. The SCS use limitations are defined in Table 2-1.
2.3 HYDROGEOLOGY
Plant 78 is located in an area with relatively abundant but unusable groundwater. Figure 2-4 illustrates the
location of water-bearing zones within WeU 8A underlying the plant vicinity. Table 2-2 summarizes the local
hydrogeologic units and their water-bearing characteristics. Reports by Carpenter (1913), Holman (1963), Bolke
and Price (1972), Eakin, et al, (1976), Hood (1976), Doelling (1980), and BatteUe (1983) describe the
groundwater resources of the area.
2-15
STATE HIGHWAY 83 "
EXPLANATION
HaB Soil Unit (See Table 2-2
For Description)
700 1400 Feet
APPROX. SCALE IN FEET
Figure 2-12
SOILS MAP
SOURCE: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
2-16
P78-914/P78T2-1.1
02/14/92
Table 2-1. USAF Plant 78 Soils (Page 1 of 2).
Symbol on Unit Description Depth
Figure 2-10 (USGS Designation) (inches)
Permiability
(Centimeters/Second) Septic Tank Absorption Use Limitations'
HaB Hansel silt loam, 1
to 6 percent slopes
(CL or ML)
0-62 1.4 x IO"* to 4.2 x IO"* Severe; moderately low permeability
HpD Hupp gravelly silt
loam, 6 to 10
percent slopes
(GM or ML)
0-18
18-60
1.4 x 10"' to 4.2 x 10"'
1.4 x 10-' to 4.2 x 10-'
Slight to moderate; slopes of 1 to 10 percent
to • KeB Kearns silt loam,
1 to 3 percent slopes
(ML or CL)
0-76 4.2 x 104 to 1.4 x 10"' Moderate to severe; moderate permeability; slopes of
1 to 2 percent
MLE Middle cobbly silt,
10 to 30 percent
slopes
(ML, GM, GC, or
CL)
0-12
12-28
(28-Fractured
limestone)
4.2 x Iff4 to 1.4 x 10-'
4.2 x Iff4 to 1.4 x 10"'
Severe; slopes of 10 to 70 percent; moderate
permeability; bedrock at depth of 24 to 28 inches
MJG Middle-Broad
association, steep
(cobbly silt loam)
(ML, GM, GC, or
CL)
0-12
12-28
(28-Fractured
limestone)
4.2 x 10-* to 1.4 x 10"'
4.2 x IO"* to 1.4 x Iff5
Severe; slopes of 10 to 70 percent; moderate
permeability; bedrock at depth of 24 to 28 inches
PWD Pomat silt of fine
loam, 6 to 10
percent slopes
(ML, CL, or SM)
0-56
56-65
4.2 x 104 to 1.4 x 10-'
4.2 x Iff4 to 1.4 x 10"'
Moderate to severe; slopes of 6 to 40 percent
P78-914/P7gT2-1.2
02/14/92
Table 2-1. USAF Plant 78 Soils (Page 2 of 2)
Symbol on Unit Description Depth
Figure 2-10 (USGS Designation) (inches)
Permeability
(Centimeters/Second) Septic Tank Absorption Use Limitations'
ThB Thiokol silt loam,
1 to 6 percent slopes
(ML)
0-60 4.2 x KT* to 1.4 x 10-' Severe; slow permeability
Wr Woods Cross silty
clay loam,
moderately saline
(ML or CL)
0-60 4.2 x IO"1 to 1.4 x 10"* Slight to moderate; moderate permeability
to •
oo
Slight - soil properties are generally favorable for use; limitations are minor and easily overcome.
Moderate - soil properties are unfavorable, but can be overcome or modified by special planning and design.
Severe - soil properties are so unfavorable and so difficult to correct or overcome as to required major soil reclamation and special designs.
Source: Chadwick, et al., 1975.
P78-914/P78TT2-2.1
02/14/92
Table 2-2. Hydrogeologic Units and Their Water-Bearing Characteristics in the Vicinity of USAF Plant 78.
Svstem Hydrogeologic Unit
Hydrogeologic
Classification
Approximate Dominant
Thickness Lithology
(feet)
Water-Bearing Characteristics
Lake Clays Possibly Perched
Aquifer
50 to 2000 Clay and silt Above water table; transmit water slowly.
Quaternary
Alluvium
Gravel
Possibly Perched
Aquifer
50 Clay, silt, sand, and gravel Above water table; transmits water slowly.
Possibly Perched
Aquifer
50 Gravel, minor sand, silt and Above water table; transmit water readily,
clay
Sandy Deposits Possibly Perched
Aquifer 50 Sand Above water table, transmit water readily.
•
Quaternary and
Tertiary
Valley-Fill Deposits Aquifer (most 200 to 450
permeable aquifer in
Blue Creek Valley
Clay, sand and gravel Within Blue Creek Valley ground water reservoir; most
deposits transmit water slowly, but sand and gravel deposits
transmit water readily, properly constructed wells may yield
several hundred gallons per minute.
Tertiary Salt Lake Group Limited Aquifer 150 Tuffaceous sandstone,
conglomerate, limestone,
and volcanic debris
Generally transmits water slowly; well yields are variable; yields
dependent on fractures and solution cavities.
Permian Diamond Creek
Sandstone
Limited Aquifer Unknown Interbedded limestone,
siltstone,
and orthoquartzite
Generally transmits water slowly; well yields are variable; yields
dependent on fractures and solution cavities.
Pennsyivanian Oquirrh Formation
Undifferentiated
Limited Aquifer Unknown Interbedded limestone,
siltstone,
and orthoquartzite
Generally transmits water slowly; well yields are variable; yields
dependent on fractures and solution cavities.
Mississippian
Manning Canyon Shale Limited Aquifer Unknown Shale and siltstone Generally transmits water slowly; well yields are variable; yields
dependent on fractures and solution cavities.
Great Blue Formation Limited Aquifer Unknown Massive limestone Generally transmits water slowly; well yields are variable; yields
dependent on fractures and solution cavities.
Source: Doelling, 1980 and Bolke and Price, 1972.
P78-914/F*78i20
2/13/92
2.3.1 GROUNDWATER
2.3.1.1 Occurrence and Movement
Groundwater in Blue Creek Valley occurs under unconfined and confined conditions. These two conditions exist
in fractured and faulted bedrock, the lake clays and gravels, unconsolidated alluvium, gravel and sandy deposits
(Bolke and Price, 1972). Precipitation, surface water infiltration, and plant discharges that infiltrate into the
sediments, may migrate slowly, vertically, and/or horizontally, to form perched water tables above the 150 foot
depth of the regional water zone. The discharge of perched groundwater may be vertical to the deeper
water-bearing zone at 150 feet, or horizontal to Blue Creek. Blue Creek may recharge shaUow aquifers in the
center of the Blue Creek VaUey. ShaUow groundwater may migrate faster in gravels in the lake clay and gravels
deposits than in the faulted and fractured bedrock. The direction of movement within the faulted and fractured
bedrock wiU be controUed by the connection of faults and fractures. Figure 2-13 shows the potentiometric
surface map of Blue Creek VaUey in 1970. RegionaUy, the groundwater flow trend is from the north to south;
however, on Plant 78 there is a westerly component of flow. The local direction of groundwater flow on Plant 78
is generaUy west from the Blue Spring HiUs to Blue Creek.
2.3.1.2 Groundwater Quahty
Groundwater quaUty in the immediate vicinity of Plant 78 is poor due to the high salinity and high total dissolved
soUds (TDS) of the water (ES, 1984). Water supply test weUs driUed near Plant 78 (Thiokol WeU Nos. 8A
and 4) encountered saline water. The TDS of both weUs exceeded the Utah water quahty standard
of 1,200 milligrams per liter (mg/L) for agricultural uses. Munk WeU No. 2, approximately 3 mUes northwest
(upgradient) of the plant, encountered fresher water with a TDS of 644 mg/L. Figure 2-14 identifies local wells
and one spring where water samples have been obtained. Table 2-3 summarizes the data for these wells.
2.3.1.3 Groundwater Uses
Groundwater at Plant 78 is not used and not potable due to high TDS. Due to the poor quaUty of groundwater
at Plant 78, water for the plant complex is suppUed from wells and springs up to 10 mUes from the plant.
Groundwater use within the vicinity of the plant is limited to one stock weU (Douglas WeU) and one domestic
water supply weU (Munk WeU No. 2). Both of these wells are located upgradient of Plant 78 and are shown on
Figure 2-14. Data for each of these weUs is summarized on Table 2-4.
The Plant 78 complex is supplied with water from Thiokol groundwater wells in HoweU, approximately eight
mUes north of Plant 78, Thiokol WeU 3A, approximately six nules southeast of the plant, and the Thiokol
Promontory weUs, approximately ten mUes south of the plant. Water is also obtained from RaUwood Springs,
approximately three mUes southeast of the plant, and Maple Springs, approximately ten mUes south of the plant.
During 1981 and 1982, Plant 78 used an average of four-miUion gaUons of water per month (ES, 1984).
2-20
EXPLANATION
—4eoo>— Potentiometric Contour; Datum Is NGVD
Direction Of Ground-Water Movement
NOTE: SEE TABLE 2-4 FOR QUALITY DATA
N
4 Miles
SCALE IN MILES
Figure 2-13
POTENTIOMETRIC SURFACE MAP OF
BLUE CREEK VALLEY AREA, 1970
SOURCE: BOLKE & PRICE, 1972; ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
2-21
Douglas Well
No Data Available
MunkWellNo.2|Q
Spc 1,100 <
TDS - ,v
Cl
PH Munk Well No. 1
No Data Available
SAND HOLLOW ROAO f
Thiokol Well No,
EXPLANATION
Cl Chloride
TDS Total Dissolved Solids
S Salinity
pH Hydrogen Ion Concentration
Spc Specific Conductance
0 Wens In Use
3 WeUs Not In Use
^^Spring
0 CM Test
• Ground Water Monitoring Well
©Gulf OH Test Well
No Data Available 1750 3500 Feet
Approximate Scale In Feet
Figure 2-14
LOCATION OF WELLS AND SPRINGS
SOURCE: ESE 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
2-: •22
P78-914/P78T2-3.1
02/14/92
Table 2-3. Historical Groundwater Quality Data for USAF Plant 78 Vicinity (Analyses are in milligrams per liter) (Page 1 of 2).
Selected Parameters
Specific Dissolved
pH Conductance Solids
Station Identification1 Date (su) (umhos/cm) (1,000) Chloride Iron Salinity
Faust Valley Road Spring 7-14-70 NA 765 NA NA NA NA
Munk Well No. 2 7-14-70 8.2 1,100 644 230 NA NA
Thiokol Well No. 4 Summer, 1958 NA NA NA NA NA 2,500
(original sample)
Thiokol Well No. 4 12-62 NA NA NA NA NA 245-256
Thiokol Well No. 4 6-63 NA NA NA NA NA 1,200
Thiokol Well No. 4 7-2-63 8.0 NA 994 236 0.076 NA
(sample No. 1)
Thiokol Well No. 4 7-2-63 6.7 NA 2,345 1,360 0.165 NA
(sample No. 4)
Thiokol WeU No. 4 7-2-63 6.7 NA 2,711 1,264 0.104 NA
(sample No. 7)
Thiokol WeU No. 4 7-2-63 6.0 NA 2,580 1,210 0.08 NA
(sample No. 8)
P78-914/P7gT2-3.2
02/14/92
Table 2-3. Historical Groundwater Quality Data for USAF Plant 78 Vicinity (Analyses are in milligrams per liter) (Page 2 of 2).
Selected Parameters
Specific Dissolved
pH Conductance Solids
Station Identification1 Date (su) (umhos/cm) (1,000) Chloride Iron Salinity
Thiokol Well No. 8A 10-2-62 7.85 NA NA 1,338 NA NA
(bottom sample)
Thiokol WeU No. 8A 10-17-62 NA 4,340 NA 1,243 NA NA
(avg. value) (avg. value)
^ Thiokol Well No. 8A 10-18-62 NA 4,183 NA 1,249 NA NA
$o (pump setting at 500 ft) (avg. value) (avg. value)
Thiokol WeU No. 8A 10-19-62 NA 4,192 NA 1,275 NA NA
(pump setting at 440 ft) (avg. value) (avg. value)
Thiokol Well No. 8A 10-22-62 NA 4,260 NA 1,232 NA NA
(pump setting at 405 ft) (avg. value) (avg. value)
Thiokol WeU No. 8A 12-63 NA NA NA NA NA 1,300-1,400
NA = Not Analyzed SU = Standard unit umhos/cm = micromhos per centimeter
1 See Figure 3-12 for station locations.
Source: USAF Plant 78 Documents; Holman, 1963; Bolke and Price, 1972.
P78-914/P78T2-4.1
02/14/92
Table 2-4. Well Data for USAF Plant 78 and Vicinity.
Well Identification
on Figure 2-14 Well Owner
Depth (Feci)
Casing Screen Total
Hydrogeological
Unit Taped
Water Level Below Surface
(Feet)
Date
Measured
Geophysical
Use Logs
Douglas
Munk Well No. 1
Munk Well No. 2
Fonnesback
Gulf Oil Test Well
Thiokol Well No. 4
Thiokol Well No. 8
Thiokol Well No. 8A
Well P-1
Well P-2
Well P-3
Well P-4
Well P-5
Well P-6
Well P-7
Well P-8
Well P-9
L.P. Douglas
J.O. Munk
J.O. Munk
H. Fonnesbeck
Gulf Oil Co.
MTI
MTI
MTI
USAF Plant 78
USAF Plant 78
USAF Plant 78
USAF Plant 78
USAF Plant 78
USAF Plant 78
USAF Plant 78
USAF Plant 78
USAF Plant 78
256
NR
NR
200
2,389
NR
0
400
256.74
179.64
84.94
102.2
127.94
93.23
90
179.4
197.5
19
Open
NR
NR
NR
NR
0
275
180
212
200
8,966
395
458
400-590 610
234-254 260
156-177 180
61-82
69-99
90
100.2
107-128 128
70-91 91
67-88 90
154-180 180
170-195 197
Valley-Fill Deposits
Valley-Fill Deposits
Valley-Fill Deposits
Valley-Fill Deposits
Silurian Age Sediments
Great Blue Formation ?
Great Blue Formation ?
Valley-Fill Deposits
Great Blue Formation ?
Valley-Fill Deposits
lake clays and gravels
lake clays and gravels
lake clays and gravels
lake clays and gravels
lake clays and gravels
lake clays and gravels
lake clays and gravels
lake clays and gravels
lake clays and gravels
256
144
156
NR
NR
254
NR
150
200.9
131
77.7
78.3
116.65
77.25
75
159.05
176.35
4-54
7-70
9-69
NR
NR
12-62
NR
12-62
1-89
1-89
1-89
1-89
1-89
1-89
1-89
7-89
7-89
Stock
Unused
Domestic
Unused
Oil Test
Unused
Dry Hole/
Abandoned
Unused
GWM
GWM
GWM
Dry Hole/
Abandoned
GWM
GWM
GWM
GWM
GWM
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
No
Yes
Yes
Yes
No
No
NR = No Record
GWM = Ground Water Monitoring
Source: USAF Plant 78 Documents; Holman, 1963; Bolke and Price, 1972; ESE, 1989.
P78-914/P78126
2/13/92
Utilizing the State of Utah Drinking Water Rules for primary water, which states that if TDS are greater than
1,000 mg/L the supplier must demonstrate that no better water is available and that TDS are not to exceed
2,000 mg/L, groundwater at the site is unsuitable for human consumption because of high TDS.
2.3.1.4 WeU Inventory
Nine shaUow groundwater monitoring weUs (P-1 through P-9) were instaUed at Plant 78 under Phase II Stage 1
and Stage 2 investigations. Monitoring weUs P-3, P-4, and P-5 are located along the NDD and E-512 surface
drainages in the northern end of Plant 78. Monitoring weU P-1 is located upgradient of the plant at the
intersection of the instaUation boundary and the FVD course. Monitoring weUs P-2, P-6, and P-7 are located
downgradient of Building M-585. Monitoring weU P-8 is located in the parking lot of BuUding E-519.
Monitoring weU P-9 is located downgradient of BuUding E-515, adjacent to the FVD. The locations of these
momtoring weUs are shown on Figure 2-14. Six of the seven wells were sampled for groundwater quahty.
Although completed as a monitoring weU, P-4 did not hold water and was not sampled for groundwater quahty.
Monitoring weU P-4 was abandoned as described in Section 3.5.7. AU momtoring wells were completed within
lake clays and gravels. Table 2-4 summarizes the weU data for each. AU Uthological, drilling data, and
geophysical logs are suppUed in Appendix C.
2.3.2 SURFACE WATER
2.3.2.1 Occurrence and Flow
Plant 78 is located in the Blue Creek VaUey drainage basin. This drainage basin is approximately 10 mUes wide
and 40 mUes long, with a north-south orientation. Blue Creek VaUey is bounded on the west by the North
Promontory Mountains and on the east by the Blue Springs Hills and the West Hills. From north to south, the
Blue Creek VaUey extends from near the Utah-Idaho border to the north end of the Great Salt Lake. The
drainage basin divides are shown in Figure 2-15.
Blue Creek is the principal stream channel within the Blue Creek VaUey drainage basin. Flow is from north to
south. At the north end of the vaUey, drainage density is low due to moderate topographic slopes characteristic
of this area. In the center of the vaUey, just upstream from Plant 78, topographic slopes are steep, with
numerous paraUel drainage channels on the west face of the North Promontory Mountains and the east face of
the Blue Spring Hills that enter Blue Creek at right angles. At the southern end of the vaUey the gradient is
nearly level due to low topographic slope, and Blue Creek enters a large mud flat characterized by the
occurrence of numerous springs, ponds, marshes, and poorly defmed channels that drain into the Great Salt
Lake. The other major hydrologic feature within the Blue Creek VaUey is Blue Creek Spring, which feeds Blue
Creek reservoir, the largest surface water body in the vaUey. This reservoir was created when Blue Creek Dam
was constructed in 1904. Blue Creek Dam has been enlarged twice, once in 1920, and again in 1950. The
current capacity of the reservoir is about 2,000 acre-feet (SCS, 1960). Water from Blue Springs is stored in the
reservoir during the winter months and used for agricultural irrigation during the spring through faU season.
2-26
i
N
10 Miles
SCALE
1 :250.000
Figure 2-15
BLUE CREEK VALLEY WATERSHED
SOURCE: ESE 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
2-27
P7M14/P78238
2/13/92
Average discharge from Blue Springs is about 10 cubic feet per second (cfs), or about 7,200 acre-feet per year.
Three to four months are required to fill the Blue Creek Reservoir with the water from the spring. The water
in the reservoir is distributed by canals owned by the Blue Creek Irrigation Company. The two main canals are
the East Canal and the West Canal; these canals are used to irrigate that portion of the valley immediately above
Plant 78 (Bolke and Price, 1972).
Blue Creek is the only perennial stream in the Blue Creek VaUey drainage basin. Prior to 1975, Blue Creek was
an intermittent stream only flowing significantly after rainfaU events and snow melts. As a result of the
earthquake in March 1975, Blue Creek became a perennial stream with year round flow. Not enough data is
currently avaUable to determine if the increased volume of discharge in Blue Creek observed after the 1975
earthquake was due to increased flow from Blue Spring or to the increased discharge of water from the
numerous springs within the upper reaches (which supply Blue Creek) of Blue Creek VaUey. Major changes
in surface water, as weU as in groundwater flow and quahty, are common in northern Utah after earthquakes
(Richens, 1984).
There are no permanent gaging stations located on Blue Creek; however, some sporadic stream flow data are
avaUable. Surface runoff is estimated to be approximately 2,200 acre-feet/year for that portion of the drainage
above the northern boundary of Township 10 north. Fifteen random discharge measurements coUected at this
point indicate flows of 0 to 17.8 cfs from 1959 to 1970 (Bolke and Price, 1972).
During the Stage 2 investigation, six stream gaging measurements were performed for Blue Creek, three of which
were conducted in December 1988, and the other three conducted in April 1989. The December measurements
were coUected at: (1) the north boundary of Plant 78; (2) a point approximately 500 feet upstream of
1400 Street; and (3) 2 mUes downstream of Plant 78 at the Highway 83 bridge. In December, the north
boundary discharge was 10.3 cfs, the 1400 Street discharge 11.5 cfs, and the Highway 83 bridge discharge 3.5 cfs.
The April measurements for these stations were 18.7, 23.1, and 16.9 cfs, respectively. Stream discharge
calculations for the six measurements are presented in Appendix C. These measurements indicate an increase
in flow for the upstream reach of Blue Creek passing through Plant 78 and a loss of flow from Blue Creek, from
the center of Plant 78 progressing downstream. The increased flow within the upstream reach is attributable
to surface water discharge from Plant 78. Loss of flow on the downstream reach is most likely due to recharging
of the underlying groundwater aquifer. The groundwater elevation is approximately 4,315 feet mean sea level
(msl) at the plant north boundary, whUe Blue Creek elevation is 4,430 feet msl. This indicates that Blue Creek
is approximately 115 feet above the water table, so the piezometric conditions for groundwater recharge to the
regional water table within this upstream reach are favorable given suitable hydrogeologic connection. The
influence of Blue Creek on the perched water table zone(s) at Plant 78, however, is unknown.
2-28
P7&-914/P78129
2/13/92
The drainage on Plant 78 is predominantly from east to west toward Blue Creek. Figure 2-16 illustrates the
drainages on the base along with their associated sub-watersheds. Runoff generated upslope from Plant 78 in
the Blue Spring Hills is largely diverted around the site by the interceptor ditch. The exception to this is the
FVD, which is channeled across the north end of Plant 78 and receives a very limited runoff contribution from
onsite. The remaining tributaries to Blue Creek originating from Plant 78 are less than a mile in length and
almost exclusively represent runoff generated from the site.
Drainage on Plant 78 is controlled by open ditches, including the FVD, and the interceptor ditch (Figure 2-16).
Open ditches also exist on both sides of most plant roads. The FVD, in the northern section of the plant,
channels surface water runoff through Plant 78 as the runoff enters the plant property along Faust VaUey Road.
An interceptor ditch, located on the eastern side of the plant, intercepts and diverts surface water runoff that
would normaUy flow through the main sections of the plant. A natural topographic depression exists at this ditch
to the southwest of BuUding M-636 and acts as a catch basin for precipitation and for surface water within the
interceptor ditch. Another topographic depression west of BuUding E-534 is manmade and acts as a sewage
treatment evaporation pond for the plant. There is no apparent discharge from this pond to surface streams.
Downgradient of Plant 78, Blue Creek enters a flat, marshy area characterized by numerous springs, streams,
and ponds. This area drains into the mud flats within Bear River Bay of the Great Salt Lake.
2.3.2.2 Surface Water Oualitv
The surface water quahty in Blue Creek is poor due to excessive concentrations of chloride (up to 2,500 mg/L)
and TDS (exceeding 5,000 mg/L) (Bolke and Price, 1972; Morton Thiokol, 1989). The stream classifications for
the section of Blue Creek and its tributaries, which run through Plant 78 are 3D (waterfowl uses) and
4 (agricultural uses) (Morton Thiokol, 1989). According to Bolke and Price (1972), water containing more than
4,500 mg/L of TDS is considered unfit for watering of livestock. The quaUty of the water in Blue Creek is
affected by irrigation return flow, surface water runoff, and surplus flow from Blue Creek Reservoir (Bolke and
Price, 1972). The quaUty may also be affected by the naturaUy occurring minerals in the Blue Creek VaUey
through which the creek flows and by naturaUy occurring cold- and hot-water springs that discharge into Blue
Creek.
Concentrations of TDS in surface water in the Blue Creek VaUey area range from about 400 to 7,700 mg/L
(Bolke and Price, 1972). TDS concentrations also fluctuate seasonaUy from a summer average of 3,800 mg/L
up to a maximum of 6,000 mg/L during the winter non-irrigation season (Morton Thiokol, 1989). Water from
smaU mountain springs contain the least amount of dissolved sohds (generaUy less than 600 mg/L), but water
from Blue Springs contains up to 2,000 mg/L of dissolved sohds. Downstream from Plant 78 (approximately
five mUes) and the Thiokol Complex, Blue Creek contains the highest known concentration of TDS (7,700 mg/L)
of any surface water in the Blue Creek VaUey (Township 10 north, Range 5 west, northwest 1/4, northeast 1/4,
2-29
EXPLANATION
DIRECTION OF
DRAINAGE FLOW
(DETERMINED BY
TOPOGRAPHIC
SLOPE)
700 1400 Feet
APPROX. SCALE IN FEET
Figure 2-16
USAF PLANT 78 SURFACE
DRAINAGE MAP
SOURCE FACILITY DOCUMENTS; ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
2-30
P78-914/P78231
2/13/92
northwest 1/4 of Section 5). The quahty of water at this site is affected by irrigation return flow, flood runoff,
surplus flow from Blue Creek Reservoir, and effluent from the sewage treatment plant at the Thiokol Complex
(Bolke and Price, 1972).
2.4 NATURAL RESOURCES
Gold, silver, copper, lead, and zinc were mined from the Promontory Mining District southwest of the Plant 78
area. Mineral deposits and old mines still may be found in this area. Agricultural lands and cattle/sheep range
are predominant in the area immediately surrounding Plant 78. Significant wildlife resources abound at the state
waterfowl management areas and Bear Creek National Wildlife Refuge to the south of Plant 78.
2.5 CULTURAL RESOURCES
Plant 78 is about five miles east of Promontory Summit, the historic location marking the meeting of the Central
Pacific and Union Pacific Transcontinental Railroads on May 10,1869. The completion of the transcontinental
railroad was important, for it opened the western states for expansion and exploitation of natural resources by
the eastern U.S. The Promontory Mountains have been used for mining intermittently since the opening of the
frontier. The Town of Promontory eventually disappeared as it became less needed as a transfer point, and was
no longer on the only transcontinental route. The old railroad grades and the historic meeting point are
protected by the National Park Service at Golden Spike National Historical Site. Native American use of this
area is not well documented, although they were known to use the wildlife resources of the Great Salt Lake.
There are no known sites of archeological significance on Plant 78.
2.6 BIOLOGY AND ECOLOGY
Vegetation covering the Blue Creek Valley (including Plant 78) is dominated by bunchgrasses (e.g., crested
wheatgrass and cheatgrass) with occasional sagebrush, rabbitbrush, and juniper shrubs along outcrops and
drainages. A great number of bird species use the Great Salt Lake marshes and Promontory Mountains nearby
and may occasionally visit or fly over Plant 78. The only fish expected to inhabit Blue Creek is the western
speckled dace (Battelle, 1983) or small carp. Among the game species found on Plant 78 are deer and pheasant.
The peregrine falcon and bald eagle are the only endangered species within the vicinity of Plant 78. These birds
may inhabit the Bear River Migratory Bird Refuge on a seasonal basis. There are no known endangered or
threatened species on Plant 78.
2.7 CLIMATOLOGY /METEOROLOGY
The climate of Plant 78 is characterized by hot, dry summers and cold, snowy winters. Temperatures range from
greater than 100 °F during the summer to -10 °F during the winter. According to National Oceanic and
Atmospheric Agency (NOAA), the semi-arid climate of the plant area has a mean annual precipitation of
15.68 inches and a mean annual snowfall of 58.1 inches. The mean annual lake evaporation for the area is
42 inches (NOAA, 1979). Selected meteorological data for Plant 78 are summarized in Table 2-5.
2-31
Table 2-5. Climatic Data for USAF Plant 78.
P78-914/P7Srr2-5.1
02/14/92
Month
Temperature (°F)
Mean
Precipitation (IN)
Mean
Snowfall (IN)
Mean
January
February
March
April
May
June
July
August
September
October
November
December
28.1
33.3
40.8
49.2
58.3
68.2
77.3
75.4
65.2
53.1
40.6
31.5
1.29
1.35
1.85
1.98
1.76
0.89
0.62
0.86
0.94
1.42
1.35
1.37
13.4
9.5
10.4
4.9
0.6
T
0.0
0.0
0.1
I. 1
6.2
II. 9
Period of Record: 1943-1982
T = Trace
Source: NOAA, 1983
2-32
3.0 FIELD INVESTIGATION PROGRAM
P7W14/P783.1
02/14/92
3.0 FIELD INVESTIGATION PROGRAM
3.1 ORGANIZATION AND DEVELOPMENT OF FIELD PROGRAM
The objectives of the Phase U Stage 1 investigation were to:
Determine the existence and extent of soil contamination at each disposal site;
Determine the existence of perched water tables;
Install monitoring wells and sample perched groundwater, where present;
Determine if surface water and sediments in drainageways leaving the site were contaminated;
Evaluate hydrologic characteristics of Blue Creek;
Establish valid background concentrations of constituents in surface water, soils, and sediments; and
Classify the sites into one of the foUowing three categories
No further action
Additional momtoring necessary
Remedial action required.
The Phase JJ Stage 2 investigation was designed to further investigate the extent and degree of contamination
at sites from Stage 1. The Phase II Stage 2 IRP objectives include:
• Literature search;
• Review of pubhc health and environmental requirements;
• Field investigation;
• Risk assessment (RA);
• Scoping and initial screening of remedial technologies;
• Development of preliminary remedial alternatives;
• Development of Data QuaUty Objectives (DQOs); and
• Preparation of the final report.
Tables 3-1, 3-2, and 3-3 show the summary of the investigative field work by site, number of water analyses, and
number of soU analyses, respectively. The foUowing sections discuss the field investigation activities as they
pertain to Phase U Stage 2 Remedial Investigation (RI) activities. Section 3.3 summarizes the field activities.
3.1.1 REMEDIAL INVESTIGATION FIELD PROGRAM
The Stage 2 RI encompassed several key elements necessary to select an appropriate remedial action. These
included:
• Determining the areal extent of contamination;
• Quantifying the movement and direction of contaminants; and
• CoUecting information on aquifer and soU characteristics and site geology.
P78-914/P7STM.1
02/14/92
Table 3-1. Field Activities and Rationale Used to Select These Activities for Phase II Stage 2 Program at Plant 78.
Site Name Field Activities Rationale
North Drainage Ditch
(Includes E-519)
E-512 Drainage Ditch
i
Collected two surface water and two surface sediment samples. Installed seven
shallow (< 7 feet) soil borings; collected two soil samples from each boring. Installed
two deep soil borings which were converted to monitoring wells. Collected three
groundwater samples (one from existing well P-3 and two from well P-8) including
one duplicate. Conducted aquifer tests on monitoring wells. Conduct soil gas survey.
Collected one surface water and one surface sediment sample. Installed three shallow
soil borings (<7 feet); collected two soil samples from each boring. Installed one
deep boring and collected seven soil samples. Installed one monitoring well and
collected one groundwater sample. Conducted aquifer test on monitoring well.
Conduct soil gas survey.
Estimate and characterize extent of
potential contamination by oils, solvents,
metals and propeUants, and potential for
migration to Blue Creek. Determine
aquifer characteristics, water quality.
Identify presence of potential contami-
nation from former laboratory at Building
E-519. ~~
Verify presence of contamination indicated
by Stage 1 results. Determine lateral
extent of potential contamination.
Characterize hydrogeology.
j
0
Blue Creek Performed stream flow measurements adjacent to plant and upstream and downstream
of plant. Drilled six shallow (<7 ft.) borings; collected two soil samples from each
boring. Collected 24 surface water and 16 surface sediment samples during two
rounds of surface water and sediment samplings.
Determine influent/effluent conditions.
Verify contamination, detected in Stage 1.
Evaluate extent and sources of potential
contamination.
M-585 French Drain Performed two soil gas investigations. Installed two deep borings. Collected ten soil
samples from borings. Installed and sampled two momtoring wells. Sampled existing
monitoring well P-2. Conducted aquifer tests on all monitoring wells.
Verify contamination detected in Stage 1.
Define lateral extent and sources of
contamination. Determine water quality,
hydraulic gradient and aquifer
characteristics.
Faust Valley Drainage
(Includes E-515)
Installed two shallow soil borings;collected two soil samples from each boring.
Installed two deep soil borings at E-515 and collected five soil samples. Collected six
surface sediment samples. Installed one monitoring well. Collected three
groundwater samples including one duplicate and one sample from existing momtoring
well P-1. Conducted aquifer tests on monitoring wells.
Characterize potential contamination from
former laboratory at Building
E-515. Estimate and characterize type and
extent of surface contamination within
FVD. Confirm background water quality
comparison. Perfonn aquifer testing to
establish hydrogeologic characteristics.
Source: ESE, 1991.
P78-914/P7gI3-2.1
02/14/92
Table 3-2. Number of Water Analyses by Site at USAF Plant 78 Phase II Stage 2.
North
Analytical Drainage M-585 Faust Valley
Parameter Method E-512 Ditch Blue Creek French Drain Drainage Ditch Total
Specific Conductance E120.1 1
(Field Test)
pH (Field Test) E150.1 1
Total Dissolved Sohds E160.1 3
Temperature E170.1 1
(Field Test)
Petroleum Hydrocarbons E418.1 3
Purgeable Halocarbons SW5030/SW8010 3
Purgeable Aromatics SW5030/SW8020 3
Semivolatile Orgamc SW3510/ 3
Compounds SW8270
3 0 3 3 10
3 0 3 3 10
3 15 3 3 27
3 24 3 3 34
5 24 3 3 38
5 24 3 3 38
5 24 3 3 38
5 15 3 - 26
Source: ESE, 1989.
"P78-914/P78T3-3.1
02/14/92
Table 3-3. Number of Soil Analyses by Site at USAF Plant 78 Phase II Stage 2.
Parameter
Analytical
Method
North
Drainage
Ditch
E-512
Drainage
Ditch
M-585 Faust Valley
Blue Creek French Drain Drainage Ditch Total
Petroleum
Hydrocarbons
Chlorinated Phenoxy
Acid Herbicides
SW3550/
E418.1
SW8150
26 14 28 10 26 104
Semivolatile Organic
Compounds
Toxic Characteristic
Leaching Procedure
SW3550
SW8270
Federal
Register
Vol. 51,
No. 114,
13 JUN 86
20 14 10 59
Soil Moisture
Content
ASTM D2216 26 14 28 10 26 104
Purgeable Halocarbons SW5030/
SW8010
26 14 28 10 26 104
Purgeable Aromatics SW5030/
SW8020
26 14 28 10 26 104
Source: ESE, 1991.
02/13/92
The following is a summary of the Phase II Stage 2 RI activities that were conducted.
3.1.1.1 Soil Gas Surveys
Two soil gas surveys were conducted at the M-585 French Drain Site (M-585) and one soil survey was conducted
at the North Drainage Ditch (NDD) and the E-512 Drainage Ditch (E-512) to determine the location of volatile
organic compounds in soil and groundwater.
3.1.1.1.1 M-585
Two soil gas surveys were conducted at M-585; one survey in December 1988 and a followup survey in the
summer of 1989. The December survey consisted of 75 PETREX™ soil gas collector tubes placed in small holes
about 2- to 3-inches in diameter and approximately one foot deep. The soil gas sampling locations were chosen
on an equidimensional grid with variable spacing to provide the required coverage of the site. The collector
tubes were allowed to equilibrate. The tubes were then retrieved, capped, and sent to PETREX™ for Curie point
desorption mass spectrometry analysis. This analyses identified the relative ion counts of volatile and semivolatile
compounds. These data were used to determine subsurface contaminant distribution and to help determine the
placement of groundwater monitoring wells P-6 and P-7.
A second soil gas survey was conducted at M-585 in the summer of 1989 to define the down gradient extent of
the groundwater contaminant plume identified at monitoring wells P-6 and P-7. A Century organic vapor
analyzer (OVA) was used to detect and measure organic vapor concentration in parts per million (ppm) in 65
probes that were inserted in the surface soil approximately two feet deep. Approximately 20 minutes after the
probes were in place, the OVA was connected to the probe, the OVA air pump engaged, and readings were
taken.
3.1.1.1.2 NDD, E-512, E-515, and E-519
In March 1990, a soil gas survey was conducted utilizing PETREX™ collector tubes at the NDD, E-512, E-515,
and E-519 sites. A total of 138 collectors were placed on a equidimensional grid along the NDD and across to
the E-512 drainage ditch. Groundwater sampling of momtoring wells P-3, P-5, P-8, and P-9 indicated that the
shallow groundwater in this area of Plant 78 contained organic solvent contamination. This survey was conducted
to further define the areal extent ofthis groundwater contamination. The procedures outlined for the PETREX™
survey conducted at M-585 were also followed for this survey.
3.1.1.2 Drillinp Activities
Shallow borings were installed and soil samples were collected at the NDD, E-512, Faust Valley Drainage Course
(FVD), and Blue Creek to further assess shaUow soU contamination identified by the Stage 1 investigation.
These borings were driUed to 8 feet and sampled at the 2- to 4-feet and 6- to 8-feet intervals. Samples were
logged, placed in appropriate sample containers, and stored in coolers on ice for subsequent laboratory analysis.
3-5
P7S-914/P7S3.6
02/13/92
Borings were logged by a ESE geologist and included depth/thickness of strata encountered, date and time of
boring installation, and identification and Unified Soils Classification System (USCS) of soils.
To assess soil contamination, hydrogeology, and geology at Plant 78, deep stratigraphic borings were installed
at M-585 (M-585B1 and M-585B2), the NDD (NDD-B1), E-512 (E-512B1), E-519 (E-519B1), and E-515
(E-515B1 and E-515B2) using an air rotary drilling method. Samples were coUected, logged, placed in
appropriate containers, and placed in coolers on ice for subsequent laboratory analysis. Monitoring weUs were
instaUed at the deep boring sites unless the boring did not produce enough water to warrant weU instaUation.
Borings not used for monitoring weU instaUation were abandoned and plugged. The stratigraphic borings were
used to assess subsurface geology and potential soU contamination. Downhole geophysical logging was also
conducted to help assess subsurface stratigraphy on borings M-585B1, M-585B2, and E-512B1.
3.1.1.3 Monitoring WeUs
Monitoring wells were instaUed in the deep borings at the M-585, E-512, E-519, and E-515 (E-515B2 only).
These weUs were used to assess the nature and extent of potential groundwater contamination. Monitoring
weU P-4 was instaUed at NDD-B1, but was later abandoned when it became dry. AJack of a weU developed
waterj2eiuing_zojie_andj^^ led to the inability of the site hydrogeologist to distinguish the correct
placementj}fJiie_weU_screen. Drilling to a total depth to accommodate the 30-foot weU screen apparently
bleached a confining zone and aUowed the perched water to percolate out of the screened zone. E-515B1 was
abandoned due to drilling problems and replaced by E-515B2. Monitoring wells were instaUed in the 8-inch
boreholes and were constructed of a threaded, 4-inch Schedule 40, Polyvinyl Chloride (PVC) pipe with 0.02-inch
factory-slotted screens, also a 4-inch Schedule 40, PVC blank pipe. The screened pipe was instaUed from the
base of the wells to 5 feet above the water table. Sand filter pack was placed in the annular space to 3 feet
above the screen. A 2-foot bentonite clay seal was placed on top of the sand pack, and the remaining borehole
space was grouted to the surface. Monitoring wells were developed by using a submersible pump and/or baUer.
Monitoring weU development data were recorded in the field in a tabular format.
3.1.1.4 Aquifer Tests
Slug/baU tests were conducted at aU Plant 78 groundwater momtoring wells to determine hydrauhc conductivity
and transmissivity. These data were used to assess the rate of groundwater flow within the water table aquifer.
3.1.1.5 Sampling Activities
SoU from both shaUow and deep borings were sampled, as mentioned previously, under the summary of drilling
activities.
Groundwater sampling was conducted for both new and previously instaUed monitoring wells to assess the nature
and extent of potential groundwater contamination. Prior to sampling, the depth to water within the monitoring
3-6
P78-914/P783.7
02/13/92
well from the top of the well casing was measured and recorded. Where possible, five well bore volumes of
water were removed (purged) from the momtoring well before sampling. Conductivity, pH, and temperature
were recorded during purging and were also measured prior to sampling. Samples were collected in appropriate
containers, packed in ice, and shipped to the laboratory for analysis.
Surface water samples were collected at the NDD, E-512, and Blue Creek to assess the nature, extent, and
potential sources of surface water contamination in and around Plant 78. Samples were collected in a manner
to minimize air bubbles, stored in appropriate containers, packed in ice, and shipped to the laboratory for
analysis.
Surface sediment samples were collected from the NDD, E-512, FVD, and at Blue Creek to assess contaminant
occurrence and source relationships at the sites. The samples were collected from the center of the ditch at a
depth of approximately 0 to 3 inches. Composites were prepared from three subsamples collected at
approximately 20-foot intervals. The samples were placed in appropriate containers and shipped to the
laboratory on ice.
Biological sampling was performed at the surface water sampling sites or at soil sampling sites to quantify any
environmental damage. After a presampling survey was conducted, three types of sampling were performed:
• Vegetation density and diversity;
• Aquatic invertebrate density and diversity; and
• Small mammal trapping.
3.1.1.6 Surveying
Each momtoring well and deep soil boring was surveyed using the Universal Transverse Mercator (UTM) Grid
System to establish its location. Elevations for the natural ground surface and the top of the PVC casing at each
momtoring well were surveyed. The accuracy for the UTM coordinates are no less than 1:10,000 (one in ten
thousand). Elevations are accurate to 0.01 feet using an established United States Geological Survey (USGS)
vertical datum. All surveying was performed by ESI Engineering, Inc. of Salt Lake City, Utah, professional land
surveyors registered in the State of Utah.
3.1.1.7 Evaluation and Screening of Data
All hydrogeologic and hydrology data were evaluated to assess the quahty of the shaUow and deep aquifer and
surface water systems at Plant 78. The potential for vertical and lateral migration of groundwater contaminants
has been addressed. The rates and directions of ground and surface water flow have been estimated. Analytical
data have been screened and tabulated. The results of the RI data evaluation have been used for the RA.
3-7
P78-914/P783.8
02/13/92
3.1.2 RISK ASSESSMENT FIELD PROGRAM
The RA encompasses several key elements necessary to select an appropriate remedial action. These include:
• Determination of federal and state Apphcable or Relevant and Appropriate Requirements (ARARs);
• Determination of the hazards by quantifying the impact on receptors through the pathways of surface
water, groundwater, biota, and air; and
• Determination of those sites where the results of the field investigation and risk assessment indicate no
significant threat to human health, human welfare, or the environment.
The overall objective of the RA was to determine the magnitude and probability of actual or potential harm to
the pubhc health or welfare or to the environment by the threatened or actual release of a hazardous substance.
The assessment was comprised of four separate components:
• Contaminant identification;
• Exposure assessment;
• Toxicity assessment; and
• Risk characterization.
Data requirements for the RA included surface water, groundwater, sediment, and soil data. The soil and
sediment data provided surficial fractions such that concentrations at the biological interface could be predicted.
Local meteorological data, as well as agricultural information, was used for the exposure assessment. Aquatic
biota sampling for species diversity was conducted to determine risk to the aquatic ecosystem. Terrestrial habitat
and community structure were also examined to determine risk to key wildlife species.
3.1.2.1 Apphcable or Relevant and Appropriate Requirements
Usually, either a federal or state agency mandates contaminant-specific ARARs represented by a concentration
(i.e., maximum contaminant levels [MCLs]). However, many contaminants do not have recognized ARARs. In
this event, a value must be determined that will protect human health and the environment from exposure to
that compound. It is therefore necessary to determine the extent to which federal or state standards are
apphcable or relevant and appropriate in regard to the contaminants identified at the site. For situations where
no values are available, criteria have been developed on the basis of intake, toxicity, and risk characterization.
3.1.2.2 Contaminant Identification
Analytical data from the RI were screened and tabulated by chemical properties such as toxicity, persistence, and
site-specific factors such as media contamination and frequency of detection. This screening process is necessary
when site contaminants are identified in order to focus subsequent efforts in the RA on a small number of
selected contaminants. The goal of the selection process is to focus on those contaminants that represent the
most toxic, mobile, persistent, or frequently occurring on site.
3-8
P7S-914/P7835
02/13/92
3.1.2.3 Exposure Assessment
An exposure assessment was conducted to identify actual or potential routes of exposure, to characterize the
exposed populations, and to determine the extent of exposure. These objectives were attained by performing
the following steps:
• Analyzing contaminant release;
• Analyzing enviromnental fate and transport of contaminants;
• Analyzing populations, sensitive subsets of the human population, and/or fish and wildlife populations
at risk; and
• Determining potential contaminant exposure pathways (e.g., direct contact, inhalation of vapors/dust,
ingestion of contaminated water or soil and ingestion of contaminated aquatic organisms).
The data evaluation performed during the RI was used to identify contaminant release and the potential
migration of contaminants. Biological sampling was performed and agricultural and demographic information
was assessed to identify populations at risk. Meteorological data, groundwater use, and groundwater movement
was assessed to help determine contaminant exposure pathways.
3.1.2.4 Toxicity Assessment
A toxicity assessment was conducted to determine the nature and extent of health and environmental hazards
associated with exposure to contaminants at the concentrations identified at the site. Toxicity data from scientific
literature were critically evaluated and interpreted, resulting in a toxicity profile for each selected contaminant
of concern. Toxicity profiles characterized the adverse health and environmental effects that were the anticipated
results of exposure to these contaminants.
3.1.2.5 Risk Characterization
The objective of a risk characterization was to estimate the incidence of adverse health or environmental effects
under the various conditions of exposure defined in the exposure assessment. This objective was attained by
integrating all of the information developed during the exposure and toxicity assessments to yield a complete
characterization of potential or actual risk. The risk characterization included an evaluation of the following
potential risks:
• Carcinogenic risks;
• Noncarcinogenic risks;
• Environmental risks; and
• Pubhc Welfare risks.
3-9
P78-914/P783.10
02/13/92
3.1.2.6 Evaluation of Data
The results of the RA were used to determine the exposure path and the risk-based exposure levels for the FS.
For those sites that indicated no significant impact upon human health or the environment, a Decision Paper
will be completed indicating that no further action is required, and that the site should be removed from the list
of sites to be investigated.
3.1.3 FEASIBILITY STUDY PROGRAM
The Feasibility Study (FS) process is integrated with and dependent upon the RI and RA. The RI provides data
with respect to the nature and extent of contamination at the site. The RA identifies the type and level of
potential risk to which human or environmental receptors may be exposed. The FS addresses those exposure
pathways identified in the RA as posing an unacceptable risk to human health and the environment in order to
mitigate the endangerment. This approach is consistent with the National Contingency Plan (NCP), which states
that the purpose of a remedial preliminary assessment is to "eliminate from further consideration those sites that
pose no threat to pubhc health or the environment" [300.420(b)(l)(i)]. Releases identified in the RI, which the
RA concludes pose no current or potential future threat, should be eliminated from consideration in the FS.
As presented in more detail in Section 4.0, the RA performed for Plant 78 determined that the levels of site-
related constituents detected in the environmental media at the site does not pose an unacceptable current or
potential future risk to human health and the environment. Thus, the results of the RA support the
implementation of the no-action alternative for Plant 78. As such, there no longer remains a need for the
performance of a FS. However, a decision document will be prepared to document the implementation of a no
action or limited action alternative. This approach is consistent with current EPA guidance. In addition. Section
104(a)(1) of CERCLA authorizes response actions only if a release may present an imminent or substantial
endangerment to the pubhc health or welfare.
In documenting the implementation of a no action or limited action alternative at the site, the decision document
will present pertinent information from both the RI and RA. Factors that will be discussed include the
environmental setting of the site, current and potential future land use, and potential human and environmental
receptors. A brief summary of the documentation to be provided in the decision document is presented below.
Plant 78 and the area directly south are used for industrial purposes. Ranching and farming are the other
predominant land uses. Plant 78 is assumed to continue to serve an industrial purpose for some time. Access
to Plant 78 is highly restricted for security reasons. These factors indicate that the institutional controls currently
in place to restrict access are sufficiently protective of human health and the environment relative to direct
contact with site constituents in soil.
3-10
P78-914/P783.11
02/13/92
Although site constituents are present in the shallow groundwater beneath the site and site constituents may
leach from soil to groundwater, the groundwater beneath the site and in the Blue Creek Valley is non-potable
and a Class IUB aquifer (EDA, 1986d). There appears to be no interconnection between the affected aquifer
and a usable aquifer. Additionally, the sodium, potassium, and chloride ions that make up the naturahy-occurring
TDS concentrations in the affected aquifer are not removed by conventional water treatment (Clark, Viessman,
and Hammer, 1971). Furthermore, usable groundwater in the Blue Creek Valley is largely appropriated
(Whetstone, 1989). The risk assessment has also shown that site-related constituents in the groundwater beneath
the site are not expected to reach the plant boundary in excess of several hundred years.
The presence of orgamc constituents in the soil and groundwater at the site does not pose a current or potential
future risk to human health and the environment via Blue Creek. Concentrations of site-related constituents of
concern in Blue Creek did not exceed estimated or established criteria protective of aquatic or terrestrial
organisms. Predicted groundwater discharge concentrations in Blue Creek, without allowing for surface water
dilution, are predicted to be less than the AWQC for aquatic life. Although livestock may have access to Blue
Creek downstream of Plant 78, TDS concentrations in the creek range from 400 to 800 mg/L. Concentrations
of up to 7,700 mg/L of TDS have been detected in Blue Creek surface water downstream of Plant 78. This value
exceeds the Utah water quahty standard of 1,200 mg/L for agriculture uses. This value is also higher than the
proposed safe upper limits of TDS for poultry, swine, horses, and dairy cattle developed in western Australia
(Clark, Viessman, and Hammer, 1971).
Based on the above discussion, implementation of a no-action or limited action alternative is appropriate for the
site and will not result in unacceptable endangerment to human health or the environment. Thus, the decision
document will recommend and justify the presentation of a no-action or limited action alternative in the Record
of Decision.
3.2 DATA QUALITY OBJECTIVES
3.2.1 INTRODUCTION
Data Quahty Objectives (DQO) are qualitative and quantitative statements which specify the quaUty of the data
required to meet the objectives of the Remedial Investigation/FeasibUity Study (RI/FS) as weU as to support
decisions during remedial response activities. The level of detail and quaUty needed depends upon the intended
use of the data, the site-specific characteristics, and should ensure sufficient data of known quahty are coUected
to support sound decisions in the RI/FS process.
EPA Guidance defines a three-stage process for DQO development (EPA, 1987c):
• Stage 1 - Identify decision types;
• Stage 2 - Identify data uses/needs; and
• Stage 3 - Design data coUection program.
3-11
P78-914/P783.12
02/13/92
The components of each stage are identified in Figure 3-1.
Analytical levels that may be required for an RI/FS are:
• Level I - Field Screening. This level is characterized by the use of portable instruments, such as an
organic vapor analyzer (OVA) or scintillation detector, that can provide real-time data to assist in the
optimization of samples for laboratory analysis and for health and safety monitoring. Qualitative data
can be generated regarding the presence or absence of certain types of contaminants (e.g., radionuclides
and volatile organics) at sampling locations. However, results are generally not chemical specific and
are not quantitative.
• Level II - Field Analysis. This level uses more sophisticated portable analytical instruments (i.e., HNu
321 Gas Chromatograph) either onsite or in a mobile laboratory. Qualitative and quantitative data can
be generated for certain compounds depending on the type of contaminant, sample matrix, analytical
procedures, and skills of the personnel.
• Level III - Laboratory Analysis. This level refers to analysis conducted by standard, documented
(Non-CLP) laboratory procedures in an offsite laboratory.
• Level IV - Contract Laboratory Program (CLP) Routine Analytical Services (RAS). This level refers
to analysis conducted by a CLP Laboratory (or a non-CLP laboratory usmg CLP or equivalent
procedures) following stringent QA/QC protocols and documentation.
• Level V - Non-Standard Methods or CLP Special Analytical Services (SAS). This level refers to analysis
where method modification or development is required for specific compounds or to achieve lower
detection limits than standard methods produce.
The DQOs are established prior to data coUection and are not a separate deliverable, rather the DQO
development process is integrated with the project planning process, and the results incorporated into the
Sampling and Analysis Plan, the Quahty Assurance Project Plan (QAPP) (November 1988), and the Work Plan
(October 1988). The foUowing sections summarize the DQOs chosen for meeting the objectives of the RI/FS
process at Plant 78, consistent with EPA Guidance (EPA, 1987c).
3.2.2 PHASE n STAGE 2 OBJECTIVES AND DQO APPROACH
The objectives of the Phase II Stage 2 investigation were to verify Stage 1 field investigation results, define the
magnitude and migration potential of contamination, perform a baseline risk assessment, and develop preliminary
and detailed alternatives for the FS response actions. DQO procedures were apphed to the identification of data
quahty and quantity needs for each general use category. The general data use categories include site
characterization, risk assessment, and evaluation of alternatives. Table 3-4 summarizes the data needs and uses
chosen for completion of the Phase II Stage 2 RI/FS. The analytical levels were assigned to the general data
use categories according to EPA guidance (EPA, 1987c). Tables 3-5 and 3-6 show the analytical levels assigned
to the analyses conducted on soU and water samples for Phase JJ Stage 2. Tables 3-7 through 3-10 summarize
3-12
STAGE 1
IDENTIFY DECISION TYPES
• IDENTIFY & INVOLVE DATA USERS
• EVALUATE AVAILABLE DATA
• DEVELOP CONCEPTUAL MODEL
• SPECIFY OBJECTIVES/DECISIONS
STAGE 2
IDENTIFY DATA USES/NEEDS
• IDENTIFY DATA USES
• IDENTIFY DATA TYPES
• IDENTIFY DATA QUAUTY NEEDS
• IDENTIFY DATA QUANT ITY NEEDS
• EVALUATE SAMPLING/ANALYSIS OPTIONS
• REVIEW PARCC PARAMETERS
STAGE 3
DESIGN DATA COLLECTION PROGRAM
• ASSEMBLE DATA COLLECTION COMPONENTS
• DEVELOP DATA COLLECTION DOCUMENTATION
Figure 3-1
DATA QUALITY OBJECTIVES
THREE STAGE PROCESS
SOURCE: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-13
P78-914/P7gT3-4.1
02/14/92
Table 3-4. Summary of Data Needs for RI/FS at Plant 78.
Media Data Needs Prioritized
Data Needs
Analytical
Levels
Analysis
Parameters
Rationale
i
h-1
Surface and
Vadose Zone
Soils
Groundwater
Hydrogeology
Surface Water &
Sediment
Biological
Sampling
Soils Deep
Soil Gas
Confirm Stage 1 results,
determine nature and extent of
contamination
Confirm Stage 1 results,
determine nature and extent of
contamination
Determine the hydraulic
parameters of aquifers
Confirm Stage 1 results,
determine nature and extent of
contamination
Determine receptor impact
Confirm Stage 1 results,
determine nature and extent of
contamination
Determine extent of volatile
organic contamination plane
Site Characteristics,
Risk Assessment,
Evaluate Alternatives
Site Characteristics,
Risk Assessment,
Evaluate Alternatives
Site Characterizations
Evaluate Alternatives
Risk Assessment
Site Characterizations
Risk Assessment
Evaluate Alternatives
Risk Assessment
Evaluate alternatives
Site Characterization
Site Characterization
Risk Assessment
Evaluate Alternatives
Site Characterization and
Optimization of Sampling
Locations
II, III, rv
III, rv
m, rv
III, rv
in, rv
i, m
Petroleum Hydrocarbons, Purgeable
Halocarbons, Purgeable Aromatics,
Semi-Volatiles, TCLP.Chlorinated
Phenoxy-Acid Herbicides
Petroleum Hydrocarbons, Purgeable
Halocarbons, Purgeable Aromatics,
Semi-Volatiles, TCLP, Chlorinated
Phenoxy-Acid Herbicides
N/A
Petroleum Hydrocarbons, Purgeable
Halocarbons, Purgeable Aromatics,
Semi-Volatiles, TCLP, Chlorinated
Phenoxy-Acid Herbicides
Petroleum Hydrocarbons, Purgeable
Halocarbons, Purgeable Aromatics,
Semi-Volatiles, TCLP, Chlorinated
Phenoxy-Acid Herbicides
Volatile Organic Compounds
Information needed to estimate
future impacts to groundwater,
physical properties to evaluate
remedial alternatives
Information needed to
determine nature and extent of
groundwater impacts and to
predict plume migration to all
receptors (environmental and
human)
Information needed to assess
potential migration and
alternatives of compounds in
the aquifer flow system
Information needed to estimate
impacts to surface water and
biota receptors whose habitat
may potentially be impacted
Information needed to assess
impacts to biota receptors
Information needed to estimate
nature and extent of impacts to
groundwater and physical
properties for evaluation of
remedial alternatives
Information needed to
approximate the plume
boundaries to plan future
sampling locations
N/A = Not applicable.
P78-914/P7SfT3-S.l
02/14/92
Table 3-5. Soil Analyses: DQO Analytical Levels.
Parameter Analytical Method Analytical Level
Petroleum Hydrocarbons SW3550/E418.1 UI
Chlorinated Phenoxy Acid Herbicides SW8150 III
Semivolatile Organic Compounds SW3550/SW8270 IV
Toxic Characteristic Leaching Federal Register Vol. 51, 111
Procedure NO. 114, 13 JUN 86
Soil Moisture Content ASTM D2216 III
Purgeable Halocarbons SW5030/8010 m
Purgeable Aromatics SW5030/8020 UJ
3-15
P7W14/P78rT3-6.1
02/14/92
Table 3-6. Water Analyses: DQO Analytical Levels.
Parameter Analytical Method Analytical Level
Specific Conductance (Field Test) E120.1 I
pH (Field Test) E150.1 I
Total Dissolved Sohds E160.1 I
Temperature (Field Test) E170.1 I
Petroleum Hydrocarbons E418.1 UI
Purgeable Halocarbons SW5030/SW8010 III
Purgeable Aromatics SW5030/SW8020 ffl
Chlorinated Phenoxy Acid Herbicides SW8150 UI
Semivolatile Orgamc Compounds SW3510/SW8270 IV
3-16
P78-914/P78T3-7.1
02/14/92
Table 3-7. Summary of Precision and Accuracy for Non-Metallic Inorganics and Petroleum Hydrocarbons.
Aqueous Matrix Solid Matrix
Method Parameter
Spike
Type
Spike
Concentration
(mg/L)
Precision Accuracy Spike Precision Accuracy
(Max RPD) (% Recovery) Concentration (Max RPD) (% Recovery)
D2216
E350.1
E418.1
Percent
Moisture
Ammoma
Petroleum
Not Apphcable
SMSC/MSC
SMSC/MSC
0.3
42.5
5
15
92-108
75-115
0.3 mg/L*
1,130 mg/kg
20
10
20
85-115
75-125
Note: SMSC = standard matrix spike compond. This represents a spike into a standard matrix, in duplicate.
MSC = matrix spike compound. This represents a spike (and a duplicate spike) into a sample matrix. It is a sample matrix spike for the
methods listed on this table.
Completeness using approved QAPP criteria is 100%.
* This represents a spike of ammoma into the acetic acid leachate.
Source: ESE, 1988.
\
P78-914/P78T3-8.1
02/14/92
Table 3-8. Summary of Precision and Accuracy for Metals.
Aqueous Matrix Solid Matrix
Method Parameter
Spike
Type
Spike
Concentration
(mg/L)
Precision
(Max RPD)
Accuracy
(% Recovery)
Spike
Concentration
(mg/kg)
Precision
(Max RPD)
Accuracy
(% Recovery)
SW6010
it
Aluminum
Antimony
Barium
Beryllium
Cadmium
Chromium
Cobalt
Copper
Iron
Lead
Manganese
Nickel
Silver
Vanadium
Zinc
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
MSC/QCC
2.0
0.5
2.0
0.05
0.05
0.2
0.5
0.25
1.0
0.5
0.2
0.4
0.05
0.5
0.2
25
25
25
25
25
25
25
25
25
25
25
25
25
25
25
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
100
400
10
10
40
100
50
100
100
100
10
100
100
25
25
25
25
25
25
25
25
25
25
25
25
25
25
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
75-125
Note: MSC = matrix spike compound. This represents a spike (and duplicate spike) into a sample matrix.
QCC = quahty control check sample. This represents a spike into a standard matrix. It is a single standard matrix spike for the methods hsted
in this table.
Completeness using approved QAPP criteria is 100%.
Source: ESE, 1988.
P78-914/P78T3-9.1
02/14/92
Table 3-9. Summary of Precision and Accuracy for Matrix Spike Compounds, Quality Control Check Samples, and Surrogates for Organic Analysis.
Aqueous Matrix Sohd Matrix
Method Parameter
Spike
Type
Spike
Concentration
(mg/L)
Precision
(Max RPD)
Accuracy
(% Recovery)
Spike
Concentration
(mg/kg)
Precision Accuracy
(Max RPD) (% Recovery)
8010 1, 1-Dichloroethene MSC/QOC 50
Trichloroethene MSC/QCC 50
Chlorobenzene MSC/QCC 50
p-Bromofluorobenzene S/QCC 30
8020 Toluene MSC/QCC 50
Benzene MSC/QCC 50
p-Bromofluorobenzene S/QCC 30
8150 2,4-D MSC/QCC 1.2
Silvex MSC/QCC 1.2
2,4,5-T MSC/QCC 1.2
Dicamba MSC/QCC 1.2
2,4-Dichloroacetic MSC/QCC 1.2
Acid
30
30
30
30
30
30
30
30
30
28-167
35-146
38- 150
28-161
46-148
39- 150
43-147
40- 130
40-130
40-130
40-130
40-130
50
50
50
50
50
50
50
50
23-192
30-151
33- 155
23-166
41-153
34- 155
38-152
40-130
40-130
40-130
40-130
40-130
Note: MSC = matrix spike compound. This represents a spike (and a duplicate spike) into a sample matrix.
QCC = quahty control check sample. This represents a spike into a standard matrix. It is a single standard matrix spike for the methods listed in this
table.
S = surrogate.
Completeness using approved QAPP criteria is 100%.
Source: ESE, 1988.
P78-914/P7ST3-10.1
02/14/92
Table 3-10. Matrix Spikes and MSD's SW846, Method 8270 Semi-Volatile Organic Analytes in Water
and Soils.
Matrix Spikes & MSD's % Recovery / % RSD
Compounds Used Water
1,2,4-trichlorobenzene 39-98
Acenapthene 46-118
2,4-dinitrotoluene 24-96
Pyrene 26-127
N-nitroso-diN-Propylamine 41-116
1,4-dichlorobenzene 36-97
Pentachlorophenol 09-103
Phenol 12-89
2-chlorophenol 27-123
4-nitrophenol 10-80
4-chloro-3-methylphenol 23-97
RSD
28
31
38
31
38
28
50
42
40
50
42
Soil
38-107
31-137
28-89
35-142
41-126
23-104
17-109
26-90
25- 102
11-114
26- 103
RSD
23
19
47
36
38
27
47
35
50
50
19
Completeness using approved QAPP criteria is 100%.
Source: ESE, 1989.
3-20
P78-914/P7S3.21
02/13/92
precision, accuracy, and completeness parameters for Stage 2.
The following sections summarize the objectives of each Phase II Stage 2 sampling effort and the DQO level
determined for meeting these objectives.
3.2.2.1 Surface and Vadose Zone Soils
Sampling objectives of the Phase II Stage 2 surface and vadose zone soils were to further assess the nature and
extent of shallow soil contamination and to confirm Stage 1 results. The data were used for input into the site
characterization, risk assessment, and evaluation of alternatives. The DQO evaluation ascertained analytical
Levels of II, UJ, and IV were appropriate to meet the objectives of this sampling effort.
3.2.2.2 Groundwater
Groundwater sampling objectives included determination of the nature and extent of potential groundwater
impacts, prediction of plume migration, and remedial alternative development. To satisfy the DQOs, Levels III
and IV analyses were chosen.
3.2.2.3 Hydrogeology
The objectives of this study were to determine the aquifer hydrauhc parameters for input into the site
characterization, risk assessment, and the evaluation of alternatives. Levels I analysis was deemed adequate to
meet the needs of this study.
3.2.2.4 Surface Water and Sediment
The objectives of these sampling efforts were to confirm Stage I results and determine the nature and extent of
contamination for input into the site characterization, risk assessment, and evaluation of alternatives. Levels III
and IV analytical levels were chosen to satisfy these needs.
3.2.2.5 Biological Sampling
The objectives of this sampling effort were to ascertain receptor impacts for input into the risk assessment and
evaluation of alternatives. The appropriate levels of analyses to meet the DQO requirements were Levels in
and IV.
3.2.2.6 Deep Stratigraphic Soil Borings
The objectives of the deep stratigraphic boring effort were to confirm Stage 1 results and determine the nature
and extent of contamination. This data was used for input into the site characterization, risk assessment, and
the evaluation of alternatives. In order to meet these objectives, the analytical levels chosen were Levels in
and IV.
3-21
P78414/P783.22
02/13/92
3.2.2.7 Soil Gas
The objective of the soil gas surveys were to ascertain the extent of the contamination plume such that the
number and location of sampling sites for subsequent investigative efforts could be maximized. Levels I and IU
were appropriate to meet these analytical data needs.
The level required to meet the objectives of the RI/FS and to satisfy the DQO requirements were in most cases
high because this phase of the investigation was beyond screening measures. The data collected and obtained
was evaluated by strict QA/QC measures such that it met or exceeded the DQO expectations.
3.3 IMPLEMENTATION OF FIELD PROGRAM AND SUMMARY OF FIELD WORK
The Phase IT Stage 2 field investigation commenced during November 1988 and continued in various stages
through March 1990. Field investigative activities included:
• Two soil gas surveys at M-585;
• One soil gas survey at NDD, E-512, E-519, and E-515;
• Surface sediment and surface water sampling at the NDD, E-512, FVD (surface sediment only), and
Blue Creek;
• A second surface water and sediment sampling of Blue Creek;
• Shallow soil borings and soil sample coUection at the NDD, E-512, FVD, and Blue Creek;
• DrUling and sediment sampling of deep borings at M-585, NDD, E-512, E-519, and E-515 (FVD);
• Conversion of deep borings at the NDD, M-585, E-512, E-519, and E-515 to groundwater monitoring
wells (after conversion of boring NDD-B1 to monitoring weU P-4, P-4 became dry and was abandoned);
• CoUection of groundwater samples from monitoring wells P-1, P-2, P-3, P-5, P-6, P-7, P-8, and P-9;
• Aquifer testing of aU momtoring wells; and
• Biological data coUection and sampling of plants, aquatic invertebrates, and smaU mammals.
3.3.1 TIME SEQUENCE OF WORK PERFORMED
Field investigations began with a soU gas survey, which was conducted between November 30 and December 17,
1988. Groundwater momtoring weU instaUation, development, sampling, and aquifer testing also began at this
time and continued through July 1989. Sampling of surface water, soils, sediments, and biota was completed
between December 1988 and March 1990.
3.3.2 IDENTIFICATION AND ROLE OF SUBCONTRACTORS
Subcontractors were employed to assist with various stages of the field program. Those firms employed and then-
respective roles foUow.
3-22
P7M14/P783.23
02/13/92
Subcontractor Activity
Boyles Brothers Drilling, Inc.
Salt Lake City, Utah
Drilling and instaUation of monitoring wells. Drilling of soU borings.
Dave's DrUUng, Inc.
Salt Lake City, Utah
DrUling and instaUation of momtoring wells.
Petrex, Inc.
Lakewood, Colorado
Supply and analyses of soU gas coUector tubes.
British Plaster Board, Inc.
Grand Junction, Colorado
Geophysical logging of monitoring weU boreholes.
Engineering Service, Inc.
Salt Lake City, Utah
Surveying of Universal Transverse Mercator coordinates and
elevations of momtoring wells.
3.4 INVESTIGATION METHODS AND SURVEYS CONDUCTED
3.4.1 GEOPHYSICAL INVESTIGATION
Boreholes E-512B1, M585B1, and M-585B2 were geophysicaUy logged by British Plaster Board Incorporated
(BPB, Inc.) of Grand Junction, Colorado. Geophysical surveys included borehole logging using a logging tool
to measure natural gamma, gamma-gamma, and neutron-neutron.
3.4.2 SOIL GAS INVESTIGATIONS
3.4.2.1 M-585 SoU Gas Survev 1
A total of 75 PETREX™ soU gas coUectors were instaUed for this survey. Forty coUectors were instaUed in a
grid pattern using a 50-foot spacing between each coUector (Figure 3-2). Thirty-five additional coUectors were
instaUed on a square grid with 25-foot spacings in the area immediately surrounding the French Drain. The
closer spacing was chosen to aUow for a more detaUed contaminant distribution analysis closer to the potential
source. Ten coUectors were instaUed as time tests. Time test coUectors were periodicaUy removed and analyzed
to judge when sufficient time had elapsed for soU gas adsorption onto the coUectors.
The coUectors were instaUed from November 30 through December 1, 1989, with the majority of the coUectors
instaUed on November 30. Time test coUectors TT5, TT6, TT7, and TT8 were removed on December 6.
Preliminary analysis of these tests indicated that the optimal time for retrieving the remaining coUectors would
be after 18 days. CoUectors 1 through 21, 73, and 74 were removed on December 17. CoUectors 22 through
72 were removed on December 18. During removal, coUectors 4, 7,11, 13,18,24,37, 42,49, 50, 62, and 65 were
unavoidably broken due to the difficulty of removing the glass tube coUectors from frozen ground. AU
3-23
Figure 3-2
SOIL GAS SAMPLE LOCATIONS
M-585 FRENCH DRAIN
SOURCE: Petrex, 1989
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-24
P78-914/P783.2S
02/13/92
charcoal-coated wires were removed from the broken coUectors and carefuUy placed into clean, unused coUector
tubes suppUed by PETREX™. CoUector 45 was found to be unusable. A cap seal was inadvertently left on
during instaUation, preventing the coUector from coUecting any soU vapors.
The second soU gas survey was conducted at M-585 from July 17 through July 21, 1989. A Century OVA,
Model 128, was used to detect and measure concentrations of organic vapors in ppm. Probes 4 feet in length
were inserted into pUot holes 2 feet deep. Approximately 20 minutes after the probes were instaUed, the OVA
was connected to the probe. An internal air pump on the OVA was used to evacuate the probe and a reading
of total orgamc vapor concentrations was taken. A total of 66 soU gas readings were taken in order to delineate
the extent of contamination. The same 50-foot grid pattern that was used in the first soU gas survey was utilized
and expanded for the second survey. Some OVA readings were also taken around the perimeter of
BuUding M-585 (Figure 3-3).
3.4.2.2 NDD. E-515. E-519. and E-512 SoU Gas Survev
A total of 138 soU gas coUectors were instaUed for this survey. The coUector points were established in a grid
pattern using a 100-foot spacing between each coUector (Figure 3-4). Groundwater sampUng of momtoring weUs
P-3, P-5, P-8, and P-9 indicated that the shaUow groundwater in the area of Plant 78 contained organic solvent
contamination. This survey was conducted to further define the distribution and areal extent of groundwater
contamination, and in particular, to delineate the downgradient extent of the groundwater contamination.
The coUectors were instaUed on March 6 and 7, 1990. Time test coUectors were removed on March 8 and 9,
1990, and indicated that the coUectors should be left in for approximately 20 days. The coUectors were removed
on March 27 and 28,1990. CoUectors 021, 022, 025,028, 039, and 142 were unavoidably broken during removal
of the glass tube coUectors from the ground. AU charcoal-coated wires were removed from the broken coUectors
and carefuUy placed into clean, unused coUector tubes suppUed by PETREX™. CoUectors 050 and 108
inadvertently bad not been instaUed.
3.4.3 SURVEYING AND PERMANENT FIELD IDENTIFICATION OF MONTTORING WELLS
Monitoring wells P-5, P-6, P-7, P-8, P-9, and boring NDD-B1 were surveyed by Engineering Service, Inc.,
professional land surveyors in the State of Utah. Map coordinates for each monitoring weU were established
to an accuracy of within 1:10,000 using the UTM Grid System. AdditionaUy, elevations for the natural ground
surface and the top of the PVC casing were determined to within 0.01 foot, using USGS vertical datum. Each
momtoring weU site was plotted on the Plant 78 base map (Plate 1). Table 3-11 lists map coordinates and
surveyed weU elevations for Stage 2.
AU monitoring weU protective steel casings were painted a safety yeUow, and the weU number was painted on
the weU casing or protective cap.
3-25
P78 STAGE 2 05/91
SOLVENT STORAGE
WASTE SOLVENT STORAGE
M-585
LEGEND
A MONITORING WELL o 100 300 500
• SOIL GAS SURVEY 111111
PROBE LOCATION
Figure 3-3
M-585 SOIL GAS SURVEY
NUMBER 2 GRID
SOURCE: ESE, 19
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-26
P78 STAGE 2 05/9'
NORTH DRAINAGE DITCH SOIL GAS SURVEY
Figure 3-4
LOCATIONS OF SOIL GAS SAMPLES, NDD, E-519, E-515
AND E-512
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-914/P78T3-11.1
02/14/92
Table 3-11. Map Coordinates and Surveyed Elevations, Stage 2 Groundwater Monitoring Wells.
Well Number Site
Designation
Universl Transverse Mercator
Northing Easting
Ground
(ft MSL)
Top of
Steel Casing
(ft MSL)
P-4* (NDD-B1)
P-5
P-6
P-7
P-8
P-9
NDD
E-512
M-585
M-585
E-519
E-515
507,298
506,740
504,271
504,039
506,879
506,551
1,744,007
1,745,898
1,747,955
1,747,636
1,747,247
1,747,728
4,463.57
4,498.17
4,540.93
4,529.52
4,517.80
4,530.70
4,500.82
4,543.41
4,531.95
4,533.55
* Well P-4 dry and abandoned.
Source: ESI Engineering, 1990.
P78-914/P783J9
02/13/92
3.5 DRILLING AND BOREHOLE PROGRAM
3.5.1 SHALLOW SOIL BORINGS AND DEEP STRATIGRAPHIC BORINGS
3.5.1.1 Shallow Soil Borings
Seventeen shallow soil borings were instaUed during soU sampling operations at the NDD, E-512, FAD, and Blue
Creek sites to assist in the evaluation of surface and shaUow subsurface sediment contamination. These borings
were instaUed to eight feet. Locations of the borings are shown in Figure 3-5.
3.5.1.2 Deep Stratigraphic Borings and Monitoring WeUs
Six deep stratigraphic borings were drilled, logged, and sampled in an effort to further delineate subsurface
stratigraphy and contamination. Deep borings were instaUed at the NDD (NDD-B1,100.2 feet), BuUding E-512
(E-512B1, 128 feet), and BuUding M-585 (M-585B1, 91 feet and M-585B2, 90 feet). These borings were
converted to groundwater momtoring wells P-4, P-5, P-6, and P-7, respectively. Two borings were instaUed at
BuUding E-515 (E-515B1,110 feet; E-515B2,197 feet) and one at BuUding E-519 (E-519B1,180.4 feet). Borings
E-519B1 and E-515B2 were converted to groundwater monitoring weUs P-8 and P-9, respectively. Boring
E-515B1 was abandoned due to drilling problems. The locations of the deep borings and wells are shown on
Figure 3-6.
3.5.2 FOOTAGE SUMMARY
A total of 896.6 feet was drilled for deep boring and monitoring weU instaUation. Total footage of shaUow soU
borings amounted to 138.5 feet.
3.5.3 GEOTECHNICAL DRILLING PROGRAM
3.5.3.1 ShaUow SoU Borings
ShaUow soU borings were instaUed by manual sampUng methods using a split-spoon sampler. The sampler was
advanced by blows delivered from a hand-driven shde hammer. Samples were obtained continuously and logged
according to the Unified SoU Classification System (USCS). DetaUed logs of borings are presented in
Appendix C. Upon completion, each soU boring was abandoned by backfilling with cuttings and surficial soils.
3.5.3.2 Deep Stratigraphic Borings and Monitoring WeUs
Drilling services for completion of the deep stratigraphic borings and momtoring weU instaUation were
subcontracted to Boyles Brothers Drilling and Dave's DrUUng, both of Salt Lake City, Utah. A Schram T-685
driU rig employing air rotary methods was used by Boyles Brothers Drilling to advance the borehole for
monitoring wells P-4, P-5, P-6, P-7, and borehole E-515B1. A Chicago Pneumatic 7,000-casing advancer rig was
employed by Dave's DrUling to driU the boreholes for momtoring wells P-8 and P-9. Samples were retrieved
using a spUt-spoon sampler (ASTM-D 1586-84) driven by a 140-pound hammer. DetaUed borehole logs and
momtoring weU completion diagrams are presented in Figures 3-7 through 3-D.
3-29
Figure 3 — 5
STAGE 2 SHALLOW SOIL
BORING LOCATIONS
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-30
P78 STAGE 2 05/91
LEGEND
GROUND WATER MONITORING
WELL AND BORING
m WELL P-7
(bore M585-B2)
DEEP STRATIGRAPHIC BORING
A NDD-B1 (WELL P-4)
0 IM 300 900 1000 I—I
Figure 3-6
STAGE 2 DEEP STRATIGRAPHIC
BORINGS AND GROUNDWATER
MONITORING WELLS
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-31
P-4
Ground
Elevation: 4463.57it. ^^-r Q.o
0 . °°-o- 0' ll o^s • a
10
20
30
40
50
60
70
80
90
100
110
120
130
Vertical Scale In Feet
1 Inch = 20 Feet
76' 12/88
•=-(4384.40' MSL)
Unstabilized
DIAMETER STEEL SURFACE CASING
AND
4" PVC STICK-UP CUT FLUSH TO GROUND
UPON WELL ABANDONMENT ON 1/26/89
TD: 99.71 ft. TD: 700.2 ft.
Figure 3-7
BORING LOG NDDB1 AND WELL
CONSTRUCTION DIAGRAM FOR P-4
SOURCE: ESE, 1991
Silty clays, very minor sand (ML/CL), moist, moderate to
low plasticity, dark brown 10 YR 3/3.
Clays, very minor sand (CL), moist, moderate pasticity,
light grayish brown 10 YR 6/2.
Sample P78-SM collected at 25 to 26.5 feet.
Clays
(Gravel fragments of dark gray quartzite.)
Sample P78-S*2 collected at 50 to 51.5 feet.
Pale brown 10 YR 6/3 with brown yellow oxidation veins
10 YR6/8.
Clays
Sample P78-S*3 collected at 75.5 to 77 feet.
Light yellowish brown 10 YR 6/4 with yellowish brown
staining throughout 10 YR 5/4.
Clays
Sample P78-SM collected at 100 to 101.5 feet,
occasional pebbles of quartzite, moist, pale brown,
10 YR 6/3 with disseminated brown yellow staining
10 YR 6/8.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-32
CD/P78/P-5/E512/B-1
P-5
Ground
Elevation:
10
4498.17 ft.
20
30
40
50
60
70
80
90
100
110
120
vy vy •Vy vy •vy vy vy •vy
vy •vy •vy
'vy
rW vy vy •vy vy vy vy vy vy vy vy vy vy •vy vy vy vy *y •vy vy vy vy vy
tvy vy vy vy •w
Evy
'vy W •Vy
vy
vy vy vy vy vy •vy •vy vy
•vy *y *y *y rvy •vy vy vy •vy
•vy vy vy •vy •vy •vy sj?
T
0.42"
L
2.97
ass
118'/89
•=-(4380.17 MSL)
130
Vertical Scale In Feet
1 Inch = 20 Feet
TD: 127.94 ft.
E-512B1
Fine-grained to very fine-grained poorly sorted silty sand,
slightly calcareous (SM), yellow brown 10 YR 5/4.
Fine-grained to very fine-grained silty sand with pebbles of
limestone and quartzite (SM/SP), 10 YR 5/4.
Silt (ML) containing fine-grained to very fine-grained sand, slightly
plastic, slightly calcareous, moist to wet. Occasional pebbles of
limestone, dolostone, and quartzite, light yellow 10 YR 6/4
to dark brown10YR3/3.
Sample P78-S*24 taken at 25 to 26.5 feet.
Sample P78-S*25 taken at 50 to 50.5 feet.
Sample P78-S*83 (duplicate) taken at 51.5 to 53 feet.
TD: 128 ft.
Gravels of limestone, dolostone, and quartzite containing very
fine-grained to fine-grained silts and sands (GM) slightly moist,
yellow brown 10 YR 5/4.
Sample P78-S*26 taken at 75 to 76.5 feet.
Poorly graded silty sand and sand silt mixtures (SM), calcareous,
containing 2 to 3 mm size chips of limestone, dolostone, and
quartzite, light yellow brown 10 YR 6/4. Sample P78-S*84 taken
at 100 to 101.5 feet. Duplicate sample P78-S*27.
Gravels of limestone, dolostone, and quartzite containing very fine-
grained to fine-grained silts and sands (GM), moist, brown 10 YR 5/3.
Clayey gravels and sand-silt mixtures (GM/SM), dry, pale brown
10 YR 6/3.
Gravels of limestone, dolostone, and quartzite containing fine-grained
sand and silts (GM), moist, pale brown 10 YR 6/3.
Sample P78-S*28 taken at 125 to 126.5 feet.
Sandy silt (ML) containing fine-grained to very fine-grained sand,
pale brown 10 YR6/3.
Figure 3-8
BORING LOG E-512B1 AND WELL
CONSTRUCTION DIAGRAM FOR P-5
SOURCE: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-33
CD/P7B/P-6/M585/B-1
Ground Elevation:
4540.93 ft.
10
20
30
40
50
60
70
80
90
100
110
120
130
Vertical Scale In Feet
1 Inch = 20 Feet
--^r 76.1' 3/89
— (4469'MSL)
Silty clay (CL), slightly moist to moist, very minor gravel of limestone
and quartzite, brown 10 YR 5/3 to light grayish brown 2.5 Y 6/2.
TD: 90.73 ft.
Sandy clay with very fine-grained sand (SC/CL), minor gravels of sandstone,
brown 7.5 YR 5/4. Sample P78-S*57 collected at 25 to 26.5 feet.
Sand, clay, and silty sand mixture (SC/SM), gravel of sandstone, limestone,
and dolostone present, moist.
Silty clay (CL) with pebbles of limestone, sandstone, and dolostone, slightly
moist, non-plastic, yellow brown 10 YR 5/4.
Clayey sand and silts (SC), minor gravels, non-calcareous,
yellow brown 10 YR 5/4.
Sample P78-S*58 collected at 51 ..5 to 53 feet.
Clayey sand, silt, and gravel mixture (SC/GC), lithic fragments.
Gravely sand and silt mixture (GC/SC), lithic fragments.
Sandy clay with very fine-grained sand (SC/CL), lithic fragments,
slightly moist, yellow brown 10 YR 5/4. Water at 73.5 feet.
Clayey gravels and sands (GC/SC), mottled texture, saturated, dark gray
10 YR 4/1 to yellow brown 10 YR 5/4, lithic fragments, PID readings 2.2 to
12.6ppm. Sample P78-S*59 collected at 75 to 76.5 feet
Gravely sandy clay (SC).
Sandy clays and silts (SC/CL), rare pebbles of quartzite, dark gray 10 YR 4/1
to yellow brown 10 YR 5/4. Sample P78-S*60 collected at 89 to 90.5 feet.
TD' 91 0 ft DuP|icate samPle P78-S*85 also collected.
Figure 3-9
BORING LOG M-585B1 AND WELL
CONSTRUCTION DIAGRAM FOR P-6
SOURCE: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-34
CD/P78/P-7/M585/B-2
P-7
Ground
Elevation:
Silty clay (CL) with very fine-grained sand, slightly calcareous,
slightly moist, yellow brown 10 YR 5/4.
Occasional pebbles of limestone and sandstone.
Silty clay to clayey sand (CL/SC), very fine-grained sand, slightly pastic,
moist, occasional pebbles, light yellow brown 10 YR 6/4. Sample
P78-S*64 collected at 25 to 26.5 feet. PID reading 25 ppm at 29 feet.
Silty clay (CL), slightly moist with occasional pebbles of limestone and
sandstone, brown 7.5 YR 4/6.
Clayey gravels poorly graded (GC), abundant fractured pebbles and lithi
fragments of limestone, sandstone, and dolostone, slightly moist, strong
brown 7.5 YR 5/16. Predominant gravels at 45 to 48 feet.
Sample P78-S*65 collected at 50 to 53 feet. Duplicate sample
P78-S*86 also collected.
Clayey gravels with siltly clays (GC/CL), fine-grained to very fine-grainec
well sorted sands, gravels consisting of sandstone, limestone, and lithic
fragments, slightly moist to wet, strong brown, 7.5 YR 4/6 to pale yellow
2.5 YR 8/2.
Sample P78-S*66 collected at 76.5 to 78 feet. Sample saturated.
Clayey gravels poorly graded (GC), abundant fractured peebbles of
chert, quartzite, and sandstone, wet, yellow brown 10 YR 5/4.
110
120
130
Vertical Scale In Feet
1 Inch = 20 Feet
Figure 3-10
BORING LOG M-585B2 AND WELL
CONSTRUCTION DIAGRAM FOR P-7
SOURCE: ESE. 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-35
Ground Elevation:
4540.93 ft
10
E515B1
20
30
40
50
60
70
80
90
100
110
120
130
#.#.>.#.#.#.
*. >.*#.>.>.*#. #. y. mf. v. y*. y.
/. •/. *#. v". >".
>.>.>. >.*«.*#. •. •»
v.y.v. >.y. "f" 'f-'f-V. V. V. •*. V.
-
v.v.v.v.v. • •"•«. #.*«.'#.>.'#.
>.-#.>.-«.'#.
Silt (ml) 10% sand. v. fine to fine grained, 2,5 YR 6/2. It grayish brown, med
plastic, dry, massive. Sand content increases to approximately 30 % at T, fine
grained. PID 0 ppm.
Clay (CL). 30% sUt, 15 % sand, fine grained, 2£YR5/2 grayish brown, moist,
med. plastic, massive. PIO 0 ppm over hole.
Gravel (GP) 3" to 4" in diameter, 30% clayey, 5% sand fine to medium grained,
massive. Pull samples P782-s*1-ss, P782-1-SS, P782-1-SV.
Interbedded w/ sandy silty days, Iron staining, ZS Y/R 5/2 grayish brown, med
plastic, massive. PID 0 ppm over hole.
CLay (CL), very candy, 20% fine grained, occasional gravels to 3/8* moist,
med. plastic, massive, 25 YR 6/2 light brownish gray. PID 0 ppm on sampte.
35" to 36* Gravel (GP) 3" to 4" in size, interbedded with clayey sand, collected sample P78-s*2-sv.
Gravel (GP) to 1/2" in diameter, 25% clay, 15% sand, fine to coarse grained,
moist, cohesive, 2JS YR 5/4 light olive brown, massive. PID 0 ppm over hole.
50* Gravel (GP), 20% sand, fme to coarse grained, sl. moist, massive, 5YR 5/3
reddish brown. Collect samples P782-s*3-ss, P782-s*3-ss, P78-s*3-sv. PID0
ppm on sample.
No cutting retum 50'-60\ hole plugging at 60*.
Gravel (GP), 20% sand, fine to coarse grained, gravels to 3/4" In diameter,
10% clay, massive sl. moist, 5YR 5/3 reddish brown. PID 0 ppm over hole.
poor cutting return from 70*-67.
87 Gravel, v. clayey. 30 % day, med. plastic, dry to sl. moist, SYR 5/2 reddish
gray. PID 0 pom over hole.
poor cutting retum to 110*.
very poor cutting retum from 60*-110*. Drill steel stuck In hole. Pull steel and
abandon hole.
Total Drifted Depth 110 feet
Hole Abandoned, No
Well Constructed
Vertical Scale In Feet
11nch «= 20 Feet
Figure 3-11
BORING LOG E-515B1
SOURCE: Hunter, 1989.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-36
CD/P78/P-B/E5197B-1
4" Rise Of Pad To Allow For
Proposed Asphalt Pavement
Ground Elevation
4517.60 ft. /
Limited Access Water-Tight
Manhole Cover (Flush Installation)
E-519/B-1
105
120
135
165 ,
180 .
TD: 179.64 ft.
Poorly graded gravel, clayey, pooriy graded Band, low plasticity, dense
slightly moist. (GP) dark grayish brown 10 YR 4/2.
Very silty, clay, low plasticity, moist, firm. (CL) brown 10 YR 5/3.
Silt, low plasticity, slightly sandy, gravelly with very fine-grained sand, moist. Some iron
oxide staining. (ML) light gray 10 YR 7/2. Clayey, grading downward into silts. Lightly
moist, non-plastic. Pebbles up to 1 1/2", mottled texture. (ML) Light gray to brown 10
YR 7/2 -10 YR 5/3. Sample P78-S*6 collected at 20-21.5 feet. TIP o 23.2 ppm.
Silts, clayey, slightly gravelly with very fine-grained sand, non-plastic.
(GP) Light gray to brown grading down into graveMO YR 6/2.
Silts, gravelly, and fine-grained sand, non-plastic to low plasticity, slightly motet.
Pebbles W-1/2" in diameter. (ML) Yellowish brown 10 YR 5/B. Brownish yellow 10 YR
6/6. Sample P78-S*7 taken at 36 - 37 feet. Clayey, minor lenses of poorly sorted,
slightly moist sandstone, low plasticity. (ML) yellowish brown 10 YR 5/8.
Sand, slightly silty, clayey, slightly moist, poorly sorted, low plasticity.
(SM) yellowish brown 10 YR 5/8.
Gravel, poorly graded, loose pebbles and cobbles up to 2* in diameter, sandy, minor
silt grading downward into gravel up to 1/2" in diameter. Moderately sorted.
(GP) yellowish brown 10 YR 5/6.
Coarse gravel, silty, clay, poorly sorted and graded, dry. Pebbles of dark gray
daystone, color variegated. (GM)
Gravel, slightly silty and clayey increasing towards bottom, slightly plastic.increasingly
moist. (GM) yellowish brown 10 YR 3/4.
Gravel with thin lenses of silty claystone, moderately plastic. (GM) yellowish brown 10
YR5/8.
Gravel with minor clayey-sllty matrix, slightly moist, slightly plastic. (GM) yellowish
brown 10 YR 5/8. Sample P78-S*B taken at 97-97.4 feet.
Poorly graded gravel with thin lenses of silty claystone, slightly moist, low plasticity.
(GM) yellowish brown 10 YR 5/8.
Silt, sandy, minor gravel, very low moisture, low plasticity.
(ML) brownish yellow 10 YR 6/8.
Clayey, dry. non-plastic.
Silt, very fine-grained sand, minor gravel, no moisture, low to non-plastic
(ML) yellowish brown 10 YR 5/8. Sample P78-S"9 taken at 137-138 feet.
Minor interbedded siltstone, slightly moist.
Minor silt with thin lenses of clay, low moisture, slightly plastic.
(ML) yellowish brown 10 YR 5/8.
Silt, very clayey, minor gravel, poorly sorted, moist, moderate plasticity, moderately
dense.
(ML) dark yellowish brown 10 YR 3/6.
Clay, minor gravel, trace of silt, moderately dense, moist, moderately plastic.
(ML) dark yellowish brown 10 YR 5/6.
Sample P78-S'10 taken at 171.4-171.8 teet.
Sanple P78-S*11 taken at 171.8-173.8 feet.
TD: 180.40 ft
Vertical Scale In Feet
1 Inch = 30 Feet
Figure 3-12
BORING LOG E-519B1 AND WELL
CONSTRUCTION DIAGRAM FOR P-8
SOURCE: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-37
CD/P78/P-9/E51!yB-2
P-9
Ground
Elevation: 4530.70 ft.
30
45
60
75
90
105
120
135
150 •
165 •
fa
•••-a
w •vy •vy •vy ^vy vy vy vy vy vy vy
t-vy tvy •vy •vy ^ fa vy vy i-vy vy vy fvy
t.vy
'vy •vy vy i-vy •vy vy
rvy vy 'w ••vy ivy *y vy vy •vy
i
•vy tvy •vy w •vy tvy •vy vy vy vy vy vy vy vy vy
tvy vy vy •vy vy vy vy vy
•P' *y vy vy •vy vy •vy
tvy
•vy tvy •vy vy .•Vy tvy •vy vy
fVy •vy vy vy •vy vy vy
T
0.6C
1. 2.85'
2.25'
178.50 7/89
18o — (4352.20 MSL)
195-
Vertical Scale In Feet
1 Inch = 30 Feet
TD: 195.27 ft.
z
E515/B-2
z
. #. #. #. I . >. *#. >. \
?t7t?t?t7i
f. f.f.f.'f.f.
'f.'f.'f.'f.'f.'f.
>. "rf . *#. '*.*#• >.>.'#.>.'#.'#.
. #. #. #. #. #.
#. r. f. #. #. #,
. #. #. #. #. #.
Silt, clayey, minor sand and gravel, dry, non-plastic, loose.
(UL) light yellowish brown 10 YR 6/4.
Sample P78-S*1 taken at 15-16.5 feet. Clay, moderately dense, slightly silty,
weathered, Fe stains, slightly moist and plastic. (CL) pale brown 10 YR 6/3.
Interbedded with silt, fine-grained, well sorted, minor gravel zones.
(CL) yellowish brown 10 YR 5/B.
Gravel, fine-grained to coarse-grained, poorly sorted, clayey, silty. dry with
interbedded slightly moist claystone.
Silt, clayey, fine-grained, slightly moist, minor gravels, sandy, slightly plastic, dense,
well sorted. (UL) pale brown 10 YR 6/3.
Sample P78-S*2 taken at 35-26.5 feet. (ML) pale brown 10 YR 7/4.
Gravel, poorly sorted, pebbles to 4", fine-grained to coarse-grained, clayey, silty.
Fine-grained to coarse-grained sand.
Dolostone and limestone gravels. (GP)
Gravel, fine-grained to coarse-grained, fragments to 2". Coarse-grained sand,
clayey, angular fragments of limestone and sandstone. (GC) pale red 10 YR 6/3.
Sandy, coarse-grained, slightly clayey, limestone/sandstone clasts and fragments.
Zones of ML, SU, GP, and GC. Silt, very sandy, fine-grained to coarse-grained,
slightly moist, calcareous veins, gravel lenses saturated with free water.
Sample P78-S*3 taken at 97-98.5 feet.
Gravel, clayey, sandy, fine-grained to coarse-grained, angular gravel fragments of
limestone and Fe stained sandstone to 3". (GC) redish brown 5 YR 5/3.
Gravel, coarse, limestone and sandstone fragments to 2", sandy, coarse-grained.
(GP) reddish brown 5 YR S3.
Silt, sandy, fine-grained to coarse-grained, medium plastic, slightly moist, massive.
(SM) pale red 10YR6/3.
Sample P78-S'4 taken at 135-136.5 feet.
Gravel (GP)
Silt (ML)
Gravel (GP)
Silt with gravel lenses (ML)
Gravel with Interbedded silts, gavels 1/8' to 1/2*. angular to sub-rounded, coarse
sand, clasts of limestone and sandstone. Occassional clasts with calcite rind. (GP)
Gravel, some volcanics, gravel fragments up to 1".
Gravel, fragments up to 3/8', very sandy, coarse sand, silt. (GP)
Silt with Interbeddedangular gravel lenses. (ML)
Gravel, coarse, 2" fragments, coarse sand. (GP)
TD: 197.0 ft
Figure 3-13
BORING LOG E-515B2 AND WELL
CONSTRUCTION DIAGRAM FOR P-9
SOURCE: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-38
P78-9M/P78339
02/13/92
3.5.4 MONITORING WELL DESIGN AND CONSTRUCTION
Six deep borings were completed as groimdwater monitoring wells. All well installations began within 24 hours
of boring completion and continued uninterrupted until completion. Monitoring wells were installed in an 8-inch
borehole and consisted of a threaded 4-inch Schedule 40 PVC pipe with 0.02-inch factory slotted screen. Slotted
PVC (also Schedule 40) screen was installed from 5 feet above the top of the water table to the bottom of the
boring, with blank PVC pipe (Schedule 40) to ground surface. The well screen and casing were carefully
steam-cleaned with approved site water from Building M-696 prior to instaUation in the hole. Centralizers were
used to assure plumbness. A clean, inert sand filter pack consisting of 10-20 mesh Colorado silica sand was
tremied in the annular space between the screen and the borehole, extending to 3 feet above the well screen.
A minimum 2-foot bentonite clay seal was placed on top of the sand pack, and the annular space was tremie
grouted with a cement/bentonite grout, extending from the bentonite seal to the ground surface. The bottom
of the well screen was capped prior to installation to prevent formation material from entering into the well, and
a vented cap was installed at the top of each monitoring well. Sohd casing extends from the top of the screen
to approximately 3.0 feet above land surface on momtoring wells P-5, P-6, P-7, and P-9. Monitoring well P-8
is flush mounted with the ground surface in the E-519 parking lot. A steel casing with a locking cap was instaUed
on each well, except P-8, for protection. Monitoring weU P-8 has a limited access water-tight manhole cover.
The foUowing materials and procedures were used in monitoring weU construction:
• Casing used in the monitoring weU was 4-inch inside diameter Schedule 40 PVC, flush-jointed and
threaded. The screen used had a slot width of 0.02 inches. Base caps and top caps were instaUed on
each of the monitoring weUs.
• Grout was composed of a Type I / Type II Portland cement/bentonite slurry. The slurry was prepared
by adding 3 to 5 pounds of bentonite and approximately 6.5 gaUons of approved water for each 94-pound
sack of Type I Portland cement.
• Bentonite peUets used in the seal were a commerciaUy available product designed for weU-sealing
purposes.
• Sand material used in the filter envelope surrounding the weU screen was clean, inert quartz sand of
10-20 mesh size.
• A protective steel casing was instaUed around aU monitoring wells except as noted for monitoring
weU P-8. This casing extended 2 to 3 feet above land surface and was seated 2 to 3 feet into the weU
seal grout. This casing was vented to the atmosphere via a lockable, hinged cap, that prevents entry of
water but is not airtight. In this manner, the momtoring weU is in open connection to the atmosphere
to aUow for water level stabilization due to natural fluctuations in barometric pressure. A 0.25-inch
diameter drainage port was instaUed. The same key was used for aU weU padlocks at the site.
• The protective steel casing was seated in a 2-foot square concrete pad 4 inches thick. The pad was
sloped away from the weU sleeve. Three 3-inch diameter concrete filled steel guard posts were instaUed
radiaUy away from the weU stick-up. The guard posts were at least 5 feet in length and enclosed in
3-39
P78-914/P78340
02/13/92
concrete to 2 feet below ground surface. The protective well sleeve and guard posts were painted safety
yellow, and the monitoring well number was marked on the sleeve exterior. For monitoring well P-8,
which was located in the parking lot at Building E-519, a grooved manhole cover was mounted flush with
the ground surface.
A sketch of the monitoring well construction was included on the boring log. It shows, by depth, the bottom of
the boring, screen location, coupling location, granular backfill, seals, grout, cave-in, and height of the PVC
casing above ground surface. After the grout seal had set (approximately 24 hours), it was checked for
settlement, and additional grout, if needed, was added to fill any depression(s).
3.5.5 MONITORING WELL DEVELOPMENT
Monitoring wells were developed using a submersible pump or bailer until the water was clear and the well
sediment free to the fullest extent practical. The pump or bailer was rinsed with approved site water from
Building M-696 (Howell pumphouse), decontaminated following procedures outlined in the Technical Work Plan
(ESE, October 1988), and allowed to air dry prior to use in the next monitoring well.
An ESE hydrogeologist recorded field pH, temperature, and conductivity at each purge volume. Physical
characteristics, including clarity, odor, sand content, color, and TIP readings, were also recorded on field sheets,
located in Appendix C.
Monitoring well development began no sooner than 24 hours after completion of the mortar collar placement.
Development proceeded until the following conditions were met:
• The monitoring well water was clear to the unaided eye,
• The sediment thickness remaining in the well was less than 5 percent of the screen length, and
• At least five well volumes (including the saturated filter material in the annulus) were removed from
the monitoring well. If the monitoring well would not produce five purge volumes, the well was purged
dry and allowed to recover.
The cap and all internal components of the monitoring well casing above the water table were rinsed vvith well
water to remove all traces of soil/sediment cuttings. This washing was conducted before and/or during
development.
3.5.6 AQUIFER TESTING
The hydrauhc conductivity of the lake clay and gravel sediments in the uppermost aquifer beneath Plant 78 area
was evaluated by conducting aquifer tests (slug/bail) in five of the six monitoring wells. Although it is recognized
that the radius of influence is smaller for this type of test than for long-term pumping tests, slug/bail tests were
selected for the Plant 78 hydrogeologic study to avoid problems associated with the disposal of large quantities
3-40
P7S-914/P78341
02/13/92
of potentially contaminated groundwater that results from pumping tests. Aquifer test plots are presented in
Appendix D.
A slug/bail test consists of instantaneously raising or lowering the water level in a well and monitoring the
recovery of the water level over time. The test is performed by rapidly introducing or withdrawing a known
volume into or from the well. The slug/bail tests performed during this investigation utilized a capped and
weighted section of stainless steel pipe, referred to as a slug.
The term "slug test" refers to the injection test in which water level is suddenly increased, and the term "bail test"
refers to the withdrawal test in which the water level is suddenly lowered. When the slug is instantaneously
lowered into the water column, the water level rises rapidly. Instantaneous withdrawal of the slug after the water
level has recovered and stabilized causes the water level to drop rapidly. Both tests should produce comparable
results under similar field conditions if a sufficient length of time is allowed to achieve maximum water level
recovery between tests. Because the main limitation on slug/bail tests is the buffering of the formation hydrauhc
conductiviry by the well sand pack, both slug and bail tests were conducted on each monitoring well to provide
verification of data (Freeze and Cherry, 1979). Because variations can occur due to the potential influences of
monitoring well construction (i.e., sand pack), conductivity data developed from slug/bail tests should be
considered only as an estimate of the true hydrauhc conductivities of the formations.
Prior to testing, the static water level in each momtoring well was measured using an electric water-level
indicator. A model PT-108C pressure transducer, manufactured by ORS EnviroLabs, Inc., with an operating
pressure range of 0-15 pounds per square inch (psi) was used to measure water levels during the aquifer tests.
Data from the transducer was recorded by a Model EL200 data logger manufactured by EnviroLabs, Inc. The
data logger was programmed to record water-level changes to within 0.01 feet at 0.2 second intervals for the first
5 minutes, 1-second intervals for 5 to 10 minutes, 10 second intervals for 10 to 20 minutes, and 20 second
intervals for 20 to 30 minutes.
After pretest measurements and programming of the data logger, the pressure transducer is lowered into the
water to a depth that is below the lowest point to which the slug will be lowered. The slug is then rapidly
lowered into the water column in the monitoring well. The 3.5-inch diameter, 11.15-foot long slug displaces
0.5 feet3 of water, which corresponds to an initial change in the water elevation in the 4-inch diameter well of
approximately 5.73 feet.
As data are coUected, water levels displayed by the data logger are examined to monitor trends and the progress
of the test. The accuracy and completeness of data are thereby reviewed before each test is terminated. Each
test was aUowed to proceed until the water level attained at least 95 percent recovery. AU data were stored in
the final memory of the data logger. Data from the data logger were transferred to diskette storage in the office.
3-41
P78-914/P783.42
02/13/92
Following completion of the slug test (injection of the slug) and stabilization of the water level, a bail test
(removal of the slug) was perfonned. The slug and pressure transducer were cleaned with an Alconox solution,
rinsed with approved site water, rinsed with ASTM Type II reagent grade deionized water, rinsed with pesticide
grade methanol, followed by a final rinse with pesticide grade hexane. The equipment was then allowed to air
dry prior to use in the next monitoring well.
3.5.6.1 Data Analysis
Test data were analyzed by means of methodology developed by Bower and Rice (1976) and updated by Bower
(1989). A summary of this method and its limitations is presented below.
The water recovery height in a monitoring well (in feet), following slug injection or withdrawal, is plotted on the
logarithmic axis (Y-axis) of semi-logarithmic paper against time, which is plotted on the normal axis (X-axis).
A line is fitted to the second straight line portion of the curve (the first straight line portion usually indicates a
high permeability zone corresponding to the well sand pack) and the hydrauhc conductivity (K) is calculated by
the following equations.
1. The monitoring well casing radius is corrected for sand pack effects utilizing equation (1):
r« - [U-»)re
2 • nrjf (D
where: ra = corrected casing radius (feet),
rc = casing radius (feet),
rw = well bore radius (feet), and
n = sand pack porosity (percent).
The porosity of the sand pack was set equal to 0.30 to solve equation (1).
In
2. Solve for by either equation (2) or (3):
For fully penetrating wells where height of the water column (H) is equal to the total water depth (D)
(H = D):
In 1.1
ln H (2)
3-42
P78-914/P7S343
02/13/92
For partially penetrating wells where height of the water column is less than the total water depth
(H < D):
w )
A + B ln
1.1
( D - H)
In L_
r .
-l
(3)
where: Re = effective radius of the well (feet),
H = distance from static water level to bottom of well (feet),
D = distance from static water level to impermeable bottom layer (saturated thickness) (feet),
L = well screen length (feet), and
A, B, and C = determined graphically as functions of L/rw.
3. Calculate the hydrauhc conductivity (K) by equation (4):
rj In
2L
(4)
where: K = hydrauhc conductivity (feet/second),
t = a picked time (in seconds) less than the t intercept (tQ) of the line plotted from the
recovery verses time graph,
Yt = recovery (in feet) corresponding to the chosen t, and
Y0 = Y intercept of the line plotted from the recovery verses time graph.
To convert K from feet/second to feet/day, multiply by 86,400. Results and discussion of the aquifer testing are
presented in Section 4.0. Calculations are given in Appendix D.
3.5.6.2 Additional Data Analysis
Groundwater gradient for each investigation site was determined using the following equation:
i = D/H (5)
where: / = Groundwater gradient (ft/ft),
D = Linear distance between measurement points in feet, and
H = Difference in water table height in feet.
3-43
P78-914/P783/44
02/13/92
Groundwater velocity for each investigation was determined by the following equation:
V = Ki/n
where: V = Groundwater velocity in feet/day (fpd),
K = Hydrauhc conductivity feet/day (fpd),
/' = Groundwater gradient (ft/ft), and
n = Aquifer porosity, assumed to be 30 percent or 0.30.
3.5.7 MONITORING WELL ABANDONMENT
Monitoring well P-4 was abandoned and plugged on January 26, 1989. At the time of completion, December
1988, a water level was recorded at 78.5 feet below ground level. In order to accommodate 30 feet of screen,
it was necessary to advance the borehole to 100 feet. Water levels taken after the monitoring well was completed
indicated the well was dry. A confining layer appeared to have been penetrated while extending the depth of
the well to accommodate the required screen length. The monitoring well was abandoned by leaving the PVC
casing in place, filling the casing with 1/2-inch bentonite pellets to a depth of 66 feet below ground surface and
grouting the remaining casing to ground level with a grout/bentonite mixture. The PVC casing was cut off at
ground level.
3.5.8 WATER LEVEL MEASUREMENTS
Water level measurements from the groundwater momtoring wells were obtained using an electronic sounding
tape manufactured by Solinst, Inc. Measurements are accurate to within 0.01 foot. The following procedures
were employed to insure accurate and safe field procedures:
• With a respirator on, the monitoring well was approached from an upwind direction.
• The precalibrated photoionization detector (PID) was zeroed to ambient air conditions.
• The monitoring well cap was removed and an immediate PID reading taken of the headspace at the top
of the casing (TOC), followed by a PID reading of the breathing zone area to assure that safe levels of
organic vapors (less than 3 ppm) were present. These readings were recorded. AU notations were
recorded in duplicate on a water level measurement form and in a bound field logbook.
• The monitoring weU number, date, time, and initials of field personnel taking measurements were
recorded.
• The length of the riser stickup from the ground surface to a measuring point marked at the TOC was
measured and recorded to the nearest 0.01 foot.
• The water level indicator probe was inserted until it reached water. The depth to water was measured
from the same measuring point at the TOC and recorded to the nearest 0.01 foot.
• The total depth of the monitoring weU was measured in the same fashion.
3-44
P78-914/P7S3.45
02/13/92
• The water-level indicator was retrieved and decontaminated.
3.6 SAMPLING PROGRAM FOR PHASE II STAGE 2 USAF PLANT 78 IRP
The number and types of samples, and the field methods for sampling various media for the Phase II Stage 2
investigation at Plant 78 are described below. Detailed information regarding sampling and decontamination
procedures, chain-of-custody and documentation requirements, instrument descriptions, and calibration protocol
is provided in the USAF IRP Plant 78 Phase II Stage 2 Quahty Assurance Project Plan (QAPP) (ESE,
November 1988).
The following will be a site-by-site discussion of Stage 2 investigations as summarized on Table 3-1. The results
and significance of findings for the Stage 2 investigation are discussed in Section 4.0.
3.6.1 TYPES AND NUMBERS OF SAMPLES TAKEN
3.6.1.1 Soil Gas Survev
To further assess soil and groundwater contamination identified by Stage 1 analysis, two soil gas surveys were
performed at M-585. A total of 75 PETREX™ soil gas coUectors were installed for Survey 1, and 66 soU probe
samples were coUected for Survey 2 (Figure 3-14).
3.6.1.2 Surface Sediment and Surface Water Samples
To verify and further define contamination identified during Stage 1 investigations, surface sediment and surface
water samples were coUected at the NDD, E-512, FVD (surface sediment only), and Blue Creek.
3.6.1.2.1 North Drainage Ditch
Two sample sites were investigated at the NDD. Surface sediment sample NDD-SS1 and surface water sample
NDD-SW1 were coUected from the NDD just east of R Street. Surface water sample NDD-SW2 was coUected
from the NDD just west of BuUding E-516. The locations of these samples are shown on Figure 3-15.
3.6.1.2.2 E-512
One site was investigated at E-512. Surface sediment sample E-512SS1 and surface water sample E-512SWS1
were taken in the E-512 drainage ditch just west of BuUding E-512. The locations of these samples are shown
in Figure 3-16.
3.6.1.2.3 Faust VaUey Drainage
Six surface sediment sites (FVD-SS1, FVD-SS2, FVD-SS3, FVD-SS5, FVD-SS6, and FVD-SS8) were sampled
along the FVD to assess potential contaminant occurrence and contamination source relationships. Surface water
samples were not coUected at FVD, because of lack of discharge. The location of the FVD sample sites are
shown in Figure 3-17.
3-45
P78 STACC 2 05/91
LEGEND
SOIL GAS SURVEY 1
SOIL GAS SURVEY 2
100 300 500
Figure 3-14
COMBINED SOIL GAS SURVEYS 1
AND 2, M-585 FRENCH DRAIN SITE
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-46
P78 STAGE 2 05/91
100 ST.
LEGEND
O—NDD-SS2 -SURFACE WATER AND
NDD-SW2 SEDIMENT SAMPLE
w
100 200 300 400 500 1000 feet
Figure 3-15
STAGE 2 SURFACE WATER AND SEDIMENT
SAMPLING LOCATIONS, NORTH DRAINAGE DITCH
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78 STAGE 2 05/91
LEGEND
O E-512SW1 - SURFACE WATER AND SEDIMENT SAMPLE LOCATION
E-512SS1
w
0 100 300 500
Figure
STAGE
E-512
3-16
2 SHALLOW
SITE
SOIL BORING LOCATIONS
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78 STAGE 2 05/91 PFIG 3-17
Figure 3-17
STAGE 2 SHALLOW SOIL
VALLEY DRAINAGE SITE
BORING LOCATION, FAUST
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-914/P783J0
02/14/92
3.6.1.2.4 Blue Creek
Two rounds of surface water and sediment sampling were conducted at Blue Creek. Fifteen sites for surface
water (BC-SWS1 through BC-SWS15) and seven sites for surface sediment (BC-SS1 through BC-SS7) were
sampled along Blue Creek during Round 1. During Round 2, nine sites for surface water (BC-SW3 through
BC-SW10) and nine sites for surface sediment (BC-SS3 through BC-SS10) were collected. Figure 3-18 shows
the locations of these sites.
3.6.1.3 ShaUow Borings
ShaUow borings were instaUed and soU samples coUected at the NDD, at E-512, along the FVD, and along Blue
Creek.
3.6.1.3.1 North Drainage Ditch
Seven shaUow borings (NDD-SB1 through NDD-SB7) were instaUed along the NDD by a hand-driven split-spoon
to depths of approximately eight feet. Two samples were coUected from each shaUow boring. The locations of
these borings are shown in Figure 3-19.
3.6.1.3.2 E-512
Three shaUow borings (E-512SB1, E-512SB2, and E-512SB3) were instaUed at the E-512 site by a hand-driven
split-spoon to depths of approximately eight feet. Two samples were coUected from each shaUow boring. The
locations of these borings are shown in Figure 3-20.
3.6.1.3.3 Faust VaUey Drainage
One shaUow boring (FVD-SB1) was instaUed along the FVD by a hand-driven split-spoon to a depth of
eight feet. Two samples were coUected from this boring. The location of this boring is shown in Figure 3-21.
3.6.1.3.4 Blue Creek
Six shaUow borings (BC-SB1 through BC-SB6) were instaUed along Blue Creek by a hand-driven split-spoon to
depths of approximately eight feet. Two samples were coUected from each boring. The locations of these
borings are shown in Figure 3-22.
3.6.1.4 Deep Borings
Deep borings were instaUed at M-585, the NDD, E-512, E-519, and E-515. Each boring was sampled to
determine the nature and extent of potential contamination.
3-50
P78 STAGE 2 OS/91
BC-SS9
BC-SW9
LEGEND
O SAMPLING EPISODE 1 (DECEMBER 1988)
• SAMPLING EPISODE 2 (MARCH 1990)
0 100 300 300
Figure 3-18
STAGE 2 SURFACE
LOCATIONS, BLUE
SEDIMENT
CREEK
AND WATER SAMPLE
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78 STAGE 2 05/91
LEGEND
A SHALLOW SOIL BORING LOCATION
0 100 200 300 400 500 1000 feet
Figure 3-19
STAGE 2 SHALLOW SOIL
NORTH DRAINAGE DITCH
BORING LOCATIONS
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78 STAGE 2 05/91
E-312 DRAINAGE
BLDG
E-512
A E-512SB3
E-512SB2
E-512SB1
LEGEND
A E-512SB1 SHALLOW BORING LOCATION
100 300 500
Figure 3-20
STAGE 2 SHALLOW
E-512 SITE
SOIL BORING LOCATIONS
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78 STAGE 2 05/91
LEGEND
FVD-SB1 SHALLOW SOIL BORING
Figure 3 — 21
STAGE 2 SHALLOW SOIL
VALLEY DRAINAGE SITE
BORING LOCATIONS, FAUST
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P7B STAGE 2 05/91
LEGEND
M <: :> s
0 100 300 500 1000 (eet A BC-SB6 - SHALLOW SOIL BORING LOCATION w
Figure 3-22
STAGE 2 SHALLOW SOIL BORING LOCATIONS,
BLUE CREEK
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-914/P7&3.56
02/14/92
3.6.1.4.1 M-585
Deep borings M-585B1 and M-585B2 were drilled at M-585. Four soil samples (M-585B1A through M-585B1D)
were coUected from M-585B1 by a spht-spoon sampler. Three soU samples (M-585B2A through M-585B2C)
were coUected from M-585B2 by a spht-spoon sampler. The locations of these borings are shown in Figure 3-23.
3.6.1.4.2 North Drainage Ditch
Deep boring NDD-B1 was driUed at the NDD. Four soU samples (NDD-B1A through NDD-B1D) were
coUected by a spht-spoon sampler. The location of this boring is shown in Figure 3-24.
3.6.1.4.3 E-512
Deep boring E-512B1 was driUed at E-512. Five soU samples (E-512B1A through E-512B1E) were coUected by
a spht-spoon sampler. The location of this boring is shown in Figure 3-25.
3.6.1.4.4 E-519
Deep boring E-519B1 was driUed at E-519. Six soU samples (E-519B1A through E-519B1F) were coUected by
a spht-spoon sampler. The location of this boring is shown in Figure 3-26.
3.6.1.4.5 E-515
Deep borings E-515B1 and E-515B2 were driUed at E-515. Three soU samples (E-515B1A through E-5151B1C)
were coUected by spht-spoon sampler from boring E-515B1. Four soU samples (E-515B2A through E-515B2D)
were coUected by spht-spoon sampler form boring E-515B2. The locations of these borings are shown in
Figure 3-27.
3.6.1.5 Groundwater Samples
Groundwater samples were coUected from monitoring wells P-1, P-2, P-3, P-5, P-6, P-7, P-8 and P-9.
Groundwater monitoring weU P-4 became dry and was abandoned. The locations of these monitoring wells are
shown in Figure 3-28.
3.6.1.6 Biological Sampling
Biological data coUection and sampling were conducted to support the Plant 78 site characterization and risk
assessment, as weU as to determine plant and animal community disturbance caused by potential environmental
damage. Biological samples coUected consisted of plants, aquatic invertebrates, and smaU mammals.
3.6.1.6.1 Sampling of Plant Communities
Ten non-random 50 meter (m) vegetation transects were conducted on or near Plant 78. Random sampling was
not an option, given the nature and frequency of ongoing operations at the facUity. The locations of the
vegetation transects are shown in Figure 3-29.
3-56
P78 STACK 05/91
• BORE M-585B1
• BORE M-585B2
LEGEND
• BORE M-585B2 - DEEP STRATIGRAPHIC BORING
W
0 100 200 300 400 500
Figure 3-23
DEEP STRATIGRAPHIC BORING
LOCATIONS, M-585 SITE
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-57
P78 STAGE 2 05/91
ion ST
LEGEND
A BORE NDDB1 - DEEP STRATIGRAPHIC BORING
0 100 200 300 400 500 1000 feet
Figure 3-24
STAGE 2 DEEP STRATIGRAPHIC BORING
LOCATION, NORTH DRAINAGE DITCH
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78 STAGE2 05/91
LEGEND 0 100 200 300 400 500
A BORE E-512B1 - DEEP STRATIGRAPHIC BORING
Figure 3-25
STAGE 2 DEEP STRATIGRAPHIC BORING LOCATION
E-512 SITE
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78 STAGE2 OS/91
E-516
LEGEND
• E-519B1 - DEEP STRATIGRAPHIC BORING
O 10O 200 300 400 500 f««t
Figure 3-26
STAGE 2 DEEP STRATIGRAPHIC
BORING, E-519 SITE
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-60
P78 STAGE 2 05/»l
E-516
LEGEND
• E-515B1 - DEEP STRATIGRAPHIC BORING
O 100 200 300 400 500 <««t
Figure 3-27
STAGE 2 DEEP STRATIGRAPHIC
BORINGS, E-515 SITE
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
3-61
P78 STAGE 2 05/91
LEGEND
9 WELL P-1 - GROUNDWATER MONITORING WELL
^ BORE NDDB1 (WELL P-4) -LOCATION OF ABANDONED
MONITORING WELL
Figure 3-28
GROUNDWATER MONITORING WELLS,
USAF PLANT 78
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78 STAGE 2 05/91
VEGETATION
TRANSECT #10
Figure 3-29
STAGE 2 VEGETATION TRANSECT LOCATIONS
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-914/P783.64
02/14/92
3.6.1.6.2 Sampling of Aquatic Ecosystems
Three sites along Blue Creek were selected for the coUection of nine stream bottom sediment samples (three
at each site). These samples were coUected to estimate the diversity and populations of aquatic invertebrates
within the creek. The locations of the sites are shown in Figure 3-30.
3.6.1.6.3 SmaU Mammal Trapping
Two areas were chosen for live trapping of smaU mammals. Ten live traps were placed within the plant
boundaries near the northeast corner, whUe another 10 traps were placed on a site just south and west of the
plant near Blue Creek (Figure 3-31). The traps were baited and placed open every night for four nights. Each
trap was checked the foUowing morning. Captured mammals were identified, and their sex, weight, length of
body, and length of taU recorded. AU captured mammals were released unharmed.
3.7 LABORATORY OA/OC PROGRAM. SUMMARY OF QAPP
The laboratory QA/QC procedures that were specified in the QAPP for this project were developed to ensure
that the foUowing project goals for analytical data quahty were met:
• QA/QC analysis data had to be generated in sufficient volume to enable the project team to verify that
the Data QuaUty Objectives (as described in Section 3.2 of this report) were met by the laboratory;
• Standard analytical protocols had to be used by the laboratory to aUow this data to be compared with
the results of other studies that have been performed at this site; and
• The data and documentation generated by the laboratory had to be litigation quahty.
In order to meet these goals, a number of requirements were specified in the QAPP. The foUowing items
outline some of the key specifications required by the laboratory:
• Standard SW846 (3rd edition) analytical protocols and requirements were foUowed for aU analyses
performed by the laboratory.
• Chain-of-custody procedures were observed for aU samples. Documentation was generated to
demonstrate that these procedures were foUowed at aU times.
• Instrument detection limits (LDLs) were generated for aU analytical methods using standard EPA
methodology. AU sample results below these values were reported as <X.XX, where X.XX represents
the numeric value for the detection limit.
• Laboratory blanks, standard matrix spikes, sample matrix spikes, sample matrix spike duplicates and
sample duplicates were analyzed during the course of this project. These QC samples were used to
ensure that the analytical methods performed by the laboratory were in control. Wherever possible,
control limit criteria was based on historical laboratory performance data. For methods in which
inadequate historical data existed for the generation of statisticaUy valid control criteria, EPA acceptance
criteria for the appropriate method (8270 and 6010) were used. AU other methods are in-house
3-64
P78 STAGE 2 05/91
Figure 3-30
STAGE 2 AQUATIC SAMPLE LOCATIONS INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
SOURCE: ESE, 1991.
P78 STAGE 2 05/9)
LEGEND
Wft. - SMALL MAMMAL TRAPPING
Figure 3-31
STAGE 2 SMALL MAMMAL TRAPPING LOCATIONS
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-914/P783.67
01/14/92
laboratory methods as specified in the PARCC tables.
• AU standards used for instrument caUbration were either directly traceable to EPA or NBS reference
materials, or the standards were checked against EPA-supplied QC check samples. Standards
traceability and verification data were thoroughly documented and are avaUable on file at the ESE
laboratory.
• Second column confirmation was required for gas chromatograph (GC) analysis procedures. This
requirement substantiates the quantitative identification of aU GC target analyses reported by the
laboratory.
• Data packages were compUed and archived for aU sample analyses. These data packages contain aU the
documentation that was generated for every analytical lot that contained Plant 78 analysis data. Enough
documentation is included in these lot folders to aUow a complete reconstruction of the analysis of the
project samples, if necessary.
The paragraphs above summarize the QA/QC program that was foUowed by the ESE laboratories during this
project. In cases where the laboratories did not comply with the QAPP requirements, documentation describing
the noncompliant procedures were generated, and corrective actions were implemented. This documentation
is supplied in Appendix E.
3-67
4.0 RESULTS AND SIGNIFICANT FINDINGS
P78-921/P784A.1
02/14/92
4.0 RESULTS AND SIGNIFICANT FINDINGS
4.1 DISCUSSION OF RESULTS
Stage 2 investigations were conducted at Plant 78 from December 1988 through March 1990. The following is a
discussion of the results of this investigation by site and a comparison with the results of the Stage 1 investigation.
4.1.1 DISCUSSION OF NON SITE-SPECIFIC ECOLOGICAL CHARACTERIZATION STUDIES
Biological data collection and sampling was conducted in support of Plant 78 site characterization and risk
assessment, and to determine plant and animal community disturbance caused by potential environmental damage.
Biological samples collected consisted of plants, aquatic invertebrates, and small mammals. Plants and mammals
were studied in non site-specific sampling and are discussed below. Aquatic sampling was conducted along Blue
Creek and is discussed in Section 4.1.7.
4.1.1.1 Terrestiral Vegetation
Vegetative cover was measured with ten 50-meter (m) transects across Plant 78 (Figure 4-1). Litter and bare
ground were observed in 68 percent of the 500 points sampled (Table 4-1). Total herbaceous cover for Plant 78
was estimated at 32 percent of the surface area, a relatively low cover total in comparison with the surrounding
area. Due to the ongoing activities at the plant, and for fire prevention, vegetation must be kept cut to a low height.
Cut vegetation in combination with the low precipitation and use of herbicides, has resulted in a low percentage of
herbaceous cover and low species diversity at Plant 78.
The only grass species observed on the transects was crested wheatgrass (Agropyron cristatum) at 13.6 percent
cover; this was the most common plant observed on transects. Shrubs found on the transects were sagebrush
{Artemisia spp.) at 7 percent cover and rabbitbrush (Chrysothamnus viscidiflorus) at 3 percent cover. The second
most common plant on Plant 78 was a small annual forb, Collinsiaparviflora, which was observed on 8.4 percent
of transect points. Another common forb was the annual Ranunculus testiculatus. Arrowgrass (Triglochin
maritima) was common down by Blue Creek. Mosses (Bryophyta) were common on many transects, but seemed
most common on the eastern, sloped transects. Other plants observed but not occurring in the transects were
junipers, cheatgrass (Bromus spp.), western wheatgrass (Agropyron smithii), ornamental trees and shrubs, and
wetland vegetation to the south of the Plant 78/Thiokol Complex (along Blue Creek).
4.1.1.2 Terrestrial Vertebrates
4.1.1.2.1 Birds
A great number of waterfowl and water associated bird species are potential visitors to Plant 78 due to its proximity
to Bear River Migratory Bird Refuge managed by the U.S. Fish and Wildlife Service (FWS), and the State of Utah
Waterfowl Management areas, which are located within five to ten miles south of Plant 78. However, the low,
4-1
P78 STAGE 2 05/91
Figure 4-1
VEGETATION TRANSECT LOCATIONS
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
Table 4-1. Flora Observed on Plant 78; Frequencies and Floristic Composition.
P78-914/P78T4-1.1
02/14/92
SPECIES OR COVER TYPE
PLOT NUMBER
1 23456789 10 TOTAL/500
LITTER
BARE GROUND / ROCK
27
5
19 21
9 9
34
6
19 26
10 10
17
12
20
13
27
16
28
10
238
100
Grasses and Shrubs
Agropyron cristatum 5 1 9 8 8 1114 4 7 1 68
Artemesia tridentata 0 000200401 7
Chrysothamnus viscidiflorus 0 000210000 3
Unknown woody flowering perennial 0 100 100000 2
Forbs and Mosses
Collinsia parviflora
Ranunculus testiculatus
Triglochin maritima
Cymopteris spp.
Bryophyta
12
0
0
0
1
20
0
0
0
0
0
0
0
1
10
0
0
0
0
2
0
8
0
0
0
0
0
0
0
2
0
1
0
0
6
0
0
9
0
0
0
0
0
0
0
10
0
0
0
0
42
9
9
1
21
Other plants observed on or near Plant 78: Juniperus sp., Ornamentals, Marsh/wetland vegetation near Bear River NWR.
P78-921/P784A^
02/14/92
monotypic vegetation on the plant limits the probable resident species to scavengers such as gulls, ravens, and
crows. Notable exceptions to the rule may be cliff swallows and bank swallows, which nest in the walls of the
canyon surrounding Blue Creek. Table 4-2 lists the birds observed on Plant 78 in April 1989, those observed near
the plant or in the refuges to the south of the plant, and the species expected or reported in the past to have
frequented the region.
Two endangered species, the bald eagle and the peregrine falcon, have been reported near Plant 78. Bald eagles
are known to winter in the Promontory peninsula, where they utilize the Great Salt Lake and associated riparian
habitats. Peregrine falcons have not been observed on or near Plant 78, but occurrence is possible due to the
mountain and cliff nesting sites available in the region. Other birds of prey seen on, or near, Plant 78 include
golden eagles, Swainson's hawk, prairie falcon, and northern harriers.
4.1.1.2.2 Mammals
The same factors that limit the diversity of resident birds on Plant 78 restrict the numbers and variety of mammals
on base. Four nights of small mammal trapping yielded only two species of small mammal, the deer mouse and
the brush mouse (Table 4-3). Other species observed on, or near, the plant include mule deer, coyote, badger,
skunk, and bobcat. A list of expected species for this area is included in Table 4-3.
4.1.2 DISCUSSION OF NON SITE-SPECIFIC HYDROGEOLOGY RESULTS
The groundwater flow system at Plant 78 represents a complex relationship between hydrogeological depositions!
features and the man-made influence of surface water discharges from the plant facilities. Data from monitoring
wells completed at Plant 78 indicate perched water-bearing zones at various elevations. The perched nature of these
zones are dependent on the interrelationship of low permeabiUty clays and silts to the more permeable gravel zones.
Stream channels, distributary channels, and low-energy flood-plain silts and clays all affect the vertical and
horizontal movement and direction of groundwater flow. In general, the gravel and sandy silt zones act as conduits
for water movement and the clays and clay-silt zones act as confining layers.
ShaUow groundwater at Plant 78 may be influenced by facility input. The water input into the groundwater system
by Plant 78 may_be_responsible for the upper shallow groundwater zones monitored by wells P-3, (P-4
abandoned), P-5, P-6, and P-7. Water in all of these momtoring wells occurs at depths less than the reported
150-foot depth for the regional aquifer in Blue Creek Valley. A deeper shallow water zone is monitored by
wells P-1, P-2. P-8^juidP-9, which may be the regional aquifer. This deeper shallow water zone may also be
influenced by plant facilities.
In 1989, Plant 78 industrial wastewater surface discharges along the NDD and E-512 ditch were connected to a
newly constructed wastewater treatment plant located near the intersection of R Avenue and 200 Street. The
plumbing of these surface water discharges may have resulted in the decreasing water level observed in monitoring
4-4
P7M14/P78T4-2.1
02/14/92
Table 4-2. Bird species observed on or near Plant 78.
Species Common Name
Larus californicus
Larus argentatus
Corvus brachyrhynchos
Corvus corax
Pica pica
Sturnella neglecta
Mimus polyglottos
Agelaius phoeniceus
Charadrius vociferus
Recurvirostra americana
Himantopus mexicanus
Catoptrophorus semipalmatus
Actitis macularia
Limosa fedoa
Ardea herodias
Egretta thula
Pelecanus ervthrorhvnchos
Falco mexicanus
Hirundo pvrrhonota
Riparia riparia
Buteo swainsoni
Circus cvaneus
Aquila chrvsaetos
Haliaeetus leucocephalus
Anas platyrhvnchos
Anas cvanoptera
Anas discors
Anas crecca
Anas acuta
Anas americana
Anas strepera
Anas clvpeata
Avthva americana
Avthva affinis
Aythva valisineria
Fulica americana
Bucephala clangula
Oxyura iamaicensis
Branta canadensis
Cygnus coumbianus
Phasianus colchicus
California gull *
Herring gull *
American crow *
Common raven *
Black-billed magpie +
Western meadowlark *
Northern mockingbird +
Red-winged blackbird +
Killdeer *
American avocet +
Black-necked stilt +
Willet +
Spotted sandpiper +
Marbled godwit +
Great blue heron +
Snowy egret +
American white pelican +
Prairie falcon *
Cliff swallow *
Bank swallow #
Swainson's hawk *
Northern harrier +
Golden eagle +
Bald eagle #
Mallard *
Cinnamon teal +
Blue-winged teal #
Green-winged teal #
Northern pintail #
American wigeon #
Gadwall #
Northern shoveler #
Redhead #
Lesser scaup #
Canvasback +
American coot +
Common goldeneye #
Ruddy duck #
Canada goose +
Tundra swan +
Ring-necked pheasant +
* - Observed on Plant 78.
+ - Observed within vicinity of Plant 78 (including nearby Refuges).
# - Reported in Plant 78 Vicinity.
4-5
F78-914/P7Srr4-3.1
02/14/92
Table 4-3. Mammals observed or expected near Plant 78.
Species Common Name
Perognathus parvus
Microdipodops megacephalus
Dipodomvs ordi
Reithrodontomys megalotis
Peromyscus crinitus
Peromvscus maniculatus
Peromyscus bovlei
Neotoma lepida
Ondatra zibethicus
Onvchomys leucogaster
Microtus pennsvlvanicus
Microtus longicaudus
Langurus curtatus
Eutamias minimus
Marmota flaviventris
Ammospermophilus leucurus
Sorex cinereus
Sorex merriami
Sorex vagrans
Sorex palustris
Swilagus idahoensis
Swilagus nuttallii
Lepus townsendii
Lepus califorinicus
Myotis lucifugus
Myotis evotis
Mvotis thvsanodes
Myotis volans
Mvotis subulatus
Lasionvcteris noctivagans
Eptesicus fucus
Lasiurus cinereus
Euderma maculatum
Corvnorhinus townsendii
Odocoileus hemionus
Antilocapra americana
Great Basin Pocket Mouse
Dark Kangaroo Mouse
Ord's Kangaroo Rat
Western Harvest Mouse
Canyon Mouse
Deer Mouse **
Brush Mouse **
Desert Wood Rat
Muskrat
Northern Grasshopper Mouse
Meadow Vole
Longtail Vole
Sagebrush Vole
Least chipmunk
Yellow-bellied Marmot
White-tailed Antelope Squirrel
Masked Shrew
Merriam's Shrew
Vagrant Shrew
Northern Water Shrew
Pygmy rabbit
NuttaU's Cottontail
White-tailed Jackrabbit
Black-tailed Jackrabbit
Little Brown Myotis
Long-eared Myotis
Fringed Myotis
Long-legged Myotis
Small-footed Myotis
Silver Haired Bat
Big Brown Bat
Hoary Bat
Spotted Bat
Townsend's Big-eared Bat
Mule Deer **
Pronghorn
Cards latrans
Taxidea taxus
Mustela frenata
Mustela ermina
Mephitus mephitus
Spigole gracilis
Procvon lotor
Fehs rufus
Coyote **
Badger **
Long-tailed Weasel
Ermine
Striped Skunk **
Western Spotted Skunk
Raccoon
Bobcat **
** - Observed on Plant 78.
4-6
P7M21/P784A.7
02/14/92
well P-3 (located along the NDD), monitoring well P-5 (E-512), momtoring well P-8 (E-519), and monitoring
well P-9 (E-515) during Stage 2 investigations. Precipitation in Utah was below average for 1988 and may also
have resulted in the decreasing water level observed in these momtoring wells. Plant 78 wastewater is treated to
acceptable discharge standards and released to Blue Creek under State of Utah Authorization to Discharge Pennit
No. UT0024805.
4.1.2.1 Upper Shallow Groundwater Zone
The upper shallow groundwater zone at Plant 78 is unconfined, heterogeneous, and transversely isotropic. This
zone is defined by monitoring wells P-3 and P-4 (abandoned) from the NDD, momtoring well P-5 from E-512, and
monitoring wells P-6 and P-7 from M-585. To facilitate a better understanding of the hydrogeology at this site,
a water elevation map has been constructed (Figures 4-2a and 4-2b). Figure 4-2a shows groundwater elevation
contours based on 1989 groundwater measurements. Figure 4-2b shows groundwater contours based on 1991
groundwater measurements.
Figure 4-2b was constructed with groundwater elevations measured by Thiokol in November 1991 for monitoring
wells P-3 and P-5. Both of these monitoring wells indicate substantial decreases in water elevation over 1989
measurements. Monitoring well P-3 shows a decrease of 15.60 feet. Momtoring well P-5 shows a decrease of
10.17 feet. As discussed in Section 4.1.2, the upper shallow groundwater zone at Plant 78 shows a possible
influence between facility wastewater disposal and possible groundwater mounding. Since construction of the
Plant 78 wastewater treatment facility in 1989, wastewater previously disposed into surface drainage ditches and
subsurface dry wells is now collected, treated, and released (under state permit) to Blue Creek. Groundwater
elevations measured in 1991 indicate that the possible groundwater mound at the facility is decreasing. Water level
measurements are listed on Table 4-4.
Upper shallow groundwater flow at Plant 78 is to the west-southwest at M-585 with an estimated hydraulic gradient
between monitoring wells P-6 and P-7 of approximately 0.026 foot/foot. Upper shallow groundwater at the NDD
and E-512 is also believed to flow towards the west-southwest. The estimated hydraulic gradient for the NDD and
E-512 area is from approximately 0.00525 foot/foot at monitoring well P-5 to approximately 0.018 foot/foot at
monitoring well P-3. This variance in hydraulic gradient across the plant is indicative of the heterogeneous nature
of the upper shallow groundwater zone at Plant 78.
Figure 4-2a was constructed with an unstabilized water level recorded at abandoned momtoring well P-4. This was
done to provide as complete a coverage of the NDD site as the data would allow. The water level contours indicate
that groundwater flow is higher along the NDD than observed at E-512 reflecting the higher hydraulic gradient
observed at monitoring well P-3.
4-7
P78 STACE 2 05/91 PFIG4-2
0100 300 500 1000 («tt
LEGEND
A*I° GROUNDWATER CONTOUR
INFERRED WHERE DASHED
Figure 4-2a
UPPER SHALLOW GROUNDWATER
ZONE, WATER TABLE MAP, 1989
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-8
P78 STAGE 2 05/91 PHG4-2P
0100 300 500 1000 fail
LEGEND
A*10 GROUNDWATER CONTOUR INFERRED WHERE DASHED
Figure 4-2b
UPPER SHALLOW GROUNDWATER
ZONE, WATER TABLE MAP, 1991
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-9
P78-914/P7ST4-4.1
02/14/92
Table 4-4. Groundwater measurements, Stage 1 and Stage 2, Plant 78.
Groundwater Stage 1 Measurements Stage 2 Measurements Feet Increase (+)
Monitoring (Feet MSL) (Feet MSL) of Decrease (-)
Well (1988) (1989) (1991) Over Time
P-1 4,311.32 4,334.87 4,346.1s1 +34.83
P-2 4,411.70 4,412.00 ~ +0.30
P-3 4,422.60 4,411.60 4.407.001 -15.6
P-4* - 4,384.40**
P-5 - 4,380.17 4,370.00' -10.17
P-6 - 4,467.26
P-7 - 4,456.97
P-8 - 4,358.70 4,354.47* -4.23
P-9 - 4,352.20 4,347.001 -5.20
(-) - No Data
MSL - Mean Sea Level
1 - Measurements supplied by Thiokol
* - WeU P-4 Abandoned
** - Unstabilized water level measurement
4-10
P78-921/P784A.11
02/17/92
The upper shallow groundwater elevations at M-585 are not contoured with the elevations at E-512 or the NDD.
The distance between measurement sites precludes making a connection between these zones. In addition, because
the upper shallow groundwater zone at Plant 78 may be due to facility input, these perched zones are probably not
connected.
4.1.2.2 Deeper Shallow Groundwater Zone
The deeper shallow groundwater zone at Plant 78 is unconfined (with the possible exception of monitoring well P-2),
heterogeneous, and transversely isotropic. Monitoring wells P-1, P-2, P-8, and P-9 are all completed in this deeper
groundwater zone, which may be the regional Blue Creek Valley aquifer. Monitoring wells P-1, P-8, and P-9
(NDD, E-519, and E-515 sites) illustrate water depths that are increasingly shallower from monitoring well P-1
(upgradient) to monitoring well P-8 (downgradient). The decreasing depth to water from monitoring well P-1 to
momtoring well P-8, which is counter to the regional trend, is probably due to facility wastewater disposal.
Monitoring well P^2, (M-585 site) shows a water level 76 feet higher than the level measured at monitoring well P-1.
This situation is caused by recharge to the groundwater zone at monitoring well P-2 from wastewater discharge at
M-585.) Monitoring wells P-1, P-2, P-8, and P-9 are included on two deeper shallow groundwater water table maps
shown in Figures 4-3a and 4-3b. Figure 4-3a shows groundwater elevation contours based on 1989 groundwater
measurements. Figure 4-3b shows groundwater elevation contours based on 1991 groundwater measurements.
The deeper groundwater flow at Plant 78 observed in the 1989 measurements is to the east of monitoring
wells P-8, P-9, and P-1, reflective of the mounding suspected to be caused by wastewater disposal. The flow
direction at momtoring well P-2 is unknown; however, based upon water elevations, the suggested direction of flow
would be toward the northeast. Both flow directions observed in the 1989 measurements in the deeper shallow
water zone appear to be localized reversals to the predominately west-southwest flow direction observed for the
, . • • • 1 " ' *
upper^ghallgw water zone. The localized reversal may be due to the mounding caused by wastewater disposal.
Figure 4-3b shows groundwater elevation contours based on 1991 groundwater measurements. The most striking
difference between the 1989 and 1991 measurements is the large decrease in the suspected groundwater mound
associated with the Plant 78 facilities. Monitoring well P-1 shows an increase of 34.83 feet since installation in
1988. Monitoring well P-9 shows a decrease of 5.20 feet and monitoring well P-8 shows a decrease of 4.23 feet
since installation in 1989 (Table 4-4).
The 1989 measurements (Figure 4-3a) indicate a localized eastward reversal in the predominately western regional
groundwater flow direction. The 1991 measurements (Figure 4-3b) indicate that the magnitude of this reversal has
greatly diminished as indicated by the overall decrease in the hydraulic gradient between wells P-9 and P-1 from
0.0125 foot/foot (1989) to 0.0044 foot/foot (1991).
c
4-11
_P7g STAGE 2 05/91 PriG4-3
1
GROUNDWATER FLOW
DIRECTION
0 100 300 500 1000 f«l — 4360 — GROUNDWATER CONTOUR
INFERRED WHERE DASHED
Figure 4-3a
DEEPER SHALLOW GROUNDWATER
ZONE, WATER TABLE MAP, 1989
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-12
P78 STAGE 2 05/91 PHG4-3B
WELL P
4346.15 ft MSLVI
0 100 500 500 10O0 fMt
LEGEND
4350 — GROUNDWATER CONTOUR
INFERRED WHERE DASHED
Figure 4-3b
DEEPER SHALLOW GROUNDWATER
ZONE, WATER TABLE MAP, 1991
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-13
P78-921/P784A.14
02/17/92
4.1.3 DISCUSSION OF RESULTS FOR THE NORTH DRAINAGE DITCH AND E-519 SITES
The geologic and hydrogeologic investigation at the NDD consists of work conducted under both Stage 1 and
Stage 2. For the purpose of this discussion, the NDD includes work accomplished at Building E-519. Three
25 foot deep borings (25A, 25B, and 25C) and momtoring well P-3 (boring 200C drilled to 90 feet) were completed
under Stage 1. The was no investigation at Building E-519 under Stage 1. Boring NDD-B1 was drilled to
100.2 feet from ground surface and groundwater monitoring well P-4 was installed, and later abandoned under
Stage 2. In addition, boring E-519B1 was drilled to 180.5 feet from ground surface, groundwater monitoring
well P-8 was installed under Stage 2 investigations. A soil gas survey encompassing the area surrounding Building
E-519 and south was also conducted under Stage 2. A determination of hydraulic conductivity was made on
monitoring wells P-3 and P-8 by slug/bail aquifer testing.
4.1.3.1 North Drainage Ditch and E-519 Geology
All borings encountered heterogeneous lake clays and gravel sediments of the Pleistocene Lake Bonneville Group.
These consists of grey to light yellowish brown (10 YR 6/3 to 10 YR 6/2), fme-grained, silty to sandy and gravely
clays, clayey and gravelly silts, and silty to sandy gravels that are slightly moist to moist. Clays are soft, nonplastic
to plastic, loose and massive. Silts are plastic to nonplastic, and moderately to poorly sorted. Fractures and root
casts are present as is occasional iron oxide staining. Gravels consist of subrounded to slightly angular clasts of
grey limestone and light brown sandstone. The gravels are matrix- to clast-supported conglomerates with a channel
to sheet-like bed geometry.
To further study the lithologic relationships at the NDD and E-519, a hydrogeologic cross-section was constructed
from boring 200B (momtoring well P-1) to boring NDD-B1 (momtoring well P-4) (Figures 4-4 and 4-5). This
cross-section also includes boring E-512B1 (monitoring well P-5) from the E-512 site. The highly variable nature
of the lake clays and gravel sediments makes lateral correlation of individual beds difficult. By concentrating on
the gravel lithology, however, a correlation between gravel units observed in these borings can be made. Total
gravel thickness decreases dramatically westward from approximately 200 feet in boring 200B (momtoring well P-1)
to approximately 43 feet in boring 200C (monitoring well P-3). At boring NDD-B1, the western most deep boring,
the gravels are absent. The dramatic thinning of the gravel zone is directly attributable to the environment of
deposition, which was a alluvial fan/delta within n larustrine setting. Deltaic alluvial fan deposition is characterized
by a rapid fining of sediment size in the down slope direction. Thinning of gravels from east to west and absence
of gravels along the northwest boundary of Plant 78 suggest an easterly or southeasterly source for the sediments.
A^westerly oriented distributary channel flowing into Lake Bonneville in this area is suggested as a likely
explanation for the origin of the sedimentary sequence observed at the NDD.
4-14
P78 STAGE 2 05/91
-643
• WELL P-5 -GROUNDWATER MONITORING WELL
A -DEEP STRATIGRAPHIC BORING
-LINE OF CROSS-SECTION
N<T :>s
Figure 4—4
LOCATION OF HYDROGEOLOGIC
CROSS-SECTIONS D-D' & E-E'
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78;
4-15
(E-519B1)
P-6<
Moo')
(E-515B2)
P-9 «».«'
t-ao't
D'
SOUTHEAST
(20OB)
EXPLANATION
CLAY Consists of silty and sandy clays. Uses classification CL.
SILT Consists of day rich silts and
sands. Uses classification ML.
SAND Consists of day rich sands, sHty sands. Uses classifications SCSUandSM.
GRAVEL Consists of pooriy sorted day rich
gravels. Uses classifications
GC, GM, and GP.
CL' Ooy ST SMt
SO Sand GR Gravel
RELATIVE
GRAIN SIZE:
7Z.4T Water Level
(445&3MSU Measurement
2-1-89 Date of Measurement
(E-512B1) Boring Number
P-5 44*t3£r Wed number and ground surface elevation.
(•2txr) Feet In frontof the line of section.
(-50") Feet behind the line of section
• 40%
20'-1 I
—I 1
0* 206" 400'
Figure 4-5
HYDROGEOLOGIC CROSS-SECTION D-D'
NORTH DRAINAGE DITCH E-512, E-519,
AND E-515
SOURCE: ESE.1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-921/P784A.17
02/14/92
4.1.3.2 North Drainage Ditch and E-519 Hydrogeology
Groundwater monitoring well P-3 was installed during Stage 1 and was screened from 62 to 82 feet from ground
surface within sand and clay rich gravels. Groundwater was measured at 66.7 feet (4,422.6 feet above MSL) at
the time of completion (March 1988). A static water level of 77.7 feet (4,411.60 feet above MSL) was measured
at the time of sampling during Stage 2 (January 1989). This is a drop of static water level of 11 feet in just under
one year. A third static water level was measured at 84.35 feet (4,407.00 feet above MSL) in November 1991.
This is drop of static water level of 4.6 feet since January 1989 and a 15.6 feet total drop in water level at
monitoring well P-3 since March 1988 (Table 4-4). Since the installation of monitoring well P-3, Thiokol has
connected building drainages along the NDD into a wastewater sewage system. This has probably decreased the
shallow groundwater recharge and may be responsible for the subsequent decrease in observed groundwater level.
Boring NDD-B1 was drilled during Stage 2 to a total depth of 105 feet from ground surface. This boring was
converted into groundwater monitoring well P-4. Screen length of 30 feet was installed from 68 to 100 feet in a
silty, sandy clay. Groundwater level was measured at 78.17 feet (4,384.40 feet above MSL) at the time of
completion (December 1988). Monitoring well P-4, however, subsequently went dry. A lack of well developed
water bearing and confining layer zones led to the inability of the site hydrogeologist to distinguish the correct
placement of the screen. Drilling to a total depth of 105 feet to accommodate the 30 foot well screen length
apparently breached a confining zone and allowed the perched water to percolate out of the screened zone.
Monitoring well P-4 was abandoned as described in Section 3.5.7.
Boring E-519B1 (Building E-519) was drilled during Stage 2 to a total depth of 180.40 feet. This boring was
converted into groundwater momtoring well P-8. A total screen length of 25 feet was installed from 155 to 180 feet
in a silty and sandy clay. Groundwater was measured at 159.1 feet (4,358.70 feet above MSL) at the time of
completion (July 1989). A static groundwater level of 163.33 feet (4,354.46 feet above MSL) was measured in
November 1991. The static water level at well P-8 has dropped 4.23 feet since July 1989 (Table 4-4). As discussed
in Section 4.1.2.2, the possible groundwater mound observed in the deeper shallow groundwater zone at Plant 78
is decreasing. The 4.23 feet drop in static water level observed at momtoring well P-8 is probably related to this
decrease.
4.1.3.2.1 Aquifer Testing
Determination of hydraulic conductivity (K) of an aquifer is essential for determining groundwater flow rates and
contaminant travel times. Values of K were determined by slug/bail tests for monitoring wells P-3 and P-8
according to the procedures and limitations described in Section 3.5.6. Subsequently, gradient and groundwater
velocities were calculated from K using equations presented in Section 3.5.6.2.
Values of V ranged from 1.70 to 1.63 feet per day (fpd) for monitoring well P-3 which yielded the highest velocity
values of all the Plant 78 monitoring wells. Converting the fpd to feet per year (fpy) (fpd x 365 days per year)
4-17
P7&921/P784A.18
02/14/92
indicates that groundwater at monitoring well P-3 could travel from 594 to 620 fpy. Monitoring well P-8 had a V
value of 0.86 fpd. Converting fpd to fpy indicates that groundwater at monitoring well P-8 could travel 313 fpy.
4.1.3.3 Analytical Results
Surface water, surface sediment, shallow and deep boring, and groundwater samples were collected along the NDD
and E-519 during Stage 2. The following is a listing of analytical data by sample type for Stage 2 and a discussion
of the Stage 1 and Stage 2 results.
4.1.3.3.1 Surface Water Samples
Two surface water samples were collected along the NDD. Figure 4-6 displays locations of these samples and
Table 4-5 lists the analytical detections for surface water samples collected at the NDD.
4.1.3.3.2 Surface Sediment Samples
Two surface sediment samples were collected along the NDD. Figure 4-6 displays the locations of these samples
and Table 4-6 lists the analytical detections for surface sediment samples collected at the NDD.
4.1.3.3.3 Shallow Soil Boring Samples
Seven shallow soil borings were installed and sampled along the NDD. Figure 4-7 displays locations for these
samples and Table 4-7 lists the analytical detections for the shallow soil samples collected at the NDD.
4.1.3.3.4 Deep Stratigraphic Boring Samples
Two deep stratigraphic borings were drilled at NDD and E-519. NDD-B1 was drilled along the ditch near the west
boundary of Plant 78. E-519B1 was drilled in the parking lot of Building E-519. Figure 4-8 displays these deep
boring locations and Table 4-8 lists the analytical detections for soil samples collected from these borings.
4.1.3.3.5 Groundwater Samples
Three groundwater samples were collected at the NDD and E-519, one from monitoring well P-3 and two from
monitoring well P-8 (Building E-519). Figure 4-9 displays the locations of these momtoring wells and Table 4-5
lists analytical detections for the groundwater samples collected.
4.1.3.3.6 Soil Gas Samples
Eighty PETREX™ soil gas collectors were installed at the NDD and Building E-519. Figure 4-10 displays the
locations of these collectors.
4-18
P78 STAGE 2 05/91 PFIG 4-5
NDD-SW1
Compound
NDD-SW2
ug/L METHOD BLANK
Compound
1,2-DCA
METHOD ug/L BLANK
4.29 ND
Pet. Hydro.
1,2-DCA
1,1,1-TCA
Chloromethane
1,1-DCA
1.1- DCE
TCE
Chloroform
1.2- DCP
257
9.93
7.53
2.81
1.16
0.688
0.626
0.262
0.45
ND
NDD-SS2
METHOD
Compound | mg/kg| BLANK
• LEGEND 0 100 200 300 400 500 1000 feet
O—NDD-SS2
NDD-SW2
-SURFACE WATER
SEDIMENT SAMPLE
W
Figure 4-6
STAGE 2 SURFACE WATER AND SEDIMENT SAMPLE
RESULTS, NORTH DRAINAGE DITCH
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
Table 4-5. Stage 2 Analytical Results for Surface and Ground Water Samples, North Drainage Ditch and E-519.
P78-914/P7ST4-5.1
02/14/92
NDD-SW1 NDD-SW2 WELL P3 P3-DUP WELL P-8 WELL P-8 DUP
Chemical Parameter 12/1/88 Method 12/1/88 Method 1/31/89 1/31/89 Method 7/26/89 7/26/89 Method
ftg/L (ppb) P78-W1 Blank P78-W2 Blank P78-W3 P78-W*28 Blank P782-W1 P78-W2 Blank
Petrol. Hydrocarbons — — 257 - - — — — 0.25
Benzene — — — — — — — _
Toluene — — ______
Ethylbenzene — — — _ Q.005
Total Xylenes — -
Bromobenzene — — — — _
Bromodichloromethane — — — — _ 0.046
Bromoform — - - _ 0.018
Bromomethane - - — _ Q.418
Carbon Tetrachloride — — — — _ 0.068
Chlorobenzene - - 1.51 1.42 0.012
Chloroethane — — _ _ Q.362
2-Chloroethylvinyl Ether - - — — _ 0.199
Chloroform - - 0.262 - 0.765 0.723 - 4.62 433 0.07
1-Chlorohexane — — — — — _
Chloromethane — — 2.81 _ 0.428
Dibromochloromethane — — _ _ _ _ _ 0.156
Dibromomethane — — ._ _ Q.06
Dichlorobenzene - - - — — - - 3.13 3.2
1.1- Dichloroethane - - 1.16 - 2.54 2.45 - >18.2 >18.2 0.148
1.2- Dichloroethane 4.29 - 9.93 - - 1.03 - 20.2 15.1
t-l,2-Dichloroethene — — — — _ 0.129
1.1- Dichloroethene - - - - _ _ _ 1080 990 0.082
1.2- Dichloropropane — — 0.450 _ 0.027
Cis-l,3-Dichloropropene — — ______ _ 0.156
t-l,3-Dichloropropene - - - _ 0.038
Dichlorodifluoromethane — — _ _____ _ 0.334
Dissolved Solids 507 - 353 - 3880 4450 -
Methylene Chloride - - _____ 3.32 2.38 0.095
1,1,1,2-Tetrachloroethane - - - - - _ _ _ _ 0.OI8
1,1,2,2-Tetrachloroethene - _ .... _ _ _ _ _ Q.192
Tetrachloroethene - - - - 0.505 0.358 - 8.87 6.37 0.192
1.1.1- Trichloroethane - - 7.53 - 465 464 _ 2610 2380 0.056
1.1.2-Trichloroethane - _ _-___.. _ 0.156
Trichloroethene _ _ 0.626 - 1410 1020 _ _ 26,900 — 25,300 0.054
Trichlorofluoromethane — _ -- _ —' — - _ 0.467
Trichloropropane — — — — — _ _ _ _ 0.13
Vinyl Chloride - - ______ _ Q.334
— = Not detected above instrument detection level.
P78-914/P78T4-6.1
02/14/92
Table 4-6. Stage 2 Analytical Results for Surface Sediment Samples, North Drainage Ditch.
NDD-SS1 NDD-SS2
Chemical Parameter 12/1/88 Method 12/1/88 Method
mg/kg (ppm) P78-S*8 Blank P78-S*9 Blank
Petrol. Hydrocarbons
Benzene
Toluene
Ethylbenzene
Total Xylenes
Bromobenzene
Bromodichloromethane
Bromoform
Carbon Tetrachloride
Chlorobenzene
Chloroethane
2-Chloroethylvinyl Ether
Chloroform
1-Chlorohexane
Dibromochloromethane
Dibromomethane
Dichlorobenzene
1,1-Dichloroethane
1.1- Dichloroethene
1.2- Dichloroethane
t-l,2-Dichloroethene
1,2-Dichloropropane
Cis-1,3-Dichloropropene
t-l,3-Dichloropropene
Dichlorodifluoromethane
Methyl Bromide
Methyl Chloride
Methylene Chloride
1,1,1,2-Tetrachloroethane
1,1,2,2-Tetrachloroethane
Tetrachloroethylene
1.1.1- Trichloroethane
1.1.2- Trichloroethane
Trichloroethylene
Trichlorofluoromethane
Trichloropropane
Vinyl Chloride
59.3 41.7
= Not detected above instrument detection level.
4-21
P78 STAGE 2 05/91 PEIG 4-6
METHOD METHOD
Compound mg/kg| BLANK Compound I mg/kgl BLANK
Methlene Chloride
NDD-SB7-
0.911 Methlene Chloride
Pet. Hydro.
rNDD—SBI
IM ST.
0.887
45.7
ND
NDD-SB2 NDD-SB3 NDD-SB4 rNDD-SB5
300 ST,
NDD-517
P A NDD-SB6
E-516
E-517
POND
VAPORATIO(4
AND
SANITARY
SEWAGE
TREATMENT
E-512 M-508
LEGEND
A SHALLOW SOIL BORING LOCATION
0 100 200 300 400 500 1000 feet
Figure 4-7
STAGE 2 SHALLOW SOIL BORING SAMPLE
RESULTS, NORTH DRAINAGE DITCH
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-914/P7ST4-7.1
02/14/92
Table 4-7. Stage 2 Analytical Results for Shallow Boring Soil Samples, North Drainage Ditch.
NDD-SB1 NDD-SB1 NDD-SB2 NDD-SB2 NDD-SB3 NDD-SB3 NDD-SB4 NDD-SB4 NDD-SB5 NDD-SB5 NDD-SB6 NDD-SB6 NDD-SB7 NDD-SB7
12/9/88 12/9/88 12/9/88 12/9/88 12/10/88 12/10/88 12/10/88 12/10/88 12/12/88 12/12/88 12/10/88 12/10/88 12/9/88 12/9/88
Chemical Parameter 4' 8' 2.3' 8' 4' 8* 4' 8' 4' 8' 4' 8' 4' 8' Method
mg/kg (ppm) P78-S'10 P78-S'll P78-S'12 P78-S*13 P78-S'14 P78-S*15 P78-S'16 P78-S'17 P78-S'18 P78-S*19 P78-S'20 P78-S'21 P78-S*22 P78-S'23 Blank
Petrol. Hydrocarbons — — 45.7
Benzene — — —
Toluene — — —
Ethylbenzene - — —
Total Xylenes — —
Bromobenzene — — —
Bromodichloromethane —
Bromoform — —
Carbon Tetrachloride — —
Chlorobenzene — — —
Chloroethane —
2-Chloroethylvinylether
Chloroform
1-Chlorohexane
Dibromochloromethane
Dibromomethane
Dichlorobenzene
1,1-Dichloroethane
1.1- Dichloroethene
1.2- Dichloroethane
t-l,2-Dichloroethene
1,2-Dichloropropane
Cis-l,3-Dichloropropene
t-1,3-Dichloropropene
Dichlorodifluoromethane
Methyl Bromide
Methyl Chloride -
Methylene Chloride - 0.911 0.887
1,1,1,2-Tetrachloroethane - - -
1,1,2,2-Tetrachloroethane
Tetrachloroethylene
1.1.1- Trichloroethane
1.1.2- Trichloroethane
Trichloroethylene
Trichlorofluoromethane
Trichloropropane
Vinyl Chloride
= Not detected above instrument detection level
P78 STAGE 2 05/91 PFIG 4-7
SAMPLE DEPTH | Compound
Compound
LEGEND
A BORE NDD-B1 -DEEP STRATIGRAPHIC BORING
Methylene Chloride
ND
ND
ND
Diethylphthalate
Trichloroethylene
Di-N-Butylphthalate
Butyl Benzylphthalate
Figure 4-8
STAGE 2 DEEP STRATIGRAPHIC BORING SAMPLE
LOCATIONS AND RESULTS, NORTH DRAINAGE DITCH
AND BUILDING E-519
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
Table 4-8. Stage 2 Analytical Results for Deep Boring Soil Samples, North Drainage Ditch and Building E-519.
P78-914/P78T4-8.1
02/14/92
Chemical parameter
mg/kg (ppm)
NDD-B1
12/1/88
P78-SM
NDD-B1
12/1/88
P78-S2
51'
NDD-B1
12/2/88
P78-S*3
76'
NDD-B1
12/5/88
P78-SM2
101'
Method
Blank
E-519B1
6/21/89
P782-S*6
36'
E-519B1
6/21/89
P782-S*7
97
E-519B1
6/2/89
P782-S*8
50'
E-S19B1
7/6/89
P782-S*9
137'
E-519B1
7/6/89
P782-S*10
171'
E-519B1
7/6/89
P782-S,ll
171'
Method
Blank 6'
Petroleum Hydrocarbons
Benzene
Toluene
Ethylbenzene
Total Xylenes
Bromobenzene
Bromodichloromethane
Bromoform
Carbon Tetrachloride
Chlorobenzene
Chloroethane
2-Chloroethylvinyl ether
Chloroform
1-Chlorohexane
Dibromochloromethane
1,1-Dichloroethane ______
1.1- Dichloroethene - -- - - -
1.2-Dichloroethane - - _____ -
t-l,2-Dichloroethene ______ _____
1,2-Dichloropropane ______ _____
Cis-l,3-Dichloropropene ______ _
t-l,3-Dichloropropene ______ _____
Dichlorodifluoromethane ______ _ _ _ _
Methyl Bromide - — ______ _ _____
Methyl Chloride ______ _____
Methylene Chloride - _ _ _ _ 4.76 - - - - -
1,1,1,2-Tetrachloroethane ______ _ _ _ _ _
1,1,2,2-Tetrachloroethane ______ _ _ _ _ _
Tetrachloroethylene ______ ______
1.1.1- Trichloroethane ______ _____
1.1.2-Trichloroethane ______ _____
Trichloroethylene ______ .... .. 0.387
Trichlorofluoromethane ______ _____
Trichloropropane — — _____ _____
Vinyl Chloride ______ _____
Bis (2EH) Phthalate - _ _ .. _ .. .. 0.14 0.13 0.18 0.24
Butyl Benzylphthalate ______ .._.._ 0.O8
Dibromomethane
Dichlorobenzene
0.05
0.04 0.04
— = Not detected above instrument detection level
P78 STAGAE 2 05/91 PFIG 4-8
DUPLICATE SAMPLE DUPLICATE SAMPLE
Compound
2-Chloroethylvinylether
1.1- DCA
1.2- DCA
PCE
1,1,1-TCA
TCE
ug/L
0.723
2.45
1.03
0.358
464
1020
METHOD
BLANK Compound
ND
ND
ND
ND
ND
ND
PCE
Cholroform
1,1-DCA
1,1,1-TCA
TCE
ug/L
0.505
0.765
2.54
465
1410
METHOD
BLANK Compound
ND
ND
ND
ND
ND
Chlorobenzene
Dichlorobenzene
Methlyene Chloride
Chloroform
PCE
1,2-DCA
1,1-DCA
1,1-DCE
1,1,1-TCA
TCE
ug/L
1.51
3.13
3.32
4.62
8.87
20.2
>18.2
1080
2610
26900
METHOD
BLANK Compound
0.012
ND
0.095
0.07
0.192
ND
0.148
0.082
0.056
0.054
Chlorobenzene
Dichlorobenzene
Methlyene Chloride
Chloroform
PCE
1,2-DCA
1,1-DCA
1,1-DCE
1,1,1-TCA
TCE
"g/L
1.42
3.2
2.38
4.53
6.37
15.1
>18.2
990
2380
25300
LEGEND
WELL P-3 -GROUNDWATER MONITORING WELL
METHOD
BLANK
0.012
ND
0.095
0.07
0.192
ND
0.148
0.082
0.056
0.054
Figure 4—9
STAGE 2 GROUNDWATER SAMPLE RESULTS,
NORTH DRAINAGE DITCH AND BUILDING E-519
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
SOURCE: ESE, 1991.
P78 STAGE 2 03/91 PFIG4-9
Figure 4-10
LOCATION OF SOIL GAS SAMPLES, NDD, E-519, E-515,
AND, E-512
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-921/P784A_S
0-,/tt/92
4.1.3.4 Discussion of Analvtical Results for NDD
Inorganic constituents were determined for NDD during Stage 1. All inorganic constituents were found to be below
the NIPDWR and NSDWR recommended levels. Major and minor element chemistry was comparable to the onsite
water, which supplies the ditch. Metal concentrations in sediments and soils were found to be comparable to
background samples collected from boring 200B, and were within reported ranges of representative U.S.
concentrations. These parameters were not analyzed under Stage 2.
4.1.3.4.1 Significance of Findings
SOIL AND SURFACE SEDIMENT ANALYTICAL RESULTS
Stage 1 sampling demonstrated the presence of methylene chloride, trichloroethylene, and petroleum hydrocarbons
in NDD soil samples. Stage 2 analytical results are discussed in the following text under the specific compounds.
Methylene chloride
Methylene chloride was detected sporadically in Stage 1 soil samples collected from borings adjacent to
Buildings E-516 and E-517. One soil sample collected from shallow soil boring NDD-SB1 at 8 feet BGS contained
a low concentration of methylene chloride of 0.911 mg/kg. Methylene chloride was also detected at 0.887 mg/kg
in a sample collected at 2.3 feet BGS in shallow soil boring NDD-SB2. Both of these borings are downgradient
of the Stage 1 surface samples collected adjacent to Buildings E-516 and E-517. Methylene Chloride was also
detected at 4.76 mg/kg in a soil sample collected from boring E-519B1 at 36 feet BGS.
Trichloroethylene
Trichloroethylene was also detected sporadically in Stage 1 soil samples collected at the NDD. The results of the
Stage 2 sampling at NDD for trichloroethylene were all below the MCL except trichloroethylene (0.387 mg/kg),
which was detected in E-519B1 at 171 feet.
The presence of methylene chloride, methyl chloride, and trichloroethylene in NDD soils is not inconsistent with
site history. The lack of verification for trichloroethylene by Stage 2 sampling, except at 171 feet in E-519B1,
suggests that the trichloroethylene detected during Stage 1 and Stage 2 sampling may be due to either sampling or
analytical laboratory contamination, or the natural degradation processes (i.e., photolysis, biodegradation, etc.) may
have removed this compound.
Petroleum Hydrocarbons
The occurrence of petroleum hydrocarbons in soil and sediment in the NDD is consistent with site history.
Buildings E-516 and E-517 are used for vehicle niaintenance and nmcmne shop activities. The relatively high levels
of petroleum hydrocarbons detected by Stage 1 sampling in surface sediment samples from NDD-516, NDD-517,
and NDD-SS2, which are near these buildings, suggests contaminant contribution from either or both of these
potential sources. Levels of petroleum hydrocarbons detected in Stage 2 results however, are much lower than
4-28
P78*21/P784A_)
02/14/92
levels detected in Stage 1. Petroleum hydrocarbons were detected in samples NDD-SB2 and NDD-SS2 at 45.7 and
59.3 mg/kg, respectively. Review of the method blank for NDD-SS2 indicates that the method blank contained
41.7 mg/kg of petroleum hydrocarbons. Given the similarity between the actual sample concentration and the
method blank concentration the detection in NDD-SS2 is not reliable and could be due to laboratory contamination.
The conflict between Stage 1 and Stage 2 petroleum hydrocarbon results may be due to individual sample variability
between the two sampling periods: Stage 1 sampling may have detected a specific petroleum hydrocarbon release
event which has passed through the site, or the decrease in petroleum hydrocarbon concentration may be due to
natural degradation.
SURFACE WATER AND GROUNDWATER ANALYTICAL RESULTS
To evaluate the quality of the surface and groundwater at Plant 78, federal and State of Utah water quality standards
(e.g., maximum contaminant levels [MCLs]) are used to indicate the quality of the water relative to drinking water.
These drinking water standards are not directly applicable to the samples collected at Plant 78. The waters collected
at Plant 78 are unsuitable for use as a drinking water source either at the installation or within the immediate vicinity
due to naturally high dissolved solids content.
Surface Water
Surface water samples collected from NDD during Stage 1 and Stage 2 indicate the presence of halomethanes,
purgable halocarbons, and petroleum hydrocarbons.
Chloroform, bromoform, bromodichloromethane, dichloromethane, and petroleum hydrocarbons were observed at
low concentrations from NDD-B1, NDD-516, NDD-517 under Stage 1. Chloromethane, chloroform,
1,1-dichloroethane, 1,2-dicUoroethane, 1,2-dichloropropane, l,l,l-trichloroethane,and trichloroethylene were
detected at low concentrations under Stage 2.
Chloroform, bromoform, bromodichloromethane, and chloromethane were observed in a sample of the Plant 78
onsite approved water collected during Stage 1 (Table 4-9). At the time of both the Stage 1 and Stage 2 sampling,
the onsite water contributed to the flow of the NDD and the majority of the halomethanes detected at low
concentrations in water sampling at Plant 78 can be attributed to chlorination of the onsite water for drinking
puiposes. The presence of chloroform 1,1-dichloroethane, 1,2-dichloroethane, 1,1,1-trichloroethane, and
trichloroethylene and petroleum hydrocarbons are, however, consistent with site disposal history.
Stage 2 surface water sample NDD-SW2 verified the presence of petroleum hydrocarbons in the NDD near
Buildings E-516 and E-517. Petroleum hydrocarbons were detected in sample NDD-SW2 at 257 /tg/L. Petroleum
4-29
P78-914/P78T4-9.1
02/14/92
Table 4-9. Detectable consituents in Onsite Water, Plant 78.
Parameter Detected Concentrations
Bromodichloromethane (/tg/L) 0.55
Bromoform (/tg/L) 1.4
Chloroform (/tg/L) 0.18
Chloromethane (/tg/L) 0.97
Dibromochloromethane (/tg/L) 0.89
Methylene Chloride (/tg/L) 0.45
Zinc (/tg/L) 180
Residue, Dissolved (/tg/L) 520
Chloride (mg/L) 130
Fluoride (mg/L) 0.36
Sulfate (mg/L) 27
N03 as N (mg/L) 0.94
NH3 + NH4 as N (mg/L) 0.015
4-30
P78-921/P784A31
02/14/92
hydrocarbons were not detected in surface water sample NDD-SW1. Laboratory analysis contained no evidence
of method contamination.
Concentrations of bromodichloromethane, bromoform, and bromomethane in the onsite water (sampled during
Stage 1) are at concentrations exceeding either EPA 10"6 Human Health Risk Criteria (HHRC) or MCLs
(Table 4-10). These compounds were not detected under Stage 2. Of the components that have established criteria,
only chloroform and chloromethane were detected under Stage 2 at concentrations exceeding EPA 10"6 HHRC.
Purgable halocarbons were also detected at low concentrations in Stage 1 surface water samples. Surface water
sampling for Stage 2 at NDD-SW2 verified the presence of these low concentrations. NDD-SW1 collected at the
same location as NDD-B1 contained 1,2-dichloroethane at a concentration below the MCL and exceeding the 10"6
HHRC. The concentration of 1,2-dichloroethane in NDD-SW2 exceeds the MCL.
Chloroform, tetrachloroethylene, 1,1 -dichloroethane, 1,2-dichloroethane, 1,1,1-trichloroethane, and trichloroethylene
were observed in water quality analysis conducted on groundwater from momtoring well P-3. Petroleum
hydrocarbons, detected in surface water and sediment sampling of the NDD, were not detected in P-3 groundwater.
The concentrations for trichloroethylene and 1,1,1-trichloroethane are much higher in P-3 groundwater than
concentrations of these analytes in NDD surface water. Laboratory analysis contained no evidence of method
contamination. Concentrations of trichloroethylene, and 1,1,1-trichloroethane exceed MCLs. 1,2-Dichloroethane
exceeds EPA 10"* HHRC but does not exceed the MCL of 5 /tg/L. Chloroform exceeds the EPA 10* HHRC but
not the 100 /tg/L MCL for total trihalomethanes.
Chloroform, chlorobenzene, methylene chloride, tetrachloroethene, dichlorobenzene, 1,1-dichloroethene,
1,2-dichloroethane, 1,1-dichloroethane, 1,1,1-trichloroethane, and trichloroethylene were detected in groundwater
from monitoring well P-8. The concentrations of trichlorethylene, 1,1,1-trichloroethane, 1,1-dichloroethene, and
1,2-dichloroethane from monitoring well P-8 are elevated over all other surface and groundwater samples at
Plant 78. Concentrations of 1,1,1-trichloroethane, 1,2-dichloroethane, 1,1-dichloroethene, tetrachloroethene, and
trichloroethylene exceed MCLs. Concentrations of chloroform and methylene chloride exceed EPA 10"6 HHRC.
The method blank analysis for these compounds did contain trace concentrations of all the above compounds except
for dichlorobenzene and 1,2-dichloroethane. Trace concentrations of these compounds observed in the method blank
analysis are below any concentration which would compromise sample results.
Data collected by the Petrex™ soil gas method are displayed in the form of isopleth contour maps based upon the
ion count flux recorded for each compound or mixture of compounds identified at each sample location. Although
a relationship between high and low ion flux counts and high and low compound concentrations in either
Groundwater
4-31
P78-914/P78T4-10.1
02/14/92
Table 4-10. Relevant Water Quality Criteria for USAF Plant 78 Based on EPA 1986 and 1988 Criteria and
Current Standards (1991) (All units in jug/L).
Parameter
Freshwater Aquatic
Life Criteria
Acute / Chronic
Human Health
(@ 10"6 Risk)
Maximum
Contaminant
Levels
Bromodichloromethane
Bromoform
Bromomethane
Carbon tetrachloride
Chlorobenzene
Chloroethane
2-Chloroethanevinyl Ether
Chloroform
Chloromethane
Dibromochloromethane
1.2- Dichlorobenzene
1.3- Dichlorobenzene
1.4- Dichlorobenzene
Dichlorodifluoromethane
1.1- Dichloroethane
1.2- Dichloroethane
1.1- Dichloroethene
t-1,2-Dichloroethene
1.2- Dichloropropane
Cis- 1,3-Dichloropropene
t- 1,3-Dichloropropene
Methylene chloride
1,1,2,2-Tetrachloroethane
Tetrachloroethene
1.1.1- Trichloroethane
1.1.2- Trichloroethane
Trichloroethene
Trichlorofluoromethane
Vinyl chloride
Ethylbenzene
Toluene
Benzene
Phenols
11,000 / NA
11,000 / NA
11,000 / NA
35,200 / NA
250 / 50
NA
NA
28,900 / 1,240
11,000 / NA
11,000 / NA
1,120 / 763
1,120 / 763
I, 120 / 763
NA
NA
118,000 / 20,000
II, 600 / NA
11,600 / NA
23,000 / 5,700
6,060 / 244
6,060 / 244
11,000 / NA
NA / 2,400
5,280 / 840
NA
NA / 9,400
45,000 / 21,900
11,000 / NA
NA
32,000 / NA
17,500 / NA
5,300 / NA
10,200 / 2,560
0.19
0.19
0.19
0.40
201'
NA
NA
0.19
0.19
NA
4002/
4002'
4002/
NA
NA
0.94
0.03
NA
NA
872/
87^
0.19
0.17
0.8
NA
0.6
2.7
0.19
2.0
1,4002/
0.66
350v
100
100
100*
5
7
100
200
5
5
2
700
1000
5
NA
i/
2/
= Not Available
= Taste and odor
= Human health criterion, EPA (1986)
= Total Trihalomethanes
Source: EPA, 1986, 1988, 1991b.
4-32
P78-921/P784AJ3
02/14/92
groundwater or soils does exist, the actual concentration of a compound in the subsurface can not be judged solely
by ion flux counts. Theisopleth contour maps of ion flux counts, therefore, should not be confused with actual soil
gas concentration but should be considered only as an indication of relative compound concentration.
Trichloroethane
Trichloroethane was detected in the majority of the NDD and E-519 soil gas collectors. Trichloroethane anomalies
are observed in the area surrounding and to the east of Buildings E-516, E-517, E-519, and M-508 (Figure 4-11).
The variable distribution observed is probably due to different migration pathways for this chemical compound.
Trichloroethylene
Trichloroethylene was detected over the majority of the NDD and E-519 soil gas survey area (Figure 4-12). An
anomaly is present northwest, north, and south of Building E-517. Another anomaly is located east of
Building E-519. Anomalies are also present east of Building E-502 and in the area surrounding Building E-516.
Tetrachloroethene
The distribution of tetrachloroethene is much more limited than the distributions for trichloroethylene and
trichloroethane (Figure 4-13). There are only minor similarities to the trichloroethylene distribution observed around
Building E-516 which has a tetrachloroethene anomaly. The southern end of Building E-517 also has an anomaly.
The only other area of importance is located at the southern end of the NDD survey where collectors 42 and 38
define an isolated anomaly.
Hydrocarbons
Hydrocarbons were detected in a limited area in a similar distribution to tetrachloroeUiene (Figure 4-14). Three
anomalies are present; one associated with the southern end of Building E-517, another associated with
Building E-516, and a third located east of Building E-519. The similarity of the tetrachloroethene and hydrocarbon
distributions in all but the anomaly at Building E-519 indicate that tetrachloroethene was used as a degreaser for
the hydrocarbons (PETREX, 1990). The anomaly at Building E-519 may indicate a hydrocarbon source area.
The chemical compounds observed at NDD are commonly used industrial solvents, degreasers, paint removers, and
chemical reagents. The presence of such compounds (with the exception of trichloroethylene which has not been
used at Plant 78 since 1973) in discharge water from Buildings E-516, E-517 and E-519 is, as stated previously,
consistent with manufacturing and maintenance uses at the site. The presence of chloroform, bromoform,
bromodichloromethane, and chloromethane may be due to the chlorination of plant water for drinking purposes.
Since 1989, all building discharge of wastewater to the NDD has been halted due to the construction of the Thiokol
wastewater treatment system.
4-33
P78 STAGE 2 05/91 PFIG 4-10
Legend
Ion Count Values
10,000-99,999
SOIL GAS COLLECTOR LOCATION
ION COUNT
Identification not possible due to
hydrocarbon interference.
Figure 4-1 1
TRICHLOROETHANE ION FLUX MAP, SOIL GAS
SURVEY, NORTH DRAINAGE DITCH
SOURCE: PETREX, 1990.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78 STAGE 2 05/91 PFIC 4-11
»0.0O0-1t9.».. I0.000-8».9»S
Legend
Ion Count Values
1,000 - 9,999
tOO 200
+ SOIL GAS COLLECTOR LOCATION
179 ION COUNT
Identification not possible due to
' ' hydrocarbon interference.
Figure 4-12
TRICHLOROETHYLENE ION FLUX MAP, SOIL GAS
SURVEY, NORTH DRAINAGE DITCH
SOURCE: PETREX, 1990.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78 STAGE 2 03/91 PFIG 4-12
Legend
Ion Count Values
—1,000 - 9,999 —
+ SOIL GAS COLLECTOR LOCATION
105 ION COUNT
Figure 4-13
TETRACHLOROETHENE ION FLUX MAP, SOIL GAS
SURVEY, NORTH DRAINAGE DITCH
SOURCE: PETREX, 1990.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78 STAGE 2 OS/9' PFIG 4-13
• *
»—' —i —\
+ + + \ , J I
. \ 7 T 100,000,-999,999' t _-__9LJ «
E-532
E-533
M-508
o tao 200
FEET
Legend
Ion Count Values
— 100,000-99,999
+ SOIL GAS COLLECTOR LOCATION 26,1 ION COUNT
Figure 4-14
HYDROCARBONS
SURVEY, NORTH
SOURCE PETREX, 1990.
ION FLUX MAP, SOIL
DRAINAGE DITCH
GAS INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-921/P784A38
02/14/92
4.1.3.4.2 Zone(s) of Contamination
Stage 1 sampling demonstrated the presence of methylene chloride, trichloroethylene, and petroleum hydrocarbons
in NDD soil samples collected from both borings and surface sampling conducted adjacent to Buildings E-516 and
E-517. Stage 2 sampling verified the presence of petroleum hydrocarbons in and around Buildings E-516 and
E-517.
Surface water sampling for Stage 1 demonstrated the presence of bromodichloromethane, bromoform,
bromomethane, 1,1-dichloroethene, and chloroform detected at levels exceeding either EPA IO"6 HHRC or MCLs.
For further evaluations and determination of potential risk, all contaminant detections (Stage 1 and Stage 2) will be
considered. Refer to Section 4.2.2.
Subsurface contamination at NDD and E-519 consists of contaminated groundwater identified by water quality
sampling of groundwater monitoring wells P-3 and P-8. The NDD and E-519 soil gas survey indicates that the
lateral extent of contamination exceeds the area monitored by wells P-3 and P-8. Figure 4-15 shows the aerial
extent of the contaminant plume indicated by both groundwater sampling and soil gas detections for the north end
of Plant 78.
4.1.3.4.3 Contamination Migration
Contamination migration is discussed in detail in Section 4.2.3.
Spatial and temporal variability in the soil and surface concentration of contaminants is observed at the NDD. As
discussed in Section 4.1.3.4.1, soil, surface water and surface sediment sample analyses of Stage 1 and Stage 2
samples yielded varying results. The only contaminants which are present in both samplings are petroleum
hydrocarbons and 1,2-dichloroethane.
Only one sampling episode was conducted in the groundwater monitoring wells at the NDD and E-519 (monitoring
wells P-3 and P-8). The extent of spatial and temporal variability for this contamination is not fully characterized.
4.1.4 DISCUSSION OF RESULTS FOR THE E-512 DRAINAGE DITCH
4.1.4.1 E-512 Drainage Ditch Geology
The geologic and hydrogeologic investigation at E-512 consists of work conducted under Stage 2. One deep boring
E-512B1 was drilled to 128 feet from the ground surface. Boring E-512B1 encountered heterogeneous lake clays
and gravel sediments of the Lake Bonneville Group. These sediments consist of light yellow to dark brown (10 YR
6/4 to 10 YR 3/3), gravely and sandy silt, fine-grained to very fine-grained, poorly sorted, silty sands, interbedded
with silty and sandy gravels, and clayey gravels with sand-silt mixtures. Silts are generally slightly plastic,
calcareous and moist. The gravels consists of subrounded to slightly angular pebble-sized clasts of grey limestone
4-38
P7B STAGE 2 OS/91 PFIG 4-1 *
643
LEGEND
• WELL P-5 —GROUNDWATER MONITORING WELL
IP GROUNDWATER PLUME INDICATED BY BOTH GROUNDWATER
SAMPLING AND SOIL GAS DETECTIONS
I 140 SM MO
Figure 4-15
LOCATION OF THE NORTH PLANT
78 GROUNDWATER CONTAMINANT
PLUME
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-39
P78-921/P784A-40
02/14/92
and dolostone, and light brown sandstone. The gravel beds are generally less than 10 feet thick although
occasionally, as in the gravel bed encountered at 75 feet, can be up to 15 feet thick. A boring profile for E-512B1
and well construction diagram for momtoring well P-5 is presented in Figure 3-9 of this report.
Total gravel thickness in boring E-512B1 is approximately 38 feet. Thinner gravel beds encountered in this boring
compared to borings east of this location indicates an easterly source for the alluvial fan deposition suggested as a
possible depositional environment for the lake clays and gravels (Figure 4-4).
4.1.4.2 E-512 Drainage Ditch Hydrogeology
Groundwater monitoring well P-5 was installed in the E-512B1 boring and screened from 128 to 107 feet in a sandy
to silty gravel zone. Static groundwater level was measured at a depth of 118 feet (4,380.17 feet above MSL) at
the time of completion (December 1988). The water level measured in monitoring well P-5 is roughly consistent
with levels observed in both momtoring well P-3 (4,411.60 feet above MSL) and boring NDD-B1 (P-4)
(4,384.40 feet above MSL) at the NDD and indicates that these wells are probably completed in the same
groundwater bearing zone. A static groundwater level of 130.16 feet (4,370.00 feet above MSL) was measured
at momtoring well P-5 in November 1991. The static water level at momtoring well P-5 has dropped 10.17 feet
since December 1988 (Table 4-4). As discussed in Section 4.1.2, the possible groundwater mound observed in both
the upper shallow and deeper shallow groundwater zone at Plant 78 is decreasing. The 10.17 foot drop in static
water level observed at monitoring well P-5 is probably related to this decrease.
4.1.4.2.1 Aquifer Testing
A slug/bail aquifer test was performed on momtoring well P-5 to determine horizontal hydraulic conductivity (K)
according to the procedures and limitations described in Section 3.5.6. Solving for V yields a value of 0.17 fpd
and indicates that groundwater at momtoring well P-5 could move up to 62 fpy.
4.1.4.3 Analvtical Results
Surface water, surface sediment, shallow and deep boring, and groundwater samples were collected at the E-512
site. The following is a discussion of the results by sample type.
4.1.4.3.1 Surface Water Samples
One surface water sample and one duplicate sample were collected from the drainage ditch at E-512. Figure 4-16
displays the sample location and Table 4-11 lists the analytical detections for those samples.
4.1.4.3.2 Surface Sediment Samples
Petroleum hydrocarbons were the only analyte detected in surface sediment sample E-512SS1. Figure 4-16 displays
this sample location. Petroleum hydrocarbons were detected at 1,320 mg/kg (Table 4-12).
4-40
P78 STAGE 2 05\91 PFIC4-15
E-512SS1
METHOD
Compound mg/kg BLANK
Pal. Hydro. 1320 5.75
E-512 DRAINAGE
DUPLICATE E-512SW1
METHOD
Compound | ug/L | BLANK
Choloform
1,1.1-TCA
0.473
4.22 NO NO
300 ST.
LEGEND
E-512SW1
E-512SS1 SURFACE WATER AND SEDIMENT SAMPLE LOCATION 100 200 300 400 500 FEET
Figure 4— 1 6
STAGE 2 SURFACE SEDIMENT AND WATER SAMPLE
RESULTS, E-512 DRAINAGE DITCH
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-914/P7r84-ll.l
02/14/92
Table 4-11. Stage 2 Analytical Results for Surface and Ground Water Samples, E-512 Drainage Ditch.
E-512SW1 E-512SW1 P5
Chemical Parameter 12/15/88 Duplicate 1/24/89 Method
/tg/L (ppb) P78 -W*5 P78-W*26 P78 - W*6 Blank
Petrol. Hydrocarbons
Benzene
Toluene
Ethylbenzene
Total Xylenes
Bromobenzene
Bromodichloromethane
Bromoform
Bromomethane
Carbon Tetrachloride
Chlorobenzene
Chloroethane
2-Chloroethylvinyl Ether
Chloroform 0.430 0.473 0.346
1-Chlorohexane
Chloromethane
Dibromochloromethane
Dibromomethane
Dichlorobenzene
1,1-Dichloroethane ~ - 0.548
1.1- Dichloroethylene ~ - 4.85
1.2- Dichloroethane ~ ~ 1.43
t-1,2-Dichloroethene
1,2-Dichloropropane
Cis-1,3-Dichloropropene
t-1,3-Dichloropropene
Dichlorodifluoromethane
Dissolved Sohds 782 746 1090
Methylene Chloride
1,1,1,2-Tetrachloroethane
1,1,2,2-Tetrachloroethene
tetrachloroethene
1.1.1- Trichloroethane 4.17 4.22 16.0
1.1.2- Trichloroethane
Trichloroethene — — 664
Trichlorofluoromethane
Trichloropropane
Vinyl Chloride
— = Not detected above instrument detection level
4-42
P78-914\P78T4-12.1
02/14/92
Table 4-12. Stage 2 Analytical Results for Surface Sediment Samples, E-512 Drainage Ditch.
Chemical Parameter E-512SS1 Method
mg/kg (ppm) 12/15/88 Blank
Petrol. Hydrocarbons 1,320 5.75
Benzene
Toluene
Ethylbenzene
Total Xylenes
Bromobenzene
Bromodichloromethane
Bromoform
Carbon Tetrachloride
Chlorobenzene
Chloroethane
2-Chloroethylvinyl Ether
Chloroform
1-Chlorohexane
Dibromochloromethane
Dibromomethane
Dichlorobenzene
1,1-Dichloroethane
1.1- Dichloroethene
1.2- Dichloroethane
t-l,2-Dichloroethene
1,2-Dichloropropane
Cis-1,3-Dichloropropene
t-1,3-Dichloropropene
DicUorob-fluoromethane
Methyl Bromide
Methyl Chloride
Methylene Chloride
1,1,1,2-Tetrachloroethane
1,1,2,2-Tetrachloroethane
Tetrachloroethylene
1.1.1- Trichloroethane
1.1.2- Trichloroethane
Trichloroethylene
Trichlorofluoromethane
Trichloropropane
Vinyl Chloride
~ = Not detected above instrument detection levels
4-43
P78-921/P784AJM
02/14/92
4.1.4.3.3 Shallow Soil Boring Samples
No analytes were detected in samples from shallow soil borings E-512SB1, E-512SB2, and E-512SB3.
4.1.4.3.4 Deep Stratigraphic Boring Samples
Seven soil samples (five regular samples and two duplicate samples) were collected from deep stratigraphic boring
E-512B1. Figure 4-17 displays the location of boring E-512B1 and Table 4-13 lists analytical detections for soil
samples collected from this boring.
4.1.4.3.5 Groundwater Sample
One groundwater sample for water quality analysis was collected at momtoring well P-5. Figure 4-18 displays the
location of monitoring well P-5 and Table 4-11 lists analytical detections for the groundwater sample collected from
this well.
4.1.4.3.6 Soil Gas Samples
Thirty-eight PETREX™ soil gas collectors were installed at E-512. Figure 4-10 displays the locations of these
collectors.
4.1.4.4 Discussion of Analvtical Results for E-512 Drainage Ditch Site
Inorganic constituents for surface water were determined for E-512 during Stage 1. All inorganic constituents were
found to be below the NIPDWR and NSDWR recommended levels. Major and minor element chemistry was
comparable to the onsite water which supplies the ditch. Metals concentrations in sediments and soils were found
to be comparable to background samples collected from the FVD control site (200B) and were within reported
ranges of representative U.S. concentrations. These parameters were not analyzed under Stage 2.
Methyl chloride
Methyl chloride was detected at 0.099 mg/kg in a soil sample collected at 20 feet in foring E-515B1.
4.1.4.4.1 Significance of Findings
SOIL AND SURFACE SEDIMENT ANALYTICAL RESULTS
Petroleum hydrocarbons were the only analyte detected in surface sediment sample E-512DD during Stage 1.
Stage 2 verified this detection in sample E-512SS1. Petroleum hydrocarbons were detected at 1,320 mg/kg.
Review of the method blank analytical data indicated that petroleum hydrocarbons were detected in the method blank
at 5.75 mg/kg. The concentration of this compound observed in the method blank analysis is below any
concentration which could compromise sample results. The presence of petroleum hydrocarbons is consistent with
the site history.
4-44
P78 STAGE 2 05\91 PFIC 4-1g
DUPLICATE SAMPLE
Somple Depth
50 ft
101 ft
Compound
Pet. Hydro.
Pet. Hydro.
METHOD
BLANK
Somple Depth i Compound
50 ft
126 ft
Pet. Hydro.
Pet. Hydro.
m
ND
ND
9/k9
36.8
18.5
BORE E-51281
METHOD
BLANK
5.75
5.75
E-S12 DRAINAGE
BLDG
E-512
300 ST.
LEGEND
• BORE E-512B1-DEEP STRATOGRPHIC BORING
0 100 200 300 400 500 FEET w
Figure 4-17
STAGE 2 DEEP STRATIGRAPHIC BORING SAMPLE RESULTS
E-512 DRAINAGE DITCH
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P7S-914/P78T4-13.1
02/14/92
Table 4-13. Stage 2 Analytical Results for Deep Boring Soil Samples, E-512 Drainage Ditch.
E-512B1 E-512B1 E-512B1 E-512B1 E-512B1 E-512B1 E-512B1
12/14/88 12/14/88 Duplicate 12/15/88 12/15/88 Duplicate 12/15/88
Chemical Parameter 26' 50' 50' 76' 101' 101' 126' Method
mg/kg (ppm) P78-S*24 P78-S*25 P78-S*83 P78-S*26 P78-S*27 P78-S*27 P78-S*84 Blank
Petrol. Hydrocarbons - 36.8 - - ~ - 18.5 5.75
Benzene
Toluene
Ethylbenzene
Total Xylenes
Bromobenzene
Bromodichloromethane
Bromoform
Carbon Tetrachloride
Chlorobenzene
Chloroethane
2-Chloroethylvinyl Ether
Chloroform
1-Chlorohexane
Dibromochloromethane
Dibromomethane
Dichlorobenzene
1,1-Dichloroethane
1.1- Dichloroethene
1.2- Dichloroethane
t-1,2-Dichloroethene
1,2-Dichloropropane
Cis-1,3-Dichloropropene
t-l,3-Dichloropropene
Dichlorodifluoromethane
Methyl Bromide
Methyl Chloride
Methylene Chloride
1,1,1,2-Tetrachloroethane
1,1,2,2-Tetrachloroethane
Tetrachloroethylene
1.1.1- Trichloroethane
1.1.2- Trichloroethane
Trichloroethylene
Trichlorofluoromethane
Trichloropropane
Vinyl Chloride
— = Not detected above instrument detection levels
4-46
P78 STAGE 2 05\91 PfIG 4-17
200 ST.
Compound
Chloroform
1.1- DCA
1.2- DCA
1,1-DCE
1.1,1-TCA
TCE
E-S12 DRAINAGE
ug/L
0.346
0.548
1.43
4.85
16.0
664
METHOD
BLANK
ND
ND
ND
ND
ND
ND
BLDG
E-512
300 ST.
LEGEND
• WELL P-5 -GROUNDWATER MONITORING WELL
0 100 200 300 400 500 FEET
w
Figure
STAGE
E-512
4-18
2 GROUNDWATER
DRAINAGE DITCH
SAMPLE RESULTS
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-921/P784A.48
02/14/92
Petroleum hydrocarbons were detected in samples collected at 50 feet (36.8 mg/kg) and 126 feet (18.5 mg/kg) in
boring E-512B1. A duplicate sample collected at 50 feet contained no detections. No duplicate sample was
collected at 126 feet. Review of the method blank results shows laboratory contamination of 5.75 mg/kg. The
concentration of this compound observed in the method blank analysis is below any concentration which could
compromise sample results.
SURFACE WATER AND GROUNDWATER ANALYTICAL RESULTS
To evaluate the quality of the surface and groundwater at Plant 78 federal and State of Utah water quality standards
(e.g., MCLs) are used to indicate the quality of the water relative to drinking water. These drinking water standards
are not directly applicable to the samples collected at Plant 78. The waters collected at Plant 78 are unsuitable for
use as a drinking water source either at the installation or within the immediate vicinity due to naturally high
dissolved solids content.
Surface Water
Petroleum hydrocarbons were detected in surface water sample collected at E-512DD under Stage 1. Bromoform,
chloroform, 1,1-dichloroethane, 1,1,1-trichloroethane, and 1,1-dichloroethene were detected at low concentrations
in the E-512DD surface water sample.
Stage 2 surface water sample E-512SES1 (and duplicate sample) did not yield any petroleum hydrocarbons. It did
contain 0.43 and 0.473 /tg/L of chloroform and 4.17 and 4.22 /ig/L of 1,1,1-trichloroethane. Laboratory analysis
contained no evidence of method contamination. Chloroform exceeds the EPA 10"* HHRC.
Groundwater
Chloroform, 1,2-dichloroethane, 1,1 -dichloroethene, 1,1 -dichloroethane, 1,1,1 -trichloroethane, and trichloroethylene
were observed in water quality analysis conducted on groundwater from monitoring well P-5.
The similarity of chloroform concentrations between surface and groundwater suggests that the chloroform may not
result from site disposal activities. The chloroform may be present due to jthe existence of chloroform in the
Plant 78 water supply which directly supplies the water present in the E-512 ditch and probably indirectly recharges
the shallow groundwater aquifer monitored by well P-5.
Chloroform, 1,2-dichloroethane, 1,1-dichloroethene, exceed the EPA IO6 HHRC. 1,2-Dichloroethane and
1,1-dichloroethene do not, however, exceed MCLs. 1,1,1-Trichloroethane does not have a 10"6 HHRC but does
have a MCL. The concentration of 16 /tg/L is well below the MCL of 200 /tg/L. The trichloroethylene
concentration of 664 /tg/L exceeds the MCL of 5 /tg/L.
4-48
P78-921/P784A^9
02/14/92
SOIL GAS SURVEY
Data collected by the Petrex™ soil gas method are displayed in the form of isopleth contour maps based upon the
ion count flux recorded for each compound or mixture of compounds identified at each sample location. Although
a relationship between high and low ion flux counts and high and low compound concentrations in either
groundwater or soils does exist, the actual concentration of a compound in the subsurface can not be judged solely
by ion flux counts. The isopleth contour maps of ion flux counts, therefore, should not be confused with actual soil
gas concentration, but should be considered only as an indication of relative compound concentration.
Trichloroethane
Trichloroethane was detected in the majority of the E-512 soil gas collectors (Figure 4-11). The dominant area of
trichloroethane contamination is associated with the Hazardous Waste Storage Yard located due south of Building
E-512. Additional areas of trichloroethane contamination exist both south and east of Building E-512 and may be
related to reported degreaser usage at Building M-508. The variable distribution observed is probably due to
different migration pathways for this compound.
Trichloroethylene
Trichloroethylene was detected over the majority of the E-512 soil gas survey area (Figure 4-12). A large anomaly
is located south of Building E-512 and may be related to reported degreaser usage at Building M-508. This large
anomaly extends into the Hazardous Waste Storage Yard.
Tetrachloroethene
The distribution of tetrachloroethene is much more limited than the distributions for trichloroethylene and
trichloroethane (Figure 4-13). There is only minor tetrachloroethene distribution observed south of Building E-512
and in the southern end of the Hazardous Waste Storage Yard. A trend of detections are also observed to be
associated with Building E-517 and may be related to waste material associated with the industrial operations at the
E-517 machine shop.
Hydrocarbons
Hydrocarbons were detected in a limited area with a similarity to the distribution observed for tetrachloroethene
(Figure 4-14). Only one anomaly is present. It is associated with the tetrachloroethene anomaly south of Building
E-512. The similarity of the tetrachloroethene and hydrocarbon distributions indicate that tetrachloroethene was used
as a degreaser for the hydrocarbons (PETREX, 1990).
The organic compounds detected at Building E-512 are commonly used industrial solvents, degreasers, paint
removers, and chemical reagents. Their presence in discharge water, shallow groundwater, and soil gas is
consistent with the reported use of paints and solvents in this area. The presence of chloroform, as stated above,
may be due to the chlorination of the water for drinking purposes.
4-49
P78-921/P784A-S0
02/14/92
4.1.4.4.2 Zone(s) of Contarrjination
Petroleumhydrocarbons, bromoform, chloroform, 1,1-dichloroethane, 1,1,1-trichloroethane, and 1,1-dichloroethene
were detected at low concentrations during Stage 1. Stage 2 surface sampling detected low concentrations of
chloroform and 1,1,1-trichloroethane. For further evaluations, all contaminant detections (Stage 1 and Stage 2) will
be considered. The zone of contamination associated with the soil, surface water, and surface sediment is
considered to involve only the E-512 Drainage Ditch (Refer to Section 4.2.2).
Subsurface contamination at E-512 consists of contaminated groundwater as detected by monitoring well P-5.
Further evidence of groundwater contamination is provided by the E-512 soil gas survey which indicates that the
lateral extent of contamination exceeds the area monitored by well P-5. Figure 4-14 shows the aerial extent of the
North Plant 78 groundwater contaminant plume indicated by both groundwater sampling and soil gas detections.
Results of the soil gas survey indicate that contamination observed in the groundwater at momtoring w
continuous with contamination observed along the NDD (Refer to Section 4.2.2).
4.1.4.4.3 Contamination Migration
Contamination migration is discussed in detail in Section 4.2.3.
Spatial and temporal variability exists in the soil and surface concentration of contaminants observed at E-512. As
discussed in Section 4.1.4.4.1, soil, surface water and surface sediment sample analyses of Stage 1 and Stage 2
samples yielded varying results. The only conbiminants which are present in both samplings are petroleum
hydrocarbons, chloroform, and 1,1,1-trichloroethane.
The conflict between State 1 and Stage 2 samplings may be due to individual sample variability between the two
sampling periods: Stage 1 sampling may have detected a specific contamination release event, which has passed
through the site, or the decrease in chemical concentration may be due to natural degradation.
Only one sampling episode has been conducted on the groundwater momtoring well P-5. The extent of spatial and
temporal variability for contamination in the groundwater at E-512 is not fully characterized.
4-50
P78-914/F.S4B.51
02/14/92
4.1.5 DISCUSSION OF RESULTS FOR THE FAUST VALLEY DRAINAGE COURSE AND E-515 SITES
The geologic and hydrogeologic investigation at the FVD and E-515 consists of work conducted under both Stage 1
and Stage 2. One deep boring (200B) was drilled to a depth of 255 feet and completed as groundwater monitoring
well P-1. No Stage 1 investigations were conducted at E-515. Borings E-515B1 and E-515B2 were drilled during
Stage 2. Groundwater monitoring well P-9 was installed in boring E-515B2 to a depth of 197 feet. A determination
of hydrauhc conductivity was made on both monitoring wells P-1 and P-9 under Stage 2.
4.1.5.1 Faust Vallev Drainage Course Geology
All borings encountered heterogeneous lake clays and gravel sediments of the Lake Bonneville Group. These
sediments consist of brownish grey to light yellowish brown (10 YR 7/4 to 10 YR 6/4), thick silty to sandy gravels,
fine-grained, and silty to sandy and gravely clays. Clays are slightly plastic to plastic, slightly cohesive to cohesive,
and massive. The gravels consist of subrounded to slightly angular pebble to cobble sized clasts of grey limestone
and light brown sandstone. The gravels are matrix to clast supported conglomerates and beds are up to 40 feet
thick. A boring profile for E-515B2 is presented in Figure 3-13.
Total gravel thickness decreases from approximately 190 feet in boring 200B to approximately 120 feet in
boring E-515B2. A regional decrease in gravel thickness from east to west suggests a gravel source to the east.
Deposition of these sediments likely occurred in a lacustrine alluvial fan delta (Figure 4-2).
4.1.5.2 Faust Vallev Drainage Course and E-515 Hydrogeology
Groundwater momtoring well P-1 was installed under Stage 1 and screened from 234.5 to 254.5 feet within a silt
and clay rich gravel zone. A static groundwater level was measured at a depth of 238 feet (4,311.32 feet above
MSL) at the time of completion (January 1987). A static water level of 214.45 feet (4,334.87 feet above MSL) was
measured at the time of sampling during the Stage 2 investigation (February 1989). This is a rise in static water
level of 23.55 feet over a two year period. A third static groundwater level of 205.17 feet (4,346.15 feet above
MSL) was measured at momtoring well P-1 in November 1991. This is rise of static water level of 11.28 feet since
February 1989 and a 34.83 feet total rise in water level at monitoring well P-1 since March 1988 (Table 4-4). The
groundwater table elevations measured at P-1 are roughly consistent with the regional water table for the Blue Creek
Valley (ES, 1984). During well development, the rapid dewatering of this well indicated that it was completed in
a nontransrnissive zone.
Boring E-515B1 was drilled at Building E-515 during Stage 2 to 90 feet and abandoned due to drilling problems.
This boring was replaced by boring E-515B2. Boring E-515B2 was drilled to a total of 197 feet and was completed
as groundwater momtoring well P-9. Screen length of 26.27 feet was installed from 169 to 195.27 feet in a sand
and clay-rich gravel. Groundwater was measured at 176.50 feet (4,352.20 feet above MSL) at the time of
completion (July 21, 1989).
4-51
P78-914/P784BJ2
02/14/92
A 34.83-foot increase in water levels was observed at monitoring well P-1 since February 1987. This increase may
be due to either the very slow groundwater recharge of this momtoring well, especially if the water level recorded
in 1987 was, in fact, an unstabilized level, or to a local increase in the regional water level. Regionally, water
levels in unconfined aquifers in the Curlew Valley west of Blue Creek Valley and in the Malad-Lower Bear River
Valley east of Blue Creek valley had an overall decline in 1988, with some localized water level increases (Burden
and others, 1989). Precipitation in northern Utah was below average for 1988. A review of precipitation data taken
at Corinne, Utah and Bear River City, Utah show precipitation at normal to less-than-normal levels. The increase
in water level at momtoring well P-1 is not due to precipitation and is unexplained. As discussed in Section 4.1.2.2,
the possible groundwater mounding observed at Plant 78 and the apparent local eastward reversal in the regional
west groundwater flow direction suspected to be caused by this mounding is decreasing. Although monitoring
well P-1 static water level is increasing, the net effect of this water level rise, along with the decreases in static
water levels observed in momtoring wells P-8 and P-9 is to counter the apparent local reversal in groundwater flow
observed in the deeper shallow groundwater zone (Figure 4-3b).
4.1.5.2.1 Aquifer Testing
Slug/bail aquifer tests were performed on momtoring wells P-1 and P-9 to determine horizontal hydraulic
conductivity according to the procedures and limitations described in Section 3.5.6.
Monitoring well P-1 had a V of 0.01 fpd, which is the lowest groundwater velocity value of all the Plant 78
monitoring wells. Converting fpd to fpy indicates that groundwater at monitoring well P-1 could move 3.6 fpy.
Monitoring well P-9 had a V of 0.85 fpd. Converting fpd to fpy indicates that groundwater at momtoring well P-9
could move 310 fpy.
4.1.5.3 Analvtical Results
Surface sediment, shallow and deep boring, and groundwater samples were collected at the FVD and E-515. The
following is a discussion of the results by sample type.
4.1.5.3.1 Surface Sediment Samples
Six surface sediment samples were collected from the FVD. One additional surface sediment sample was collected
as a duplicate. Figure 4-19 displays sample locations and Table 4-14 summarizes analytical detections for the
surface sediment samples.
4.1.5.3.2 Shallow Borings
No analytes were detected in samples from shallow boring FVD-SB1, located next to groundwater monitoring
well P-1. In addition, samples collected from shallow boring BC-SB6, which is located at the junction of the FVD
and Blue Creek, also contained no detectable levels of analytes. Figure 4-20 shows the location of these shallow
borings.
4-52
P78 STAGE 2 05/91 PFIG4-18
METHOD
BLANK
FVD-SS8
Rl ANK
1,1,1-TCA 0.716
LEGEND
O FVD-SS1 -SURFACE SEDIMENT SAMPLE
0 IOC 200 300 400 500
Figure 4-19
STAGE 2 SURFACE SEDIMENT SAMPLE ANALYTICAL
RESULTS, FAUST VALLEY DRAINAGE
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
SOURCE: ESE, 1991.
P78-914/P78T4-14.1
02/14/92
Table 4-14. Stage 2 Analytical Results for Surface Sediment Samples, Faust Valley Drainage (Page 1 of 2).
FVD-SS1 FVD-SS2 FVD-SS3 FVD-SS5 FVD-SS6 FVD-SS8 FVD-SS8
Chemical Parameter 12/7/88 12/7/88 12/7/88 12/7/88 12/7/88 12/15/88 Duplicate Method
mg/kg (ppm) P78-S*71 P78-S*72 P78-S*73 P78-S*75 P78-S*76 P78-S*100 P78-S*80 Blank
Petrol. Hydrocarbons
Benzene
Toluene
Ethylbenzene
Total Xylenes
Bromobenzene
Bromodichloromethane
Bromoform
Carbon Tetrachloride
Chlorobenzene
Chloroethane
2-Chloroethylvinyl Ether ~
Chloroform
1-Chlorohexane
Dibromochloromethane
Dibromomethane
Dichlorobenzene
1,1-Dichloroethane
1.1- Dichloroethene
1.2- Dichloroethane
t-l,2-Dichloroethene
1,2-Dichloropropane
Cis-l,3-Dichloropropene ~
t-1,3-Dichloropropene
Dichlorodifluoromethane —
Methyl Bromide
Methyl Chloride
Methylene Chloride
1,1,1,2-Tetrachloroethane ~
1,1,2,2-Tetrachloroethane ~
Tetrachloroethylene
1.1.1- Trichloroethane 0.588 0.723 0.824 0.579 0.716 0.108 0.130
1.1.2- Trichloroethane
Trichloroethylene
Trichlorofluoromethane
Trichloropropane
Vinyl Chloride
2,4-D
2,4-DB
4-54
P78-914/P78T4-14.2
02/14/92
Table 4-14. Stage 2 Analytical Results for Surface Sediment Samples, Faust Valley Drainage (Page 2 of 2).
FVD-SS1FVD-SS2 FVD-SS3 FVD-SS5 FVD-SS6 FVD-SS8 FVD-SS8
Chemical parameter 12/7/88 12/7/88 12/7/88 12/7/88 12/7/88 12/15/88 Duplicate Method
mgAg (PPm) P78-S*71 P78-S*72 P78-S*73 P78-S*75 P78-S*76 P78-S*100 P78-S*80 Blank
2,4,5-TP/ Silvex
Dalapon
Dicamba
Dicbloroprop
Dinoseb
MCPA
MCPP
~ = Not detected above instrument detection levels
4-55
P78 STAGE 2 05/91 PFIG 3-17
LEGEND
A FVD-SB1 SHALLOW SOIL BORING 0 100 ZOO 300 400 500
Figure 4-20
STAGE 2 SHALLOW SOIL BORING LOCATION, FAUST
VALLEY DRAINAGE
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-914/P784B.57
02/14/92
4.1.5.3.3 Deep Boring Samples
Seven samples were collected from borings E-515B1 and E-515B2. Figure 4-21 shows the locations of these
borings and Table 4-15 list the analytical detections for these samples.
4.1.5.3.4 Groundwater Samples
One groundwater sample from momtoring well P-1 (FVD) and two samples from monitoring well P-9 (E-515) were
collected and analyzed for water quality. Figure 4-22 displays locations of momtoring wells and summarizes
analytes detected in the groundwater samples. Table 4-16 lists analytical detections for the groundwater samples
collected at the FVD and E-515.
4.1.5.3.5 Soil Gas Samples
Twenty-three PETREX™ soil gas collectors were installed at Building E-515. Figure 4-10 displays the locations
of these collectors.
4.1.5.4 Discussion of Results for FVD and E-515
4.1.5.4.1 Significance of Findings
Surface sediment, soil, and groundwater samples were collected from the FVD during Stage 1 and Stage 2. No
surface water samples were collected during Stage 1 or Stage 2 because the FVD was dry during these sampling
periods.
Several sampling locations were chosen during Stage 1 to represent background conditions upgradient of the Plant 78
manufacturing facilities. These locations included soil boring 200B, groundwater momtoring well P-1, and surface
sediment location FVD/NE. The downgradient surface sediment location, FVD/R was chosen to provide an
indication of surface geochemical conditions where the FVD exits Plant 78. A summary of inorganic background
analytical data for FVD samples is presented in Table 4-17.
Inorganic constituents were determined for all surface sediment and soil samples and one groundwater sample
(monitoring well P-1) from the FVD under Stage 1. All inorganic constituents were found to be below the
NIPDWR and NSDWR recommended levels. The concentrations of all metals in sediments and soils were within
representative ranges of these elements in soils and surface sediments in the western U.S. Sediment samples were
not analyzed for metals and inorganics under Stage 2. The groundwater sample collected from monitoring well P-9
under Stage 2 was analyzed for metals. The only metals detected with MCL's were barium, chromium, and
selenium. None of these metals had concentrations above their MCL's.
4-57
P78 STAGE 2 05/91 PFIG 4-A
BORE E-515B1
Sample Depth
20 ft
35 ft
50 ft
Compound
Methyl Chonde
Methyl
Chloride
Methyl
Chloride
Bis (2EH)
phthalate
Butyl (BZ)
phthalate
mg/kg
0.11
0.108
0.099
ND
0.18
Method
Blank
ND
ND
ND
0.17
2.9
E-516
Sample Depth
H AVE.
BORE E-515B2
Compound mg/kg
15 ft
35 ft
97 ft
135 ft
Acetophenone
Bis (2EH)
phthalate
Jutyl (BZ) >hthalate
LEGEND
B
pht
Acetophenone
Bis (2EH)
phthalate
Butyl (BZ)
phthalate
Vinyl Choride
Bis (2EH)
phthalate
Butyl (BZ)
phthalate
Vinyl
Chloride
Bis (2EH)
phthalate
0.09
0.22
1.0
0.06
0.12
0.47
0.0004
0.18
0.23
0.0004
0.10
Method
Blank
0.10
1.7
2.3
0.10
1.7
2.3
ND
1.7
2.3
ND
1.7
0 100 200 300 400 500 <e«t
• E-515B1 - DEEP STRATIGRAPHIC BORING
Figure 4-21
STAGE 2 DEEP BORING SAMPLE
RESULTS, FAUST VALLEY DRAINAGE
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-58
P78-914/P78T4-15.1
02/14/92
Table 4-15. Stage 2 Analytical Results for Deep Stratigraphic Boring Samples, E-515.
Chemical
Parameter
(mg/kg)
E-515B1-1
(20ft)
6/2/89
P782-S*l
E-515B1-2
(35ft)
6/2/89
P782-S*2
E-515B1-3
(50ft)
6/2/89
P782-S*3
Method
Blank
E-515B2-1
(15ft)
7/13/89
P782-S*12
E-515B2-2
(35ft)
7/14/89
P782-S*13
E-515B2-3
(97ft)
7/18/89
P782-S*14
E-515B2-4
(135ft)
7/18/89
P782-S*15
Method
Blank
Methyl Chloride 0.11 0.108 0.099
Vinyl Chloride
Acetophenone ~ NA
Bis2(EH)phthalate 0.10 NA - 0.17
Butyl Benzyl phthalate ~ ~ 0.18 2.9
0.0004 0.0004
0.09 0.06 - - 0.10
0.22 0.12 0.18 0.10 1.7
1.0 0.47 0.23 - 2.3
~ = Not detected above instrument detection level
NA = Not Analyzed
P78 STAGE 2 05/91 PFIG4-19
METHOD
Compound [ ug/L i BLANK
Chloroform
1,2-DCA
Chloromethane
1,1,1-TCA
TCE
0.248
0.424
2.41
2.71
5.53
LEGEND
WELL P-9 —GROUNDWATER MONITORING WELL
Compound
PCE
Chloromethane
Chloroform
1,2-DCA
Dichlorobenzene
Chlorobenzene
1,1-DCA
1,1 -DCE
1,1,1-TCA
TCE
Duplicate
Compound
PCE
Chloromethane
Chloroform
1,2-DCA
Dichlorobenzene
Chlorobenzene
1,1 -DCA
1,1 -DCE
1,1.1-TCA
TCE
USA.
0.881
1.08
1.00
1.46
2.79
3.73
4.39
146
387
5780
METHOD
BLANK
ugA.
1.00
ND
1.08
1.51
2.70
4.19
4.78
139
377
5390
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
METHOD
BLANK
0.056
0.428
0.07
ND
ND
0.012
0.148
0.082
0.156
0.054
0 100 200 300 400 500 feet
Figure 4-22
STAGE 2 GROUNDWATER SAMPLE
RESULTS, FAUST VALLEY DRAINAGE
AND BUILDING E-515
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-60
P78-914/P78T4-16.1
02/14/92
Table 4-16. Stage 2 Analytical Results for Ground Water Samples, Faust Valley Drainage and Building
E-515.
Pl P9 P9 Duplicate
2/10/89 Method 6/89 6/89 Method
P78-W*25 Blank P782-W*3 P782-W*4 Blank
Chemical parameter
Mg/L (ppb)
Petrol. Hydrocarbons
Benzene
Toluene
Ethylbenzene
Total Xylenes
Bromobenzene
Bromodichloromethane
Bromoform
Bromomethane
Carbon Tetrachloride
Chlorobenzene
Chloroethane
2-Chloroethylvinyl Ether
Chloroform 0.248
1-Chlorohexane
Chloromethane 2.41
Dibromochloromethane
Dibromomethane
Dichlorobenzene
1,1-Dichloroethane
1.1- Dichloroethylene
1.2- Dichloroethane 0.424
t-l,2-Dichloroethene
1,2-Dichloropropane
Cis-l,3-Dichloropropene
t-1,3-Dichloropropene
Dichlorodifluoromethane
Dissolved Sohds 890
Methylene Chloride
1,1,1,2-Tetrachloroethane
1,1,2,2-Tetrachloroethene
Tetrachloroethene
1.1.1- Trichloroethane 2.71
1.1.2- Trichloroethane
Trichloroethene 5.53
Trichlorofluoromethane
Trichloropropane
Vinyl Chloride
3.73
1.00
1.08
2.79
4.39
146
1.46
0.881
387
5780
4.19
1.08
2.70
4.78
139
1.51
1.00
377
5390
0.012
0.07
0.428
0.148
0.082
0.156
0.054
= Not detected above instrument detection level
4-61
P78-914/F78T4-17.1
02/14/92
Table 4-17. Summary of Stage 1 Inorganic Analytical Results in Soil Borings and Sediments, Faust Valley Drainage Course.
Site United States Average Composition
Soil Borings
—(mg/kg)
Sediments
(mg/kg)
Parameter 200B1200B2 200B3 200B4 200B5 200B6 200B7 200B8 FVD/NE FVD/R Range Mean Reference
Antimony
Beryllium
Cadmium
Chromium
Copper
Lead
Nickel
Silver
Thallium
Zinc
<15 <21 <16 <13 <14 <14 <25 <16
0.34 0.79 0.60 0.58 0.43 0.33 0.58 0.87
1.8
13
10
2.1
17
15
1.7
15
12
1.5
12
9.7
1.2 1.5
13 23
8.7 9.7
<7 <9.8 <7.5 <6.3 <6.7 7.8
12 12 12 9.3 8.9 16
1.6 1.9
14 12
12 9.7
<7.2 8.9
13 12
<6.5 <6.2
3.9 8.1
<0.80 <0.7
7.3 8.3
4.5
<4.7
<3.4
< 0.54 < 0.76 <0.58 <0.49 <0.52 <0.53 <0.56 <0.60 <1.0
< 0.24 < 0.37 <0.30 <0.29 <0.27 <0.29 < 0.31 0.33 0.38
49 52 50 40 35 32 45 49 29
6.2
8.9
8.3
<0.99
0.27
34
< 1-2.6 0.47 Shacklette & Boerngen, 1984
<1-15 0.68 Shacklette & Boerngen, 1984
0.41-1.5 NA Klein, 1972
3-2000 41.0 Shacklette & Boerngen, 1984
2-300 21.0 Shacklette & Boerngen, 1984
< 10-700 17.0 Shacklette & Boerngen, 1984
< 5-700 15.0 Shacklette & Boerngen, 1984
0.01-5.0 1.0 Wedopohl, 1969-1974
0.02-2.8 NA Smith & Carson, 1977
10-2100 55.0 Shacklette & Boerngen, 1984
NA = Not Available
Source, ESE 1989.
P78-914/P784B.63
02/14/92
SURFACE SEDIMENT ANALYTICAL RESULTS
Petroleum Hydrocarbons
The relative uniformity of petroleum hydrocarbon concentrations detected in surface sediments under Stage 1
sampling suggest a non-point source. Aerial application of herbicides and pesticides, operations that may have used
petroleum hydrocarbons as a carrier was originally suggested as a possible source for the widespread, low level
petroleum contamination observed. Lack of confirmation under Stage 2 sampling, however, indicates that the
petroleum hydrocarbons detected may not be due to non-point source activities. The decrease in contamination may
be due to individual sample variability between the two sampling periods, the detection of a petroleum hydrocarbon
release event which has since dissipated, or natural degradation.
Organics
Stage 2 sampling indicated the widespread occurrence of low levels of 1,1,1-trichloroethane. 1,1,1-trichloroethane
is widely used as an industrial solvent at Plant 78. The FVD, however, does not serve as a drain for any of the
Plant 78 drainage ditches. Any surface flow within the FVD would arise from either offsite drainage into the FVD
upgradient of Plant 78 or from localized, non-channeled surface run-off originating on Plant 78. Due to the lack
of plant drainage into the FVD, the source of the 1,1,1-trichloroethane present in the FVD may be due to an source
upgradient of the installation and not due to Plant 78 activities.
BORING ANALYTICAL RESULTS
Boring E-51SB1 had low concentrations of methyl chloride in samples collected from 20 feet, 35 feet, and 50 feet.
Samples from boring E-515B2 did not have any detections for methyl chloride. The concentrations of methyl
chloride in the samples were within the same range as the method detection limit. Laboratory analysis contained
no evidence of method contamination for methyl chloride.
Vinyl chloride was detected at 0.0004 mg/kg in samples collected from 97 feet and 135 feet in boring E-515B2.
The concentrations of vinyl chloride in the samples were within the same range as the method detection limit.
Laboratory analysis contained no evidence of method contamination of vinyl chloride.
Low concentrations of acetophenone, bis-2-(EH)-phthalate, and butryl benzyl phthalate were also detected in samples
from both borings. Review of the detections for method blank analyses indicates that these compounds are due to
laboratory contamination.
!
SURFACE WATER AND GROUNDWATER ANALYTICAL RESULTS
During both Stage 1 and Stage 2 sampling, the FVD was dry. No surface water samples were collected. One
groundwater sample was collected from monitoring well P-1 under stage 1 and contained no detectable organic
compounds. Three groundwater samples, one from momtoring well P-1 and two from monitoring well P-9 (E-515)
were collected under Stage 2. Monitoring well P-1 contained low concentrations of chloroform, chloromethane,
4-63
P78-914/P7S4B.64
02/14/92
1,2-dichloroethane, 1,1,1-trichloroethane, and trichloroethylene. Monitoring well P-9 contained low concentrations
pf chlorobenzene, chloroform, and dichlorobenzene. In addition, monitoring well P-9 contained of
1,1,1-trichloroethane, trichloroethylene, 1,1-dichloroethane, 1,1-dichloroethene, 1,2-dichloroethane,
tetrachloroethene, and chloromethane.
Review of the method blank detection for the samples from monitoring well P-9 showed low concentrations of all
these compounds except for dichlorobenzene and 1,2-dichloroethane. The concentrations of these compounds
observed in the method blank analysis are, however, below any concentrations which could compromise sample
results.
Monitoring well P-1, which contained no detectable concentrations of organic compounds when sampled for Stage 1,
had low concentrations of organics when sampled for Stage 2. This sample was later determined to have been
possibly cross-contaminated during sampling and, therefore, analytical results were unusable. The sampling crew
arrived at the momtoring well site to find that the protective locking well cap was broken, the well casing cap was
missing, the monitoring well was open, and the dedicated bailer and bailing rope were missing. Initial efforts to
sample monitoring well P-1 during January 1989 were unsuccessful due to an obstruction within the well casing.
This obstruction was later found to be caused by the dedicated well sampling bailer and rope, which had been
dropped into the well. Several unsuccessful attempts in January 1989 were made to remove this obstruction.
Monitoring well P-1 was finally successfully sampled in February 1989 after the obstruction was removed. Purging
of monitoring well P-1 prior to sampling was accomplished by hand bailing instead of pumping due to the very low
recharge of the well. The bailer used (5-gallon stainless steel) had previously been used as a substitute "slug" in
a slug/bail aquifer test on groundwater monitoring well P-3. The bailer was decontaminated after use in momtoring
well P-3 according to procedures outlined in the QAPP, however, it appears that some contamination remained on
the bailer and may have been responsible for the cross-contamination observed in the sample collected from
momtoring well P-1.
Concentrations of chloroform, chloromethane, 1,2-dichloroethane, and tetrachloroethene in momtoring well P-9
exceed EPA 10"* HHRC. Concentrations of 1,1-dichloroethylene, 1,1,1-trichloroethane, trichloroethylene exceed
MCLs.
The organic compounds detected in momtoring well P-9 are commonly used industrial solvents, degreasers, paint
removers, and chemical reagents. Their presence in the groundwater at E-515 is consistent with the reported use
of paints and solvents in this area. The presence of chloromethane and chloroform may be due to the chlorination
of Plant 78 water for drinking purposes.
4-64
P78-914/P784B.65
02/14/92
SOIL GAS SURVEY
Data collected by the Petrex™ soil gas method are displayed in the form of isopleth contour maps based upon the
ion count flux recorded for each compound or mixture of compounds identified at each sample location. Although
a relationship between high and low ion flux counts and high and low compound concentrations in either
groundwater and soils does exist, the actual concentration of a compound in the subsurface can not be judged solely
by ion flux counts. The isopleth contour maps of ion flux counts, therefore, should not be confused with actual soil
gas concentration but should be considered only as an indication of relative compound concentration.
Trichloroethane
Trichloroethane was detected in the area surrounding Building E-515 (Figure 4-11). The trichloroethane
contamination is associated with the "acid drain'' at E-515. Additional areas of minor tetrachloroethane
contamination exists to the south and southeast of Building E-515.
Trichloroethylene
Trichloroethylene was detected only in collectors 134 and 133 at the "acid drain" at Building E-515 (Figure 4-12).
Tetrachloroethene
Tetrachloroethene was not detected in the soil gas survey at Building E-515 (Figure 4-13).
Hydrocarbons
Hydrocarbons were not detected in the soil gas survey at Building E-515 (Figure 4-14).
4.1.5.4.2 Zone(s) of Contamination
The relative uniformity of petroleum hydrocarbon concentrations detected at the FVD under Stage 1 sampling
suggest a non-point source. Lack of confirmation under Stage 2 sampling, however, indicates that the petroleum
hydrocarbons detected may not be due to non-point source activities. The lack of confirmation may be due to
individual sample variability between the two sampling periods, the detection of a petroleum hydrocarbon release
event which has since dissipated, or that the decrease in petroleum hydrocarbon concentration may be due to natural
degradation.
Stage 2 sampling indicated the widespread occurrence of low concentrations of 1,1,1-trichloroethane in surface
sediments. Very low concentrations of methylene chloride and vinyl chloride were sporadically detected in samples
from deep stratigraphic borings. The source of the 1,1,1-trichloroethane present in the FVD is unknown. During
both Stage 1 and Stage 2 sampling, the FVD was dry. No surface water samples were collected.
4-65
P78-914/P784B.66
02/14/92
For further evaluations all contaminant detections (Stage 1 and Stage 2) will be considered. The zone of
contamination associated with the soil and surface sediment is considered to involve only the FVD thus, further
analyses of surface contamination for the site will involve only the FVD.
One groundwater sample was collected from momtoring well P-1 under Stage 1 and contained no detectable organic
compounds. Three groundwater samples, one from momtoring well P-1 and two from monitoring well P-9 at E-515
were collected under Stage 2. Both momtoring wells P-9 and P-1 contained detectable concentrations of organic
compounds. The sample collected from monitoring well P-1, however, was later detennined to have been possibly
cross-contaminated during sampling and the results unusable.
Until 1989, wastewater disposal practices at Plant 78 consisted of disposal into surface ditches, subsurface dry wells,
and into a surface holding and evaporation pond (SSTEP). Over this approximately 30-year time period, the
groundwater mound would have probably reached a maximum many years before the installation of groundwater
monitoring well P-1. Momtoring well P-1 did not have any evidence of orgamc compound contamination when
sampled under Stage 1. It is unlikely that contaminated groundwater identified at momtoring wells P-8 and P-9,
in conjunction with the groundwater mounding, would suddenly reach upgradient into the monitoring well P-1 area
of Plant 78 when momtoring well P-1 was resampled under Stage 2.
Five samples collected from borings E-515B1 and E-515B2 contained very low concentrations of methyl chloride
and vinyl chloride. These detections were within the method detection range but below the Practical Quantation
Limit (PQL) for these analytes.
Subsurface contamination at the FVD and Building E-515 consists only of contaminated groundwater. The E-515
soil gas survey indicates that the lateral extent of possible groundwater contamination exceeds the area monitored
by momtoring well P-9. Figure 4-14 shows the aerial extent of the contaminant plume indicated by both
groundwater sampling and soil gas detections for the north end of Plant 78. The E-515 soil gas survey indicates
that contamination observed in the groundwater at momtoring well P-9 is continuous with groundwater contamination
observed along the northern end of Plant 78. Groundwater contamination does not extend upgradient of momtoring
well P-9 at the Plant 78 complex.
4.1.5.4.3 Contamination Migration
Contamination migration is discussed in detail in Section 4.2.3.
Spatial and temporal variability in the soil and surface concentration of contaminants was observed at the FVD.
As discussed in Section 4.1.5.4, surface sediment and soil boring analyses of Stage 1 and Stage 2 samples yielded
varying results. Petroleum hydrocarbons present in soil samples from boring 200B were not observed in either
4-66
P78-914/P784B.67
02/14/92
Stage 1 or Stage 2 sampling. 1,1,1 -Trichloroethane was detected in all the FVD surface samples under Stage 2 but
was not observed during Stage 1.
Only one sampling episode was conducted at groundwater momtoring well P-9. The extent of spatial and temporal
variability for this contamination is not fully characterized.
4.1.6 DISCUSSION OF RESULTS FOR THE M-585 FRENCH DRAIN SITE
The geologic and hydrogeologic investigation at M-585 consists of work conducted under both Stage 1 and Stage 2.
Eight 50-foot stratigraphic borings (50A through 50F) and one deep boring (200A) were drilled during Stage 1.
Boring 200A was converted to groundwater monitoring well P-2. Two deep borings were drilled under Stage 2.
M-585B1 was drilled to 91 feet and was completed as groundwater momtoring well P-6. M-585B2 was drilled to
90 feet and was completed as groundwater momtoring well P-7. Figures 3-10 and 3-11 are boring profiles and well
construction diagrams for these wells. A determination of hydraulic conductivity was made on momtoring
wells P-2, P-6, and P-7 by slug/bail aquifer testing.
4.1.6.1 M-585 French Drain Geology
Borings M-585B1 and M-585B2 both encountered heterogeneous lake clays and gravel sediments at the Lake
Bonneville Group. M-585B1 encountered yellow-brown to dark gray (10 YR 5/4 to 10 YR 4/1), interbedded sandy
and silty clays, clayey sands and silts, and silty and sandy gravels. Clays and silts are slightly moist, nonplastic,
and have a mottled texture. The gravels consists of subrounded to slightly angular pebble sized clasts of grey (10
YR 4/1) limestone and dolostone, and light brown (10 YR 5/3) sandstone. Boring M-585B2 encountered 15 to
30 feet thick of yellow brown to light yellow brown (10 YR 5/4 to 10 YR 6/4) sandy and silty clay, interbedded
with poorly sorted to graded, angular to subround, pale yellow (2.5 YR 8/2) silty and clayey gravels. Clays and
silts are slightly moist. The gravels are comprised of pebbles of limestone, dolostone and sandstone.
Thickness of gravel beds penetrated at boring 200A were approximately 120 feet. Interbedded gravel, sand, and
silt was observed in a correlative zone in M-585B1. (See cross-section, Figure 4-23.) These thick gravel beds
appear to have been deposited in an alluvial depositional system. Thick clay-rich gravel beds suggest deposition
in the proximal facies of an alluvial fan complex with an easterly sediment source.
4.1.6.2 M-585 French Drain Hydrogeology
Monitoring well P-2 was installed under Stage 1 and was screened from 177.1 to 156.6 feet in a sand-rich gravel
zone. A groundwater level was measured at a depth of 130 feet (4,409.21 feet above MSL) at the time of
completion. This elevation is consistent with the level observed during Stage 2, 128.35 feet (4,412.00 feet above
MSL). Monitoring well P-6 was screened from 70 to 90 feet in a sand and clay rich gravel zone. Static
groundwater level was measured at 76.1 feet (4,469.00 feet above MSL) at the time of completion (January 1989).
4-67
NORTHEAST
(M-585B2)
P-6 4540.93'
STj SD ( GR
(200A)
P-2 4539.21'
CL ST SD. GR J I I l
* • *
76T(4469'MSL} 3-14-89
128.35 J-
(4412'MSO
1-31-89
SOUTHWEST
(M-585B2)
P-7 4529.52'
CL/SC
4540'-,
CL,ST| SD| GR
CL
4420-
4-XXf-
4360-1
LOCATION OF CROSS-SECTION E-P
IS SHOWN ON RGURE 4-4
EXPLANATION
CLAY Consists of silty and sandy clays. Uses classification CL
SILT Consists of clay rich silts and
sands. Uses classification MI-
SAND Consists of clay rich sands, silty
sands. Uses classifications
SC, SL, and SM.
GRAVEL Consists of poorly sorted clay rich gravels. Uses classifications
GC, GM, and GP.
CL' Clay ST Silt
SD Sand
GR Gravel
RELATIVE
GRAIN SIZE:
72.47 Water Level
(4456.3 MSU Measurement
2-1-89 Date of Measurement
(M-585B1)
P-6 4SOSX
20'-,
*>
H
0
2 io--{
o
c
>
Boring Number
VM number and* ground surface eievcHoo.
5-
I I I 1
40'
Horizontal Scale
Figure 4-23
GEOLOGICvUYDROGEOLOGIC CROSS-
SECTION E-E', M-585 FRENCH DRAIN SITE
SOURCE: ESE. 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
A-f.9.
P78-914/P784B.69
02/14/92
Monitoring well P-7 was screened from 67 to 86.5 feet also in a clay and silt rich gravel. Static groundwater level
was measured at 72.47 feet (4,456.30 feet above MSL) at the time of completion (January 1989).
Monitoring wells P-6 and P-7 are screened within the upper shallow groundwater zone (Figure 4-2). Groundwater
flow direction at M-585 is west-southwest towards Blue Creek with an estimated groundwater gradient of
approximately 0.026 foot/foot.
Monitoring well P-2 is screened within the lower shallow groundwater zone (Figure 4-3). This deeper zone at
M-585 shows evidence of semi-confined to confined conditions. It is unclear if P-2 is tapping the regional shallow
Blue Creek Valley aquifer observed at monitoring well P-1. Monitoring well P-2 has a water level measurement
of 4,412.00 MSL where as monitoring well P-1 has a water level measurement of 4,334.87 MSL. This is a
difference of 77.13 feet and would require a reversal of groundwater flow direction counter to the Blue Creek
Valley regional trend, which is approximately north to south. The higher water level in momtoring well P-2 may
have its source from wastewater discharge activities at Building M-585.
4.1.6.2.1 Aquifer Testing
Aquifer tests were performed on momtoring wells P-2, P-6, and P-7 to determine horizontal hydrauhc conductivity
according to the procedures and limitations described in Section 3.5.6.
Solving for V, monitoring well P-2 with has a V of 0.43 fpd. Converting fpd to fpy indicates that groundwater
at monitoring well P-2 could travel 157 fpy. Monitoring well P-6 was a groundwater velocity of V = 0.63.
Converting fpd to fpy indicates that groundwater at momtoring well P-6 could travel 230 fpy. Monitoring well P-7
has a range of groundwater velocity determinations from a V of 1.21 to 0.76 fpd. Converting fpd to fpy indicates
that groundwater at monitoring well P-7 could travel from 277 to 441 fpy.
4.1.6.3 Analvtical Results
Deep boring soil and groundwater samples were collected at M-585. In addition, two soil gas surveys were also
conducted at the French Drain. The following is a discussion of the results by sample type matrix.
4.1.6.3.1 Deep Stratigraphic Boring Samples
Seven soil samples were collected from the two deep stratigraphic borings (M-585B1 and M-585B2). Figure 4-24
shows the locations of these borings and Table 4-18 lists the analytical detections for these samples.
4.1.6.3.2 Groundwater Samples
Three groundwater samples were collected at M-585 for water quality analysis from monitoring wells P-2, P-6,
and P-7. The location of these monitoring wells are shown on Figure 4-25 and Table 4-19 lists analytical detections
for these.
4-69
P78 STAGE 2 03/91
Bore Sample
M-585B1A
M-585B1B
Duplicate
M-585B1C
M-585B1D
Duplicate
METHOD
Depth |compound|mg/kg| BLANK
26 ft
52 ft
52 ft
76 ft
89 ft
89 ft
ND
ND
ND
ND
TCE
TCE
ND
ND
ND
ND
0.298
0.199
W
ND
ND
ND
ND
ND
ND
M-585B2
Method
Bore Sample | Depth| Compound mg/kg Blank
M-585B2A
M-585B2B
Duplicate
M-585B2C
26 ft
51 ft
51 ft
75 ft
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
LEGEND
• M-585B2 - BORE SAMPLE LOCATION
0 100 200 300 400 500 1000 feet
Figure 4—24
STAGE 2 DEEP STRATIGRAPHIC
BORING RESULTS, M585 FRENCH
DRAIN
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-70
Table 4-18. Stage 2 Analytical Results for Deep Stratigraphic Boring Samples, M-585 French Drain Site.
P78-914/P78T4-18.1
02/14/92
Chemical
Parameter
(mg/kg) (ppm)
M-585B1A M-585B1B M-585B1C M-585B1D
(25ft) (51ft) (75ft) (89ft)
1/11/89 1/12/89 l/l2/89 1/12/89
P78-S*57 P78-S*58 P78-S'59 P78-S*60
Duplicate
M-585B1D
(89ft)
1/12/89
P78-S*85
M-585B2A
(26ft)
1/19/89
P78-S*64
M-585B2B
(51ft)
1/20/89
P78-S*65
Duplicate
M-585B2B
(51ft)
1/20/89
P78-S«86
M-585B2C
(76ft)
1/20/89 Method
P78-S'66 Blank
Petrol. Hydrocarbons
Benzene
Toluene
Ethylbenzene
Total Xylenes
Bromobenzene
Bromodichloromethane
Bromoform
Bromomethane
Carbon Tetrachloride
Chlorobenzene
NA NA NA NA NA NA NA NA NA NA
Chloroethane
2-Chloroethylvinyl Eether
Chloroform
1-Chlorohexane — — — — — — — _ _
Chloromethane NA NA NA NA NA NA NA NA NA NA
Dibromochloromethane — - - - — - _
Dibromomethane — — — — — — — — _ _
Dichlorobenzene __ __ _ _ __ _
1,1-Dichloroethane _ .. — _ _ _ __
1.1- Dichloroethylene — — — — — — _
1.2- Dichloroethane — - - - - — - - __
t-l,2-Dichloroethene - - - - - - - - - _
1,2-Dichloropropane — — — — — — — — — —
Cis-l,3-Dichloropropene — — — — — — — — — —
t-l,3-Dich!oropropene - — - — - — .... _ _
Dichlorodifluoromethane — — - — - — - — — -
Dissolved Solids NA NA NA NA NA NA NA NA NA NA
Methylene Chloride — - - - - — - — —
1,1,1,2-Tetrachloroethane -
1,1,2,2-Tetrachloroethene __________
Tetrachloroethene — - - - - _ __ __
1.1.1- Trichloroethane - - _ _ _
1.1.2- Trichloroethane - - - -
Trichloroethylene - 0.298 0.199
Trichlorofluoromethane — — _ _
Trichloropropane — - - - -
Vinyl Chloride _____
= Not detected above instrument detection level NA = Not Analyzed
P78 STAGE 2 05/91 PFIG4-21
Compound
Vinyl Chloride
T-1.2-DCE
PCE
Trichlorofluromethane
Benzene
Toluene
Chlorobenzene
1,2-DCA
1,1-DCA
1,1-DCE
"1,1,1-TCA
TCE
ug/L
0.511
1.12
1.48
5.72
14.8
23.2
25.2
40.2
110
690
1030
1890
METHOD
BLANK
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
WELL P-7
Compound
Benzene
Chlorobenzene
1.1- DCA
1.2- DCA
1,1-DCE
TCE
Chloroform
1,1,1-TCA
ug/L
3.77
4.47
14.4
76.2
931
1580
2580
3320
METHOD
BLANK
ND
ND
ND
ND
ND
ND
ND
ND LEGEND
• WELL P-7 - GROUNDWATER MONITORING WELL
0 100 200 300 400 500 1000 feet
Figure 4-25
STAGE 2 GROUNDWATER ANALYTICAL
RESULTS, M-585 FRENCH DRAIN
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-72
Table 4-19. Stage 2 Analytical Results for Ground Water Samples, M-585 French Drain Site (Page 1 of 2).
P78-914/P78T4-19.1
02/14/92
Y1W22 P78-W23 P78-W24 P78-W22 P78-W*23 P78-W*24
Chemical Parameter P6 P7 P2 Method Chemical Parameter P6 P7 P2 Method
Mg/L (ppb) 1/24/89 1/28/89 1/29/89 Blank ng/L (ppb) 1/24/89 1/28/89 1/29/89 Blank
Petrol. Hydrocarbons
Benzene
Toluene
Ethylbenzene
Total Xylenes
Bromobenzene
Bromodichloromethane
Bromoform
Bromomethane
Carbon Tetrachloride
Chlorobenzene
Chloroethane
2-ChloroethylvinyI Ether
Chloroform
1-Chlorohexane
Chloromethane
Dibromochloromethane
Dibromomethane
Dichlorobenzene
1,1-Dichloroethane
1.1- Dichloroethylene
1.2- Dichloroethane
t-l,2-Dichloroethene
1,2-Dichloropropane
Cis-l,3-Dichloropropene
t-1,3-Dichloropropene
Dichlorodifluoromethane
Dissolved Solids
Methylene Chloride
1,1,1,2-Tetrachloroethane
1,1,2,2-Tetrachloroethene
Tetrachloroethene
1.1.1-Trichloroethane
1.1.2- Trichloroethane
Trichloroethene
Trichlorofluoromethane
Trichloropropane
Vinyl Chloride
14.6
23.2
3.77
25.2 4.74
2580 1.00
110
690
40.2
1.12
950
1.48
1030
1890
5.72
0.511
14.4
931
76.2 0.705
7770
3320
1580
1040
0.266
Acenapthene
Acenapthylene
Acetophenone
Aniline
Anthracene
4-Aminobiphenyl
Benzidine
Benzo(A)Anthracene
Benzo(B)Fluoranthene
Benzo(K)Fluoranthene
Benzo(A)Pyrene
Benzo(G,H,I)Perylene
Alcohol
Benzoic Acid
Butyl Benzyl Phthalate
Bis(2-Chloroethyl) Ether
Bis(2-Chloroethoxy) Methane
Bis(2-Ethylhexyl) Phthalate
Bis(2-Chloroisopropyi) Ether
4-Bromophenyl Phenyl Ether
4-Chloroaniline
1- Chloronaphthalene
2- Chloronaphthalene
2-Chlorophenol
4-Chloro-3-Methylphenol
4-Chlorophenylphenyl Ether
Chrysene
Dibenz(A,J) Acridine
Dibenzo(A,H) Anthracene
Dibenzofuran
Di-N-Butylphthalate
1.3- Dichlorobenzene
1.2- Dichlorobenzene
1.4- Dichlorobenzene
3.3- Dichlorobenzidine
2.4- Dichlorophenol
Table 4-19. Stage 2 Analytical Results for Ground Water Samples, M-585 French Drain Site (Page 2 of 2).
P78-914/P78T4-19.2
02/14/92
P78-W22 P78-W23 P78-W24 P78-W22 P78-W23 P78-W24
Chemical Parameter P6 P7 P2 Method Chemical Parameter P6 P7 P2 Method
Ug/L (ppb) 1/24/89 1/28/89 1/29/89 Blank ,tg/L (ppb) 1/24/89 1/28/89 1/29/89 Blank
Diethylphthalate
P-Dimethyllaminobenzene
7,12-Dimethylbenz(A) Anthrance
A-A-Dimethylphenethylamine
2,6-Dichlorophenol
2,4-Dimethylphenol
Dimethylphthalate
4,6-Dinitro-2-Methylphenol
2,4-Dinitrophenol
2,4-Dinitrotoluene
2,6-Dinitrotoluene
Diphenylamine
1,2-Diphenylhydrazine
Ethyl Methanesulfonate
Di-N-Octylphthalate
Fluoranthene
Fluorene
Hexachlorobenzene
Hexachlorobutadiene
Hexachlorocyciopentadiene
Hexachloroethane
Indeno(l,2,3-CD) Pyrene
Isophorone
3-Methylcholanthrene
Methyl Methanesulfonate
2-Methylnaphthalene
Naphthalene
1- Naphthylamine
2- Naphthylamine
2- Nitroaniline
3- Nitroaniline
4- Nitroaniline
Nitrobenzene
N-Nitorso-Di-N-Butylamine
N-Nitrosodimethylamine
N-Nitrosodiphenylamine
N-Nitrosopiperidine
Pentachlorobenzene
Pentachloronitrobenzene
Phenacetin
2-Methylphenol
4-Methylphenol
2-Nitrophenol
4-Nitrophenol
N-Nitrosodi-N-Propylamine
Pentachlorophenol
Phenanthrene
2-Picoline
Pronamide
Phenol
Pyrene
1.2.4.5-Tetrachlorobenzene
1.2.4- Trichlorobenzene
2.3.4.6-Tetrachlorophenol
2.4.5-Trichlorophenol
2.4.6- Trichlorophenol
= Not detected above instrument detection level
P78-914/P784B.75
02/14/92
4.1.6.3.3 Soil Gas Samples
Seventy-five PETREX™ soil gas collectors were installed at M-585 for soil gas survey 1 (Figure 4-26). Sixty-six
soil gas probes were installed at M-585 during soil gas survey 2 (Figure 4-27).
4.1.6.4 Discussion of Analvtical Results for M-585
4.1.6.4.1 Significance of Findings
Metals and inorganic constituents were determined for M-585 samples during Stage 1. Major element groundwater
composition from monitoring well P-2 is consistent with concentrations observed in the FVD background momtoring
well (P-1). Metal concentrations in soil samples were comparable to background samples collected from the FVD
(boring 200B), and were within reported ranges of representative U.S. concentrations. These parameters were not
analyzed for during Stage 2.
Determination of orgamc analytes in soil samples collected during Stage 1 indicated the presence of low
concentrations of petroleum hydrocarbons. Methylene chloride was also observed in three samples. Groundwater
chemical analyses from monitoring well P-2 contained low concentrations of chloroform, methylene chloride,
1,1,1-trichloroethane, and toluene.
DEEP STRATIGRAPHIC BORING ANALYTICAL RESULTS
Two soil samples (standard and duplicate) taken from boring M-585B1 at 89 feet contained low concentrations of
trichloroethylene (0.298 mg/kg and 0.199 mg/kg, respectively). All other soil samples collected from M-585 deep
borings contained no detectable organic analytes. The low levels of petroleum hydrocarbons detected in Stage 1
boring sampling were not confirmed by Stage 2 sampling.
GROUNDWATER ANALYTICAL RESULTS
All groundwater samples from momtormg wells P-2, P-6, and P-7 contained detectable concentrations of chlorinated
solvents. Samples collected from momtoring wells P-6 and P-7, however, contained much higher concentrations of
these contaminants than did the sample from momtoring well P-2.
Monitoring Well P-2
Chloroform, 1,2-dichloroethane, and 1,1,1-trichloroethane were detected at low concentrations in monitoring
well P-2. Only chloroform exceed the EPA 10"* HHRC.
Monitoring Well P-6
Tetrachloroethene, trichlorofluromethane, benzene, chlorobenzene, 1,2-dichloroethane, 1,1-dichloroethene,
1,1,1-trichloroethane, t-l,2-dichloroethene, vinyl chloride, toluene, 1,1-dichloroethane, and trichloroethylene were
detected in momtoring well P-6. Benzene, 1,1-dichloroethene, 1,2-dichloroethane, 1,1,1-trichloroethane, and
4-75
Figure 4-26
SOIL GAS SAMPLE LOCATION
M-585 FRENCH DRAIN
SOURCE: PETREX, 1989
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-76
P78 STAGE 2 05/91 PFIG 4-23
SOLVENT STORAGE
WASTE SOLVENT STORAGE
M-585
N
LEGEND
± MONITORING WELL 0 100 300 500
• SOIL GAS SURVEY
PROBE LOCATION
Figure 4—27
M-585 SOIL GAS SURVEY
NUMBER 2 GRID
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-77
P78-914/P784B.78
02/14/92
trichloroethylene, exceed MCLs. Chlorobenzene, tetrachloroethane, and trichlorofluromethane exceed EPA 10-*
HHRC. 1,1-Dichloroethane was also detected at a high concentration, however, there is no MCL or IO"6 HHRC
for this compound.
Monitoring Well P-7
Benzene, chlorobenzene, 1,1-dichloroethene, 1,2-dichloroethane, 1,1-dichloroethane, trichloroethylene, chloroform,
and 1,1,1-trichloroethane were detected in monitoring well P-7. Concentrations of 1,1-dichloroethene,
1,2-dichloroethane, 1,1,1-trichloroethane, and trichloroethylene exceed MCLs. Benzene and chloroform were
detected at concentrations, which exceed EPA 10"* HHRC.
The northern extent of soil gas contamination identified at M-585 extends approximately 100 feet to the north of
monitoring well P-6. The source of this contamination appears to be related to a septic tank leach field for
wastewater from Building M-585. The western end of the potential groundwater contamination plume probably
coincides with the soil gas detections mapped approximately 300 feet west of momtormg well P-7. It is believed
that this contamination originated at the M-585 French Drain.
SOIL GAS SURVEYS 1
Soil gas survey 1 utilizing Petrex™ soil gas collectors was conducted to further define the area! extent of soil and
water contamination identified during Stage 1, to investigate a southwest trending anomaly identified by an
electro-magnetic survey conducted during Stage 1 and, to assist in locating sites for two additional groundwater
monitoring wells (P-6 and P-7) to be installed under Stage 2.
Data collected by the Petrex™ soil gas method are displayed in the form of isopleth contour maps based upon the
ion count flux recorded for each compound or mixture of compounds identified at each sample location. Although
a relationship between high and low ion flux counts and high and low compound concentrations in either
groundwater and soils does exist, the actual concentration of a compound in the subsurface can not be judged solely
by ion flux counts. The isopleth contour maps of ion flux counts, therefore, should not be confused with actual soil
gas concentration but should be considered only as an indication of relative compound concentration.
Trichloroethylene
The trichloroethylene map (Figure 4-28) shows three anomalies. The main anomaly is centered around the French
Drain where very high ion flux counts are present. This anomaly extends to the southwest. A second anomaly is
present due north of the French Drain where a high ion flux count was recorded at collector 28. This anomaly
extends towards the southwest to the edge of the survey. The third anomaly is located at the southwest end of the
M-585 soil gas survey area.
4-78
t
• £830
• 14C
• 4013
• 2942 • 178
Q 3602
• 1918 • 2167
• 309
O 3182
• 1122
LEGEND
• P-2 Ground Water Monitoring
Well Location
• Soil Gas Sample Location
50 100
FEET
Igure 4-28
SOIL GAS SURVEY, TRICHLOROETHYLENE
(TCE) ION FLUX, M-585 FRENCH DRAIN SITE
SOURCE: Petrex. 1989
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-79
P78-914/P784B.80
02/14/92
Anomaly two appears to be related to a septic sewer leach field for wastewater from Building M-585 and is not
related to the French Drain. The groundwater flow at M-585 is to the southwest and contamination originating at
the French Drain would migrate to the southwest.
Anomaly three is located at the west boundary of the survey and is separated from the other two anomalies by low
concentration areas. The relative concentration of ion flux for this anomaly suggests that the concentration of
trichloroethylene contamination may be increasing to the southwest.
Trichloroethane
The trichloroethane map (Figure 4-29) shows three anomalies. There are two areas of high ion flux, one closest
to the French Drain indicated by collectors 75, 15, and 4, and one directly southwest, indicated by collectors 42,
43, 49, 71, and 72. A third anomalous area is located due north of the French Drain. These high ion count areas
correspond very well to the trichloroethylene anomalies observed and also suggest an additional source of
contamination at M-585 related to the septic leach field.
Tetrachloroethylene
The tetrachloroethylene map (Figure 4-30) shows two anomalous areas. The first is centered around and to the
southwest of the French Drain. The second is an isolated high at collector 39 on the west end of the survey grid.
High ion flux counts at collectors 27, 28, and 30, located to the north and northwest of the French Drain, indicate
a second source of tetrachloroethylene contamination related to the septic tank leach field. The high ion count for
collector 39 is isolated. This high reading, however, does correspond with the western terminus of the second
anomaly identified for trichloroethylene.
Chloroform
The chloroform flux map (Figure 4-31) shows one very well defined anomaly centered around and directly
southwest of the French Drain. Levels of chloroform flux diminish rapidly to background levels within a short
distance of the French Drain. Chloroform does not appear to be associated with the septic tank leach field, as
indicated by the three other compounds.
SOIL GAS SURVEY 2
The results of soil gas survey 1 (Stage 2) led to the identification of two areas of possible contamination other than
the French Drain, one located north of the French Drain, and one located to the southwest. Groundwater sampling
at these two locations (momtoring wells P-6 and P-7) confirmed contamination in these areas. The investigations
indicate that contaminant levels increase at the survey boundaries. Therefore, a second soil gas survey (Stage 2)
was conducted to investigate the aerial extent of this contamination.
4-80
• 10278
• 15244 • 138*6
I • 9042
_ 36550
n 27120 • 49478
• 12668
• 37238
O 70266 p_2 D 49836
_* 28168
• Vmy*^ Q194629
/o 95741 / y**™
_*7795 ^Oj A 6150
I ° 3051 o
/ DM343
• 63254
• 3182
• 2230
• 13727
• 862
a 682
• 1328
• 1519
• 837
• 4945 • 9391 • 1456
• 529
• 1372
• 5920 a 839
• 906
• 1402
• 1122
• 734
Q 1925
D 1799
LEGEND
P-2 Ground Water Monitoring
Well Location
• Soil Gas Sample Location
50 100
FEET
Figure 4-29
SOIL GAS SURVEY, TRICHLOROETHANE
(TCA) ION FLUX, M-585 FRENCH DRAIN SITE
SOURCE: Petrex, 1989
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-81
• 144
• 529
P-6
O 916
d 317
D 434
D 210
• 0
• 172
a 198
a o
a 217 • 396 • 368
a o
a 132
a 2M
a • • 104
• 739 • 226
O 288 • 406 a 160
• 0
• Ul
• 190
• 102 • 134
• 221 • 0
• 161 • 293
_ 270 #p*7
• 200
• 141
LEGEND
• P-2 Ground Water Monitoring
Well Location
• Soil Gas Sample Location
0 50 100
1 1 I
FEET
O 420
Figure 4-30
SOIL GAS SURVEY,
ETRACHLOROETHYLENE (PCE) ION FLUX,
M-585 FRENCH DRAIN SITE
SOURCE: Petrex, 1989
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-82
e 40630 fAy*
Xp9Sm6 D103633
85<>y D136Z76#J
ID 91478 ° 78870
4034 X \
D143334 D128001
Q 0
• 0
O 0
O 0
D 0 D 0
a p D 0
a o a o
o o a o
D o a o a o
a o a o a o
a o a o a o
a o a o
a o P-7 a o
a o
LEGEND
P-2 Ground Water Monitoring
Well Location
• Soil Gas Sample Location
50
-J-
100
FEET
Tgure 4-31
SOIL GAS SURVEY. CHLOROFORM
ON FLUX, M-585 FRENCH DRAIN SITE
SOURCE: Petrex. 1989
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-83
P78-914/P784B.84
02/14/92
A total organic vapor map was constructed for the results of this second survey and is shown in Figure 4-32.
Contours are drawn with each interval indicating an increase in the relative organic vapor concentration in ppm.
For comparison, the results for the first soil gas survey are also shown.
North Anomaly
This area was identified by soil gas survey 1. Subsequent groundwater momtoring well sampling (monitoring
well P-6) confirmed chlorinated solvent contamination. Organic vapor detections extend approximately 100 feet
to the north of monitoring well P-6 where soil gas readings drop to background levels. Organic vapor detection
also extended eastward toward Building M-585. Relatively high levels of organic vapors were detected along the
western side of Building M-585.
Western Anomaly
This area was also identified by soil gas survey 1. Sampling of monitoring well P-7 confirmed chlorinated solvent
contamination in groundwater. Organic vapor detection extends in a linear fashion approximately 300 feet to the
southwest from monitoring well P-7. Organic vapor values range from 1.0 ppm along the edge of the plume up
to 30 ppm under the pavement of G Avenue at the end of the survey grid. Organic vapors are generally higher
under pavement. This is probably due to the collection of vapors within the porous road construction materials with
the pavement acting as an impermeable barrier for soil gas dispersion.
Trichloroethylene and trichloroethane were detected at high ion flux in soil gas at M-585. Although
trichloroethylene was the only solvent of these two detected in the Stage 1 groundwater sampling, trichloroethane
is also a commonly used industrial solvent.
The groundwater sample collected from momtoring well P-2 also indicated that chloroform and toluene are present
at low concentrations at the site. Chloroform is commonly present in Plant 78 onsite water, due to the chlorination
for drinking. Chloroform can be a difficult parameter to detect via the PETREX™ soil gas method due to weak
partitioning of chloroform in the vapor phase. The high concentration of chloroform in M-585 groundwater,
however, allows for a reliable soil gas detection and suggests that the chloroform is due to site activities.
4.1.6.4.2 Zone(s) of Contamination
Stage 1 sampling demonstrated the presence of methylene chloride and petroleum hydrocarbons in soil samples
collected from borings west of M-585. Stage 2 sampling did not verify the presence of petroleum hydrocarbons
in soil samples collected from borings M-585B1 and M-585B2. One sample collected at a 90-foot depth in boring
M-585B1 contained a low concentration of trichloroethylene. For further evaluations all contaminant detections
(Stage 1 and Stage 2) will be considered. The zone of surface contamination associated with M-585 is considered
to only involve the area delineated by these borings. (Refer to Section 4.2.2.)
4-84
P78 STAGE 2 05/91 PFIG4-28
1
LEGEND
A MONITORING WELL
SOIL GAS SURVEY 1 SHOWN BY DOTS
CONTAMINANT PLUME SHOWN BY PATTERN
W
SOIL GAS SURVEY 2
SHOWN BY NUMBERS
ORGANIC VAPOR IN ppm
100 300 500
Figure 4-32
STAGE 2 SOIL GAS SURVEY
RESULTS M-585 FRENCH DRAIN
SITE
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-85
P78-914/P784B.86
02/14/92
Subsurface contamination at M-585 consists of contaminated groundwater. Two soil gas surveys conducted under
Stage 2 indicate that the lateral extent of possible groundwater contamination exceeds the area monitored by
wells P-2, P-6, and P-7. Figure 4-33 shows the aerial extent indicated by both groundwater sampling and soil gas
detections for M-585. This aerial extent is the zone of contamination associated with the subsurface contamination
at M-585 (Refer to Section 4.2.2).
4.1.6.4.3 Contamination Migration
Contamination migration is discussed in detail in Section 4.2.3.
As discussed in section 4.1.6.4, surface sediment and soil boring analyses of Stage 1 and Stage 2 samples yielded
varying results. Petroleum hydrocarbons present in soil samples from boring 200A, and borings 50A through 50F
were not observed in Stage 2 subsurface sampling. Methylene chloride detected in borings 50E and 50F was not
detected in the other 50-foot borings or in boring 200B during Stage 1 and was not detected in any Stage 2 samples.
Trichloroethylene detected in two samples from boring M-585B1 (two samples collected at 89 feet) under Stage 2
was not detected in any of the Stage 1 sampling.
Sampling of momtoring well P-2 was conducted under both Stage 1 and Stage 2. No important variance in
contaminant content was observed between these two sampling episodes. Only one sampling episode was conducted
at groundwater monitoring wells P-6 and P-7. The extent of spatial and temporal variability for this contamination
is not fully characterized.
4.1.7 DISCUSSION OF THE RESULTS FOR BLUE CREEK
4.1.7.1 Blue Creek Geology
No site specific geological investigation was conducted at Blue Creek. Six shallow soil borings were sampled to
investigate potential surface and subsurface contamination along the creek.
4.1.7.2 Blue Creek Hydrogeology
No groundwater momtoring wells were installed at Blue Creek under Stage 1 or Stage 2 investigations.
4.1.7.3 Analvtical Results
Surface water, surface sediment, and soil samples were collected at Blue Creek during Stage 2 investigations. The
following is a discussion of the results by sample type.
4.1.7.3.1 Surface Water Samples
Twenty-four surface water samples were collected for analysis from Blue Creek. Figures 4-34 and 4-35 display
sample locations and a summary of detectable analytes in surface water samples. Tables 4-20 and 4-21 list
analytical detections for surface water samples collected at Blue Creek.
4-86
P78 STAGE 2 05/91
LEGEND
• WELL P-6 -GROUNDWATER MONITORING WELL
Figure 4-33
LOCATION OF THE GROUNDWATER
CONTAMINANT PLUME, M-585
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
SOURCE: ESE, 1991.
4-87
P78 STAGE 3 05/91 PFIG 4-31
AIR FORCE PLANT 78
1,1,1-TCA 0.304 mg/kg P«1 HC 66.5 mg/kg
XyUmts 3.62 ug/L
1,2-OCA 2.>2 ug/L
PCE 1.43 ug/L
CLCH3 0.472 ug/L
1.2-DCA 8.26 ug/L
1,2-DCP 0.24 ug/L
Pel HY 067 i
CLCHJ 3.74 3.74 ug/L
1,2-DCA 27.7 ug/L 1.2-OCP 1.22 ug/L
2-CHVE 0.73 ug/L
PCE 0.3? ug/L
LEGEND
O SAMPLING EPISODE 1 (DECEMBER 1988)
• SAMPLING EPISODE 2 (MARCH 1990)
s
0 100 MO JOG 400 SOO
Figure 4-34
STAGE 2 SURFACE SAMPLE
RESULTS, BLUE CREEK NORTH
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-88
P7B STAGE 2 OS/91 PFIG 4-32
AIR FORCE PLANT 78
PROPERTY LINE
LEGEND
O SAMPLING EPISODE 1 (DECEMBER 1988)
• SAMPLING EPISODE 2 (MARCH 1990)
0 100 200 SOO 400 500
Figure 4—35
STAGE 2 SURFACE SAMPLE
RESULTS, BLUE CREEK SOUTH
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-89
F78-914/P7_T4-20.1
02/14/92
Table 4-20. Stage 2 Analytical Results for Surface Water Samples, Blue Creek (Round 1, December 1988).
P78-W7 P78-W8 P78-W*9 P78-W*10 P78-W11 P78-W27 P78-W*12 P78-W13 P78-W14 P78-W15 P78-W16 P78-W17 P78-W19 P78-W20 P78-W21
Chemical Parameter BC-SWS1 BC-SWS2 BC-SWS3 BC-SWS4 BC-SWS5 Duplicate BC-SWS6 BC-SWS7 BC-SWS8 BC-SWS9 BC-SWS10 BC-SWS11 BC-SWS13 BC-SWS14 BC-SWS15 Method
Mg/L (ppb) 12/14/88 12/14/88 12/14/88 12/14/88 12/15/88 Sample 12/2/88 12/2/88 12/2/88 12/2/88 12/2/88 12/2/88 12/3/88 12/3/88 12/3/88 Blank
Petrol. Hydrocarbons — — — 147
Benzene _________ ----------
Toluene ------------------
Ethylbenzene - - — - - — - - — ______
Total Xylenes - - - - - 3.62 ------
Bromobenzene —
Bromodichloromethane- - - —
Bromoform — - — —
Bromomethane — — — —
Carbon Tetrachloride — -
Chlorobenzene - - - —
Chloroethane - - — —
2-Chloroethylvinyl Ether - - -
Chloroform - - - 0.608
1-Chlorohexane ____..
f" Chloromethane 3.74 0.472 0.410 - 2.68 2.16 0.453
Dibromochloromethane- -
Dibromomethane — — —
Dichlorobenzene —
1,1-Dichloroethane - - -
1.1- Dichloroethylene - - -
1.2- Dichloroethane - 0.611 0.617
t-l,2-Dichloroethene - -
1,2-Dichloropropane ------ 1.22 0.242 - - 0.623 0.669 - - -
Cis-l,3-Dichloropropene - ----- - ---- ----- —
t-l,3-DichIoropropene ------- --- -- — -- -- - -
Dichlorodifluoromethane ______________
Dissolved Solids 3660 3600 3630 3660 3450 3350 3810 3840 3810 3700 3850 3780 362 3150 3260
Methylene Chloride - - - - - - - - - - - - - -
1,1,1,2-Tetrachloroethane - - - - - _ _ _ _
1,1,2,2-Tetrachloroethene ______________
Tetrachloroethene ______ 0.352 - - 1.43 - - 0.473
1.1.1- Trichloroethane — — — — — — -
1.1.2-Trichloroethane ------ 0.615
Trichloroethene ______
Tricftlorofluoromethane ______
Trichloropropane -
Vinyl Chloride ____________ 0.229
0.733
27.7 8.26 5.76 2.82 14.0 15.5 4_4 4.40 4.81
0.615
— = Not detected above instrument detection levels
P78-914/P784T-21.1
02/14/92
Table 4-21. Stage 2 Analytical Results for Surface Water Samples, Blue Creek Drainage (Round 2,
March 1990).
Duplicate
Oiemical parameter BC-SW3 BC-SW4 BC-SW5 BC-SW6 BC-SW7 BC-SW8 BC-SW9 BC-SW10 BC-SW10 Method
Mg/L (ppb) 3/90 3/90 3/90 3/90 3/90 3/90 3/90 3/90 3/90 Blank
Petrol. Hydrocarbons - -- -- -- --156
Benzene __________
Toluene __________
Ethylbenzene __________
Total Xylenes __________
Bromobenzene __________
Bromodichloromethane __________
Bromoform __________
Bromomethane __________
Carbon Tetrachloride __________
Chlorobenzene __________
Chloroethane __________
2-Chloroethylvinyl Ether __________
Chloroform __________
1-Chlorohexane __________
Chloromethane __________
Dibromochloromethane __________
Dibromomethane __________
Dichlorobenzene __________
1,1-Dichloroethane __________
1.1- Dichloroethylene __________
1.2- Dichloroethane __________
t-1,2-Dichloroethene __________
1,2-Dichloropropane __________
Cis-l,3-Dichloropropene __________
t-1,3-Dichloropropene __________
Dichlorodifluoromethane __-_____ — —
Dissolved Solids __________
Methylene Chloride _________ 0.415
1,1,1,2-Tetrachloroethane __-____ — _-
1,1,2,2-Tetrachloroethene __________
Tetrachloroethene __________
1.1.1- Trichloroethane __________
1.1.2- Trichloroethane __________
Trichloroethene __________
Trichlorofluoromethane __________
Trichlorop ropane __________
Vinyl Chloride __________
— = Not detected above instrument detection level.
* = Not analyzed
4-91
P78-914/P784B.92
02/14/92
4.1.7.3.2 Surface Sediment Samples
Sixteen surface sediment samples were collected from Blue Creek. Figures 4-34 and 4-35 display sample locations
and sumn__rizes detectable analyte concentrations. Tables 4-22 and 4-23 list analytical detections for surface
sediment samples collected at Blue Creek.
4.1.7.3.3 Shallow Boring Samples
Six shallow soil borings were sampled at Blue Creek. Figure 4-36 displays sample locations and summarizes
detectable analyte concentrations. Table 4-24 lists analytical detections for shallow boring samples from Blue Creek.
4.1.7.3.4 Aquatic Ecosystem Sampling
Blue Creek was sampled at three locations: a site upstream from Plant 78 (BC-AS1), a site near the center of the
drainage on Plant 78 (BC-AS2), and a site downstream from Plant 78 (BC-AS3) (Figure 4-37). Three sediment
samples were collected from each location, and the benthic invertebrates in the sediment identified and counted.
The results of this investigation are presented in Table 4-25. Presented with the raw counts of species numbers are
estimates of diversity (the Shannon-Wiener Index), a measure of evenness, and the number of taxa in each sample.
Samples 1 through 3 are from the upstream samples, 4 through 6 are from the sites near the center of Plant 78, and
samples 7 through 9 are from downstream from Plant 78.
4.1.7.4 Discussion of Analvtical Results for Blue Creek
Metals and inorganic constituents were determined for Blue Creek surface water sediment samples during Stage 1.
All inorganic constituents were found to be below the NIPDWR and NSDWR recommended levels. Major and
minor element chemistry provided no indication of any degradation in water quality between upgradient (BC/NB)
and down gradient (BC-TWS) samples. Metal concentration in sediments and water were found to be comparable
to background samples collected from the FVD, and were within reported ranges of representative U.S.
concentrations. These parameters were not analyzed during Stage 2.
Stage 1 results demonstrated low concentrations of bromoform, chloromethane, methylene chloride,
trichloroethylene, benzene, and petroleum hydrocarbons in surface water samples. The results of the Stage 2
sampling (sampling episode 1) only verified the presence of chloromethane in Blue Creek surface waters.
Compounds detected in Stage 2 surface waters (episode 1) are chloroform, xylenes, chloromethane,
2-chloroethylvinyl ether, 1,2-dichloroethane, 1,2-dichloropropane, tetrachloroethane, 1,1,1-trichloroethane,
1,1,2-trichloroethane, and vinyl chloride. Surface water samples collected for sampling episode 2 had no detectable
constituents.
Stage 1 sampling of Blue Creek surface sediment demonstrated the presence of low concentrations of petroleum
hydrocarbons. Petroleum hydrocarbons were only detected in two of the seven samples collected. Sampling
4-92
Table 4-22. Stage 2 Analytical Results for Surface Sediment Samples, Blue Creek Drainage (Round 1, December 1988).
P78-914/P78T4-22.1
02/14/92
P78-S*50 P78-S'51 P78-S'81 P78-S*52 P78-S'53 P78-S*54 P78-S*55 P78-S'56 Chemical Parameter BC-SS1 BC-SS2 DUPLICATE BC-SS3 BC-SS4 BC-SS5 BC-SS6 BC-SS7 Methoci mg/kg(ppm) 12/14/88 12/15/88 12/15/88 12/2/88 12/2/88 12/2/88 12/2/88 12/2/88 Blank
Petrol. Hydrocarbons - 887 - 66.5 - - 5.75
Benzene — — - - - - .... _
Toluene — — — .... _
Ethylbenzene — — — — — _
Total Xylenes _.. _ ___ __ _
Bromobenzene — — — ~ — —
Bromodichloromethane — — — — — _
Bromoform __ _ ___ _..
Carbon Tetrachloride .... _ _ _ ..
Chlorobenzene _.. _ ___ _.. _
Chloroethane — — — _.. .. __ _
2-Chloroethylvinyl Ether - - - - ....
Chloroform - - - - — - _
1-Chlorohexane _.. _ — „ _
Dibromochloromethane — — ___ .... _
Dibromomethane — — — — —
Dichlorobenzene — — - ___ .... _
1,1-Dichloroethane - - - - - -
1.1- Dichloroethene _.. _ ___
1.2- Dichloroethane — - - - — - _
.-1,2-Dichloroethene — - - - - .. _
1,2-Dichloropropane — — - _.. _ .. _ _
Cis-l,3-Dichloropropene - — - — _.. —
t-1,3-Dichloropropene - - — - - - —
Dichlorodifluoromethane .... - _ _ _ _ _
Methyl Bromide — — — — — —
Methyl Chloride _.. .. ___ __ _
Methylene Chloride - - — — — .... _
1,1,1,2-Tetrachloroethane .... _ _ .. _ _ _
1,1,2,2-Tetrachloroethane - - - - - -
Tetrachloroethylene — - - — - __ _
1.1.1-Trichloroethane - 0.098 0.100 - - 0.642 - 1.02
1.1.2- Trichloroethane - - - ___ __ _
Trichloroethylene — — ___ —
Trichlorofluoromethane — - - — - -
Trichloropropane - - — - - ....
Vinyl Chloride - - - -
- = Not detected above instrument detection level
P78-914/P78T4-23.1
02/14/92
Table 4-23. Stage 2 Analytical Results for Surface Sediment Samples, Blue Creek Drainage (Round 2,
March 1990).
Duplicate
Chemical Parameter BC-SS3 BC-SS4 BC-SS5 BCSS6 BC-SS7 BC-SS8 BC-SS9 BC-SS10 BC-
SS10 Method
mg/kg (ppm) 3/90 3/90 3/90 3/90 3/90 3/90 3/90 3/90 3/90 Blank
Petrol. Hydrocarbons
Benzene
Toluene
Ethylbenzene
Total Xylenes
Bromobenzene
Bromodichloromethane
Bromoform
Carbon Tetrachloride
Chlorobenzene
Chloroethane
2-Chloroethytvinyl Ether
Chloroform
1-Chlorohexane
Dibromochloromethane
Dibromomethane
Dichlorobenzene
1,1-Dichloroethane
1.1- Dichloroethene
1.2- Dichloroethane
t-1,2-Dichloroethene
1,2-Dichloropropane
Cis-1,3-Dichloropropene
t-l,3-Dichloropropene
Dichlorodifluoromethane
Methyl Bromide
Methyl Chloride
Methylene Chloride
1,1,1,2-Tetrachloroethane
1,1,2,2-Tetrachloroethane
Tetrachloroethylene
1.1.1-Trichloroethane
1.1.2- Trichloroethane
Trichloroethylene
Trichlorofluoromethane
Trichloropropane
Vinyl Chloride
— = Not detected above instrument detection level
4-94
P78 STAGE 2 05/91 PFIG 4-33
LEGEND
j_ BC-SB3 -SHALLOW SOIL BORING LOCATION vr<f",r
'Figure 4-36
STAGE 2 SHALLOW SOIL BORING LOCATIONS,
BLUE CREEK
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
Table 4-24. Stage 2 Analytical Results for Shallow Boring Soil Samples, Blue Creek Drainage.
P78-914/P78T4-24.1
02/14/92
P78-S*38 P78-S*39 P78-S*40 P78-S*41 P78-SM2 P78-SM3 P78-S*44 P78-S*82 P78-S*45 P78-SM6 P78-S*47 P78-SM8 P78-SM9
BC-SB1 BC-SB1 BC-SB2 BC-SB2 BC-SB3 BC-SB3 BC-SB4 Duplicate BC-SB4 BC-SB5 BC-SB5 BC-SB6 BC-SB6
Chemical Parameter 12/8/88 12/8/88 12/8/88 12/8/88 12/8/88 12/8/88 12/14/88 Sample 12/14/88 12/5/88 12/5/88 12/5/88 12/5/88 Method
mg/kg (Ppm) 4' 8' 4' 8' 4' 8' 4' 8' 4' 8' 4' 8' Blank
Petrol. Hydrocarbons
Benzene
Toluene
Ethylbenzene
Total Xylenes
Bromobenzene
Bromodichloromethane
Bromoform
Carbon Tetrachloride
Chlorobenzene
Chloroethane
2-Chloroethylvinyl Ether
Chloroform
1-Chlorohexane
Dibromochloromethane — ______ _ _
Dibromomethane - ______ —
•f* Dichlorobenzene - ______ - _
cf
1,1-Dichloroethane - ______ _ _
1.1- Dichloroethene - ______ _ _
1.2- Dichloroethane _______ __
t-l,2-Dichloroethene - ______ _ _
1,2-Dichloropropane - ______ _ _
Cis-l,3-Dichloropropene - ______ — _
t-l,3-Dichloropropene - ______ _ _
Dichlorodifluoromethane — ______ _ _
Methyl Bromide - ______ _ _
Methyl Chloride - ______ _ _
Methylene Chloride - ______ _ _
1,1,1,2-Tetrachloroethane - ______ _ _
1,1,2,2-Tetrachloroethane _______ __
Tetrachloroethylene - ______ _ _
1.1.1-Trichloroethane - ______ 0.113 0.068
1.1.2-Trichloroethane - ______ _ _
Trichloroethylene - ______ _ _
Trichlorofluoromethane — ______ _ _
Trichloropropane
Vinyl Chloride
— = Not detected above instrument detection level
w
i___a__.
LEGEND
-AQUATIC SAMPLE LOCATION
Figure 4—37
STAGE 2 AQUATIC SAMPLE LOCATIONS
BLUE CREEK
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
P78-914/P78T4-25.1
02/14/92
Table 4-25. Stage 2 Species and Total Numbers of Aquatic Invertebrates, Shannon-Wiener Diversity Index, and Evenness in Blue Creek (Page 1 of 2).
Upstream
BC-AS1
Sample Number
Middle
BC-AS2
Sample Number
Downstream
BC-AS3
Sample Number
8 Total All
Tubificidae 224 80 16
Limnodrilus hoffmeisteri 200 96 16
Limnodrilus udekeiamus — — 8
OSTRACODA 65
HYDRA
COLLEMBOLA
Hirundinae
Mooreobdella microstama
HvaUella azteca 2 64 8
Embobdella spp. 1
Aselius spp. — 16
Hydropsychidae — — 8
Hydropsvche spp. — — 8
Hvdropsvche spp. (pupae)
Cheumatopsyche spp.
Cheumatopsvche spp. (pupae)
Svmphitopsvche spp.
Coenagrionidae
40
56
24
1
1
11 4
16
32
32
16
16
24
8
4
4
168
8
12
12
64
16
3
3
1
407
419
33
65
1
1
4
4
279
1
31
17
36
12
85
16
5
8
P78-914/P78T4-25.2
02/14/92
Table 4-25. Stage 2 Species and Total Numbers of Aquatic Invertebrates, Shannon-Wiener Diversity Index, and Evenness in Blue Creek (Page 2 of 2).
Sample Number SAMPLE NUMBER Sample Number
123 456 789 Total All
DIPTERA (Adult) 2 2
Simulium spp. 64 — 40 96 8 44 1 253
Cricotopus bicinctus — — — — — — — 8 — 8
Cricotopus cylindraceus — 256 40 — 8 32 8 — 1 345
Cricotopus trifacia 8 — — — — 16 — — — 24
Paratrichocladius spp. — 80 32 12 80 496 158 118 6 982
Crvtochironomas blarina 8 — — — — — — — — 8
Polvpedilum brevionnematum 112 — — 40 — — — — — 152
Chironomus riparius — — 8 12 — — — — — 20
Paratendipes spp. — — — 12 — — — — — 12
Rheotarvtarsus spp. — — — 4 — — — — — 4
TOTAL IN SAMPLE 628 592 208 215 148 752 206 466 19 3235
SHANNON-WIENER INDEX 1.98 2.15 2.78 2.83 1.87 1.78 1.17 2.53 2.85 (MEAN) 2.22
EVENNESS 0.68 0.86 0.86 0.81 0.64 0.58 0.52 0.78 0.88 (MEAN) 0.76
NUMBER OF TAXA 8 6 10 12 8 9 5 12 10 (TOTAL) 29
NOTE: Numbers presented in column are actual counts of species in elutate. For number per square meter, multiply by 14.3.
P78-914/P784B.100
02/14/92
verified that minor petroleum hydrocarbon contamination does exist around Buildings M-627 and M-697, however,
the widespread occurrence observed by Stage 1 sampling was not confirmed. 1,1,1-Trichloroethane was detected
in low concentrations in three of the seven samples. One of the detection was for sample BC-SS7, which was
collected one-half mile upgradient of Plant 78. Detection of 1,1,1-trichloroethane in surface sediment samples
yielded no consistent pattern. Nine surface sediment samples were collected from Blue Creek under sampling
episode 2. These samples contained no detectable constituents.
Six shallow soil borings were installed along Blue Creek. Only boring BC-SB4 contained detectable concentrations
of 1,1,1-trichloroethane.
Sampling and analysis of the aquatic ecosystem shows that no statistically significant differences were found for any
comparison between the sampling sites. All nine samples collected from Blue Creek were above 0.5 in evenness,
and the mean S-W index for each sample site was above 2.0. While Blue Creek does have low numbers of taxa
and low diversity, it is attributed to the inconsistency of water flow and width of the stream. There is no evidence
from this study of contaminant related adverse effects on the benthic invertebrate community.
The presence of organic compounds such as 1,1,1-trichloroethane and petroleum hydrocarbons in Blue Creek
samples is not inconsistent with the site history, however, the low levels of occurrence and lack of clear verification
by Stage 2 samplings suggests that the different compounds detected during Stage 1 sampling may be due to
sampling variability or that both Stage 1 and episode 1 of the Stage 2 samplings may have delineated a specific
contamination event(s), which were passed through the site. Some of the compounds detected in Blue Creek surface
water (halomethanes) may be attributed to chlorination of the onsite water for drinking purposes or to off-site usage
or disposal not related to Plant 78 (i.e., 1,2-dichloropropane).
Sampling episode 2 of Stage 2 contained no detectable compounds in either Blue Creek surface water or surface
sediment. Lack of detection of any compounds could indicate that the contamination event(s) previously detected
have moved through the site or natural degradation processes (i.e., photolysis, biodegradation, etc.) may have
removed these compounds.
4.1.7.4.1 Significance of Findings
SURFACE WATER ANALYTICAL RESULTS
Stage 1 results for organic analytes in Blue Creek surface water contained low concentrations of bromoform,
chloromethane, methylene chloride, trichloroethylene, benzene, and petroleum hydrocarbons.
Two sampling episodes were conducted during Stage 2 to verify the results of Stage 1 sampling, to investigate the
extent of this contamination, and to obtain samples from Blue Creek upstream of Plant 78 to provide background
chemical levels. Blue creek was sampled at the 14 locations shown in Figures 4-34 and 4-35 in December 1988.
4-100
P78-914/P784B.101
02/14/92
Nine samples were collected for the second sampling episode in March 1990. No orgamc contamination was
observed in the March 1990 sampling, thus, the discussion below pertains to contaminants detected in the first
sampling episode.
2-Chloroethvlvinvl Ether
2-Chloroethylvinyl ether was detected at 0.733 /ig/L in sample BC-SWS6. This compound has no MCL or 10"*
HHRC.
Chloroform
Chloroform was detected in sample BC-SWS4 at 0.608 /ig/L. This compound does not exceed the MCL but does
exceed the EPA 10^ HHRC of 0.19 /tg/L.
1.2-Dichloroethane
The two background surface water samples, BC-SWS15, taken one mile upgradient of Plant 78, and BC-SWS14,
taken one-half mile upgradient of Plant 78, contained detectable levels of 1,2-dichloroethane. The source of
1,2-dichloroethane is unknown. It may be related to a contamination event upstream of BC-SWS15 or to
agricultural or industrial activity(s) on farm land along Blue Creek upstream of Plant 78.
1,2-Dichloroethane was detected in 11 ofthe 14 Blue Creek surface water samples ranging from 0.611 /ig/L to 27.7
/tg/L. Although an upstream source of 1,2-dichloroethane is indicated by the Stage 2 sampling, Plant 78 is a
contributing factor to the 1,2-dichloroethane present in Blue Creek as evidenced by the increase of
1,2-dichloroethane concentrations at BC-SWS11 and BC-SWS6. The 1,2-dichloroethane concentrations exceed the
MCL at sample locations BC-SWS6, BC-SWS7, BC-SWS8, BC-SWS10, BC-SWS11, and BC-SWS13. The
remaining detections except for BC-SWS2 and BC-SWS3 exceed EPA 10-6 HHRC.
Chloromethane
Chloromethane was detected at low concentrations in 6 of the 14 samples collected from Blue Creek. Several
potential sources may exist that could contribute to this contamination. It is present in the onsite water supply, is
commonly used as a catalysts in polymerization processes for resins, used as a laboratory reagent, a component of
propeUants, in the manufacture of herbicides, and as an impurity in industrial solvents. The low concentrations of
chloromethane detected indicate that the chloromethane in Blue Creek is probably due to chlorination of the Plant 78
water supply. All samples collected for episode one which contained concentrations of chloromethane exceed the
EPA 10* HHRC. There is no MCL for chloromethane.
1.2-Dichloropropane
1,2-Dichloropropane was detected in 4 of the 14 samples collected from Blue Creek. The detection of
1,2-dichloropropane is not inconsistent with the Plant 78 history. 1,2-Dichloropropane is commonly used as an
4-101
P78-914/P784B.102
02/14/92
industrial solvent, an additive to gasoline, and as an additive to other solvents such as carbon tetrachloride and
perchloroethane. 1,2-Dichloropropane is also used as an agricultural soil fumigant to control nematodes. The
concentrations detected at Blue Creek are low and since Blue Creek drains an extensive agricultural area above
Plant 78, the presence of 1,2-dichloropropane may be due to offsite agricultural application(s). All
1,2-dichloropropane concentrations do not exceed the MCL of 5 /.g/L.
1.1.1 -Trichloroethane
1.1.1- Trichloroethane was only detected in sample BC-SWS13. The concentration of 0.615 /tg/L is near the method
detection limit for the analysis. This concentration does not exceed the MCL of 200 /tg/L. There is no EPA 10*
HHRC for 1,1,1-trichloroethane.
1.1.2- Trichloroethane
1,1,2-Trichloroethane was only detected in sample BC-SWS6 at a concentration of 0.615 /tg/L. This concentration
just exceeds the EPA 10-* HHRC of 0.6 /tg/L. There is no MCL for 1,1,2-trichloroethane.
Vinyl Chloride
Vinyl chloride was detected in sample BC-SWS13 at 0.229 /tg/L. This concentration is below the EPA 10"6 HHRC
of 2 /tg/L. There is no MCL for vinyl chloride.
Tetrachloroethene
Tetrachloroethene was detected in only 3 of the 14 Blue Creek samples. Samples BC-SWS6, BC-SWS9, and
BC-SWS13 at 0.352 /tg/L, 1.43 /tg/L, and 0.473 /tg/L, respectively. The concentrations observed in BC-SWS6
and BC-SWS13 are below the EPA 10* HHRC of 0.8 /tg/L. The concentration of sample BC-SWS9 exceeds the
EPA 10* HHRC. None of these samples exceeds the MCL of 5 /tg/L.
Total Xylenes
Total xylenes was only detected in sample BC-SWS9 at a concentration of 3.62 /tg/L. This sample does not exceed
the MCL of 1,000 /tg/L.
SURFACE SEDIMENT ANALYTICAL RESULTS
Stage 1 sampling of Blue Creek surface sediment demonstrated the presence of low concentrations of petroleum
hydrocarbons. Two sampling episodes were conducted during Stage 2 to verify the results of Stage 1 sampling,
to investigate the extent of this contamination, and to obtain samples from Blue Creek upstream of Plant 78 to
provide background chemical levels. In first sampling episode, conducted in December 1988. Blue Creek was
sampled at the seven locations shown on Figures 4-34 and 4-35. Nine sediment samples were also collected for
the second sampling episode in March 1990. No organic contamination was observed in the March 1990 sampling,
thus, the discussion below pertains to contaminants detected in the first sampling event.
4-102
P78-914/P784B.103
02/14/92
Petroleum Hydrocarbons
Petroleum hydrocarbons were only detected in two of the seven samples collected. Sampling verified that minor
petroleum hydrocarbon contamination does exist around Buildings M-627 and M-697, however, the widespread
occurrence observed by Stage 1 sampling was not confirmed.
1.1.1 -Trichloroethane
1,1,1-trichloroethane was detected in low concentrations in three of the seven samples collected. Sample BC-SSS
is located near Building M-627 where minor petroleum hydrocarbon contamination was detected in Stage 1 and
Stage 2 sampling. Sample BC-SS7 was collected one-half mile upgradient of Plant 78. Detection of
1,1,1-trichloroethane in surface sediment samples yielded no consistent pattern.
SHALLOW BORING SAMPLES
Six shallow soil borings were installed along Blue Creek. Two samples were collected form each boring at 4- and
8-foot depths. Only shallow boring (BC-SB4) contained contamination.
1.1.1 -Trichloroethane
1,1,1-trichloroethane was detected at low concentrations in both the 4 foot (duplicate sample) and 8 foot samples
collected at the BC-SB4 site located at the intersection of the Thiokol Road and 1500 Street.
AQUATIC ECOSYSTEM SAMPLES
A statistical comparison (Table 4-25) of the three aquatic ecosystem sample sites (Figure 4-37) for evenness,
diversity index, and number of taxa was completed using a Kruskal-Wallace nonparametric procedure. No
significant differences were found for any comparison between the three sites. Shannon-Wiener (S-W) Indices
below 2.0, and evenness measures below 0.5 are indicative of a stressed ecosystem. All nine samples collected
from Blue Creek were above 0.5 in evenness, and the mean S-W index for each sample site was above 2.0. While
Blue Creek does have low numbers of taxa and low diversity, this situation is probably due to the inconsistency of
water flow and width of the stream. There is no evidence from this study of contaminant-related adverse effects
on the benthic invertebrate community.
Most notable on the list of aquatic invertebrate species (Table 4-25) are leaches (Hirundinae and Mooreobdella spp.)
and Black-flies (Sinulium spp.). The remainder of the invertebrate species are common arthropods, crustaceans,
trichopterans, and other dipterans. Fish populations consisted of minnows and dace and were not sampled in this
study.
4-103
P78-914/P784B.104
02/14/92
4.1.7.4.2 Zone(s) of Contamination
Stage 1 surface sampling demonstrated the presence of low concentrations of bromoform, chloromethane, methylene
chloride, trichloroethylene, benzene, and petroleum hydrocarbons. Stage 2 sampling (episode 1) verified the
occurrence of chloromethane and petroleum hydrocarbons. Widespread low concentrations of 1,2-dichloroethane
in surface water samples and 1,1,1-trichloroethane in surface sediment samples were identified under Stage 2
sampling. Stage 2 sampling (episode 2) did not detect any contamination. For further evaluations all contaminant
detections (Stage 1 and Stage 2) will be considered.
No groundwater momtoring wells exist along Blue Creek and the extent of subsurface contamination of the
groundwater, if any, is unknown. One shallow soil boring BC-SB4 contained low concentration of
1,1,1 -trichloroethane.
4.1.7.4.3 Contamination Migration
Contamination migration is discussed in detail in Section 4.2.3
Spatial and temporal variability does exist in the soil and surface concentration of contaminants observed at Blue
Creek. As discussed in Section 4.1.7.4, surface water and sediment analyses of Stage 1 and Stage 2 samples
yielded varying results.
Stage 2 sampling (episodes 1 and 2) both yielded different results. 1,2-dichloroethane, chloromethane,
1,2-dichloropropane were detected in surface water in sampling episode 1. There were, however, no detections of
these compounds in surface water samples for sampling episode 2.
Petroleum Hydrocarbons and 1,1,1-trichloroethane were detected in surface sediment samples during Stage 1 and
were also detected in sampling episode 1 during Stage 2. There were, however, no detection of these compounds
in surface sediment samples for sampling episode 2.
4-104
P78-914/P7S4C.105
02/14/92
4.2 BASELINE RISK ASSESSMENT
Because of the large number of analytes examined in the Stage 1 and Stage 2 studies, four indicator chemicals
were selected as the focus of the baseline risk assessment. The indicator chemicals are intended to represent
the environmental fate and health effects of all contaminants origmating on the site.
Data from the Stage 1 and 2 sampling programs were considered during the indicator chemical selection process,
and the number of detections were summarized for each media (Tables 4-26 and 4-27). Duplicate samples and
observed organic compounds in momtoring well P-1 observed during Stage 2 were not considered in the
calculation of the number of detections. Phenols and other organics were not detected in Stage 1, and thus are
not listed in Tables 4-26 or 4-27. Inorganics were not determined to be elevated with respect to background
levels in the Stage 1 study (ESE, 1989), and so they were not included in later sampling programs or the risk
assessment. Tables 4-28 and 4-29 present maximum observed concentrations in each media by location for
Stage 1 and Stage 2 sampling programs, respectively.
Four indicator chemicals were selected from the contaminants detected in soil sediment, and water. The criteria
used to select the indicator chemicals were as follows:
• Verification of occurrence in both Stage 1 and Stage 2 sampling;
• Frequency of detections in soil, sediments, or water, as compared to the other analytes;
• Concentrations higher than available background data;
• Water solubility (moderate to high) and K^. (low to moderate) data indicate potential mobility in the
environment; and
• Moderately to highly toxic.
Methylene chloride and petroleum hydrocarbons were the most frequently detected compounds in the Stage 1
sampling program (Table 4-26). Maximum concentrations detected in each media at each location sampled
during Stage 1 are presented in Table 4-28. Methylene chloride is a frequent laboratory contaminant. Although
many soil samples from the Stage 1 sampling effort contained methylene chloride, almost no detections occurred
in the same locations during Stage 2 (Tables 4-26 and 4-27). Methylene chloride also occurred in onsite water
supplies. Based on the lack of Stage 2 verification of methylene chloride occurrence at Plant 78, and its presence
in Plant 78 onsite water, methylene chloride was considered to be an unreliable indicator chemical for the risk
assessment. Petroleum hydrocarbons as an unspecified mixture are difficult to use as indicator chemicals,
because the toxicological and chemical properties cannot be quantified.
4-105
P78-914/P78T4-26.1
02/14/92
Table 4-26. Screening Process for Selection of Indicator Chemicals - Stage 1 Sampling Program.
Number of Detections
Chemical SW GW Soil Sed Total Tox. WS BCF
Chloromethane 2 0 0 0 2 M,NC M S
Bromomethane 2 0 0 0 2 H,NC - - -
Methylene chloride 3 1 18 0 22 H,PC L S 5
1,1-DCE 3 0 1 0 4 H,PC M S 5.6
1,1-DCA 3 0 0 0 3 H,PC M S
Chloroform 4 110 6 H,PC M S 3.75
1,1,1-TCA 4 1 0 0 5 M,NC H S 5.6
Bromodichloromethane 2 0 0 0 2 M,NC -
TCE 2 0 1 0 3 H,PC H S 10.6
Dibromochloromethane 2 0 0 0 2 M,NC -
Bromoform 5 0 0 0 5 H,NC H S
Tetrachloroethene 2 0 0 0 2 H,PC H I 31
Petroleum Hydrocarbons 2 0 45 21 68 M,NC - I
Toxicity (Sax. 1984 .
TJ - Unknown
N - None
L - Low (LD50 = 4,000 - 40,000 mg/kg)
M - Moderate (LD50 = 400 - 4,000 mg/kg)
H - High (LD50 = <400 mg/kg)
PC - Possible or probable carcinogenic effects
NC - No carcinogenic effects reported
Water Solubility (EPA. 1986a)
I - Insoluble in water (< 1,000 mg/L)
S - Soluble in water (> 1,000 mg/L)
SW-Surface Water Samples
GW-Groundwater Samples
Sed-Sediment Samples
Tox-Toxicity
K^-Soil/Water Partition Coefficient
WS-Water Solubility
BCF-Bio Concentration Factor
K~ (EPA. 1986a)
L-Low(<10ml/g)
M - Moderate (10 - 100 ml/g)
H - High (>100 ml/g)
Source: ESE, 1989.
4-106
P78-914/P78T4-27.1
02/14/92
Table 4-27. Screening Process for Selection of Indicator Chemicals - Stage 2 Sampling Program.
Number of Detections
Chemical SW GW Soil Sed Total Tox. WS BCF
Benzene
Toluene
Chlorobenzene
0
0
0
2
1
4
0
0
0
0
0
0
2
1
4
H,PC
H,NC
M,NC
M
H
H
S
I
I
5.2
10.7
10
Xylenes
Dichlorobenzene
Chloromethane
1
0
7
0
2
1
0
0
0
0
0
0
1
2
8
M,NC
M,PC
M,NC
H
H
M
I
I
S
Vinyl Chloride 1 1 0 0 2 H,PC M S
Methylene chloride 0 1 2 0 3 H,PC L S
Trichlorofluoromethane 0 10 0 1 M,PC H S
56
1,1-DCE
1,1-DCA
t-l,2-Dichloroethene
1
1
0
5
6
1
0
0
0
0
0
0
6
7
1
H,PC M
H,PC M
S
S
5.6
Chloroform
1,2-DCA
1,1,1-TCA
3
13
3
6
6
7
0
0
9
9
19
21
H,PC
H,PC
M,NC
M
M
H
3.75
1.2
5.6
1,2-Dichloropropane
1,1,2-TCA
TCE
Carbon Disulfide
5
1
1
0
0
7
0
0
0
0
0
0
5
1
8
M,NC
H,PC
H,PC
2-Chloroethylvinyl Ether 1 0 0 0 1 H,NC
Tetrachloroethene 3 4 0 0 7 H,PC
Petroleum Hydrocarbons 1 0 3 4 8 M,NC
H,-
M
M
H
H
M
S
S
S 10.6
31
Toxicity (Sax. 1984)
U - Unknown
N - None
L - Low (LD50 = 4,000 - 40,000 mg/kg)
M - Moderate (LD50 = 400 - 4,000 mg/kg)
H - High (LD50 = <400 mg/kg)
PC - Possible or probable carcinogenic effects
NC - No carcinogenic effects reported
Water Solubility (EPA. 1986a)
I - Insoluble in water (< 1,000 mg/L)
S - Soluble in water (> 1,000 mg/L)
K.- (EPA. 1986a)
L - Low (<10 ml/g)
M - Moderate (10 - 100 ml/g)
H - High (> 100 ml/g)
SW-Surface Water Samples
GW-Groundwater Samples
Sed-Sediment Samples
Tox-Toxicity
K^-Soil/Water Partition Coefficient
WS-Water Solubility
BCF-Bioconcentration Factor
4-107
P7_-914/P78T4-28.1
02/14/92
Table 4-28. Maximum Observed Concentrations in each Media by Location - Stage 1.
ANALYTE BLUE CREEK SSTEP FVD E-512 NDD M-585
SEDIMENTS - /tg/kg
Petroleum Hydrocarbons 129 197 25.2 1620 999 NA
SOILS - /tg/kg
Petroleum Hydrocarbons NA
Chloroform NA
Methylene Chloride NA
TCE NA
1,1-DCE NA
NA
NA
NA
NA
NA
69.5
NA
NA
NA
NA
NA
NA
NA
NA
NA
28.9
0.11
5100
0.25
0.9
148
ND
3500
ND
ND
SURFACE WATER - /tg/L
Petroleum Hydrocarbons 0.115
Chloroform ND
Methylene Chloride 0.470
TCE 0.070
1,1-DCE ND
Bromoform 0.075
Chloromethane 0.210
1,1-DCA ND
1,1,1-TCA ND
Bromodichloromethane ND
Bromomethane ND
Dibromochloromethane ND
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
8.03
0.100
ND
ND
0.072
0.230
ND
0.056
2.60
ND
ND
ND
0.841
1.15
ND
0.068
0.500
5.40
ND
0.530
13.0
4.00
0.59
4.80
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
GROUNDWATER - /tg/L
Tetrachloroethene ND
Chloroform NA
Methylene Chloride NA
1,1,1-TCA NA
NA
NA
NA
NA
NA
NA
NA
NA
ND
NA
NA
NA
0.310
NA
NA
NA
NA
0.485
0.348
0.176
NA - Not Analyzed
ND - Not Detected
Source: ESE, 1989.
4-108
P78-921/P78T4-29.1
02/14/92
Table 4-29. Maximum Observed Concentrations in Each Media by Location - Stage 2 (Page 1 of 2).
ANALYTE BLUE CREEK FVD E-512 NDD M-585
(includes (includes
E-515) E-519)
SEDIMENTS • mg/kg
Petroleum Hydrocarbons 887 - 1320 59.3 NA
1,1,1-TCA 1.02a 1.02 - - NA
SOIL • mg/kg
Petroleum Hydrocarbons - - 36.8 45.7
Methyl Chloride - 0.11 - 0.099
Methylene Chloride - - - 4.76
1,1,1-TCA 0.113 ....
Butyl Benzylphthalate - 1.0* - 0.08
Bis (2 E,H) phthalate - 0.22* - 0.24
Diethylphthalate - - - 0.05
Di-n-Butylphthalate - - - 0.04
Acetophenone - 0.09* -
TCE - ... 0.298
Vinyl Chloride - 0.0004
SURFACE WATER - /tg/L
Chloroform 0.608 NA 0.473 0.262 NA
1,1-DCA - NA - 1.16 NA
1.1- DCE - NA - 0.688 NA
1.2- DCA 27.0 NA - 9.93 NA
1.1.1- TCA 0.615 NA 4.22 7.53 NA
TCE - NA - 0.626 NA
Xylene 3.62 NA - - NA
2-Chlorovinyl Ether 0.733 NA - - NA
Chloromethane 3.74 NA - 2.81 NA
1,2 Dichloropropane 1.22 NA - 0.450 NA
Tetrachloroethene 1.43 NA - - NA
1.1.2- TCA 0.615 NA - - NA
Vinyl Chloride 0.229 NA - - NA
Petroleum Hydrocarbons - NA - 257 NA
4-109
P78-921/P7_T4-2S_
02/14/92
Table 4-29. Maximum Observed Concentrations in Each Media by Location - Stage 2 (Page 2 of 2).
ANALYTE BLUE CREEK FVD
(includes
E-515)
E-512 NDD
(includes
(E-519)
M-585
GROUNDWATER - /tg/L
(P-9) (P-5)
(P-3
and P-8)
(P-2, P-6,
and P-7)
Chloroform
1,1-DCA
1.1- DCE
1.2- DCA
1,1,1-TCA
TCE
Chloromethane
Tetrachloroethene
Vinyl chloride
Benzene
Toluene
Chlorobenzene
t-l,2-DCE
Trichlorofluromethane
Carbon Disulfideb
Dichlorobenzene
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
1.08
4.78
146
1.51
387
5,780
1.08
1.0
4.19
0.346
0.548
4.85
1.43
16.0
664
4.62
18.2
1,080
20.2
2,610
26,900
2.81
8.87
75
2.79
1.51
24
3.2
2,580
110
931
76.2
3,320
1,890
1.48
0.511
14.6
23.2
25.2
1.12
5.72
1.9"
a = gradient of site
b = LP results
NA - Not Analyzed
= Not detected
* = Compound detected in method blank with concentration greater than soil sample
4-110 O
P78-914/P784C.111
02/14/92
1,1,1-Trichloroethane (1,1,1-TCA), chloroform, bromoform, and trichloroethylene (TCE) were also detected three
or more times out of the approximately 118 total samples collected for organic analysis during Stage 1. The
selection criteria were applied as follows:
• 1,1,1-TCA - five detections, was not detected in onsite water supplies, moderately toxic, slightly soluble,
high K^;
• Chloroform - six detections, occurred in onsite water supplies at concentrations an order of magnitude
less than the maximum detected in samples, highly toxic, soluble, moderate K-.;
• Bromoform - five detections, occurred in onsite water supplies at concentrations similar to the maximum
in water samples, highly toxic, soluble, high K,,.; and j
• TCE - three detections, was not detected in onsite water supplies, highly toxic, soluble, high K,,..
Bromoform was not considered further as an indicator chemical for the risk assessment, because the detections
may have resulted from cross contamination from the onsite water supply. 1,1,1-TCA, chloroform, and TCE are
considered as contaminants of concern based on Stage 1 data. '
Many analytes occurred less than five times in the Stage 2 study (Table 4-27) for the 91 samples for organic
contaminants. Maximum concentrations are presented in Table 4-29. The following chemicals from the Stage 2
sampling program fit the above selection criteria:
• 1,2-Dichloroethane (1,2-DCA) - 19 detections, occurred upgradient in surface water, although some
samples from onsite were much greater, moderately toxic, soluble, low to moderate K-,c;
• Chloromethane - eight detections, occurred in onsite water supplies at levels similar to samples,
moderately toxic, soluble, moderate K^;
• Chloroform - nine detections, occurred in onsite water supplies, although some samples were much
higher than background levels, highly toxic, soluble, moderate K^.;
• TCE - eight detections, did not occur upgradient or in onsite water supplies, highly toxic, soluble, high
• 1,1,1-TCA - 21 detections, occurred in upgradient sediments, moderately toxic, slightly soluble, high K^.;
• 1,1-Dichloroethane (1,1-DCA) - seven detections, did not occur upgradient or in onsite water supplies,
moderately toxic, soluble, moderate IC^.;
• Tetrachloroethene - seven detections, did not occur upgradient or in onsite water supplies, moderately
toxic by routes other than intravenous, slightly soluble, high K^; and
• 1,1-Dichloroethene (1,1-DCE) - six detections, did not occur upgradient or in onsite water supphes,
highly toxic, soluble, moderate K„..
Table 4-30 presents environmental data for these contaminants detected in groundwater at concentrations
exceeding the EPA maximum contaminant levels (MCLs).
4-111
P78-914/P78T4-30.1
02/14/92
Table 4-30. Plant 78 Contaminants Detected in Groundwater at Concentrations Exceeding EPA MCLs.
Henry's
Highest Law
Detection Concentrations MCL Constants
Chemical Frequency1 0*g/L) 0*g/L) K-. Log K_, (atm x m3/mol)
Benzene 2 14.6
Chloroform 15 2,580
1,2-Dichloroethane 19 76.2
1,1-Dichloroethylene 10 1,080
Tetrachloroethylene 9 8.87
1,1,1-Trichloroethane 26 3,320
Trichloroethylene 11 26,900
5 83 2.12 5.59E-3
100 31 1.97 2.87E-3
5 14 1.48 9.78E-4
7 65 1.84 3.4E-2
5 364 2.6 2.59E-2
200 152 2.51 3.0 E-2
5 126 2.38 9.1 E-3
1 Combined Stage 1 and Stage 2 sampling programs
Source: ESE 1989, 1991.
4-1L2
P7_-914/P784C.113
02/14/92
Benzene and vinyl chloride are both considered by the EPA to be known human carcinogens (Class A). The
highest concentration of vinyl chloride detected at the site (0.511 /ig/L) was lower than the EPA MCL (2 /ig/L).
The highest concentration of benzene detected at the site (14.6 /tg/L) was only slightly higher than the EPA
MCL (5 /tg/L). Both of these compounds were detected infrequently at the Plant 78 site, and as a result, were
not selected as contaminants of concern for the baseline risk assessment.
1,2-DCA was one of the most frequently detected contaminants during the Stage 2 study. The chemical
properties of this contaminant indicate a potential for migration, and the moderate toxicity indicates potential
for toxic effects. 1,2-DCA was therefore selected as an indicator chemical. 1,2-DCA is used to represent the
other dichlorinated ethanes and ethenes (1,1-DCA and 1,1-DCE) because of the widespread occurrence of this
compound on the site. 1,1-DCE is more toxic than 1,2-DCA, and it was detected at higher concentrations.
However, 1,1-DCE is only considered as a Class C carcinogen, whereas 1,2-DCA is classified as a B2 carcinogen.
Although frequently detected, chloromethane was rejected as an indicator chemical due to its presence in onsite
drinking water supplies (Table 4-9) and its appearance in many of the method blanks. The sample
concentrations tended to be low, and may be a result of background contamination due to chlorination.
Chloroform also occurred in the method blanks and in onsite dririking water (Table 4-9); however, at least one
detection in groundwater was quite high and was not the result of background contamination. Chloroform also
occurred in surface and groundwater during the Stage 1 sampling program and was considered an indicator
chemical based on Stage 1 data. The chemical properties indicate a potential for migration, and the toxicity
indicates a potential for toxic effects. Therefore, chloroform was selected as an indicator chemical.
TCE occurred in surface water and groundwater. Although the K^. value for TCE is high, it is water soluble
and migration offsite should be considered a potential problem. TCE has potential carcinogenic effects and
several detections were quite high (Table 4-29). Therefore, TCE was selected as an indicator chemical.
1,1,1-TCA was selected as an indicator chemical due to frequency of detections in both the Stage 1 and Stage 2
studies. Although the high K^. indicates strong binding to soil and, therefore, less potential for offsite migration
than a contaminant with a low to moderate K^, 1,1,1-TCA is moderately toxic and water soluble, suggesting a
potential for concern.
Although the highest concentration of tetrachloroethylene (8.87 /tg/L) was shghtly higher then the EPA MCL
(5 /tg/L), most detections of tetrachloroethylene were low. In addition, concentrations and toxicity of
tetrachloroethylene were much lower than for TCE, which was selected as a contaminant of concern. As a
result, tetrachloroethylene was not considered as a contaminant of concern.
4-113
P78-914/P784C.114
02/14/92
The final indicator chemicals selected for the Plant 78 baseline risk assessment were chloroform, 1,2-DCA,
1,L>TCA, and TCE.
4.2.1 WASTE CHARACTERIZATION
Waste characterization involves an in-depth examination of the physical and chemical properties and toxicity of
the indicator chemicals (Tables 4-31,4-32, and 4-33). Toxicity assessments were performed for the four indicator
chemicals by reviewing the available literature for information on acute and chronic health effects on human and
nonhuman biota, as well as effects on the environment. Environmental fate is predicted for each of the indicator
chemicals as data are available, including persistence, bioaccumulation, and breakdown products.
4.2.1.1 Chloroform
4.2.1.1.1 Ambient Levels
Chloroform has been detected in various food types at levels ranging from 0.4 to 33 /tg/kg (EPA, 1985a).
Ambient air concentrations are less than 1 ppb or lower (EPA, 1985a). Chloroform occurs in chlorine-treated
water at estimated mean levels of 41 /tg/L (EPA, 1985a). The background tropospheric concentration of
chloroform ranges from 20 to 40 ppb (NAS, 1978).
4.2.1.1.2 Health Effects
GENERAL
Chloroform is a Group B2 carcinogen (probable human carcinogen) as indicated by increased incidence of
hepatocellular carcinomas in male and female mice, renal epithelial tumors in male rats, hepatomas in female
mice, and kidney tumors in male mice (EPA, 1985a). There is inadequate evidence for human carcinogenicity
based on studies on consumption of chlorinated drinking water, because other carcinogens were present in the
water (EPA, 1985a). The Maximum Contaminant Level (MCL) for chloroform is 100 /tg/L (EPA, 1987b). The
Ambient Water Quahty Criterion (AWQC) for the protection of human health for the 10"* risk level is 0.19 /tg/L,
and the AWQC for the protection of freshwater aquatic organisms and their uses is 1,240 /tg/L (EPA, 1986c).
The threshold limit value (TLV) for chloroform is 50 mg/m3 (10 ppm) (ACGIH, 1988).
INGESTION
Chloroform is rapidly absorbed through the gastrointestinal tract (EPA, 1985a). Absorption approaches
100 percent in mice, rats, and monkeys dosed with 14C-chloroform perorally (Brown et al., 1974; Taylor et al.,
1974). Rats dosed with 2,500 ppm chloroform in drinking water for 90 days exhibited increased mortality, liver
lesions, and decreased growth rate (Chu et al., 1982). Rats dosed with 200, 400, 600, 900, or 1,800 ppm
chloroform in drinking water for 90 days exhibited dose related signs of depression and decreased water
consumption (Jorgenson and Rushbrook, 1980). Oral doses of 126 milligrams per kilogram body weight per day
(mg/kg bw/day) administered to pregnant rats caused maternal toxicity but no embryocidal or teratogenic
4-114
P78-914/P78T4-31.1
02/14/92
Table 4-31. Physical, Chemical, and Topological Properties of the Indicator Chemicals at USAF Plant 78.
Chemical
Chemical
Abstract
Service
(CAS) No.
Molecular Water Vapor Henry's Law
Weight Solubility Pressure Constant
(g/mole) (mg/L) (mmHg) (atm m'/mol)
Half-life (days.
K_ Toxicologic Toxicity Surface Ground
(ml/g) LogK_, FishBCF Class Rating Air Water Soil Water
Chloroform 67-66-3
1,2-DCA 107-06-2
1,1,1-TCA 71-55-6
TCE 79-01-6
119
99
133
131
8.20E3
8.69E3
7.20E2
1.10E3
1_1E2
6.1E1
1.23E2
5.79E1
2.87E-3
9.14E-4
0.03
9.10E-3
31
14
152
126
1.97
1.48
2-51
2.38
3.75
1.2
5.6
10.6
PC
PC
NC
PC
H 80 0.3-30
H 36-127 0.005-0.2
M
H
>365
<10
>180
1-12
mos/
yrs
>180
Parameters defined in Table 4-26.
Source: ESE, 1991.
P78-914/P78T4-3_1
02/14/92
Table 4-32. Summary of Toxicity Values for Potential Noncarcinogenic Effects.
Chronic RfD" Confidence Critical Uncertainty and
Chemical (mg/kg-day) Levelb Effect RfD Source Modifying Factors
Oral Route
CHCI3 0.01 Medium Fatty cysts in liver IRIS, 1990 UF=1000;MF=1
1,2-DCA - - - IRIS, 1990
1,1,1-TCA 9xl0 2 Medium Fatty changes in liver; IRIS, 1990 UF=1000;MF=1
decreased weight gain
TCE - - - IRIS, 1990
Inhalation Route
CHCI3 - - - IRIS, 1990
1,2-DCA - - - IRIS, 1990
1,1,1-TCA 3X10"1 - Hepatotoxicity HEAST, 1991 UF=1000
TCE - - - IRIS, 1990
a RfD expressed as an administered dose in given medium.
b Confidence level from IRIS, either high, medium, or low.
Source: EPA, 1990; EPA, 1991.
4-116
P78-914/P78T4-33.1
02/14/92
Table 4-33. Summary of Toxicity Values for Potential Carcinogenic Effects.
Chemical
Slope Factor (SF) Weight of Evidence Cancer
(mg/kg-day) Unit Risk Classification TyP6" SF Source
Oral Route
CHCI3
1,2-DCA
TCE
6.1 x 10'3
9.1 x 10'2
1.1 x 10"2
(Mg/L)1
1.7 x 10'7
2.6 x IO"6
3.2 x 10"7
B2
B2
B2
IRIS, 1990
IRIS, 1990
HEAST, 1990
Inhalation Route
CHCI3
1,2-DCA
TCE
8.1 x 10'2
9.1 x 10'2
1.7 x IO"2
(Mg/m3)"1
2.3 x 10 s
2.6 x 10 s
1.7 x 10 6
B2
B2
B2
IRIS, 1990
IRIS, 1990
HEAST, 1990
" Identified for Class A carcinogens only (EPA, 1989).
4-117
P78-914/P784C.118
02/14/92
effects; fetal toxicity, hepatitis, and death of dams occurred at 316 mg/kg bw/day (Thompson et al., 1974). A
13-week study with Sprague-Dawley rats given chloroform orally demonstrated that 30 mg/kg bw/day had no
adverse effects (Palmer et al., 1979). The next higher dose, 150 mg/kg bw/day, caused increased hver weight
with fatty necrosis, gonadal atrophy, and cellular proliferation in the bone marrow. Oral doses of chloroform
greater than 100 mg/kg bw/day in female rabbits were toxic to both dam and fetus (Thompson et al., 1974).
INHALATION
The toxicity of chloroform to humans exposed via inhalation has been documented as a result of the use of
chloroform as an anesthetic. Chloroform is a central nervous system (CNS) depressant, and has been associated
with cardiac, hepatic, and renal effects (EPA, 1985a). At exposure concentrations of greater than 1,000 ppm for
20 to 30 minutes, human symptoms were (lizziness, headache, giddiness, and tiredness (EPA, 1985a).
Chronic data for exposure by inhalation are available for laboratory animals. Chronic exposure of rats and dogs
to 25 ppm resulted in sublethal effects, such as increased kidney weight in rats and cloudy swelling of renal
tubular epithelium in both rats and dogs (Torkelson et al., 1976). Inhalation studies with mice indicate that death
occurred at concentrations of 8,000 ppm within 3 hours, and within 2 hours at 12,500 ppm death occurred within
2 hours (Von Oettingen, 1955). Pregnant rats exposed to 30 ppm chloroform in ambient air had a significant
incidence of fetal abnormalities, including delayed skull ossification and rib abnormalities (Schwetz et al., 1974).
Inhalation of 50 ppm had no effect on male or female rabbits, whereas the next higher dose of 85 ppm caused
pneumonitis, and hepatic and renal pathology (Torkelson et al., 1976).
DERMAL ABSORPTION
Chloroform is absorbed dermally and produces irritation and delayed healing in rabbits (Torkelson et al., 1976).
Dermal applications of 1,000 mg/kg bw resulted in degenerative changes in kidney tubules of exposed rabbits
(Torkelson et al., 1976). Irritation is observed in humans foUowing apphcation to skin (EPA, 1985a).
METABOLISM AND EXCRETION
The volatility of chloroform has presented difficulties in the in vivo study of its distribution and metabolism
(Cohen and Hood, 1969). Volatile anesthetics such as chloroform are removed so rapidly by exhalation that
comparatively little metabolism is found (Van Dyke and Chenoweth, 1965). In rats, 70 percent of a single
intraduodenal administration of chloroform will be expired in air unchanged, and 4 percent expired as carbon
dioxide (Paul and Rubinstein, 1963). Detoxification of chloroform primarily occurs in the hver. Approximately
4.02 percent of an injected anesthetic dose is metabolized to methylene chloride via enzymatic and nonenzymatic
processes (Van Dyke and Chenoweth, 1965). Metabohc dehalogenation of chloroform produces formaldehyde,
which oxidizes to formate. Formate can further oxidize to carbon dioxide with hver formaldehyde dehydrogenase
4-118
P7S-914/P784C.119
02/14/92
as the necessary enzyme. Formate has been determined as the end-product of the reaction catalyzed by
formaldehyde dehydrogenase (Rubenstein and Kanics, 1964).
Chloroform is lipid soluble and passes readily through cell membranes to produce narcosis of the central nervous
system (Cornish, 1975), depletion of hver glutathione (Ilett et al., 1973), gonadal and bone marrow abnormalities
(Palmer et al., 1979), and carcinomas of several tissues. Gastromtestinal absorption is slower than inhalation,
but assimilation is approximately 100 percent (Fry et al., 1972), and lethal tissue levels can be reached in a range
of minutes to a few hours (Von Oettingen, 1955).
AQUATIC ECOSYSTEMS
The 48-hour LCJQ for Daphnia magna is 28,900 /ig/L (EPA, 1985a). The 96-hour LC50 values for rainbow trout
(Salmo gairdneri) and bluegill (Lepomis macrochirus) for static test conditions range from 43,800 to 66,800 /tg/L
and from 100,000 to 115,000 /ig/L, respectively (Bentley et al., 1975). Water hardness is positively correlated
with the toxicity of chloroform to rainbow trout embryo and larva; at 50 mg/L water hardness, the 27-day LQo
was 2,030 /tg/L, whereas at 200 mg/L hardness, the 27-day LCJO was 1,240 /tg/L (Birge et al., 1979). At
concentrations of 10,600 /tg/L for 23 days, a 40 percent incidence rate of teratogenesis was observed in rainbow
trout embryos (Birge et al., 1979). Information on the toxicity of chloroform to aquatic plants was unavailable
in the literature reviewed.
Bioconcentration factors of 6 were obtained for bluegill foUowing a 14-day exposure, and tissue half-life was less
than 1 day (EPA, 1978). Therefore, significant bioconcentration by aquatic life is not expected to occur.
TERRESTRIAL ECOSYSTEMS
Significant chronic effects on wUdlife from long-term exposure are unlikely due to the chemical and physical
properties of chloroform (NAS, 1978). Quantitative data on the toxicity of chloroform to mammalian or avian
wUdlife, crops, and hvestock were unavailable in the literature reviewed.
4.2.1.1.3 Environmental Fate
In the troposphere, chloroform is diluted rapidly to low concentrations (NAS, 1978). Degradation of chloroform
occurs in air by reaction with hydroxyl radicals (EPA, 1985a). Its half-life in air is approximately 3 months (EPA,
1985a). Although precipitation may cause chloroform to be removed from the atmosphere, volatilization from
soU and water wiU result in most of the chloroform removed in this manner returning to the air (EPA, 1985a).
Volatilization is the primary removal mechanism from surface water; expected half-life is 1-31 days (EPA, 1985a).
Half-life in rivers has been predicted as 40 hours (EPA, 1985a), and observed to be 1.2 days in a field monitoring
study (Zoeteman et al., 1980). Chloroform is not expected to photolyze under environmental conditions
4-119
P78-914/P7S4C120
02/14/92
(Callahan et al., 1979). Biodegradation is not expected to be an important loss mechanism for chloroform in
water, although the data are conflicting. Chloroform is expected to be persistent in groundwater (EPA, 1985a).
Chloroform is highly volatile, and therefore is not expected to accumulate in terrestrial or aquatic environments.
Chloroform will volatilize from soil to air or leach from soil to groundwater. The high vapor pressure (159 mm
Hg at 20°C) indicates volatilization will be rapid (EPA, 1985a). The low indicates that adsorption to soils
or sediments will not be significant (EPA, 1985a). Chloroform adsorbs more strongly to soils high in organic
matter; it does not adsorb to sand (Dilling et al., 1975). Data regarding biodegradation in soils were not
available in the literature reviewed.
4.2.1.2 1.2-Dichloroethane
4.2.1.2.1 Ambient Levels
Ambient levels of 1,2-Dichloroethane (1,2-DCA) in air (including samples from urban areas) are less than
0.5 ppb (WHO, 1987). Average concentrations in the vicinity of industrial production are less than 40 /tg/m3,
and the air in cities is between 0.3 and 6.5 /tg/m3 (WHO, 1987). Most groundwater and surface water
concentrations are less than 1.0 /tg/L (Letkiewicz et al., 1982). Drinking water concentrations are also below
1 /tg/L (WHO, 1987). Water treated with chlorine tends to have higher incidence of 1,2-DCA than unfinished
water (WHO, 1987). This may be a result of a reaction between alkenes and hypochlorite during the
chlorination process (EPA, 1985b).
There are no reports of 1,2-DCA occurring naturaUy in food items (WHO, 1987).
4.2.1.2.2 Health Effects
GENERAL
1,2-DCA is rapidly absorbed by direct contact and inhalation (WHO, 1987). 1,2-DCA is toxic to humans if
ingested, inhaled, or absorbed through skin and mucus membranes (WHO, 1987). 1,2-DCA is hpophihc and
distributes throughout human tissue. 1,2-DCA is toxic to the hepatic and renal systems (EPA, 1980a), and is
considered a Group B2 carcinogen (EPA, 1987a).
The principle acute effect in mammals is central nervous system (CNS) depression; symptoms include nausea,
dizziness, cyanosis, rapid but weak pulse, and unconsciousness (EPA, 1987a). Acute exposures often lead to
death from respiratory and circulatory failure, or renal damage (EPA, 1987a).
Chronic exposure to 1,2-DCA results in neurologic changes and gastrointestinal problems (EPA, 1980a).
Bioaccumulation is unlikely because elimination from tissue is rapid, as indicated by a tissue half-life of 6-8 hours
(Urusova, 1953).
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Mutagenic and carcinogenic results have been reported from animal studies (EPA, 1985b). 1,2-DCA has induced
squamous cell carcinoma in the stomach, hemangiosarcomas and uterine tumors in rats, mammary gland tumors,
lymphomas and pulmonary tumors in mice (Riihimaki and Ulfvarson, 1986). EPA (1980a) suggests that for the
maximum protection of human health from potential carcinogenic effects through ingestion of contaminated
water and aquatic organisms, the ambient water concentration of 1,2-DCA should be zero. The recommended
AWQC for the 10'5 to the 10"7 risk levels range from 9.4 /tg/L to 0.094 /tg/L for consumption of contaminated
drinking water and aquatic organisms (EPA, 1980a). For consumption of aquatic organisms only, the
recommended AWQC for the 10"5 to the 10"7 risk levels range from 2,430 /tg/L to 42.3 /tg/L, respectively (EPA,
1980a). The MCL for 1,2-DCA is 5 /tg/L (EPA, 1980a). The AWQC for the protection of freshwater aquatic
organisms and their uses is 20,000 /tg/L (EPA, 1980a). The long-term health advisory for a child is 740 /tg/L,
and for an adult is 2,600 /tg/L (EPA, 1987). The TLV for 1,2-DCA is 40 mg/m3 (10 ppm) (ACGIH, 1988).
INGESTION
1,2-DCA is rapidly absorbed following ingestion. Death can result in humans ingesting as little as 8 ml
(approximately 10 g) (EPA, 1985b). Ingestion of 15 to 200 ml of 1,2-DCA can result in neurological effects and
mortality (EPA, 1987).
The LDJO values for rats and mice are 0.68-0.85 g/kg and 0.413-0.489 g/kg bw, respectively (McCollister et al.,
1956; Munson et al., 1982). 1,2-DCA is carcinogenic in B6C3F1 mice and Osborne-Mendel rats foUowing
administration of doses in the range of 50-300 mg/kg bw administered by gavage in oU (WHO, 1987).
Subchronic and chronic oral administration of 200 mg/kg bw and higher doses caused decreased growth rate and
increased mortality in mice (EPA, 1985b). Chronic exposure of rats to 34 mg/kg bw/day resulted in increased
mortality due to nonneoplastic lesions, including bronchopneumonia and endocardial thrombosis (EPA, 1985b).
In a recent study, white leghorn chickens were oraUy exposed to 250 and 500 mg/kg diet (WHO, 1987). From
the fourth month of laying onwards, decreased egg weight was observed at both dose levels, while at the higher
dose level the number of eggs and feed intake were also reduced. 1,2-DCA did not affect serum composition,
growth, semen characteristics, or fertility in the chickens (Alumot et al., 1976).
INHALATION
1,2-DCA is rapidly absorbed foUowing inhalation (EPA, 1985b), accumulating primarily in adipose tissue and
not in the hver (WHO, 1987). Inhalation first affects the CNS, and inflammation of the respiratory tract can
occur. Cyanosis may occur either as a result of respiratory insufficiency due to depression of the CNS or by
bronchial obstruction due to inflammation (WHO, 1987). Adverse CNS effects were observed in humans at air
concentrations between 10 and 100 ppm (EPA, 1985b). Workers exposed to 10 ppm and higher concentrations
for undefined exposure durations had symptoms such as tender livers, emaciation, burning eyes, nausea, and
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vonuting; however, benzene was also present (Cetnarowicz, 1959). Autopsy reports on exposed workers
frequently mention damage to the lungs, hver and kidneys (WHO, 1987).
Inhalation studies indicate a 6-hour LC^ value for mice and rats of 1,060 mg/m3 and 5,100 to 6,660 mg/m3,
respectively (WHO, 1987). The No Observed Effect Level (NOEL) in rats was 200 ppm for 7-hour exposures
(Spencer et al., 1951). Subchronic and chronic animal studies did not indicate adverse effects on survival, growth,
clinical chemistry, body weight, or histology at levels less than 100 ppm (EPA, 1985b). High mortality occurred
at 400 to 500 ppm in rodents exposed several times (EPA, 1985b).
DERMAL ABSORPTION
1,2-DCA is absorbed across intact skin, and dermal absorption can be a significant route of exposure into the
body (Tsuruta, 1975; Tsuruta, 1977). Undiluted 1,2-DCA applied directly to guinea pigs produced microscopic
but no gross skin reaction within the first 12 hours of exposure; histopathology indicated karyopyknosis,
perinuclear edema, spongiosis and junctional separation of the skin (Kronevi et al., 1981). In similar tests on
rabbits, moderate erythema and edema were observed 24 hours after dermal apphcation. Microscopy on the
third day revealed necrosis and other lesions such as ulceration and acanthosis (Duprat et al., 1976).
METABOLISM AND EXCRETION
Metabolism of 1,2-DCA has a significant role in the manifestation of toxic, carcinogenic, and mutagenic effects
(WHO, 1987). Two metabolic pathways exist, one beginning with cytochrome P-450 mediated oxidation and the
other beginning with glutathione conjugation (WHO, 1987). Cytochrome P-450 enzymes catalyze the oxidative
transformation of 1,2-DCA to form reactive intermediates, which result in the formation of 2-chloroacetaldehyde
and 2-chloroethanol (Riihimake and Ulfvarson, 1986). Reactive intermediates are also formed when 1,2-DCA
is metabolized via glutathione conjugation (WHO, 1987).
Mice excreted 89 percent of an oral dose in 48 hours and 89 percent of an interperitoneal dose in 24 hours
(Yllner, 1971; Mitoma et al., 1985). The rate of elimination from blood and tissues in rats appears to depend
on the exposure level; the higher the exposure level the slower the elimination rate of 1,2-DCA after both oral
and inhalation exposure (WHO, 1987). Half-life in blood of rats exposed orally to 25 mg/kg bw was 25 minutes,
whereas half-life at an oral dose of 150 mg/kg bw was 57 minutes (Spreafico et al., 1980). Half-life in blood
following 6-hr inhalation exposures increased from 13 minutes at a dose of 202 mg/m3 to 22 minutes at a dose
of 1,012 mg/m3 (Spreafico et al., 1980).
Excretion of 1,2-DCA occurs primarily via expired air from lungs or in urine. The major excretory products in
expired air include the parent compound and carbon dioxide; whereas some of the major excretory products in
urine include thiodiacetic acid, chloractic acid, and 2-chloroethanol (Yllner, 1971).
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AQUATIC ECOSYSTEMS
Aquatic species most sensitive to 1,2-DCA exposure are members of the class Crustacea. The 24 and 48-hour
LCJO values for D. magna are 250 and 220 mg/L, respectively (EPA, 1985b). The NOEL for D. magna is
68 mg/L (LeBlanc, 1980). The 24 and 96-hour LQo values for bluegill are greater than 600 and 430 mg/L,
respectively (Buccafusco et al., 1981). A 7-day LC^ for guppies {Poecilia reticulata) of 106 mg/L was observed
for static test conditions, and a 96-hour LCso of 116 mg/L was observed for fathead minnows (Pimephales
promelas) in an open flow-through test (EPA, 1980a). For a 32 day early-life stage test with fathead minnows,
the estimated acceptable concentration was 29 to 59 mg/L (Benoit et al., 1982). Body weight of the juveniles
was reduced at concentrations of 59 mg/L in water. Survival of juveniles, percentage of normal larvae at hatch,
and the hatchability of the embryos was not affected by the exposure concentrations (Benoit et al., 1982).
Bioconcentration of 1,2-DCA in aquatic species is unlikely, due to its physical and chemical properties. In a
tracer study, a bioconcentration factor of 2 was established for bluegill in flowing water (WHO, 1987). The
half-life for the elimination of 1,2-DCA from fish tissues is 1 to 2 days (WHO, 1987).
TERRESTRIAL ECOSYSTEMS
1,2-DCA is used as a seed fumigant, usually in combination with carbon tetrachloride. 1,2-DCA vapor is both
lethal and mutagenic for barley seeds at 3 mg/m3 over a 24-hour exposure period (Ehrenberg et al., 1974).
1,2-DCA is nontoxic to many species of economically important plants (Gast and Early, 1956). 1,2-DCA is toxic
to invertebrates when used as a fumigant (EPA, 1985b), but data were unavailable for invertebrate toxicity in
relation to soil concentrations in the literature reviewed. Toxicity data for mammalian and avian wildlife were
unavailable in the literature reviewed.
4.2.1.2.3 Environmental Fate
1,2-DCA is persistent in air for 2 to 4 months (Howard and Evenson, 1976; EPA 1975). 1,2-DCA is degraded
slowly in the presence of air, moisture, and light, yielding primarily carbon oxides, hydrogen chloride, and some
phosgene (WHO, 1987). Rainout and adsorption on atmospheric aerosols is unlikely because of the high vapor
pressure and low solubility of the compound (WHO, 1987). 1,2-DCA is oxidized by hydroxy radicals in air to
form formyl chloride, hydrogen chloride, carbon dioxide, carbon monoxide, and monochloracetyl chloride (WHO,
1987). 1,2-DCA absorbs light within the solar spectral region and photolytic transformation is possible (WHO,
1987).
Volatilization is the primary loss mechanism from surface water, whereas oxidation and photolysis are not
expected to be significant (EPA, 1985b). The estimated half-life in surface water ranges from 8 minutes to
4 hours (EPA, 1985b). 1,2-DCA does not tend to biodegrade in aquatic systems (Jafvert and Wolfe, 1987;
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Wilson et al., 1983); biodegradation at 14 days ranges from 14 to 30 percent (Tabak et al., 1981). 1,2-DCA is
persistent in ground water with an undetermined half-life of months to years (EPA, 1985b).
1,2-DCA is not strongly adsorbed to soil as indicated by estimated K^. values ranging from 19 to 43 (EPA,
1985b); therefore, 1,2-DCA may percolate into ground water or partition to the atmosphere. 1,2-DCA adsorbs
to bentonite clay and peat moss, but not to dolomite limestone and silica (WHO, 1987). 1,2-DCA has been
detected in ground water in areas of contaminated soil (EPA, 1985b). Volatilization is the most significant
removal process of 1,2-DCA from soil (WHO, 1987).
4.2.1.3 1.1.1-Trichloroethane
4.2.1.3.1 Ambient Levels
No known natural sources of 1,1,1-Trichloroethane (1,1,1-TCA) exist (EPA, 1984). TCA is ubiquitous in the
atmosphere at low levels (EPA, 1987a). Ambient air concentrations in urban areas are approximately 20 ppb
(0.108 mg/m3) (EPA, 1984). 1,1,1-TCA is frequently observed in groundwater because it is fairly mobile
through soils; approximately 3.0 percent of all pubhc drinking water wells contain levels of 0.5 /tg/L (ppb) or
higher (EPA, 1987a). Pubhc drinking water supply systems using surface water as their source normally contain
lower 1,1,1-TCA levels than systems supphed by groundwater (EPA, 1987a).
4.2.1.3.2 Health Effects
GENERAL
The primary acute health hazard of TCA relates to its anesthetic properties and ability to produce a narcotic
effect (McCarthy and Jones, 1983). Narcotic effects are induced fairly rapidly (Riihimaki and Ulfvarson, 1986).
Exposure to moderate concentrations causes transient symptoms such as headache, (hzziness, drowsiness and
CNS depression (Riihimaki and Ulfvarson, 1986). At high concentrations, anesthesia and respiratory and
circulatory failure may lead to death; the most serious risks to human health are with the use of 1,1,1-TCA in
enclosed spaces (Riihimaki and Ulfvarson, 1986). [
Chloroethane compounds such as 1,1,1-TCA can degrade to phosgene, which[causes adverse health effects within
30 to 60 minutes following exposure to concentrations of 12.5 ppm by inhalation (EPA, 1984). Exposure to any
chloroethane compound should be minimized, since four chemicals in tliis class are known carcinogens in
laboratory animals, and all are structurally related (EPA, 1984). 1,1,1-TCA is classified as a Group D carcinogen
(not classified due to inadequate animal evidence of carcinogenicity) (EPA, 1987b). Specific symptoms of
1,1,1-TCA poisoning include unconsciousness, CNS depression, and respiratory symptoms such as coughing,
breathlessness, and chest tightness (Parker et al., 1979).
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At least 30 fatalities have been associated with exposure to 1,1,1-TCA, mostly due to deliberate inhalation or to
accidental occupational exposures (IARC, 1979). Affected organs include heart, lungs, hver, kidneys, and CNS;
the heart is the most vulnerable organ (Nelly and Blau, 1985). For the protection of human health from toxicity
due to ingestion of contaminated water and aquatic organisms, the ambient water quahty criterion is 18.4 mg/L
(EPA, 1980a). For the protection of human health from toxic properties of 1,1,1-TCA ingested through
contaminated aquatic organisms alone, the AWQC is 1.03 g/L (EPA, 1980a). The long-term health advisory for
children and adults is 35,000 and 125,000 /tg/L, respectively (EPA, 1987a). The MCL is 200 /tg/L (EPA, 1987b).
An EPA AWQC for freshwater aquatic life is unavailable; however, the AWQC for the protection of health
associated with human consumption of both water and aquatic organisms is 18.4 mg/L (EPA, 1980a). The
ACGIH (1988) TLV for 1,1,1-TCA is 1,900 mg/m3.
INGESTION
A major source of exposure to TCA occurs from the ingestion of contaminated d'rinking water. Torkelson et al.
(1958) observed LDjo values of 12.3 g/kg bw for male rats, 10.3 g/kg bw for female rats, 11.2 g/kg bw for female
mice, 5.7 g/kg bw for female rabbits, and 11.2 g/kg bw for male guinea pigs. Studies involving the admimstration
of 1,1,1-TCA by gavage concluded that concentrations ranging from 250 to 1,500 mg/kg bw will cause diminished
growth rates and decreased survival in rats (Buckner et al., 1985).
INHALATION
Inhalation of 1,1,1-TCA vapor is a common route of entry (EPA, 1987a). Inhaled 1,1,1-TCA rapidly equihbrates
with arterial capillary blood across the lung alveolar endothelium. Human subjects exposed to 1,1,1-TCA
reported no significant adverse effects at concentrations of 2.28 to 3.25 mg/L for up to 450 minutes, whereas at
concentrations of 4.95 to 5.5 mg/L for 75 minutes, hghtheadedness, loss of coordination, and loss of equilibrium
were reported (Aviado et al., 1976). It is estimated that a NOEL for short-term exposure of humans to
1,1,1-TCA is in the range of 350 to 500 ppm (1,890 to 2,700 mg/m3) (EPA, 1984). Acute pulmonary congestion
and edema are found in human fatalities resulting from inhalation of 1,1,1-TCA (Caplan et al. 1976; Bonventre
et al., 1977). Inhalation of chloroethanes in general can lead to hver and/or kidney injury, pulmonary irritation,
and damage to the hemopoietic system (Parker et al., 1979). Most fatal cases are due to solvent abuse or
inhalation exposure in the work place (McCarthy and Jones, 1983).
DERMAL TOXICITY
All chloroethanes are irritating to the skin. Absorption of 1,1,1-TCA through the skin by direct contact is slow
(EPA, 1984). Repeated or prolonged exposure to 1,1,1-TCA can defat the skin and cause dermatitis (Parker
et al., 1979). Other dermal reactions to 1,1,1-TCA include dryness, cracking, scaliness, and inflammation (Parker
et al., 1979).
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METABOLISM AND EXCRETION
1,1,1-TCA is metabolized to a very limited extent in animals and humans. Results of human inhalation studies
indicated only 6.0 percent of absorbed 1,1,1-TCA was metabolized (EPA, 1987a). Transformation of the parent
compound may occur by hydroxylation to trichloroethanoL followed by partial oxidation of trichloroethanol to
trichloroacetic acid. Two urinary metabolites, trichloroethane and trichloroacetic acid, represented approximately
3.0 percent of the total excreted dose. Hake (1960) found C14 labeled 1,1,1-TCA was less than 3.0 percent
metabolized in rats foUowing a single intraperitoneal injection.
Metabolism occurs primarUy in the hver, and to an unknown extent in other tissues (IARC, 1979). The primary
metabolites are 2,2,2-tricbloroethanol and trichloroacetic acid (EPA, 1984; IARC, 1979). Approximately
1 percent of the 2,2,2-trichloroethanol is excreted by the lung (EPA, 1987a). Hake et al. (1960) reported
0.09 percent of a large dose of 1,1,1-TCA was retained in the skin of rats as the parent compound as long as
25 hours foUowing an interperitoneal dose. The blood contained 0.02 percent of the dose, fat contained
0.02 percent of the dose, and 0.01 percent of the dose was observed in other tissues.
1,1,1-TCA distributes throughout the body, readUy crossing the blood-brain barrier. Holmberg et al. (1977)
studied the distribution of 1,1,1-TCA in mice after inhalation exposure and observed simUar concentrations in
kidney and brain at a given exposure concentration, but concentrations in hver were twice those observed in
kidney and brain foUowing exposures to 100 ppm or more. 1,1,1-TCA has not been demonstrated to directly
cross the placental barrier into the fetus, although it may be expected to do so due to its chemical and physical
properties.
AQUATIC ECOSYSTEMS
Acute 96-hour EQo tests using chlorophyU a and ceU number as measured responses were conducted with a
green alga, Selenastrum capricomutum (EPA, 1978). The highest concentration of 1,1,1-TCA tested was
669,000 pg/L, which did not produce adverse effects within 96 hours (EPA, 1978).
Alexander et al. (1978) conducted acute toxicity tests with fathead minnows under static and flow-through
conditions; 96-hour LCso values for the flow-through and static tests were 52,800 /ig/L and 10,500 /tg/L,
respectively. The 48-hr LCso for D. magna exceeded the highest exposure concentration of 530,000 /tg/L (EPA,
1978).
A measured steady-state bioconcentration factor of 9 was observed for bfuegUl exposed to 1,1,1-TCA (EPA,
1978). Thus, significant bioconcentration is not expected to occur.
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TERRESTRIAL ECOSYSTEMS
Data regarding the toxicity of 1,1,1-TCA to plants, invertebrates, or avian or mammalian wUdlife were not
available in the literature reviewed.
4.2.1.3.3 Environmental Fate
1,1,1-TCA is released by evaporation to the atmosphere as a result of industrial practices (EPA, 1987a).
Reaction with hydroxyl radicals is the principle mechanism by which 1,1,1-TCA is removed from the troposphere
(EPA, 1984). The lifetime of 1,1,1-TCA in the troposphere is in the range of 5 to 10 years (EPA, 1984), and
the estimated half-life is one or more years (EPA, 1987a). Photo-oxidation products of 1,1,1-TCA include
hydrogen chloride, carbon oxides, phosgene, and acetyl chloride. 1,1,1-TCA is stable in the troposphere, and
significant amounts of the parent compound are conveyed to the stratosphere (EPA, 1984).
1,1,1-TCA is resistant to hydrolysis; the rate constant for hydrolysis at 25°C in unbuffered water at a pH of 7.0
is approximately 4 x 10'3 days (Nelly and Blau, 1985). The estimated half-life in water is greater than 6 months
(EPA, 1987a).
Data were unavailable in the literature reviewed regarding the environmental fate and persistence of 1,1,1-TCA
in soil.
4.2.1.4 Trichloroethylene
4.2.1.4.1 Ambient Levels
No known natural sources for TCE exist (EPA, 1985c). TCE is widely distributed in the aquatic environment,
and has been detected in drinking water supphes, natural waters, and aquatic organisms (EPA, 1980c; EPA,
1985c). TCE has been detected in human tissue, food supphes, and in air (Pearson and McConnelL 1975).
Detectable levels of TCE have been observed in groundwater used for water supphes from various areas; median
levels in finished waters from these sources were 0.31 pg/L (range 0.11 - 53.0 pg/L) (EPA, 1985c).
Contaminated wells and water supphes with levels as high as 330 pg/L have been reported (EPA, 1979).
Four percent of 330 groundwater wells across the U.S. had detectable levels of TCE; of these detections,
70 percent ranged from 0.5 to 5 pg/L (EPA, 1985c). TCE can increase as a result of chlorination; 32 percent
of finished water from surface water supphes has been found to contain TCE at levels ranging from 0.06 to
3.2 pg/L (mean levels 0.47 pg/L) (EPA, 1985c).
4.2.1.4.2 Health Effects
GENERAL
In humans, TCE has been observed to cause mild eye irritation, nausea, anesthetic, analgesic, behavioral, and
neurotoxic effects (EPA, 1985c). Most symptoms are a result of effects on the central nervous system.
Gastrointestinal and respiratory symptoms are frequently reported. Following chronic industrial exposures,
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central nervous system effects did not cease with termination of exposure (EPA, 1985c). Embryo toxicity and
teratogenicity have been observed in experimental animals. Significant increases in hepatocellular carcinomas
have occurred in male and female B6C3F1 mice, malignant lymphomas have occurred in female NMRI mice,
and renal adenocarcinomas have occurred in male Fischer 344 rats (EPA, 1985c).
The OSHA standard established in 1972 is 100 ppm (525 mg/m3) in air as a TWA over an 8-hour workday
(EPA, 1985c). NIOSH has determined this level to be too high for protection against carcinogenic effects, and
recommends a level of 25 ppm (EPA, 1985c). ACGIH has established a TLV of 50 ppm.
To protect human health from the carcinogenic effects of TCE ingested as a result of ingesting water or
contaminated aquatic organisms, the recommended level in water is zero (EPA, 1980b). Because zero may be
an unattainable goal, the levels in water that correspond to 10 s, 10"6, and 10"7 risk are 27, 2.7, and 0.27 pg/L,
respectively. If water is not ingested, but aquatic organisms will be consumed, the recommended levels in water
that correspond to the above risk estimates are 807, 80.7, and 8.07 pg/L, respectively (EPA, 1980b).
AWQC for the protection of freshwater aquatic life have not been established, however, data indicate that toxicity
to freshwater aquatic life occur at levels as low as 45,000 pg/L, and might be lower if more sensitive species were
tested (EPA, 1980b).
INGESTION
Because TCE is nonpolar, uncharged, and Upophihc, it can be expected to cross the gastrointestinal mucosa by
passive d_ffusion (EPA, 1985c). The principal target organs for orally exposed animals tend to be the hver,
kidney, and immunological system.
Tucker et al. (1982) reported an LD10 of 1,161 mg/kg bw for mice, and a single dose of 750 mg/kg bw did not
kill any mice. Mice acutely exposed (14 days) to 240 mg/kg bw/day TCE exhibited increased kidney weight, and
elevated ketone and protein levels were observed at these dose levels. Hematology effects (decreased red blood
cell count, altered coagulation and prothrombin time) were observed.
INHALATION
Humans exposed to 0, 100, 300, or 1,000 ppm (0, 538, 1,644, or 5,380 mg/m3) for 2-hour intervals exhibited
significant changes in depth perception and behavioral tests at the 1,000 ppm dose levels (Vernon and Ferguson,
1969). Changes in EEG were observed in workers exposed to 50 to 100 ppm TCE. Other workers exposed to
200 ppm for 7 hours/day for 5 days exhibited eye irritation, dryness of throat, and other mild symptoms (EPA,
1985c).
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Exposure to 30,000 ppm (161,000 mg/m3) for 20 minutes was lethal to dogs (Baker, 1958). Studies detailing
behavioral effects indicate activity level in rats significantly decreases following exposure to 1,000 to 1,200 ppm
(5354 to 6425 mg/m3) for a single exposure (EPA, 1985c). For multiple exposures over periods greater than 5
weeks, depressed activity occurred at levels as low as 100 ppm (538 mg/m3) (EPA, 1985c).
DERMAL TOXICITY
Dermal absorption occurs with direct contact; uptake is dependent on the type and area of skin exposed. The
dermal absorption rate in mice ranges from 7.82 to 12.1 pg/min/cm2, whereas in humans the rate is estimated
to be slow (EPA, 1985c).
Dermal irritation is observed foUowing exposure to TCE. Effects include reddening, skin burns, and generalized
dermatitis on contact with concentrated solution (EPA, 1985c). Contact with dilute aqueous solutions has not
been reported to cause dermal effects. A hypersensitive response was observed in humans (Phoon et al., 1984)
as a result of dermal contact through industrial exposure to vapor or solution at concentrations estimated
between 9 and 169 ppm and exposure durations of 2 to 5 weeks.
METABOLISM AND EXCRETION
In rats, approximately 90 to 95 percent of an oral dose of TCE was observed to appear in urine and expired air;
this indicates almost complete absorption by the oral route, as weU as mmcating the primary routes of excretion
(Daniel, 1963). Rapid absorption from the Gl tract is indicated by peak blood concentrations, which occur within
1 hour in mice and 3 hours in rats (EPA, 1985c). Administration of the dose in an aqueous vehicle, as opposed
to corn oU, reduces the absorption time significantly (EPA, 1985c).
The blood/gas partition coefficient is 9.92 at human body temperature (37°C). Thus, uptake of TCE in air by
the lungs is rapid (EPA, 1985c). TCE then distributes to aU body tissues, but tends to partition to lipids. TCE
crosses both the blood-brain and the placental barriers.
Biotransformation occurs in the hver to three principle metabolites (trichloroethanol, TCE-glucuronide, and
trichloroacetic acid) (EPA, 1985c). These metabolites are excreted in urine. TCE is also excreted unchanged
in expired air.
AQUATIC ECOSYSTEMS
TCE is acutely toxic to D. magna at levels of 85.2 mg/L in a static 48-hour LC^, test (EPA, 1978). Chronic tests
indicated no adverse effects on D. magna at 10 mg/L, the highest level tested (EPA, 1978). In a natural pond,
a single dose of 0.025 and 0.110 pg/L decreased D. magna populations, but increased phytoplankton populations
(Lay et al., 1984). The 96-hour LCJQ in a flow-through test with fathead minnows was 40.7 mg/L (Alexander
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et al., 1978). Behavioral effects have been observed in fathead minnows at levels as low as 21,900 pg/L (EPA,
1980b).
TCE does not accumulate in aquatic organisms to any great extent. Bioconcentration factors of 17 for bluegill
were observed after an exposure duration of 14 days (EPA, 1978). The biological half-life is less than one day,
suggesting that residue accumulation is not a concern for aquatic life (EPA, 1980b).
TERRESTRIAL ECOSYSTEMS
TCE has been observed in soil from industrial areas at levels of 5.6 pg/kg (EPA, 1985c).
4.2.1.4.3 Environmental Fate
Although TCE is relatively stable, it is not expected to persist in the environment because it photooxidizes in air,
it volatilizes from water, and it is not highly soluble in water (EPA, 1980b).
In air, vertical and horizontal mixing of TCE occurs, and transport is dependent on persistence of TCE, which
in turn is a function of free hydroxyl radicals (EPA, 1985c). Free hydroxyl radicals are the primary scavenging
mechanism for TCE in the atmosphere. The estimated lifetime for TCE is 54 hours (Edney et al., 1983),
assuming an atmospheric hydroxyl radical concentration of 106 molecules/cm3. Other estimates of atmospheric
residence times range from 11 to 15 days (EPA, 1985c). Approximately 20 percent of the TCE in air is expected
to be destroyed daily (Singh et al., 1979). Phosgene and dichloroacetyl chloride are the two principle degradation
products that have been observed in air as a result of photooxidation (EPA, 1985c).
TCE degrades slowly in water; estimated half-lives are 1-12 days in surface water (EPA, 1985c). Volatilization
is the major way TCE is lost from water; rate of volatilization from water depends on the aeration rate (EPA,
1985c). Smith et al. (1980) estimated a half-life of 3 hours in shallow rapidly moving streams, whereas a half-life
of 10 days or longer was estimated for ponds and lakes.
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4.2.2 SOURCE AND RELEASE CHARACTERIZATION
This section defines the most probable release mechanisms (such as volatilization or leaching) in relation to
contaminant sources at Plant 78, as well as likelihood of release of each of the indicator chemicals and the
probable magnitude of the releases. A release is any process that allows contaminants to migrate across the site
boundary. For the purposes of the risk assessment, each potentiaUy contaminated area (contaminant source)
within the Plant 78 boundary is considered as a separate area of concern.
4.2.2.1 Contaminant Sources
4.2.2.1.1 Faust VaUey Drainage Course
The FVD is approximately 4,500 feet long from the east to the west boundary, and approximately 5 feet wide
near the bottom of the ditch. The ditch is V-shaped and unlined.
The indicator chemicals were not detected in any media in the FVD during the Stage 1 sampling program
(Table 4-34). Numerous detections of 1,1,1-TCA were observed in the FVD sediments during the Stage 2
sampling program (N = 6; mean = 0.590 ± 0.253 mg/kg). These detections ranged from 0.108 to 0.824 mg/kg
(Table 4-35). The other indicator chemicals were not detected in FVD sediments during the Stage 2 sampling
program. The major probable release mechanisms for 1,1,1-TCA (the only indicator chemical observed at this
area of concern) from sediments is volatilization (sediment to air) and leaching (sediment to groundwater). All
of the indicator chemicals were detected in groundwater from momtoring weU P-1 during Stage 2; however, these
detections were suspect and were not used.
Fugitive dusts were not considered because of the volatility of the indicator chemicals, which makes the possibility
of exposure to fugitive dusts unlikely. Surface water was not sampled in the FVD during Stage 1 or Stage 2.
None of the indicator chemicals were detected in soils near the FVD. Volatilization from groundwater to air
is not considered a likely event due to the depth to groundwater (greater than 30 feet).
4.2.2.1.2 North Drainage Ditch
The NDD is an unlined ditch approximately 3,000 feet long from the beginning to the boundary, and
approximately 2 feet wide near the bottom of the ditch. NDD also includes the acid drain from BuUding E-519.
Two of the indicator chemicals (chloroform and TCE) were detected in NDD soils during the Stage 1 sampling
program, although only TCE was detected in soils during Stage 2 (one sample at 171 feet). None of the
indicator chemicals were detected in sediments from the Stage 1 or Stage 2 sampling programs. AU of the
indicator chemicals have been detected in surface water from the NDD during Stage 1 and 2, and aU were
detected in groundwater (monitoring wells P-3 and P-8) during Stage 2 (Tables 4-34 and 4-35).
4-131
P78-914/P78T4-34.1
02/14/92
Table 4-34. Concentrations of the Indicator Chemicals in each Media by Area of Concern - Stage 1 Sampling
Data. Values in parenthesis are the arithmetic mean + standard deviation and the number of
observations (N).
Soil
(Mg/kg)
Sediment
0*gAg)
Surface Water
(Mg/L)
Groundwater
(Mg/L)
FVD
Chloroform
1,2-DCA
1,1,1-TCA
TCE
NA
NA
NA
NA
NDD
Chloroform
1,2-DCA
1,1,1-TCA
TCE
0.11
0.25
0.057 - 1.15
(0.769 ±0.617; N=3)
0.10 - 13.0
(7.37±6.6; N=3)
0.068
E-512
Chloroform
1,2-DCA
1,1,1-TCA
TCE
0.100
2.60
M-585*
Chloroform
1,2-DCA
1,1,1-TCA
TCE
NA
NA
NA
NA
NA
NA
NA
NA
0.485
0.176
* Duplicates were averaged to obtain a single data point for each indicator chemical for each of the well
sampled. The single data point from each well was then averaged with that of the other well to obtain a
mean value for area M585.
NA = Not Analyzed
- = Not detected above instrument detection levels
4-132
P78-914/P78T4-35.1
02/14/92
Table 4-35. Concentrations of the Indicator Chemicals in each Media by Area of Concern - Stage 2 Sampling
Data. Values in parenthesis are the arithmetic mean ± standard deviation and the number of
observations (N).
Soil
(mg/kg)
Sediment
(mg/kg)
Surface Water
(Mg/L)
Groundwater
(Mg/L)
FVD
Chloroform
1,2-DCA
1,1,1-TCA
TCE
0.108 - 0.824
(0.524 +0.268; N=7)
NA
NA
NA
NA
Momtoring Well P-9
1.00 - 1.08
(1.04 ±0.04; N=2)
1.46 - 1.51
(1.48 ±0.025; N=2)
377 - 387
(382 ±5; N=2)
5,390 - 5,780
(5,585 ±195; N=2)
NDD
Chloroform
1,2-DCA
1,1,1-TCA
TCE
0.3871
0.262
4.29 - 9.93
(7.11±3.99; N=2)
7.53
0.626
Monitoring Wells P-3 and P-8
0.723 - 4.62
(2.66±1.92; N=4)
1.03 - 20.2
(12.11 ±8.11; N=3)
464 - 2,610
(1,479±1,018; N=4)
1,020 - 26,900
(13,657 ±12,456; N=4)
E-512.
Chloroform
1,2-DCA
1,1,1-TCA
TCE
0.43 - 0.473
(0.45 ±0.02; N=2)
4.17 - 4.22
(4.195±0.02; N=2)
Momtoring Well P-5
0.346
1.43
16.0
664
M-585
Chloroform
1,2-DCA
1,1,1-TCA
TCE 0.199 - 0.2982
(0.248 ±0.049; N=2)
NA
NA
NA
NA
Monitoring Well P-2. P-6. and P-7
NA 1.00 - 2,580
(1,290.5 ± 1,289.5; N=2)
NA 0.705 - 76.2
(39.04±30.83; N=3)
NA 0.266 - 3,320
(1,450 ±1,387.4; N=3)
NA 1,580 - 1,890
(1,735 ±155; N=2)
NOTE: A straight arithmetic mean and standard deviation were used for these calculations.
Non-detects were not valued in these calculations.
— = Not detected
NA = Not Analyzed
1 This value was detected in a sample collected at 171 feet below land surface.
2 These values were detected in samples coUected at 89 feet below land surface.
4-133
P78-914/P7S4D.134
02/14/92
Volatilization (surface water and soil to air) is the most probable release mechanism from the NDD. Leaching
from contaminated soil or surface water to groundwater is also a possible release mechanism at this area of
concern. Volatilization from groundwater to air is not considered a likely event due to the depth of the
groundwater (greater than 30 feet).
4.2.2.1.3 E-512 Drainage Ditch
The E-512 ditch is an unlined ditch approximately 1,000 feet long and up to 2 feet wide.
Chloroform and 1,1,1-TCA were detected in E-512 surface water during both the Stage 1 and Stage 2 sampling
programs. AU of the indicator chemicals were detected in groundwater at E-512 during the Stage 2 sampling
program. No detections occurred in Stage 2 soU or sediment samples (Tables 4-34 and 4-35).
Volatilization from soil to air was not considered a probable release mechanism for E-512 due to the lack of
surface soU or sediment contamination. Volatilization (surface water to air) and leaching (surface water to
groundwater) are the most probable release mechanisms in E-512. Due to the depth to groundwater (greater
than 30 feet), volatilization to air is not considered a significant pathway and will not be examined further.
Leaching from soil or sediments into groundwater was not considered a significant release mechanism in this
area because no contamination has been verified in these media.
4.2.2.1.4 M-585 French Drain
The M-585 drain is an underground disposal system without surface discharge. TCE was the only indicator
chemical detected in soil samples during the Stage 2 program. AU of the indicator contaminants were detected
in groundwater during the Stage 2 program. Momtoring wells P-6 and P-7 exhibited groundwater highly
contaminated with the indicator chemicals. The indicator chemicals chloroform and 1,1,1-TCA were detected
at low levels in groundwater from monitoring weU P-2 during the Stage 1 and Stage 2 sampling (Tables 4-34
and 4-35). TCE, chloroform, and 1,1,1-TCA were also detected in soU gas samples coUected from M-585.
The possible release mechanisms at this area of concern include volatilization from groundwater to air; however,
due to the depth to groundwater (greater than 30 feet), this exposure pathway is considered insignificant and wiU
not be examined further. Groundwater is not considered a release source but a mechanism of transport.
Groundwater contamination wiU be addressed further under Contaminant Fate and Transport. Volatilization
from soil, sediments, or surface water to air was not considered a probable release mechanism for M-585 due
to the lack of surface soU or sediment contamination, and lack of surface water.
4-134
P78-914/P784D.135
02/14/92
4.2.2.1.5 Blue Creek
Blue Creek is not considered a source because it is outside the Plant 78 boundary. Contamination in Blue Creek
is addressed under Section 4.2.3 (Contaminant Fate and Transport).
4.2.2.2 Quantitation of Potential Release Mechanisms
4.2.2.2.1 Particulate Release
Soil particulates may enter the atmosphere via natural forces, such as wind, or due to anthropogenic causes, such
as vehicular traffic. Residual contaminants bound to surficial soils may be transported as suspended particulates
or dusts, and thus, may migrate from source areas when environmental conditions are favorable. Factors
influencing the potential for dust entrainment into the atmosphere include surface roughness, surface soil
moisture, soil particle sizes, kind and amounts of vegetative cover, amount of soil surface exposed to the eroding
wind force or vehicular traffic, physical and chemical properties of the soil, wind velocity and other
meteorological conditions (EPA, 1989). The only surface locations found to contain the contaminants of concern
(COCs) at Plant 78 include sediments in the FVD and Blue Creek. These sediments are typically kept moist
due to surface water flow and are protected from the eroding force of the wind by the depth of these drainage
ditches. These factors combine to inhibit the formation of fugitive dusts from the FVD and Blue Creek.
Because surface contamination was not observed at the other source areas, fugitive dusts are not considered to
be a significant release mechanism for Plant 78.
4.2.2.2.2 Volatilization from Soil or Sediments
Volatilization from surface soil or sediment is predicted by assuming that the soils were uniformly contaminated
to a depth of approximately 5 feet (1.52 m). For this scenario, the mathematical description of Thibodeaux and
Hwang (1982) has been adapted to estimate the air exposure concentration. The volatilization flux (q.)
(mg/m2-sec) was expressed as:
(1)
\2xt2
where: De
C.
effective diffusion constant (m2/sec),
concentration in soil or sediment in mass per unit volume (mg/m3) [Ctoil or
C^d (mg/kg) x p (kg/m3)], and
t time in seconds.
4-135
P78-9M/P784D.136
02/14/92
The effective diffusivity (D.) is a function of the molecular difnisivity of the contaminant in air (D_), the
molecular ch_fusivity of the contaminant in water (Dw), the soil-water partition coefficient (KJ, as weU as the
specific porosity characteristics of the contaminated soil. However, when the Henry's Law constant is small (less
than 1), the gas phase resistance is much greater than the liquid phase resistance (i.e., water diffusivity is much
lower than air diffusivity). Thus, the water diffusivity may be reasonably neglected, and D. may be expressed,
based on the effective cliffusion coefficient equations of Jury et al. (1983) as:
where: n, = air-filled porosity (0.1),
n~ = water-filled porosity (0.3),
n = total soil porosity (0.4),
Da = contaminant molecular diffusivity in air (m2/sec),
H° = dimensionless Henry's Law constant,
K„ = adsorption or soil-water partition coefficient (mL/g), and
p = bulk density (assumed to be equal to 1.6 g/mL or 1.6 x 103 kg/m3).
The important parameters used in the evaluation of De for chloroform and TCE from the NDD and for
1,1,1-TCA from FVD are summarized in Table 4-36. TCE from M-585 was not included in this analysis because
the depth of contamination was 89 feet below ground surface. Volatilization from this depth would not be
reasonably expected. The organic carbon content of the soil (foc) was assumed to be 2 percent (ESE, 1989).
The values of the soil parameters indicated in the parenthesis in equation (2) are standard values.
Substituting the values into equation (2) provides the foUowing effective diffusion coefficients for the observed
indicator chemicals:
Chemical D. (m2/sec)
Chloroform 3.02 x 10"9
1,1,1-TCA 2.69 x IO"9
TCE 2.21 x 10"9
The time required to deplete the soU of contaminants is approximately the same as the time for contamination
at the bottom of the soU column to a_ffuse to the surface.
4-136
P78-914/P78T4-36.1
02/H/92
Table 4-36. Parameters used in the estimation of volatilization fluxes of contaminants from soils or sediments.
Contaminant Mol. Wt. Kj K,, H° Da
(g/mole) (mL/g) (x 103 m3/kg) (cm2/sec)
Chloroform 119 31 0.62 0.12 0.086
1,1,1-TCA 133 152 3.04 0.59 0.082
TCE 131 126 2.52 0.37 0.083
* Kd = K-,. x foc, where foc (fraction of organic carbon) is estimated as 0.02.
4-137
P78-914/P784D.138
02/14/92
The diffusion time scale in days (tj) is defmed as:
where: h = distance between the surface and depth of contamination.
Using De from above and an assumed uniform depth of soil contamination of 1.52 meters (5 feet), td becomes:
Chloroform 7.65x10s sec ( ~ 24 yr)
1,1,1-TCA 7.99xl08 sec ( ~ 25 yr)
TCE 1.05x10s sec (-33 yr)
When the actual diffusion time td is greater than 32 years, the contaminant flux will cease, suggesting that all of
the contamination has aUffused to the soil surface. Since the flux decreases with time, exposure concentrations
will decrease also. For this exposure risk assessment, an average flux (q_) for the exposure period is needed.
This average flux over any exposure period from t, to t2 can be expressed as:
h
(4)
)
Using equation (1) for q. and integrating from tj = 0 to t2 = td yields:
a, = f
tl
(5)
where: [CsoJ x p = contaminant concentration in mass per unit volume of soil as defined
in equation (1).
Equation (5) was used to estimate the volatilization flux rates of 1,1,1-TCA from FVD sediments observed during
Stage 2 samphng and of chloroform and TCE from NDD soils observed during Stage 1 sampling. The results
are presented in Table 4-37.
4-138
P78-914/P78T4-37.1
02/14/92
Table 4-37. Volatilization Flux Rates of Contaminants in Soil or Secliment.
De Csoil or Csed* Flux Rate
Area (m2/sec) (mg/kg) (mg/m2-sec)
FVD
1,1,1-TCA 2.89 xlCr9 0.824 5.01 x IO"6
NDD
Chloroform 3.02 x 10'9 1.1 x 10"* 6.99 x 1010
TCE 2.21 xlO"9 25x10* 1.16 x 1010
* Values derived from Tables 4-34 and 4-35.
4-139
P78-914/P784D.140
02/14/92
4.2.2.2.3 Volatilization from Surface Water to Air
The volatilization rate of contaminants from surface waters in the NDD and E-512 areas was predicted according
to EPA (1988). The flux of a volatilizing chemical (q_,) in mg/m2-sec was calculated from:
q_«r = C_, (6)
where: = volatilization rate constant (m/sec), and
C_, = contaminant concentration in surface water (mg/m3 or /ig/L).
The parameter k, can be evaluated from the two-film theory, in which the volatilization rate constant is given
by:
(*v r1 = (^ r1 + ( H° kg r1 0)
where: k, = mass transfer coefficient in the liquid phase (m/sec),
kg = mass transfer coefficient in the gas phase (m/sec), and
H° = dimensionless Henry's Law constant.
The mass transfer coefficients in equation (7) were evaluated by estimating the environmental parameters
presented in Table 4-38. These parameters were assumed to be the same for NDD and E-512 drainage areas.
The foUowing calculations were performed to determine k,. First, the surface transfer rate of dissolved oxygen
(k.') in feet/day was estimated as foUows:
*; = Kz (g)
where: lc. = oxygen reaeration coefficient (day1), and
z = stream depth (feet).
Based on Owens empirical expression (Thomann, 1972):
1/0.67
k = 21.6 x — (9)
' -1.85
where: V = stream or ditch linear velocity in ft/sec, and
z - stream depth in feet.
4-140
P78-914/P78T4-38.1
02/14/92
Table 4-38. Enviroiunental parameters used in the estimation of contaminant volatilization flux
from NDD and E-512 surface water.
Parameter Value
Stream depth (z) 0.75 ft.
Stream width (w) 2.0 ft.
Stream linear velocity (v) 0.5 ft/sec
Wind Speed (Vw) 9.8 ft/sec (3 m/sec)
4-141
P78-914/P784D.142
02/14/92
Substituting the values from Table 4-38 into equation (9), the oxygen reaeration coefficient becomes:
K = 2L6 x i°___!L (10>
(0.75)185
to yield a k. of 23 day"1. This k_ value can then be used along with z (0.75 feet) to determine the surface transfer
rate of dissolved oxygen (k.') defined by equation (8). The surface transfer rate is converted to (m/sec) as
follows:
v-(5H«">«m"(_ day
.64 x 104 sec
to yield a k_' of 6.08 x IO"5 m/sec.
Once k,' is known, the mass transfer coefficient of the chemical in the liquid phase can be estimated as follows:
1 { MW j
where: k, and k.' have units of (m/sec), and
MW is the molecular weight of the contaminant.
Substituting the value for k_' into equation (11), the mass transfer coefficient in the liquid phase becomes only
a function of the molecular weight of the chemical:
k = { J2- r5
X ( 6.08xl0"5 ) (12) 1 \ MW )
To calculate k8 in equation (7), the following equation was used:
s [ MW ) '
The gas phase transfer rate (kg') in cm/hr was obtained from an empirical relationship developed by Mills (EPA,
1988), who showed that:
kJ = 700K (14)
a w
where: Vw = wind speed in m/sec.
4-142
P78-914/P784D.143
02/14/92
With a wind speed of 3 m/sec (see Table 4-38), kg' becomes:
kg' = (700)(3)
= 2100 cm/hr
= 5.80 x IO"3 m/sec.
Substituting kg' into equation (13), the mass transfer coefficient in the gas phase becomes only a function of the
molecular weight of the chemical:
equation (15), respectively. The volatilization rate constant (k,,) for each contaminant was then determined by
substituting kj, k„ and H° in equation (7). The results are presented in Table 4-39.
The maximum surface water concentration (C_,) of each contaminant and the calculated ky were used in
equation (6) to estimate the mass of contaminant volatilizing from a unit area of surface water per unit time.
Table 4-40 presents the flux calculation results. These estimates are conservative because maximum
concentrations were used to predict flux, and surface water is periodic and does not actually provide a continual
flux.
4.2.2.2.4 Volatilization from Groundwater to Air
Volatilization from groundwater to air was not considered a probable release mechanism because the aquifers
in the Plant 78 area are 30 feet or more below the ground surface.
4.2.2.2.5 Leaching from Surface Water to Groundwater
Precipitation is expected to have a minimal impact on leachate generation, because liquid waste will percolate
to the water table due to gravity (EPA, 1988) and because rainfall is minimal (maximum nearly 20 inches or
50.8 cm/yr; average rainfall 14.88 inches or 37.80 cm/yr). A form of Darcy's law was used to estimate volumetric
flux from the surface water source (EPA, 1988):
(15)
Usmg the molecular weights of the contaminants, the values of k, and kg were evaluated from equation (12) and
Q, = K. x i x A (16)
where: Q,
K.
= volume loading rate (L/day),
= Darcy's coefficient or soil hydrauhc conductivity (feet/day),
= hydrauhc gradient (feet/feet), and
= area (ft2).
I
A
4-143
F.8-914/P78T4-39.1
02/14/92
Table 4-39. Volatilization rate constants and mass transfer coefficients of the contaminants from
NDD and E-512 areas.
Contaminant MW K, Kg H° K,
(g/mole) (m/sec) (m/sec) (m/sec)
Chloroform 119 4.4 x 10 s 3.6 x 10'3 0.12 4.0 x10 s
1,2-DCA 99 4.6 x 10 s 3.8 x IO"3 0.04 3.5 x IO"5
1,1,1-TCA 133 4.3 x 10 s 3.5 x IO"3 0.59 4.2 x 10 s
TCE 131 4.3 x 10 s 3.5 xlO"3 0.37 4.2 x 10 s
IQ - mass transfer coefficient, liquid phase.
K. - mass transfer coefficient, gas phase.
K, - volatilization rate constant.
H° - Henry's Law Constant.
4-144
P78-9.4/P78T<M0.1
02/14/92
Table 4-40. Contaminant volatilization fluxes from surface waters in NDD and E-512 Drainage Ditches.
Contaminant k, C_, q_„
(m/sec) (mg/m3)* (mg/m2-sec)
NDD
Chloroform 4.0 x 105 1.15 4.6 x 10'5
1,2-DCA 3.5 xlO"5 9.93 3.5x 10^
1,1,1-TCA 4.2 x 10 s 13.0 5.5x10^
TCE 4.2 xlO"3 0.626 2.6 x 105
E-512
Chloroform 4.0 x 10 s 0.473 1.9x10*
1,1,1-TCA 4.2 x 10 s 4.22 1.8 x 10"4
* Maximum observed concentrations from Tables 4-34 or 4-35 (1 mg/m3 = 1 /tg/L).
4-145
F78-914/P784D.146
02/14/92
Substituting values into equation (16) gives the foUowing results:
K. = 7.21 x 1CT4 ft/day,
i = 0.0079 ft/ft,
A = area of 2000 ft2 for the E-512, and an area of 6000 ft2 for the NDD.
Qj = 0.011 L/day for the E-512, and 0.034 L/day for the NDD.
The value for K, is an average of the range in Chadwick et al. (1975).
The volume loading rate is used to calculate contaminant loading rate (pg/day) with an equation developed for
lagooned fluids:
Lc = CsxQ1 (17)
where: Lc = contaminant loading rate (pg/day),
Ct = contaminant concentration in fluid (pg/L), and
Qj = volume loading rate (L/day).
This equation is appropriate for use with lagooned fluids, where the ground beneath the source is saturated.
When the ditches have liquid in them, this probably is representative of the situation, because the ditches are
unlined and the soU is absorptive. During winter sampling efforts, ponded water was observed in the NDD and
E-512.
The volume loading rates from surface water to groundwater are presented in Table 4-41.
4.2.2.2.6 Release to Groundwater (Leaching)
The FVD and the NDD are the only areas of concern on Plant 78 that exhibit a potential for leaching from soU
or sediment to groundwater. Soils in the M-585 area also contain a constituent of concern (TCE), however, this
contamination was present only at a depth of 89 feet below ground surface. This depth precludes any significant
leaching at the M-585 area because precipitation events at the surface are not expected to provide sufficient
hydrauhc loading to leach constituents from soU at a depth of 89 feet. The soU sample in which TCE was
detected at the NDD during Stage 2 was also excluded from this analysis because it was coUected from a depth
of 171 feet below the land surface. Sohd material (contaminants in soU) wiU dissolve into percolating
precipitation and migrate as a solute. Precipitation provides the hydrauhc loading that drives the rate of release.
4-146
P78-9.4/P78T4-41.1
02/14/92
Table 4-41. Release Rates from Surface Water to Groundwater.
Analyte Cs Lc
(Mg/L) 0*g/day)
NDD
Chloroform 1.15 0.039
1,2-DCA 9.93 0.338
1,1,1-TCA 13.0 0.442
TCE 0.626 0.021
E-512
Chloroform 0.473 0.0052
1,1,1-TCA 4.22 0.046
4-147
P7W1./P784D.148
02/14/92
The loading rate (Lc) to groundwater can be calculated using the following general equation (EPA, 1988) for
landfilled sohds:
Lc = qxAxC0 (18)
where: Lc - contaminant loading rate (mass/time),
q = percolation rate (length/time),
A = area of contamination (length squared), and
C„ = equihbrium solubility of the contaminant.
The percolation rate (q) is defined as the depth of downward water movement over time. It is estimated by the
foUowing equation (EPA, 1988):
q = HL + Pr - ET - Qr (19)
where: HL = hydrauhc loading from manmade sources (depth per unit time),
Pr = precipitation (depth per unit time),
ET = evapotranspiration (depth per unit time), and
Qr - runoff (depth per unit time).
Data regarding hydrauhc loading from manmade sources and local runoff conditions were unavailable. For this
analysis, it was assumed that the extent of both of these quantities is slight (negligible), and as a result, they were
disregarded.
Short-term leaching into groundwater is predicted from a maximum yearly rainfall estimate of nearly 20 inches
(50.8 cm/yr). Evapotranspiration (ET) is estimated by using measured Class A pan evaporation rates in the
foUowing equation (EPA, 1988):
ET = EVAP x Cet x Qeg (20)
where: EVAP = site specific or region specific evaporation rate,
Cet = correction factor for converting evaporation rates to evapotranspiration rates
from turf grass, and
Cv.g = correction factor for converting evapotranspiration from turf grass to
evapotranspiration from other vegetative cover types.
4-148
P7W14/P784D.149
02/14/92
Values for Ctt (0.5) and Q,„ (0.6) were obtained from EPA (1988), based on site specific conditions (moderate
winds of 170-425 km/day, relative humidity of 40-70 percent). The annual evaporation rate value of 50 inches
(127 cm/yr) was obtained from Farnsworth et al. (1982).
Therefore:
ET = 127 cm/yr x 0.5 x 0.6
= 38.1 cm/yr
These values were substituted into equation (19) to calculate the short-term percolation rate for the site,
q = 50.8 cm/yr - 38.1 cm/yr
= 12.7 cm/yr
The long-term percolation rate is predicted from the average yearly rainfall estimate of nearly 15 in/yr
(38.1 cm/yr). Using the same value of ET calculated above, the long-term percolation rate is estimated to be
0.0 cm/yr (i.e., precipitation equals evapotranspiration). For calculation purposes, it was assumed that 1 cm/yr
is available for percolation to groundwater for the long-term estimate.
The concentration of the indicator chemicals in the percolating water is estimated for both short- and long-term
exposures with K-,. and the mean soil/sediment concentration in each area of concern:
*" • F^T <21)
water Joe
where: K^. = soil water partition coefficient normalized for organic carbon,
foc = fraction of organic carbon in soil or sediment,
Qou = concentration in soil or sediment (as mg/kg), and
= concentration in water at equilibrium (as mg/L).
Rearranging equation (21) to solve for the concentration in water yields:
C C*°a (22)
An organic carbon content of 2 percent was assumed for the sediment and soil at Plant 78.
4-149
P78-914/P784D.150
02/14/92
Using the preceding equations, the short-term and long-term loading rates for the indicator contaminants were
estimated for the FVD and the NDD.
FVD
The estimated area of the FVD is 20,902,500 cm2. The loading rate of 1,1,1-TCA in the groundwater at Plant 78
(FVD) is estimated for both short- and long-term exposures.
The long-term loading rate (Lcl) of 1,1,1-TCA at the FVD is estimated to be:
Ld = 1 cm/yr x 20,902,500 cm2 xCD
where: CQ = C_0lJ
Kg,, x f o-
C0 = 0.59 mg/kg
152 L/kg x .02
= 0.194 mg/L
then: Lcl = 20,902,500 cm3/yr x 0.194 mg/L
= 4,055 mg/yr
= 4.06 g/yr
The short-term loading rate (L_) for 1,1,1-TCA at the FVD is estimated to be:
La = 12.7 cm/yr x 20,902,500 cm2 x 0.194 mg/L
= 51,500 mg/yr
= 51.5 g/yr
NDD
The area of the NDD is 5,574,000 cm2. The loading rate of TCE and chloroform in the groundwater at Plant 78
(the NDD) are estimated for both long- and short-term exposures.
The long-term loading rate of TCE at the NDD is estimated to be:
Lcl = 1 cm/yr x 5,574,000 cm2 x C0
where: C0 = C__01j
x fo-
C0 = 2.5 x 10"* mg/kg
126 L/kg x 0.02
= 9.92 x 10 s
4-150
P78-914/P784D.151
02/14/92
then: Lcl = 5,574,000 cm3/yr x 9.92xl0"5 mg/L
= 0.553 mg/yr
= 5.53x 10"* g/yr
The short-term loading rate for TCE at the NDD is estimated to be:
L_ = 12.7 cm/yr x 5,574,000 cm2 x 9.92x10 s mg/L
= 7.02 mg/yr
= 7.02 x 10'3 g/yr
The long-term loading rate of chloroform at the NDD is estimated to be:
Ld =1 cm/yr x 5,574,000 cm2 x C0
where: C0 = C„„
C0 = 1.1 x 10^ mg/kg
31 L/kg x 0.02
= 1.77x10^
then: Lcl = 5,574,000 cm3/yr x 1.77X10"4 mg/L
= 0.987 mg/yr
= 9.87 xlO4 g/yr
The short-term loading rate for chloroform at the NDD is estimated to be:
L_ = 12.7 cm/yr x 5,574,000 cm2 x 1.77X10"4 mg/L
= 12.5 mg/yr
= 1.25 x 10'2 g/yr
The predicted short- and long-term mass release rates due to leaching are summarized in Table 4-42. All of the
estimated loading rates to groundwater are low and suggest that leaching to groundwater is not a significant
release mechanism. Average annual precipitation in the area is so low that when accounting for
evapotranspiration, there is no net percolation into the soil. Percolation of water and leaching of contaminants
may more likely occur as a result of plant-generated water flowing through the ditches. However, due to dry
conditions during sampling periods, data are insufficient to predict loading rates for gravity influenced liquid
waste percolation.
4-151
P78-914/P78T4-42.1
02/14/92
Table 4-42. Summary of Release Mechanisms and Releases by Area.
Release Mechanism Area of
Concern
Chemical Flux Rate
(mg/m2-sec)
Mass Release
(g/yr)
Volatilization
(sediment/soil to air)
(surface water to air)
FVD
NDD
NDD
E-512
1,1,1-TCA
CHCI3
TCE
CHCI3
1,2-DCA
1,1,1-TCA
TCE
CHCI3
1,1,1-TCA
5.01 x IO"6
6.99 x 1010
1.16 x 10'9
4.6 x 10"5
3.5 x 10"4
5.5 x 1Q~*
2.6 x 10*
1.9 x 10 s
1.8 x IO"1
Leaching
(sediment/soil to groundwater) FVD
NDD
(surface water to groundwater) NDD
E-512
1,1,1-TCA
CHCI3
TCE
CHCI3
1,2-DCA
1,1,1-TCA
TCE
CHCI3
1,1,1-TCA
51.5 (4.06)1
1.25 x 10"2
(9.87 x 10"4)
7.02 x 10'3
5.53 x 10^
1.4 x 10*
1.2 x IO4
1.6 x 10"4
7.7 x IO"6
1.9 x 10 s
1.7 x 10*
1 Short-term (long-term) mass release rates.
4-152
P78-914/P784E.153
02/14/92
The volumetric flow rate of the groundwater under the FVD was estimated based on the hydrauhc conductivity
of the aquifer, the thickness of the aquifer, the width of the aquifer at the point of loading, and the effective
porosity of the aquifer. The hydrauhc conductivity of the aquifer was estimated to be 0.88 feet/day. The
thickness of the aquifer was assumed to be 50 feet and the width of the aquifer at the point of loading was
assumed to be 290 feet. The effective porosity of the aquifer was assumed to be 0.33. Using these assumptions,
a volumetric flow rate of 4,210 fP/day or 1.19 x 105 L/day was calculated.
Combining the loading rate of 1,1,1-TCA at the FVD with the volumetric flow rate yields an estimated short
term concentration of 1.19 x 10"3 mg/L, and a long term concentration of 9.35 x 10'5 mg/L directly below the
FVD.
For the NDD, all of the assumptions for the estimates of the volumetric flow rate are the same as for the FVD,
except for the width of the aquifer at the point of loading. For the NDD, the width was assumed to be 900 feet.
Using this information, a volumetric flow rate of 13,068 tf/day or 3.70 x 10s L/day was calculated.
4.2.3 TRANSPORT AND FATE OF CONTAMINATION
In this section, the fate and transport of contaminants is arranged by media. Transport media are the means
by which contaminants may move from the area of concern to offsite locations. The environmental transport
media are air, surface water, and groundwater. Another transport medium consists of contaminated game
species (aquatic or terrestrial) that may move on and off the site. However, due to the low bioaccumulation
potential (as indicated by fish BCF in Table 4-31), neither aquatic nor terrestrial biota are expected to be
significant transport mechanisms offsite. Thus, only transport of contaminated surface water, groundwater, or
air are of concern. To arrive at a conservative estimate, exposure point concentrations were calculated without
considering biological transformation.
4.2.3.1 Surface Water Fate
The ditches on Plant 78 (NDD, FVD, and E-512) are periodically dry. At one time, the ditches carried industrial
wastewaters, but that practice has been discontinued. Currently, the ditches primarily carry storm runoff. The
FVD has been dry during all ESE sampling activities (Stage 1 and Stage 2) at Plant 78. The surface water in
the ditches flows from east to west towards Blue Creek. The direction of surface water flow in Blue Creek is
from north to south along the western boundary of the site.
The contaminants of concern were detected in surface water from the NDD and E-512 ditch (Tables 4-34
and 4-35). Two of the indicator chemicals (1,2-DCA and 1,1,1-TCA) have been detected in Blue Creek
upgradient of Plant 78 (Figure 4-32). Given the distance involved (1 mile upstream of the site), it is highly
unlikely that 1,2-DCA observed upgradient in surface water at levels exceeding 4 /tg/L is site-related. Similarly,
4-153
P7S-91./P784E.154
02/14/92
1,1,1-TCA detected in sediments about 500 feet upgradient of the northern boundary of Plant 78 at
concentrations of 1.02 mg/kg is probably not site related.
Instead of using models to predict runoff to Blue Creek, monitoring data were used to indicate transport and
exposure point concentrations of the indicator chemicals offsite (Table 4-43). These data indicate that levels of
the indicator contaminants in Blue Creek increase at a point midway between the north and the south boundaries
of the plant (Figures 4-38 and 4-39). The concentrations then decrease downgradient until, at the south
boundary, the concentrations of chloroform and 1,1,1-TCA are below detection in surface water and seciiments
and 1,2-DCA in surface water is at or below the concentrations observed upgradient of the plant. The single
detection of TCE in surface water is suspect. It is close to the detection limit, and less than the certified
reporting limit. While TCE may be present in surface water from Blue Creek, levels are low and could not be
quantified. This detection of TCE was not used further in the quantitative risk assessment.
Blue Creek is a contaminant transport mechanism. However, volatilization from surface water may occur.
Volatilization flux rates were calculated as previously described in equations (7) through (15) of Section 4.2.2.
The environmental parameters for Blue Creek (Table 4-44) are different from those used to estimate
contaminant volatilization fluxes for NDD and E-512. Wind speed was unchanged from prior calculations.
Volatilization is expected to be the primary removal mechanism of the indicator chemicals from surface water
in Blue Creek. Based on available persistence information for each of the indicator chemicals (Table 4-45),
only 1,1,1-TCA is expected to remain in surface water for any length of time (half-life of greater than 180 days).
The estimated half-lives of the other indicator chemicals are much lower; 1,2-DCA has a half-life of less than
1 day, and minimum estimates for chloroform and TCE are both 1 day. Maximum half-life estimates for
chloroform and TCE are 31 and 12 days, respectively (Table 4-45).
At this time, leaching from sediments in Blue Creek into groundwater cannot be estimated, due to inadequate
data regarding the water balance between Blue Creek and the underlying aquifer. Considering the low levels
of contaminants observed in surface water and sediments, significant groundwater contamination due to leaching
is not expected to occur.
Using the values in Table 4-44 in equations (9) and (10), the oxygen reaeration coefficient (k,) and oxygen
surface transfer rate (k_') were obtained:
k. = 28.3 day1
V = 9.98 x 10 s m/sec
4-154
P78414/F"78T4-43.1
02/14/92
Table 4-43. Concentrations of the Indicator Chemicals in Blue Creek Sediments and Surface Water.
Sediment
(mg/kg)
Surface Water
(Mg/L)
STAGE 1
Chloroform
1,2-DCA
1,1,1-TCA
TCE 0.070
STAGE 2
Chloroform
1,2-DCA
1,1,1-TCA
TCE
0.100 - 1.02
(0.44+0.41; N=4)
0.608
0.611 - 27.7
(8.87 ±8.34; N=9)
0.615
NOTE: Samples coUected upstream from Blue Creek were included in calculations because they were treated
as a resident concentration being introduced into Plant 78 waters.
= Not detected
4-155
P78 STAGE 2 05/91 PFIC 4-40
BC-SWS1S LOCATED ONE MIL-OP GRADIENT ON BLUE CREEK
|l.2-PCA 4.4Q ug/L|
BC-SS7
Jh.1.1—TCA 1.02 mg/kg|
BC/MO
CLCH3 0.08 ug/l CK2CHCL 0.32 ug/l IC6H6 0.74 ug/l AIR FORCE PLANT 78
' BC-SWS13
' ND/BC
CLCH3 0.453 ug/L CH2CHCL 0.2M ug/L 1,2-DCA 4.54 ug/L 1,1,1-TCA 0.615 ug/L TCE 0.473 uq/L
EVAPORATION
CLCH3 2.166 ug/L
1.2-DAC 15.5 ug/L
1.2-PCP 0.668 ug/L
1,1,1-TCA 0.304 mg/kg
P«t HC 66.5 mg/kg
Xylwwi 3.62 ug/L
1,2-DCA 2.02 ug/L
PCt 1.43 ug/L
CLCH3 0.472 ug/L
1,2-DCA 8.26 ug/L
1.2-DCP 0.24 ug/L
BC-SS3
Pal. HY 887
BC-SWS6
CLCH3 3.7* 3.74 ug/L
1.2-DCA 27.7 ug/L
1,2-DCP 1.22 ug/L
2-CHVE 0.73 ug/L
PCE 0.35 ug/L
-PRDPFRTY I IMF
BC-SWSIO
CLCH3 2.66 ug/L
1,2-DCA 14.0 ug/L
1.2-OCP 0.62 ug/L
ICLCH3 0.19 ug/L
| TCE 0.07 ug/L
LEGEND
O SAMPLING EPISODE 1 (DECEMBER 1988)
• SAMPLING EPISODE 2 (MARCH 1990)
+ STAGE 1 SAMPLES
A STAGE 2 SHALLOW SOIL BORING SAMPLES
1,1,1-TCA 4' 0.113 mg/kg
1,1,1-TCA 8' 0.068 mg/kg
0 100 MO SOO 400 SOO
Figure 4-38
STAGE 1 AND STAGE 2 SAMPLE
RESULTS, BLUE CREEK NORTH
SOURCE: ESE. 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-156
P7B STAGE 2 05/91 PflO 4-41
AIR FORCE PLANT 78
PROPERTY LINE LEGEND
O SAMPLING EPISODE 1 (DECEMBER 1988)
• SAMPLING EPISODE 2 (MARCH 1990)
-f- STAGE 1 SAMPLE
N
CLCH3 0.21 ug/l
MECL 0.47 ug/l
s
0 100 200 300 400 500
Figure 4-39
STAGE 1 AND STAGE 2 SAMPLE
RESULTS, BLUE CREEK SOUTH
SOURCE: ESE, 1991.
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-L57
P78-914/P78T444.1
02/14/92
Table 4-44. Average values of the envhonmental parameters used in the estimation of contaminant
volatilization fluxes from Blue Creek.
Parameter Value
Depth 1 ft
Width 12 ft
Linear velocity 1.5 ft/sec
Wind speed 9.8 ft/sec (3 m/sec)
4-158
P78-914/P78T4-45.1
02/14/92
Table 4-45. Summary of Fate of Contaminants of Concern in Abiotic Media.
Half Life (davs) Primary Removal
Air Surface Water Groundwater Soil Mechanism
Chloroform 80 0.3 - 30 - ~ Volatilization
1,2-DCA 36 - 127 0.005 - 0.2 ~ Months to Volatilization
years
1,1,1-TCA >365 >180 >180 ~ Volatilization
TCE <10 1-12 - - Volatilization,
Photooxidation
Source: EPA, 1986.
4-159
P78-914/P784E.160
02/14/92
Mass transfer coefficients were obtained with equations (11) and (13). The equations for the mass transfer
coefficient in the liquid phase (k,) (including k,') and the mass transfer coefficient in the gas phase (kg)
(including kg') are as follows, respectively:
= (9 98 x io-5) (23)
' \MW)
^-T'25 (5.83 x 10"3) (15) K = P^f'25 (5.83 x 10"3) * \MW)
Substituting the molecular weights of chloroform, 1,2-DCA, 1,1,1-TCA and TCE into equations (23) and (15)
and using the resulting k, and kg values in equation (8), (lc,)"1 = (k,)'1 + (H°k^~l, the volatilization rate constants
(ky) were obtained. The results are presented in Table 4-46.
The maximum surface water concentrations (Cw) from Stage 1 and Stage 2 sampling events (Tables 4-34
and 4-35) were used in equation (6), (q^ = l^C,,,), to estimate the volatilization flux rates (Table 4-47). A flux
rate is not given for TCE, because data evaluation indicated that this detection was very close to the CRL, and
is therefore a questionable value.
4.2.3.2 Groundwater Fate
Groundwater from the Plant 78 area flows westward down the face of the Blue Spring Hills and is diverted 90
degrees, flowing south at the center of the valley (Bolke and Price, 1972). The upper and deeper shallow
aquifers at Plant 78 are contaminated in two separate areas. One plume exists in the northern section of
Plant 78 near the NDD, FVD, and Building E-519 (momtoring wells P-3, P-5, P-8, and P-9). The second plume
exists in the area near site M-585 (monitoring wells P-2, P-6, and P-7). Estimated half-lives for the indicator
chemicals in groundwater are in the range of months to years.
To predict the time it would take for the contaminants to migrate from the shallow aquifers toward downgradient
areas, it was assumed that a slug or parcel of the chemical would move with the groundwater from the source
along the groundwater flow path toward the site boundary and Blue Creek. As the groundwater flows, the
contaminant also moves, but at a slower speed due to retardation by adsorption. This chemical transport velocity
(Vc) in feet/year can be expressed as:
Vc = _V (24)
Rd
where: V^ = groundwater flow velocity (feet/year), and
Rd = retardation factor.
4-160
P78-914/P78T4-46.1
02/14/92
Table 4-46. Volatilization rate constants and mass transfer coefficients for contaminants from Blue Creek.
Contaminant MW K, Kg H°
(g/mole) (m/sec) (m/sec) (m/sec)
Chloroform 119 7.19 x IO5 3.64 x IO"3 0.12 6.15 x 10 s
1,2-DCA 99 7.53 x 10 s 3.81 x IO 3 0.04 5.04 x10 s
1,1,1-TCA 133 6.99 x10 s 3.54 xlO"3 0.59 6.76 x 10 s
TCE 131 7.02 xlO"5 3.55 x IO"3 0.37 6.66 x 10 s
Kj - mass transfer coefficient, liquid phase.
Kg - mass transfer coefficient, gas phase.
Ky - volatilization rate constant.
H° - Henry's Law Constant.
4-161
P78-914/P78T4-47.1
02/14/92
Table 4-47. Summary of Release Mechanisms and Flux Rates for Blue Creek.
Flux Rates (mg/m2-sec)
Area of Concern Release Mechanism Chloroform 1,2-DCA 1,1,1-TCA TCE
Blue Creek Volatilization 3.74 x 10 s 1.40 x IO 3 4.16 x10 s
4-162
P78-914/P784E.163
02/14/92
Groundwater flow velocity was estimated by averaging flow velocities at monitoring wells P-6 and P-7 for M-585
(monitoring well P-2 was not included), and by averaging flow velocities at monitoring wells P-3, P-5, P-8, and
P-9 for the northern plume:
M-585 WeU feet/dav NDD
P-6
P-7
Mean
0.63
0.99
0.81
WeU
P-3
P-5
P-8
P-9
Mean
feet/dav
1.63
0.17
0.86
0.85
0.88
Rephcate values for monitoring weU P-7 were averaged before calculating for M-585. Groundwater flow
velocity at monitoring weU P-6 was 0.63 feet/day, and at monitoring weU P-7 was 1.21 and 0.76 feet/day. Flow
velocities at monitoring weU P-7 (1.21, 0.76 feet/day) were averaged to provide a value of 0.99 feet/day.
Averaging the single data point for monitoring weU P-7 with that of monitoring weU P-6 provided a mean flow
velocity of 0.81 feet/day for M-585. The mean groundwater flow velocity for northern plume was 0.88 feet/day.
The retardation factor, Rd, was estimated from Kent et al. (1985):
(P f
ra Joe Rd = 1 + (25)
where: p,
foc
n
KoC
= aquifer bulk density (assumed to be equal to 1.6 g/ml),
= fraction of organic carbon (assumed to be 0.02),
= aquifer porosity (0.33), and
= organic carbon partition coefficient of the chemical (ml/g).
Substituting the values of p„ f^ and n, the retardation factor becomes:
Rd = 1 + 9.70 x 10'2 K^ (26)
Using equation (26), retardation factors for each of the four indicator chemicals were calculated (Table 4-48).
After calculating Vc from equation (24), the travel times (t) in years of the contaminants were estimated from:
t = JL (27)
where: x = distance from source to receptor site
4-163
P7W14/P7ST4-48.1
02/14/92
Table 4-48. Retardation factors of the four indicator chemicals used in the contaminant migration analysis.
Contaminant K„c Rd
(ml/g)
Chloroform 31 4.00
1,2-DCA 14 2.36
1,1,1-TCA 152 15.7
TCE 126 13.2
4-164
P78-914/P784E.165
02/14/92
The distance in the direction of groundwater flow from M-585 to the site boundary and Blue Creek along the
groundwater flow path is approximately 4,000 feet and 4,250 feet, respectively. The contaminant transport
velocities and travel times were calculated with equations (24) and (27) (Table 4-49). The travel times from
M-585 range from 32 to 224 years, assuming that biodegradation and other dissipation mechanisms do not take
place during contaminant migration.
The estimated distance in the direction of groundwater flow from the northern plume to the site boundary and
Blue Creek along the groundwater flow path is approximately 1,375 and 2,250 feet, respectively, from the tip of
the plume. All wells in the NDD area, including monitoring well P-5 at E-512, momtoring well P-8 at E-519,
and monitoring well P-9 at E-515 are considered to be part of the NDD area aquifer. The contaminant transport
velocities and travel times were calculated with equations (24) and (27). The travel times range from 10 to 110
years, assuming that biodegradation and other dissipation mechanisms do not take place during contaminant
migration (Table 4-50).
The dissolved contaminant concentration is expected to be diluted as groundwater from the sources moves
toward the site boundary and Blue Creek and mixes with uncontaminated groundwater. The contaminant
exposure concentrations resulting from dilution were estimated by making the foUowing assumptions:
• Dissolved contaminants would not degrade during groundwater migration,
• Aquifer thickness in the source and receptor areas is approximately the same, and
• Effects of longitudinal and vertical dispersion are not significant.
As the contaminants in groundwater migrate toward downgradient receptors, the plume wiU disperse lateraUy.
This lateral dispersion results in a decrease in contaminant concentration during transport in the aquifer. To
estimate the extent of dilution, an order-of-magnitude calculation procedure utilizing the aforementioned
assumptions was employed. This determined the plume width at the receptor, relative to that at the source. The
derivation of the lateral hydrodynamic dispersion equation is treated as a Fickian dispersion process
(Csanady, 1973):
o = -fl Dt (28)
where: a the standard deviation of the dispersing contaminant (feet),
dispersion coefficient (feetVday), and
the time of travel (days).
D
t
4-165
P7S-914/P78T4-49.1
02/14/92
Table 4-49. Contaminant transport velocities and travel times from M-585 to site boundary and Blue Creek.
Contaminant
(ft/day)
Travel Time in Days (Years) to
Boundary Blue Creek
Chloroform
1,2-DCA
1,1,1-TCA
TCE
0.202
0.343
0.052
0.061
19,801 (54)
(32)
(211)
(180)
21,040 (57)
(34)
(224)
(191)
4-166
P7&914/P78T4-50.1
02/14/92
Table 4-50. Contaminant transport velocities and travel times from the northern plume to site boundary and
Blue Creek.
Contaminant
(ft/day)
Travel Time in Davs (Years) to
Boundary Blue Creek
Chloroform
1,2-DCA
1,1,1-TCA
TCE
0.220
0.373
0.056
0.067
6,250 (17)
3,686 (10)
24,554 (67)
20,522 (56)
10,227 (28)
6,032 (17)
40,179 (110)
33,582 (92)
4-167
P78-914/P784E.16S
02/14/92
Hydrodynamic dispersivity (feet) through porous media (Freeze and Cherry, 1979) is expressed as:
D = a V, (29)
where: a = the hydrodynamic dispersivity (feet), and
V! = the average linear velocity of groundwater (feet/day).
The time of travel:
t = V, (30)
where: X = distance from source to receptor (feet).
According to Gelhar et al. (1985):
Substituting D and t into the equation for <r.
oc = 0.033 X
2 (0.033 X) Vl X
(31)
(32)
= 0.26 X
In Fickian dispersion, more than 95 percent of the contaminant will be contained within ±2 standard deviations
(a) of the plume centerline. Therefore, the full width of the plume is 4 a = 1.03 X. This dispersed width must
be added to the initial width at the source area to obtain the full width of the plume at the receptor area,
Wr = Wt + 1.03 X (33)
where: Wr = width at the receptor area, and
W, - width of the source area.
The exposure concentration was estimated by taking into account the dilution ratio based on the plume widths,
as follows:
C = C
r 3 \WTJ
(34)
4-168
P78-914/P784E.1S9
02/14/92
where: Cr = receptor concentration (pg/L),
Cs = source concentration (pg/L), and
W,/Wr = reciprocal of dilution ratio (dilution ratio = Wr/W,).
A currently available and best estimate of the contaminant plume width at the M-585 source (Ws) is 290 feet.
The distance of this plume source along the groundwater flow path to the site boundary is 4,000 feet. Using
equation (33):
Wr = 290 + 1.03 (4,000 feet)
= 4,410 feet
Thus, the reciprocal of dilution ratio (dilution ratio « 15) becomes:
Ws/Wr = 290/4,410 = 0.07
Substituting the Ws/Wr value in equation (34), and a value for chloroform in the M-585 shaUow aquifer at a
maximum concentration of 2,580 pg/L (Tables 4-34 and 4-35), the receptor concentration outside the boundary
was estimated from equation (34) as foUows:
Cr = 2,580(0.07) « 180 pg/L
Equation (33) was used to determine Wr for a distance from M-585 to a hypothetical receptor at Blue Creek.
Wr was determined from equation (33) to be 4,670 feet (Wt = 290 feet and D = 4,250 feet) and Ws/Wr « 0.06.
From equation (34), the chloroform concentration at a receptor location at Blue Creek is 2,580 (0.06) or
approximately 150 pg/L.
Wr values were calculated for the northern plume based on a Wt of 900 feet, a distance to the boundary of
1,375 feet, and a distance to Blue Creek of 2,250 feet. Wr at the boundary and Blue Creek is 2,302 and 3,218
feet, respectively. The Ws/Wr ratio for the boundary and Blue Creek is 0.39 and 0.28, respectively.
The receptor concentrations of the contaminants at M-585 and the northern plume were estimated with equations
(33) and (34). The results are presented in Table 4-51. Groundwater concentrations are not expected to be
elevated due to input from leaching.
4.2.3.3 Atmospheric Fate
The prevailing winds at Plant 78 are from the north in the morning and from the north or south-southeast in
the afternoon. Average wind speed is assumed to be 3 m/sec (EPA, 1988). Upon reaching the surface of the
4-169
P78-914/P78T4-51.1
02/14/92
Table 4-51. Concentrations of the Contaminants in Groundwater at the Site Boundary and Blue Creek.
Site Contaminant Source Receptor Concentration (pg/Ll
Concentration (pg/L)1 Boundary Blue Creek
M-585 (includes monitoring wells P-6 and P-7)
Chloroform 2,580 180 150
1,2-DCA 76.2 5 5
1,1,1-TCA 3,320 230 200
TCE 1,890 130 110
Northern Plume* (includes momtoring wells P-3, P-5, P-8, and P-9)
Chloroform 4.62 1.80 1.29
1,2-DCA 20.2 7.88 5.66
1,1,1-TCA 2,610 1,020 731
TCE 26,900 10,500 7,530
1 Maximum concentration observed or maximum average value for duplicate analysis.
* Monitoring well P-9 (E-515) and momtoring well P-5 (E-512) are considered as part of the northern plume
for purposes of the groundwater fate analysis.
P78-914/P784E.171
02/14/92
soil or surface water, volatile contaminants can remain temporarily airborne at the source or, most likely, travel
a certain distance to eventually reach offsite receptors. The atmospheric fate of these airborne contaminants is
highly dependent on site meteorological conditions (particularly wind direction and velocity).
The nearest residences are located approximately 2 miles to the south, 1 mile to the north, and about 0.75 mile
to the west. Because the contaminants would be expected to disperse significantly over these distances, a
hypothetical receptor location nearer to the source at the site boundary was selected. Although no actual
receptors have been identified at this location, this exposure point provides for a conservative evaluation of the
atmospheric fate of the volatile contaminants generated onsite.
The air exposure point concentration was estimated from volatilization of soil contamination at the FVD and
NDD source areas, as well as volatilization of surface water contaminants at the NDD and E-512 source areas.
The distance to the nearest receptor at the site boundary from each contaminated source area was estimated
based on the shortest distance from the source to the site boundary. The hypothetical receptor points were
located at the site boundary approximately 1,250 feet (380 m) from the FVD, 750 feet (228 m) from E-512 and
approximately 10 feet (3 m) from the NDD. Because the distance from the NDD to the site boundary is very
small, the air concentrations at the offsite receptor point is the same as the onsite receptor point (i.e., no
appreciable dispersion is anticipated).
4.2.3.3.1 Volatilization from Surface Water
The exposure concentrations of the contaminants associated with volatilization from surface waters in NDD and
E-512 were estimated by assuming a human (such as a child wading) is in a well-mixed box above the stream
into which the air from the atmosphere and the contaminants from the water enter. It was also assumed that
the box has an area of 1 m2 (1 m x 1 m) and is 1.5 m high. For the exposure scenario described above, the air
concentration (Cg) can be expressed as:
q = .iQfpox area)(t) (35)
box volume
where:
box area
box volume
t
contaminant flux rate (mg/m2-sec),
lm2,
(1.5 m)(l m)(l m) = 1.5 m3, and
time it takes for air moving parallel to the surface water to change the air
in the box (1 m/[3 m/sec] or 1/3 sec).
In terms of q^:
Cg = (q-)(l m*Kl/3 serf
(1.5 m3)
(36)
4-171
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Substituting the volatilization flux rates from Table 4-40 into equation (36), the air exposure concentrations of
the contaminants in NDD and E-512 areas were estimated. The results are summarized in Table 4-52. Air
concentrations resulting from surface water flux from Blue Creek are considered here (even though Blue Creek
is outside the boundary and is not a source). This is because potential receptors would be on the bank, as
described above for the box model, and not downwind from where the flux is occurring.
4.2.3.3.2 Volatilization from Soil or Sediment
The exposure concentrations of the contaminants resulting from volatilization from soils or sediments in the FVD
and the NDD were calculated by using the foUowing conservative assumptions for humans potentiaUy exposed
at or near source areas:
• The source is infinitely wide in the crosswind direction,
• The receptor is in the source area at the downwind edge,
• Vertical dispersion has resulted in uniform mixing of the contaminants from the ground to the
breathing zone (1.5 m), and
• No contaminant has dispersed outside the breathing zone.
These assumptions were applied to a box model with no transverse dispersion in which the contaminant
concentration in the box (Q,) can be expressed as:
Q, = _Mb- (37)
Vb
where: Mb = contaminant mass entering the box per unit time (mg/sec), and
Vb = volume of air entering the box per unit time (m3/sec).
For a box with a unit width of 1 m (although the result does not depend on width by Assumption 1) and under
a condition with an upwind length of source L (approximate average length of individual source areas
perpendicular to wind direction), Q, can be equated to:
Q, = ( qr)(l m)(L) (38)
(windspeed)(breathing height)(unit width)
= (q,)(l m)(L)
(3 m/sec)(1.5 m)(l m)
Using L = 1,370 m for the FVD and L = 914 m for the NDD and the calculated flux rates (q^) in Table 4-37,
the exposure concentrations of the contaminants were estimated from equation (38). The results are presented
in Table 4-53.
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P78-914/P78T4-52.1
02/14/92
Table 4-52. Air Exposure Concentrations at the Source Onsite or Blue Creek Resulting from Volatilization from
Surface Water.
Site
Contaminant
of
Concern
Flux Rate (qj
(mg/m2-sec)
Air Exposure
Concentration
(mg/m3)
NDD Drainage Ditch
Chloroform
1,2-DCA
1,1,1-TCA
TCE
4.6 x 10'5
3.5 x 10"4
5.5 x 10"4
2.6 x IO"5
1.0 x IO'5
7.8 x 10'5
1.2 x 10"4
5.8 x 10"6
E-512 Drainage Ditch
Chloroform
1,1,1-TCA
1.9 x 10 s
1.8 x 10"4
4.2 x 10"6
3.9 x IO"5
Blue Creek
Chloroform
1,2-DCA
1,1,1-TCA
3.7 x 10s
1.4 x IO"3
4.2 x 10"5
8.2 x 10'6
3.1 x 10"4
9.2 x 10"*
4-173
P7M13/P78T4-53.1
02/14/92
Table 4-53. Air Exposure Concentrations at the Source Resulting From Volatilization From Contaminated Soil
or Sediments.
Site
Contaminant
of
Concern
Flux Rate (q,,)
(mg/m2-sec)
Air Exposure
Concentration
(mg/m3)
FVD
1,1,1-TCA 3.04 x IO"* 9.0 x 1CT*
NDD
Chloroform
TCE
3.76 x 10"10
8.04 x 1010
8.0 x 10 s
2.0 x IO"7
4-174
P78-914/P784E.175
02/14/92
For purposes of this risk assessment, a simplified procedure for evaluating the atmospheric fate of compounds
released from uncontrolled waste sites (EPA, 1988) was used to estimate the contaminant concentration in air
at a distance (x) from the source.
This procedure is based on the two main mechanisms affecting the movement of substances in air (i.e., advection
and dispersion), in which the contaminant concentration in air can be expressed by the foUowing equation (EPA,
1988):
CW = jQ
w (39> n a; oz U
where: C(x) = air concentration of a substance at a distance (x) from the site (mg/m3),
j = frequency of wind direction toward exposure point (expressed as a fraction),
Q = contaminant release rate from the site (mg/sec),
TT = 3.1416,
ay = dispersion coefficient in the lateral or crosswind direction (meters),
trz = dispersion coefficient in the vertical direction (meters), and
U = mean wind speed (3.0 m/sec).
The contaminant release rate (Q) can be further defined by the foUowing equation:
Q = q, x A (40)
where: Q = contaminant release rate from the site (mg/sec),
qe = effective contaminant flux rate (mg/m2-sec) as evaluated for volatilization from soU
and surface water from Tables 4-37 and 4-38, and
A = area of contaminated source (m2).
The lateral and vertical dispersion coefficients are a function of the downward distance from the source area to
the receptor point and are obtained from EPA (1988). For purposes of this analysis, it was assumed that the
source area acts as a point source. This is a conservative assumption based on the analysis of Turner (1970),
which suggests that apphcation of this methodology for an area source should consider the virtual point source
to be located some distance upwind of the actual source location. Under atmospheric stability class D conditions
(slightly overcast conditions during day and night), as recommended by EPA (1988), the appropriate lateral
dispersion coefficients (try) 380 m downwind from FVD and 228 m downwind of E-512 are 30 m and 18 m,
respectively. The vertical dispersion coefficients (crz) for the FVD and E-512 are 15 m and 10 m, respectively.
4-175
P78-914/P784E.176
02/14/92
It was assumed that 30 percent of the time, winds are in the direction of the offsite exposure point. Thus,
j = 0.3.
Using this data, along with contaminated areas of 2,090 m2 at the FAD and 186 m2 at E-512, and substituting
equation (40) for Q, the previous equation (39) simplifies to:
For the FVD:
For the E-512:
„ _ (0.3) (2090 m2) (g<) (41)
'w " (3.1416) (30 m) (15 m) (3 ffl/sec)
C(x) = (0.148 sec/m) qe
„ _ (0.3) (186 ffl2) (q) (42)
"(x) " (3.1416) (18 ffl) (10 ffl) (3 m/sec)
C(x) = (0.033 sec/m) qe
The effective flux rate of each contaminant was obtained from Tables 4-37 and 4-40. The results of the
calculations for the offsite air exposure point concentrations are presented in Table 4-54.
The half-lives for the indicator chemicals in air range from less than 10 days for TCE to greater than 365 days
for 1,1,1-TCA (Table 4-45).
The exposure point concentrations are summarized in Tables 4-55 (for the exposure at the source) and 4-56 (for
the exposure downgradient of the source). Blue Creek is listed in Table 4-56 because the receptor is assumed
to be on the bank at the location where flux is occurring. Where flux occurs from more than one media,
exposure concentrations are additive for that source and media. This situation occurred in the NDD, where
contaminants volatilized from soil and surface water to air.
4.2.3.4 Uncertainty Analvsis
There is approximately one order of magnitude uncertainty or less in the groundwater receptor concentration
modeling. Using the fate and transport equations, it was determined that contaminants in the northern plume
would require from 10 to 110 years to reach the west (downgradient) boundary of the installation or Blue Creek.
Using the date of construction of Plant 78 (1962) and the distance that contamination has migrated within the
groundwater since that date, approximately a 30-year time period, a rate of transport can be obtained for
comparison to the rates determined through the fate and transport modeling. For example, the contaminant
plume determined at the M-585 site has migrated approximately 500 feet in 30 years. This would indicate a 16
feet/year migration rate in order to achieve the distribution observed. Using fate and transport modeling, it was
4-176
P78-914/P78T4-54.1
02/14/92
Table 4-54. Air Exposure Concentrations At Site Boundary Downwind of Source Area.
Source Area/ qe C(l)
Chemical (mg/m2-sec) (mg/m3)
FVD, (sediment)
1,1,1-TCA
E512 (surface water)
Chloroform
1,1,1-TCA
*NDD (surface water)
Chloroform
1,2-DCA
1,1,1-TCA
TCE
*NDD (soU)
Chloroform
TCE
3.04 x 10 ' 4.50 x 10 '
1.9 x 10s
1.8 x 10"4
6.27 x 10"7
5.94 x 10"6
4.6 x 10'5
3.5 x IO4
5.5 x 10^
2.6 x 10 s
1.0 x Iff5
7.8 x 10 s
1.2 x 10"4
5.8 x IO"6
3.76 x Iff10
8.04 x Iff10
8.0 x 10"8
2.0 x 10'7
Exposure concentrations are the same as for an exposure point at the source due to the proximity of
the NDD to the boundary.
4-177
P7S-914/P78T4-55.1
02/14/92
Table 4-55. Summary of Estimated Exposure Point Concentrations at a Source Onsite.
Air
(mg/m3)
Surface Water*
(Mg/L)
Groundwater
(Mg/L)
Soil
(mg/kg)
FVD
Chloroform
1,2-DCA
1,1,1-TCA
TCE
9.0 x W4 0.59*
NDD***
Chloroform
1,2-DCA
1,1,1-TCA
TCE
1.01 x 10 s
7.8 x 10"5
1.2 x 10A
6.0 x 10"*
1.15
9.93
13.0
0.626
0.00011
0.00025
E-512
Chloroform
1,2-DCA
1,1,1-TCA
TCE
M-585
Chloroform
1,2-DCA
1,1,1-TCA
TCE
4.2 x 10"*
3.9 x IO"5
0.473
4.22
* Concentrations presented are the highest concentrations observed in Stage 1 or Stage 2 sampling.
** Concentration is the geometric mean of all values in the FVD because 1,1,1-TCA was found throughout
the length of the ditch.
*** Value is the sum of estimated exposure concentrations from volatilization from surface water and from
soil/sediments.
4-178
P7M14/P78T4-56.1
02/14/92
Table 4-56. Estimated Exposure Point Concentrations Downwind or Downgradient at the Boundary (or Blue
Creek) by Area of Concern.
Air
(mg/m3)
Surface Water
(Mg/L)
Groundwater*
(Mg/L)
Soil
(mg/kg)
FVD
Chloroform
1,2-DCA
1,1,1-TCA
TCE
4.50 x 10 '
NDD
Chloroform
1,2-DCA
1,1,1-TCA
TCE
1.0 x 10*
7.8 x 10*
1.2 x 10"*
6.0 x IO"6
4.29
1.80 (1.29)
7.88 (5.66)
1,020 (731)
10,500 (7,530)
E-512**
Chloroform
1,2-DCA
1,1,1-TCA
TCE
6.27 x 10"7
5.94 x 10*
0.473
4.22
M-585
Chloroform
1,2-DCA
1,1,1-TCA
TCE
180 (150)
5(5)
230 (200)
130 (110)
E-519***
Chloroform
1,2-DCA
1,1,1-TCA
TCE
Blue Creek
Chloroform
1,2-DCA
1,1,1-TCA
TCE
8.23 x 10*
3.08 x W*
9.15 x 10*
0.608
27.7
0.615
Value in the parenthesis are for groundwater concentrations at the time the plume reaches Blue Creek,
other values are for concentrations at the boundary.
Surface water samples were not coUected at the boundary; therefore, the contaminant concentrations
were conservatively assumed to be the same as at the source area.
Addressed as part of the NDD.
4-179
P78-914/P784E.180
02/14/92
estimated that it would require from 32 to 224 years to achieve the observed distribution. Using the estimated
observed plume migration of 16 feet/year, between 250 and 266 years would elapse before the groundwater
plume from M-585 would reach the Plant 78 boundary and Blue Creek, respectively. The northern contaminant
plume has a minimum downgradient extent of approximately 2,000 feet. To obtain the observed distribution in
30 years would require a 66 feet/year migration rate, and the plume from the NDD would reach the boundary
and Blue Creek in 21 and 34 years, respectively. The fate and transport modeling estimates indicate that it would
take 10 to 110 years to observe the contaminants at the boundary and Blue Creek.
4.2.4 EXPOSURE PATHWAYS
Exposure is the contact of humans or other organisms with site-related contaminants. In order for a chemical
to produce an effect, there must be a pathway from the source to the biologic receptor. The conceptual exposure
model for the Plant 78 site is integrated and summarizes the information concerning source areas, contaminant
migration pathways and exposure routes into a combination of exposure pathways. Table 4-57 presents the
conceptual model for the Plant 78 site. This model identifies the key potential release mechanisms, transport
media, exposure points, exposure media, exposure routes, and receptors for each source area. The potential
exposure pathways considered for humans and nonhuman biota for Plant 78 include: dermal absorption by direct
contact; inhalation of vapors and dusts; ingestion of contaminated water or soil; ingestion of contaminated crops
and livestock; ingestion of contaminated game species; and, ingestion of contaminated aquatic organisms. AU
exposure pathways are summarized in Table 4-58; complete pathways are indicated as being feasible, whereas
incomplete pathways are indicated as not feasible.
A complete exposure pathway consists of the foUowing four elements (EPA, 1986a):
• Source and mechanism for chemical release,
• Environmental transport medium,
• Point of potential biological contact, and
• An exposure route (i.e. ingestion, inhalation, dermal absorption) at the contact point.
AU four of these components are necessary to form a complete exposure pathway. If one or more of the
components is lacking, there is little possibility of an effect due to site contamination. The points of biological
contact are discussed below for each potential exposure route. In general, most human receptors at Plant 78
are distant from the contaminant sources. Conservatively, two points of contact were considered: a worker
directly at the source and a hypothetical receptor at the site boundary or Blue Creek.
4.2.4.1 Direct Contact
There is little potential for direct human contact at Plant 78 because the area is closed to the pubhc, and
extensive measures are taken at the site to ensure that trespassing does not occur for security and safety reasons.
Dermal absorption is therefore expected to be a rare event, occurring only in workers contacting surface water,
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P78-914/P78T4-57.1
02/14/92
Table 4-57. Conceptual Exposure Model for Plant 78.
Contaminated Media Release Mechanism Transport Media Exposure Point Exposure Media/ Potential Receptors
Exposure Route
Soil Volatilization
Leaching
None
Air
Groundwater
None
Onsite
Boundary
Boundary
Onsite
Inhalation of vapors Workers, biota
Inhalation of vapors Future residents, biota
Direct contact Workers, biota
i—i oo
Sediment Volatilization
Leaching
None
Air
Groundwater
None
Onsite
Boundary
Boundary
Onsite
Inhalation of vapors Workers, biota
Inhalation of vapors Future residents, biota
Direct contact Workers, biota
Surface water Volatilization
Leaching
None
Air
Groundwater
Surface water
Onsite
Boundary
Blue Creek
Boundary
Onsite
Boundary
Blue Creek
Inhalation of vapors Workers, biota
Inhalation of vapors Future residents, biota
Direct contact
Direct contact
Workers, biota
Future residents, biota
Groundwater None Groundwater Boundary Future Residents
P78-914/P78T4-38.1
02/14/92
Table 4-58. Summary of Potential Exposure Pathways (Page 1 of 3).
PotentiaUy Exposed Pathway
Population Exposure Media/Exposure Routes Feasible Reason for Selection or Exclusion
Current Land Use
Residents
Residents
Inhalation of chemicals volatilized No
from soU onsite; volatiles move offsite
with air pattern
Inhalation of chemicals volatilized No
from surface water onsite; volatiles
move offsite with air
Nearest residences are 0.75 to 1 mUe from boundary of site; levels expected to
be low and risk minimal
Nearest residences are 0.75 to 1 mUe from boundary of site; levels in air
expected to be low and risk minimal
Residents
Residents
Residents
Residents
Ingestion of chemicals in
groundwater from local weUs
Inhalation of chemicals volatilized
from groundwater from local weUs
Ingestion of contaminated livestock
or game exposed on Plant 78, or
aquatic life from Blue Creek
Dermal absorption by children of
chemicals in surface water in Blue
Creek
No Groundwater not potable in the area surrounding the site; in addition, plume is
not expected to reach hypothetical weUs instaUed on the boundary in excess of
one hundred years
No Groundwater not potable in the area surrounding the site; in addition, plume is
not expected to reach hypothetical weUs instaUed on the boundary in excess of
one hundred years
No Bioconcentration and bioaccumulation factors for the indicator chemicals
indicate that contaminant transfer from water to tissue will not occur to a
significant extent
Yes ChUdren may occasionaUy contact Blue Creek for short time periods
Residents Dermal absorption by children of Yes ChUdren may occasionaUy contact Blue Creek for short time periods
chemicals in sediments in Blue Creek
P78-914/P78T4-58.2
02/14/92
Table 4-58. Summary of Potential Exposure Pathways (Page 2 of 3).
PotentiaUy Exposed Pathway
Population Exposure Media/Exposure Routes Feasible Reason for Selection or Exclusion
Residents Incidental ingestion by children of
chemicals in surface water or
sediments in Blue Creek.
Yes ChUdren may occasionaUy contact Blue Creek for short time periods
Industrial
Workers
Inhalation of chemicals volatilized
from surface water, sediments, or
soUs on the site; exposure occurs at
the area of concern
Yes Maintenance workers may occasionaUy be exposed
Industrial
Workers
Direct contact and dermal absorption
of chemicals in surface water,
sediment or soUs on the site;
exposure occurs at the area of
concern
Yes Maintenance workers in the E-512 or NDD area may occasionaUy be exposed
Industrial
Workers
Incidental ingestion of chemicals in
sediment or soUs on the site;
exposure occurs at the area of
concern
Yes Maintenance workers in the FVD areas may occasionaUy be exposed
Wildlife Direct contact with contaminated soU
or sediment onsite; exposure occurs
at the area of concern
Yes Nonhuman biota occur on Plant 78
WUdlife Inhalation of chemicals volatilized
from sediments or sou's onsite;
exposure occurs at the area of
concern
Yes Nonhuman biota occur on Plant 78
Livestock Consumption of surface water from
Blue Creek downgradient of Plant 78
Yes Livestock may access Blue Creek
Table 4-58. Summary of Potential Exposure Pathways (Page 3 of 3).
P78-914/P78T4-583
02/14/92
Potentially Exposed Pathway
Population Exposure Media/Exposure Routes Feasible Reason for Selection or Exclusion
Aquatic Life
Future Land Use
Residents
Residents
Residents
Residents
Direct contact with chemicals in Blue
Creek
Inhalation of chemicals volatilized
from soil, sediments, or surface water
and transported to the boundary
Inhalation of chemicals volatilized
from Blue Creek
Ingestion of groundwater
Dermal contact with groundwater
Yes Aquatic life occurs in Blue Creek
Yes Hypothetical resident at boundary
Yes Hypothetical resident living next to Blue Creek
No Groundwater not potable in the area surrounding the site; in addition, plume is
not expected to reach hypothetical wells instaUed on the boundary in excess of
one hundred years
No Groundwater not potable in the area surrounding the site; in addition, plume is
not expected to reach hypothetical weUs instaUed on the boundary in excess of
one hundred years
Residents Dermal contact with soU or surface No
water at boundary
Risk is expected to be minimal and conservatively addressed by the current
resident scenario where chUdren were modeled swimming in Blue Creek
P78-914/P784E.185
02/14/92
sediments, or soil. Because soil contamination is not widespread, and contaminant concentrations are very low,
direct contact with contaminated soil is considered a rare event (even by workers at the source). Due to the
volatility of the indicator chemicals, contaminants in the upper centimeters of soil/sediment (the point of human
contact) are expected to be lower than concentrations in deeper strata. Any adverse health effects relating to
dermal absorption are expected to be less than those resulting from inhalation or ingestion, due to low
concentrations and the apparent relative toxicity by the different routes of exposure.
Nonhuman biota may be exposed by direct contact with surface water, sediments, or soil during feeding, drinking,
or burrowing activities. Dermal absorption is species specific and dependent on the type of activity that results
in direct contact; however, due to the lack of widespread soil/sediment contamination, the direct contact of
contaminated soils/sediments will not be considered further for nonhuman biota. Based on low concentrations,
infrequent contact, and the apparent relative toxicity by the different routes of exposure, any adverse health
effects relating to dermal absorption are expected to be less than those resulting from inhalation or ingestion.
Aquatic species, however, may be exposed by direct contact with surface water in Blue Creek. Aquatic life are
continually exposed to their environment, and may be sensitive to certain chemicals.
4.2.4.2 Inhalation of Vapors and Dusts
Volatilization from surface water, soil, and sediments can result in air contamination. Inhalation of dusts are
not expected to be a significant exposure pathway, due to the volatility of the contaminants of concern.
Inhalation of volatiles is a potential pathway for human and nonhuman biota for all of the indicator chemicals.
Workers at the plant are probably the most highly exposed human group, because residences in the surrounding
area are quite distant from the site boundaries. Nonhuman biota may also be exposed to volatiles from
contaminated surface water, sediment, or soil.
4.2.4.3 Ingestion of Water and Soil
Groundwater is not utilized in the Plant 78 area as a drinking water source due to poor water quahty due to high
TDS in the immediate vicinity of Plant 78. It is unlikely that potable water wells would be instaUed directly
downgradient of Plant 78 on the east side of Blue Creek, because the area is managed for industrial purposes.
Additional potable water wells can only be instaUed if water rights and treatment facilities become avaUable
(Whetstone, 1989); therefore, future groundwater use in the area is limited. The nearest potential exposure point
for groundwater is the nearest residence, approximately 2 mUes south of Plant 78. At this time, the source of
domestic water for this residence is unknown. The nearest wells, according to BLM (1979), are 4.5 mUes
downgradient of Plant 78. Groundwater discharge to Blue Creek is unlikely.
Surface water from Blue Creek is not utilized immediately downgradient of Plant 78 for drinking water or
irrigation purposes. However, hvestock and wildlife may access Blue Creek and consume surface water. It is
unlikely that chUdren or other human receptors wiU contact Blue Creek and ingest water due to the low
4-185
P78-914/P784E.186
02/14/92
population density in the area, the distance to the nearest residences, the high TDS of the water, and the lack
of game fish that would attract fisherman.
"Workers on Plant 78 may ingest limited quantities of soil/sediment due to eating without washing their hands.
Nonhuman biota such as wildlife may also ingest soil during feeding and burrowing activities. Livestock do not
occur directly on Plant 78 and, therefore, have limited access to potentiaUy contaminated soU. Furthermore,
except the FVD, widespread soU and sediment contamination is not evident at any area of concern. Levels in
the FVD sediments were low, but occurred across the plant. Because the FVD is a steep ravine distant from
most buUdings, it is unlikely that a worker would spend much time in the FVD.
4.2.4.4 Ingestion of Crops and Livestock
Crops are not irrigated with surface water from Blue Creek downgradient of Plant 78 and are therefore not
expected to be a significant exposure pathway. At this time, aU known irrigation wells are upgradient from the
site. It is possible that the weU located 4.5 mUes downgradient of the plant is used for crop watering activities;
however, due to the volatility of the contaminants of concern and the lack of bioaccumulation indicated for other
organisms, uptake of the indicator chemicals by crops does not appear to be a significant exposure pathway.
Livestock are not expected to be a significant exposure pathway to humans based on estimated bioaccumulation
of the indicator chemicals. The octanol-water partition coefficient (K^) for each of the indicator chemicals and
equations from Kenaga (1980) were used to predict bioaccumulation factors (BAF) in hvestock:
Log BAF = (-3.457 + 0.500 (log K^)) (43)
where: BAF = bioaccumulation factor, and
K^y = octanol-water partition coefficient.
The estimated Log BAF and BAF values are as foUows:
Log BAF BAF
chloroform = -2.47 0.0034
1,2-DCA = -2.71 0.0019
1,1,1-TCA = -2.20 0.0063
TCE = -2.27 0.0054
The bioaccumulation factor represents concentration in tissue compared to concentration in diet. The predicted
values are less than one and bioaccumulation is not indicated for any of the COCs.
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P7M14/P784R187
02/14/92
4.2.4.5 Ingestion nf Game, Species and Aquatic Organisms
Game species are not expected to be a potential exposure pathway to humans based on the BAF values
estimated for the indicator chemicals. Aquatic organisms are also not anticipated as an exposure pathway,
because the fish bio-accumulation factors (BAF) for the COCs are very low (Table 4-31).
4.2.4.6 Comparison to Requirements. Standards, and Criteria
4.2.4.6.1 Established Criteria
The exposure point concentrations (Tables 4-55 and 4-56) were compared to both established and estimated
criteria to determine potential health risks. Federal and state pubhc health and environmental standards must
be reviewed to determine the extent to which they are apphcable or relevant and appropriate in regards to the
constituents identified at the site. In addition, other federal or state advisories, criteria, and guidance must be
examined to determine if they are relevant and appropriate for the development of remedial actions for the site.
Apphcable requirements are those standards or criteria promulgated under federal or state law that specifically
address the circumstances at a site if an action were not being undertaken pursuant to CERCLA requirements.
Relevant and appropriate requirements are defined as those standards designed to apply to circumstances similar
to those encountered at CERCLA sites, even though they may not be legally apphcable. Potential ARARs for
the indicator chemicals are summarized in Table 4-59.
The maximum contaminant levels (MCLs) for groundwater are defined in the National Primary Drinking Water
Standards (EPA, 1987c and 1991) and the State of Utah Primary Drinking Water Standards (State of Utah,
1990).
Other standards and criteria that apply to Plant 78 are the Ambient Water Quahty Criteria (AWQC) for the
protection of freshwater aquatic life and its uses and for the protection of human health (EPA, 1986). The State
of Utah has not published any aquatic life water quahty standards for the COCs. The indicator chemicals are
not regulated as yet under the Clean Air Act (CAA), or by National Ambient Air Quahty Standards (NAAQs).
The American Council of Governmental Industrial Hygienists (ACGIH) Threshold Limit Values (TLVs) are
used to indicate adverse effects to workers exposed via inhalation. The EPA Health Advisories (HAs) for
1,2-DCA and 1,1,1-TCA are presented in Table 4-60. The HAs are nonregulatory criteria based on
noncarcinogenic human health effects from exposure to drinking water and/or consumption of fish.
GROUNDWATER
The predicted groundwater concentrations at the boundary or Blue Creek exceeded potential ARARs at the sites
mentioned below.
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Table 4-59. Summary of Potential ARARs.
Utah Utah
Drinking Ambient Water Quahty Criteria (ug/L) Water
MCL Water Freshwater Human Health Human Health Quahty TLV
Chemical (pg/L) Rules Life Water and Fish* Fish Only Standards (mg/m3)
Chloroform 100** 100** A: 2.89 x 104 1.9 x Iff1 1.57 x 10l NA 50(10)***
C: 1.24 x10s
1,2-DCA 5 5 A: 1.18 x10s 9.4 x Iff1 2.43 x 102 NA 40(10)
C: 2.00 xlO4
1,1,1-TCA 200 200 A: - 1.84 x IO4 1.03 x 106 NA 1,900 (350)
C:
TCE 5 5 A: 4.5 x 104 - 8.07 x 101 NA 268(50)
C: ~
* Values are for the 10"6 risk level.
** As total trihalomethanes.
*** Values in parenthesis are in ppm.
A: Acute values, may be criteria or lowest effect concentrations (LEC) recommended by EPA.
C: Chronic values, may be criteria or lowest effect concentrations (LEC) recommended by EPA.
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Table 4-60. Summary of EPA Health Advisories for 1,2-DCA and 1,1,1-TCA1 (wg/L).
Exposure Duration 1,2-DCA 1,1,1-TCA
1 day (10 kg child) 7402 100,000
10 day (10 kg child) 7402 40.0002
Long term (10 kg child) 740 40,000
Long term (70 kg adult) 2,600 100,000
Lifetime (70 kg adult) NA 200
1 EPA, 1987a.
2 One or ten day HA unavailable; EPA recommends the long term value.
NA Not Apphcable.
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M-585
Chemical
Chloroform
1,2-DCA
1,1,1-TCA
TCE
BOUNDARY BLUE CREEK
MCL MCL
MCL.HA
MCL MCL
NORTHERN PLUME
BOUNDARY BLUE CREEK
MCL MCL
MCL,HA MCL,HA
MCL MCL
Use of these criteria is highly conservative because the groundwater is nonpotable due to naturaUy occurring high
TDS and there is a lack of potential receptors identified either on or offsite.
SURFACE WATER
The AWQC for the protection of freshwater aquatic life were not exceeded at any site for any contaminant of
concern. The AWQC for the protection of Human Health were exceeded based on both water and fish
consumption. Chloroform and 1,2-DCA exceeded criteria at NDD (onsite) and chloroform exceeded criteria
at E-512 onsite.
The AWQC for freshwater aquatic life were not exceeded in Blue Creek. The AWQC for Human Health,
based on consumption of both water and fish, were exceeded for 1,2-DCA and chloroform. Fish of a size or
species expected to be consumed by humans are unlikely to occur in Blue Creek near Plant 78. In addition, it
is unlikely that either current or future receptors would consume water directly from the ditches or from Blue
Creek prior to treatment.
SOIL
SoU ARARs do not exist.
SEDIMENT
Potential sediment ARARs do not exist.
AIR
Estimated concentrations ofthe contaminants of concern in air did not exceed the TLVs for protection of worker
health either onsite or downwind of the source areas.
4.2.4.6.2 Estimated Criteria
AQUATIC LIFE
An aquatic life criterion for 1,1,1-TCA was estimated because an AWQC for the protection of freshwater
organisms was unavailable. The LCJQ for fathead minnows (10,500 ug/L) was divided by a factor of 100 to
convert the acute lethal value to a chronic nonlethal value. EPA (1986b) uses a conversion factor of 1/10 the
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LCJO for aquatic organisms, as compared to environmental concentrations, to assume a no-risk situation.
Therefore, the uncertainty factor apphed to this situation is considered appropriately conservative to protect any
sensitive species. The estimated chronic surface water criterion for 1,1,1-TCA for aquatic life is 105 ug/L.
4.2.4.7 Wildlife and Domestic Livestock
4.2.4.7.1 Surface Water Ingestion by Nonhuman Biota
Criteria for ingestion of surface water were estimated for wildlife and domestic livestock from the Lowest
Observed Adverse Effect Levels (LOAELs) and No Observed Effect Levels (NOELs) from the toxicity data
reviewed. These criteria are not intended to serve as remedial goals, but only as indicator levels of risk to
nonhuman biota other than aquatic life. Chronic exposure data were considered more appropriate than acute
or subacute data, and sublethal effects data were considered preferable to lethal effects data.
The LOAEL for chloroform for a mammalian species was 200 mg/L administered to rats in (Irinking water for
90 days (Jorgenson and Rushbrook, 1980). Decreased water consumption and behavior changes were observed.
IRIS (1990) cites a study with dogs where the LOAEL was 1.9 mg/kg bw/day. Converting this dose to a
drinking water dose as follows:
LOAEL m mg/kglday = mg/L
Water Consumption L/kg/aay
yields a comparative LOAEL 38 mg/L for dogs which is less than the value for rats. An uncertainty factor of
1,000 was apphed because of the limited toxicity data available (i.e., few species, no avian data, and no livestock
data, limited chronic and sublethal effects data, converting dietary values to drinking water values, etc.) and to
adjust LOAEL values to NOELs. The estimated acceptable level in water is 0.038 mg/L (38/tg/L).
The LOAEL for 1,2-DCA where increased mortality was observed was 34 mg/kg bw/day for chronically exposed
rats (EPA, 1985b). A 200 gm rat consumes 25 ml water daily (Sax, 1984). The LOAEL in drinking water would
be:
LOAEL m mg/kglday _ mgfL
Water Consumption Ljkgjday
The comparative LOAEL was 272 ug/L. An uncertainty factor of 1,000 was apphed because of the limited
toxicity data available (i.e., few species, no avian data, and no hvestock data, limited chronic and sublethal effects
data, converting dietary values to drinking water values, etc.) and to adjust LOAEL values to NOELs. The
resulting estimated acceptable level in water is 272 ug/L.
The LOAEL for 1,1,1-TCA was 250 mg/kg bw/day for rats dosed acutely and subacutely (Bruckner et al., 1985).
The LOAEL in drinking water for a 200 gm rat consuming 25 ml drinking water daily is 2,000 mg/L. Decreased
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growth rate and decreased survival were observed at this dose level. An uncertainty factor of 1,000 was apphed
because of the limited toxicity data available (i.e., few species, no avian data, and no livestock data, limited
chronic and sublethal effects data, converting dietary values to drinking water values, etc.) and to adjust LOAEL
values to NOELs.
The LOAEL for TCE was 2.5 mg/L for rats exposed to TCE in ottnking water (Tucker et al, 1982). Less
uncertainty was involved with this estimate, since drinking water was the source of exposure for the toxicity study.
Therefore, an uncertainty factor of 100 was apphed for interspecies variation, limited data, and converting a
LOAEL to a NOEL. The resulting estimated acceptable level in drinking water for terrestrial wildlife and
livestock is 25 ug/L.
The surface water criteria for hvestock and wildlife at which no adverse effects are expected are:
• CHC13 = 38 ug/L,
• 1,2-DCA = 272 ug/L,
• 1,1,1-TCA = 2,000 ug/L, and
• TCE = 25 ug/L.
4.2.4.7.2 Inhalation
Inhalation toxicity information for wildlife species were unavailable for the indicator chemicals. The NOEL
(when available) or the sublethal LOAEL for mammals in air for each indicator chemical was, therefore, used
to indicate acceptable levels. Chronic data were considered more appropriate than acute, and sublethal data
were considered more appropriate than lethal. The estimated acceptable air concentrations are:
• CHCI3 = less than 25 ppm (chronic LOAEL; Torkelson et al, 1976),
• 1,2-DCA = 100 ppm (chronic NOEL; EPA, 1985b),
• 1,1,1-TCA = 350 ppm (short-term NOEL; EPA, 1984), and
• TCE = less than 100 ppm or 538 mg/m3 (subchronic LOAEL; EPA, 1985c).
4.2.4.7.3 Sediment/Soil Ingestion
Ingestion of contaminated soil and sediment was considered for workers and wildlife. However, soil
contamination does not appear to be widespread, although one sample from the NDD had detections. Sediments
throughout the FVD were contaminated at low levels; hvestock do not have access to the FVD. Due to the
volatility of the indicator chemicals, the top strata of soil are probably less contaminated than deeper strata. Soil
and sediment criteria are largely unavailable. Based on the limited extent of exposure, criteria were not
estimated for nonhuman biota. Human health risks were determined from estimated intakes compared to
toxicity values.
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4.2.4.7.4 Dermal Exposure for Nonhuman Biota
Dermal absorption was considered not to present a significant exposure, due to the limited amount of surface
soil and sediment contamination, and the low levels of surface water contamination. Dermal contact by aquatic
life was considered previously under Aquatic Life.
4.2.5 IDENTIFICATION OF RECEPTORS
Due to the low population density of this region, there are relatively few points for human contact other than
workers in the Plant 78 area. Points of contact considered in a risk assessment include homes, schools, towns,
or other human population centers (Figure 4-40). A survey was conducted to determine human populations and
activities in the Plant 78 vicinity. The nearest residence is approximately 0.75 miles from the northwest boundary
of Plant 78. This residence is upgradient with respect to surface water, and downgradient with respect to
prevailing winds, which blow from the north and from the south-southeast (Figure 4-41). The next nearest
residences are approximately 1.0 mile or more from the northern boundary of Plant 78. Six residential properties
with hvestock are located 1 to 2 miles north of Plant 78. There is one residence 2 miles south of the site. No
churches, towns, shopping centers, or schools were observed in the vicinity of the site in 1989. The entire
population of Box Elder County (excluding Brigham City) as reported by the U.S. Census Bureau in March 1989
is 21,950.
Current land use in the Plant 78 area is presented in Figure 4-42. Plant 78 and the area directly south are
industrial. Ranching and farming are the other predominant land uses. Future land use is unknown, but it is
assumed that Plant 78 will continue to serve an industrial purpose for some time. Surface wind roses for the
Plant 78 area are presented in Figure 4-41.
Access to Plant 78 is highly restricted for security and safety reasons. Access is restricted by an 8-foot security
fence around the entire Plant 78 complex, guarded gates, a private security system, and the requirement of
identification badges. Workers may spend limited time performing building maintenance (such as painting) or
groundwork (such as weed control). An infrequent 8-hour exposure period is likely for these workers.
Recreational activities are not expected to occur on Plant 78. Residential activity patterns may be expected in
the areas outside the boundaries, as well as work activity due to farming. However, given the distance from
nearby urban areas and the unique qualifications for its current use, it is likely that this facihty will remain
industrial. Therefore, residential land use onsite as a future scenario was not considered. As to future offsite
land use, it was assumed that residences would be built directly at the Plant 78 boundary.
The climate is very arid, with as httle as 14.88 inches of rain annually. Vegetation tends towards low shrubs,
grasses, and bare ground.
4-193
Figure 4-40
POTENTIAL HUMAN AND LIVESTOCK
RECEPTORS; SPRING 1989
SOURCE: ESE, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-194
NOTE: Peroentage represents direction from which wind blows.
Figure 4-41
SURFACE WIND ROSES FOR 8:00 AM
AND 4:00 PM AT THIOKOL PLANTS ITE
SOURCE: THIOKOL/WASATCH DIVISION, 1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
4-195
EXPLANATION
= Industrial
- Cropland and Pasture
= Other Agricultural Land
= Rangeland
= Reservoirs
Nonforested Wetland
= Dry Salt Flats
I
N
1 MILE
SCALE
Figure 4-42
LAND USE MAP OF
USAF PLANT 78 AND VICINITY
SOURCE: ESE.1991
INSTALLATION RESTORATION
PROGRAM USAF PLANT 78
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Surface water from the site drains into Blue Creek, which enters a wildlife refuge approximately 12 miles
downstream. Due to the low population density as well as distance from the nearest downstream house to Blue
Creek, there is no indication of surface water use for domestic purposes within 2 miles downgradient of the plant.
Onsite access is controlled and limited to plant personnel, and no trespassing onto the site is known or suspected
to occur. There is a remote possibility that children may wade in Blue Creek downstream of the site, however,
much of Blue Creek is shallow in the summer, and swimming is not expected. Livestock and wUdlife may drink
from Blue Creek, however, due to high TDS, the water is nonpotable.
Groundwater is also nonpotable, due to naturaUy occurring high TDS. Drinking water for the facihty is brought
in from potable wells some distance from the site. Water rights are required within Blue Creek VaUey and along
the east side of the Promotory Mountain Range. AU current groundwater rights are owned by Thiokol and
others (Whetstone, 1989). One stock weU exists north (upgradient) of Plant 78, and one domestic supply weU
exists nearly 2 mUes northwest of Plant 78 (ESE, 1987a). Groundwater flow is from the northeast to the
southwest across Plant 78. The nearest known weU downgradient of Plant 78 is nearly 2 mUes south.
Livestock in the area of Plant 78 are indicated in Figure 4-40. Cattle and sheep were observed in the area north
of the plant, and cattle were observed south of the plant along Highway 83. Barley was grown in the sections
directly north of the site during the spring of 1989.
WUdlife are abundant in the Plant 78 area. Approximately 1,600 buck deer were harvested by 2,931 hunters in
the 1,000,000 acres of the Box Elder subunit of which Plant 78 is a part (Rensel, 1989). Upland game hunting
is also very good in the Plant 78 area (Rensel, 1989). Mule deer, Hungarian partridge, chukar partridge,
mourning dove, and cottontail rabbits are the major game species. Blue Creek does not support game fish.
Waterfowl occur in Blue Creek and in the wildlife refuge downstream.
Bald eagle and peregrine falcon, both endangered species, occur seasonaUy in the Plant 78 area; bald eagles are
winter visitors. Golden eagles were observed in the Plant 78 area during the 1989 field program. During a hve
trapping study as part of the biological assessment, the only smaU prey species coUected at Plant 78 during the
1989 field season were deer and brush mice.
Aquatic invertebrates were coUected to determine stream diversity at locations above, below, and midsite of
Plant 78. There was no significant difference in diversity between any of the sampling locations.
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4.2.6 THREAT TO HUMAN HEALTH
In this section, threat to human health is summarized by area of concern from data presented in the previous
sections. The predicted exposure point concentrations (Table 4-55 and 4-56) were used to estimate intakes from
contaminated media. Chronic daily intake is calculated with the foUowing general equation (EPA, 1989):
Intake (mg/kg-day) = C„ x IR x ET x EF x ED (44)
BW x AT
where: C(x) = contaminant concentration at the exposure point in specific media (mg/kg, mg/m3),
IR = ingestion or inhalation rate (L/day, m3/hour),
ET = pathway specific exposure time (hours/day),
EF = pathway specific exposure frequency (days/year),
ED = exposure duration (years),
BW = body weight (kg), and
AT = averaging time (exposure period averaged over _X_ days, or ED x 365 days/year).
Intakes were estimated for each exposure pathway and land use scenario. A carcinogenic effect of CDl was not
calculated for 1,1,1-TCA because it is not considered to be a potential human carcinogen (IRIS, 1990; EPA,
1989). The intakes are highly conservative because maximum values were used to predict the exposure point
concentrations. The receptors differ by exposure pathway based on the most apphcable or sensitive receptor for
the exposure scenario.
4.2.6.1 Inhalation
Intake by a worker at the source, or a resident at the boundary, due to exposure of volatilization from
contaminated soU, sediment, or surface water, was calculated as foUows:
Intake (mg/kg-day) = CA x IR x ET x EF x ED (45)
BWx AT
where: CA = contaminant concentration in air (mg/m3) (Table 4-55 and 4-56),
IR = 0.83 m3/hour average adult inhalation rate 2.5 m3/hour (worker) doing moderate
work,
ET =8 hr/day (worker), 24 hr/day (resident),
EF = 50 days/year (worker), 350 days/year (resident),
ED = 25 years (worker), 30 years (resident),
BW = average adult body weight (70 kg), and
AT = 25 years x 365 days/year (worker noncarcinogenic); 30 years x 365 days/year
(nonresident carcinogenic); 70 years x 365 days/year (carcinogenic).
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Outside activities at the Plant 78 instaUation are kept to a minimum for safety reasons. As a result, workers are
expected to spend a maximum of 50 days per year doing outside grounds maintenance activities that could result
in exposure. An ED of 25 years was used to represent an average worker's exposure period as recommended
by the EPA (1991). The CA values are from Tables 4-55 and 4-56.
Calculated chronic daily air intakes (CDl) (mg/kg-day) from volatilization of surface water, sediment, or soU are
given in the foUowing list.
Intake by Residents at Boundary or
Intake by Worker at Source Blue Creek
Area Chemical \ \
Noncarcinogenic Carcinogenic Noncarcinogenic Carcinogenic
FVD 1,1,1-TCA 3.5x10* - 1.2 x 10'7
NDD CHClj 3.9 xlO7 1.4 x 10"7 2.7 x 10* 1.2x10*
1,2-DCA 3.1x10* 1.1x10* 2.1x10* 1.9x10*
1,1,1-TCA 4.7x10* -- 3.3x10*
TCE 2.3 xlO"7 8.4x10* 1.6x10* 7.0 x 10"7
E-512 CHC13 1.6 xlO7 5.9x10* 1.7 x 10"7 7.3x10*
1,1,1-TCA 1.5x10* - 1.6x10*
Blue CHCI3 - - 2.2x10* 9.6 x IO"7
Creek 1,2-DCA - - 8.7x10* 3.6x10*
1,1,1-TCA - - 2.5x10*
In instances where more than one media was contaminated, the intakes due to inhalation were added. For
example, the NDD had air contamination resulting from both soU and surface water (Table 4-54). Thus, intake
due to exposure to chloroform or TCE is the sum of intake from surface water and soU.
Inhalation of contaminants by workers is not expected to occur as a result of fugitive dusts (due to the volatility
of the contaminants), or volatilization from groundwater (due to the depth of the aquifer). Because of the
estimated length of time for the groundwater plumes to reach either a hypothetical receptor at the boundary or
Blue Creek (as much as several thousand years), inhalation due to groundwater use is not expected to occur.
4.2.6.2 Ingestion
There is little potential for ingestion of contaminants in groundwater for three reasons: (1) the length of time
(estimated of 10 to 224 years) it takes for the plumes to reach either the boundary or Blue Creek; (2) the nearest
downgradient weU is at least two mUes downgradient, such that it could take the plumes weU over 100 years to
migrate to the nearest residence; and (3) surface water and groundwater are not utilized as drinking water source
in the Plant 78 vicinity due to high TDS. Because the likelihood that exposure to groundwater is low,
groundwater exposures via drinking water were not evaluated.
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There is little chance of recreational contact in Blue Creek with resulting incidental ingestion, because Blue
Creek is small and the distance to the nearest house is nearly one mile. Although not realistic, a swimming
exposure scenario was evaluated. Because incidental ingestion could occur through swimming, surface water
intakes were calculated. Of the three contaminants of concern detected in Blue Creek (CHC13, 1,2-DCA,
1,1,1-TCA), only 1,2-DCA exceeded MCL values (maximum detection 27.7 ug/L; MCL 5 ug/L). Assuming
children could get access to Blue Creek, which has limited access in this restricted area, and incidentally ingest
surface water while swimming:
Intake (mg/kg-day) = CW x CR x ET x EF x ED (46)
BW x AT
where: CW = 0.028 mg/L 1,2-DCA, 0.00061 mg/L CHC13,0.00062 mg/L 1,1,1-TCA (Table 4-56),
CR = 0.050 1/hour (EPA, 1989),
ET = 2 hours/event, assumed,
EF =60 events/year,
ED = 7 years (between ages 8 to 15),
BW = 35 kg, and
AT = (7 years x 365 days/year), (70 years x 365 days/year).
Intake Bv Residents at Blue Creek (mg/kg-davl
Area Chemical Noncarcinogenic Carcinogenic
Blue Creek CHC13 2.9 x 10"7 2.9 x 10 s
1,2-DCA 1.3 x 10 s 1.3 x Iff*
1,1,1-TCA 2.9 x 10'7 2.9 x 10"8
The number of events is nearly nine times the national average (EPA, 1989). Intake of 1,2-DCA is thus
1.3 x 10"5 mg/kg-day for noncarcinogenic effects and 1.3 x 10"6 mg/kg-day for carcinogenic effects based on
current concentrations in Blue Creek. The contaminants below the MCLs were also modeled for intake by
ingestion. Ingestion of surface water by workers was not evaluated because this exposure pathway was very
unlikely. Worker contact with surface water is evaluated for dermal and inhalation exposure.
Incidental ingestion of soil or sediments by workers at the source who might fail to wash following outdoor
activities was considered for the FVD and NDD (EPA, 1989). It was assumed that little incidental ingestion of
sediments would occur for Blue Creek.
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Intake (mg/kg-day) = C. x IR x CF x FI x EF x ED (49)
BW x AT
where: Cs = soil or sediment concentration (mg/kg),
IR = ingestion rate of 100 mg/day,
CF = conversion factor of 10"* kg/mg,
FI = fraction ingested from contaminated source (assume 100%),
EF = 50 days/year,
ED = 25 years,
BW = 70 kg (adult), and
AT = ED x 365 days/year for noncarcinogens; 70 x 365 days/year for carcinogens.
The maximum values in soil or sediments were used for Cs:
FVD 1,1,1-TCA 0.824
NDD CHC13 0.00011
TCE 0.00025
Intake by workers due to incidental ingestion from soil or sediments (mg/kg-day) is thus:
Area Chemical Carcinogenic Noncarcinogenic
FVD 1,1,1-TCA - 1.6 xlO'7
NDD CHCI3 7.7 xlO12 2.2 xlO11
TCE 1.7 x 10 " 4.9 x Iff11
4.2.6.3 Dermal
Workers at the source may contact surface water, soil, or sediments. It is not likely that children will access Blue
Creek for swimming, but the potential dermal chemical intakes from surface water were modeled conservatively
for children:
Absorbed Dose (mg/kg-day) = CW x SA x PC x ET x EF x ED x CF (47)
BW x AT
where: CW = concentration in water (mg/L),
SA = skin surface area available for contact (cm2), or 820 cm2 for adult male worker's
hands and 1,300 cm2 total surface area for a 8 to 15 year old male (EPA, 1989),
PC = dermal permeabihty constant for water (8.0 x 10"4 cm/hr),
ET = 2 hours/day (swimming), 4 hours/day (worker),
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EF = 60 days/year (swimrning), 50 days/year (worker),
ED = 7 years (swimming); 25 years (worker),
CF = volumetric conversion factor (1 1/1000 cm3),
BW = 35 kg (young male); 70 kg (worker), and
AT = ED x 365 days/year for noncarcinogens; 70 x 365 days/year for carcinogens.
ED, ET, and EF were assumed for workers and children. Children were assumed to swim in Blue Creek 15
days/month from May-August. Worker contact with onsite sources is assumed to be infrequent.
The SA for young males was obtained from averaging total surface area values for 6 to 15 year-olds (EPA, 1989).
Dermal permeabihty for TCE and 1,1,1-TCA (cm/hr) are reportedly slow for humans (EPA, 1985c; EPA, 1984),
but due to lack of values, the dermal permeabihty constant for water was used (EPA, 1989). The exposure point
concentrations from Tables 4-55 and 4-56 were converted to mg/L:
Area Chemical
Exposure Point Concentration (mg/L)
Source Blue Creek or Boundary
NDD
E-512
Blue Creek
CHC13
1,2-DCA
1,1,1-TCA
TCE
CHCI3
1,1,1-TCA
CHCI3
1,2-DCA
1,1,1-TCA
0.0012
0.0099
0.013
0.00063
0.00047
0.0042
0.0043
0.00047
0.0042
0.00061
0.028
0.00062
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Dermal intakes from surface water (mg/kg-day) were calculated with the above concentrations and equation (47)
as follows:
Area Chemical
Worker at the Source
Noncarcinogen Carcinogen
Residents at Boundary or Blue
Creek
Noncarcinogen Carcinogen
NDD CHCI3
1,2-DCA
1,1,1-TCA
TCE
6.16 x IO"9
5.1 x 10"8
6.7 x IO*
3.2 x IO"9
2.2 x IO"9
1.8 x 10'8
1.2 x 10"9
E-512 CHCI3
1,1,1-TCA
2.4 x ICV9
2.2 x IO"8
8.6 x IO"1
Blue
Creek
CHCI3
1,2-DCA
1,1,1-TCA
6.0 x IO"9
2.7 x IO"7
6.1 x IO"9
6.0 x 1010
2.7 x IO"8
Dermal uptake resulting from contact with contaminated sediments or soils was modeled for a worker at the
source. Contaminated sediments and soils are not as mobile as surface water, and the only place they occur is
at the NDD, FVD, and in Blue Creek. Sediments and soils onsite were assumed to not move toward the
boundary because the process of movement is likely to cause desorption and result in the loss of concentration
to water or air. Thus, those soils and sediments onsite or directly in Blue Creek provide the most conservative
estimate. Sediments in the NDD did not have measurable contaminant levels, although soils did. Maximum
sediment/soil levels in mg/kg are:
1.1.1-TCA
0.824 I'VDsediment
NDDMI1
Blue Creek,^, 0.304
CHCk
0.00011
TCE
0.00025
The dermal intake from soil exposure is determined by equation (48) (EPA, 1989):
Absorbed Dose (mg/kg-day) = C, x CF x SA x AF x ABS x EF x ED
BW x AT
(48)
where: Cs = concentration in sediment or soil (mg/kg),
CF = conversion factor (10* kg/mg) (EPA, 1989),
4-203
P78-914/P784E.204
02/14/92
SA = skin surface area (cm2/event), or 820 cm2 for adult male worker's hands and
1,300 cm2 for a male child less than 15 yrs wading in Blue Creek (EPA, 1989),
AF = soil to skin adherence factor (2.77 mg/cm2 for clay) (EPA, 1989),
ABS = absorption factor (assumed to be 25 percent or 0.25),
EF = 60 days/year (child in Blue Creek), 50 days/year (worker),
ED = 7 years (child in Blue Creek), 25 years (worker),
BW = 35 kg (young male), 70 kg (worker), and
AT = (ED x 365 days/year for noncarcinogens; 70 x 365 days/year for carcinogens).
The ABS was assumed to be 0.25 from soil across intact skin. Children were assumed to swim or play in Blue
Creek 15 days each month from May to August. Worker exposure was assumed to be infrequent because outside
activities are limited due to safety constraints.
Intake (mg/kg-day) by workers at the source or children swimming in Blue Creek from dermal absorption from
contact with contaminated soils and sediments is thus:
Area Chemical Carcinogenic Noncarcinogenic
FVD 1,1,1-TCA - 9.2 xlO"7
NDD CHC13 4.4 xlO11 1.2 xlO"10
TCE 9.9 x IO"11 2.8 x IO"10
Blue Creek 1,1,1-TCA ~ 1.3 x 10"6
Intakes were totaled by exposure route and summarized in Table 4-61 to give an estimate of total intake as a
result of site related contamination.
For noncarcinogens, the noncancer hazard quotient (HQ) was calculated as:
HQ = E/RfD (50)
where: E = intake (CDl) or exposure level, and
RfD = reference dose
Total exposure risk is given by pathway and chemical in Table 4-62. Oral RfD values were used to assess risk
from dermal exposure (EPA, 1989), although the risk becomes more uncertain due to route-to-route
extrapolation. For inhalation hazard estimates when inhalation RfDs were unavailable, oral RfDs were
substituted. Because all of the hazard quotients are less than unity, noncarcinogenic risks are not indicated for
any of the exposure pathways.
4-204
P78-914/P78T4-61.1
02/14/92
Table 4-61. Summary of Exposure Intakes for Current and Future Land Uses (Page 1 of 2).
Population Exposure Pathway Chemical
Chronic Daily Intake (CDl) (mg/kg-day)
Carcinogenic Effects Noncarcinogenic Effects
CURRENT
Workers Inhalation of chemicals volatilized from
soil, sediment, or surface water at the
source
Workers Dermal absorption of chemicals directly
from surface water at the source
Workers Dermal absorption of chemicals from soil
or sediment at the source
Workers Incidental soil or sediment ingestion at the
source
Residents Dermal absorption of chemicals in surface
water by children swimming in Blue Creek
Residents Dermal absorption of chemicals in
sediments by children swimming in Blue
Creek
Residents Incidental ingestion of surface water by
children swimming in Blue Creek
CHC13
1,2-DCA
1,1,1-TCA
TCE
CHC13
1,2-DCA
1,1,1-TCA
TCE
CHCI3
1,2-DCA
1,1,1-TCA
TCE
CHCI3
1,1,1-TCA
TCE
CHCI3
1,2-DCA
1,1,1-TCA
1,1,1-TCA
CHCI3
1,2-DCA
1,1,1-TCA
1.9 x IO 7
1.1 x IO"6
8.4 x 10*
3.0 x 10"9
1.8 x 10*
1.2 x 10"9
4.4 x 1011
9.9 x .1011
7.7 x IO12
1.7 x Iff11
6.0 x 1010
2.7 x 10*
2.9 x 10*
1.3 x 10*
2.9 x 10*
5.4 x 10"7
3.1 x 10*
4.1 x 10*
2.3 x 10'7
8.6 x 10"9
5.1 x 10*
6.7 x 10*
3.2 x 10'9
1.2 x 1010
9.2 x 10"7
2.8 x IO12
2.2 x 10n
1.6 x 10"7
4.9 x 10 "
6.0 x IO"9
2.7 x 10'7
6.1 x 10*
1.3 x 10*
2.9 x 10"7
1.3 x 10*
2.9 x 10"7
P78-914/P78T4-61.2
02/14/92
Table 4-61. Summary of Exposure Intakes for Current and Future Land Uses (Page 2 of 2).
Population Exposure Pathway Chemical
Chronic Daily Intake (CDl) (mg/kg-day)
Carcinogenic Effects Noncarcinogenic Effects
FUTURE
Residents
Residents
Inhalation of chemicals volatilized from
soil, sediment, or surface water onsite and
transported to boundary
Inhalation of chemicals volatilized from
Blue Creek with residents living next to
bank
CHC13
1,2-DCA
1,1,1-TCA
TCE
CHCI3
1,2-DCA
1,1,1-TCA
1.3 x 10"6
1.9 x 10'6
7.0 x 10"7
9.6 x IO"7
3.6 x 10'5
2.9 x IO"6
2.1 x 10 s
3.5 x IO"5
1.6 x 10"6
2.2 x 10"6
8.7 x 10 s
2.5 x 10*
P78-914/P78T4-62.1
02/14/92
Table 4-62. Chronic Hazard Index Estimates.
Exposure
Pathway/
Chemical
CDl
(mg/kg-day)
CDl Adjusted
for Absorption
RfD
(mg/kg-day)
RfD Source Hazard
Quotient
CURRENT
Inhalation of Volatilized Chemicals at the Source
CHCI3
1,2-DCA
1,1,1-TCA
TCE
5.4 x 10'7
3.1 x ICV6
4.1 x ICV5
2.3 x IO"7
No
No
No
No
0.011
0.3
HEAS, 1991
HEAS, 1991
HEAS, 1991
Dermal absorption of chemicals in surface water by workers at the source2
CHCI3 8.6X10"9 Yes 0.01
1,2-DCA 5.1 xlO"8 Yes
1,1,1-TCA
TCE
6.7 x IO"8
3.2 x IO'9
Yes
Yes
0.09
HEAS, 1991
HEAS, 1991
HEAS, 1991
Incidental soil/sediment ingestion by workers at the source
CHCI3
1,1,1-TCA
TCE
2.2 x Iff"
1.6 x 10"7
4.9 x Iff11
No
No
No
0.01
0.09
Dermal absorption from soil or sediment by workers at the source2
CHCI3 1.2 xlO10 Yes 0.01
1,1,1-TCA 9.2 xlO"7 Yes 0.09
TCE 2.8 xlO10 Yes
HEAS, 1991
HEAS, 1991
HEAS, 1991
HEAS, 1991
HEAS, 1991
HEAS, 1991
Dermal absorption of chemicals in surface water in Blue Creek by residents2
0.01 HEAS, 1991 CHCI3
1,2-DCA
1,1,1-TCA
6.0 x 10^
2.7 x 10"7
6.1 x 10*
Yes
Yes
Yes 0.09 HEAS, 1991
Dermal absorption of chemicals in sediments in Blue Creek by residents2
1,1,1-TCA 1.3 x 10* Yes 0.09 HEAS, 1991
Ingestion of Chemicals in Surface Water in Blue Creek by children playing
0.01 CHCI3
1,2-DCA
1,1,1-TCA
2.9 x IO"7
1.3 x 10*
2.9 x IO"7
NO
NO
NO 0.09
HEAS, 1991
HEAS, 1991
HEAS, 1991
5.4 x 10*
1.4 x Iff4
8.6 x IO"7
7.4 x 10'7
2.2 x IO"9
1.8 x 10*
1.2 x 10*
1.0 x 10*
6.0 x Iff7
6.8 x 10*
1.4 x 10*
2.9 x 10*
3.2 x 10*
FUTURE
Inhalation by a future resident of chemicals volatilized from soil, sediment, or surface water and
transported to the boundary
CHClj
1,2-DCA
1,1,1-TCA
TCE
2.9 x 10*
2.1 x 10*
3.5 x 10*
1.6 x 10*
No
No
No
No
0.011
0.3
Inhalation by a future resident living next to the bank of Blue Creek
0.011 CHCI3
1,2-DCA
1,1,1-TCA
2.2 x 10*
8.7 x 10*
2.5 x Iff*
No
No
No 0.3
HEAS, 1991
HEAS, 1991
HEAS, 1991
HEAS, 1991
HEAS, 1991
2.9 x 10"*
1.2 x 10"
2.2 x 10"
8.3 x 10*
1 Oral RfD used because inhalation RfD unavailable.
2 Oral RFD used because dermal RfD is unavailable.
4-207
P78-914/P784EJ08
02/14/92
4.2.7 CARCINOGENIC RISKS
For carcinogens, the slope factor (SF) was used to determine the chemical specific and total pathway risk. Risk
is determined by equation (51):
Risk = CDl x SF (51)
where: CDl = chronic daily intake averaged over 70 years,
SF = Slope factor (mg/kg-day)'1, and
Risk = unitless probability of an individual developing cancer.
Risks are summarized in Table 4-63. None of the individual exposure pathways exceed a IO* risk estimate;
however, total site risk estimated at 4.6 x 10* for combined future and current residents. Many of the
assumptions in the exposure assessment were highly conservative for instance in the receptor identification, no
immediate human receptors were observed. When the future resident scenario is removed from the site total
risk, and risk calculated only for workers and current residents, the predicted risk is 2.4 x 10"7. In addition, the
carcinogens are all B2 weight of evidence chemicals. This indicates probable human carcinogenicity but lacking
evidence of such in humans. Therefore, excessive carcinogenic risks are not predicted for current or future
human receptors as a result of any of the probable exposure scenarios.
4.2.8 THREAT TO WILDLIFE
At all areas of concern, predicted exposure concentrations were less than the estimated or estabhshed criteria
protective of aquatic or terrestrial organisms.
The observed levels in surface water were orders of magnitude lower than the AWQC for freshwater aquatic
life. Furthermore, field investigations of aquatic life diversity in Blue Creek did not indicate any significant
difference between upgradient areas and the downgradient Plant 78 boundary. Obvious population impacts as
a result of site-generated contamination are thus not indicated in Blue Creek.
The estimated air concentrations at the source areas (Table 4-55) and downgradient (Table 4-56) are lower than
the acceptable concentrations predicted based on laboratory animal studies. Thus, inhalation of site-generated
contamination is not expected to result in adverse effects in nonhuman biota.
i
The surface water concentrations at the source areas are less than those predicted acceptable for drinking water
ingestion based on LOAELs and NOELs for laboratory animals. The estimated levels that will not result in
adverse effects are uncertain, but conservative in that the lowest available value was used to predict criteria, and
an uncertainty factor of 100 or 1,000 was apphed to reduce the level further.
4-208
P78-914/P78T4-63.1
02/14/92
Table 4-63. Summary of Chemical Specific Carcinogenic Risks for each Exposure Pathway and Total Carcinogenic Risk (Page 1 of 2).
Chemical CDl CDl Inhalation or Weight of Cancer SF Source CDl
(mg/kg-day)
CDl
Adjusted
for
absorption
Inhalation or
Oral SF1,2
(mg/kg-day)-1
Weight of
Evidence
Cancer
Type
Chemical
Specific
Risk
Total
Pathway
Risk
Total
Exposure
Risk
CURRENT
Inhalation of Volatilized Chemicals bv Workers at the Source.
CHC13 1,2-DCA
TCE
1.9 x IO"7
1.1 x Iff6
8.4 x Iff8
No
No
No
8.1 x Iff2
9.1 x IO"2
1.7 x Iff2
B2
B2
B2
Dermal Absorption of Chemicals bv Workers Direclv From Surface Water at the Source2
CHCI3
1,2-DCA
TCE
3.0 x 10"9
1.8 x IO"8
1.2 x IO'9
Yes
Yes
Yes
6.1 x Iff3
9.1 x 10'2
1.1 x Iff2
Incidental Ingestion of Soil or Sediment bv Workers at the Source.
CHCI3
TCE
7.7 x Iff12
1.7 x Iff11
No
No
6.1 x IO 3
1.1 x IO"2
B2
B2
B2
B2
B2
Liver
Circulatory
System
Lung
Kidney
Circulatory
System
Liver
Kidney
Liver
1991
1991
1991
1991
1991
1991
1991
1991
1.5 x 10"8
1.0 x Iff7
1.4 x IO"9
1.8 x Iff11
1.6 x 10'9
1.3 x 10 "
4.7 x Iff14
1.9 x Iff13
1.2 x IO"7
1.6 x Iff9
2.4 x Iff1
Dermal Absorption of Chemicals From Soil or Sediment by Workers at the Source2.
CHCI3
TCE
4.4 x Iff"
9.9 x Iff"
Yes
Yes
6.1 x 103
1.1 x 10'2
B2
B2
Kidney
Liver
1991
1991
2.7 x Iff13
1.1 x Iff12 1.4 x Iff1
Dermal Absorption of Chemicals in Surface Water bv Residents in Blue Creek2,
CHCI3 6.0 x Iff10 Yes
1,2-DCA 2.7 x 10 s Yes
6.1 x Iff3
9.1 x Iff2
Ingestion of Chemicals in Surface Water bv Residents in Blue Creek.
CHCH3
1,2-DCA
2.9 x Iff8
1.3 x 10"6
No
No
6.1 x Iff3
9.1 x 102
B2
B2
B2
B2
Kidney
Circulatory
System
Kidney
Circulatory
1991
1991
1991
1991
3.7 x Iff12
2.5 x IO"9
1.8 x Iff10
1.2 x Iff7
2.5 x Iff5
1.2 x Iff7
TOTAL CURRENT 2.4 x 10-7
P78-914/P78T4-63.2
02/14/92
Table 4-63. Summary of Chemical Specific Carcinogenic Risks for each Exposure Pathway and Total Carcinogenic Risk (Page 2 of 2).
Chemical CDl CDl Inhalation or Weight of Cancer SF Source Chemical Total Total
(mg/kg-day) Adjusted Oral SFU Evidence Type Specific Pathway Exposure
for (mg/kg-day)-1 Risk Risk Risk
absorption
FUTURE RESIDENTS
Inhalation of Chemicals Volatilized From Soil. Sediment, or Surface Water, and Transported to Boundary.
CHC13 1.3x10* No 8.1 xlO2 B2 Liver 1991 1.1 x Iff7
1,2-DCA 1.9 xlO6 No 9.1x102 B2 Circulatory 1991 8.3 x Iff7
TCE 7.0 xlO"7 No 1.7 xlO2 B2 System 1991 1.2x10* 9.5 x 10"7
Lung
Inhalation Of Chemicals Volatilized From Surface Water In Blue Creek Bv Residents On Bank.
CHC13 9.6 x Iff7 No 8.1 xlO"2 B2 Liver 1991 7.8x10*
1,2-DCA 3.6 x10 s No 9.1 x 10"2 B2 Chculatory 1991 3.3x10* 3.4x10*
System
TOTAL FUTURE 4.4 x 10*
TOTAL CARCINOGENIC RISK 4.6 x 10*
TOTAL CANCER RISK (WEIGHT OF EVIDENCE B2) 4.6 x 10*
Values for TCE are interim (Heas, 1991).
The oral slope factor was adjusted with an absorption efficiency of 0.25 percent (EPA, 1989) and apphed as the dermal toxicity value (SF). Divide by 0.25 to derive
the original oral SF.
P78-914/P784E211
02/14/92
The soil and sediment concentrations at the source areas were very low (< 1 ppm). Area of contamination was
limited to the FVD, and one sample from the NDD. Because of the limited extent of contamination, adverse
effects due to soil ingestion or dermal contact are not considered likely.
4.2.9 NO THREAT TO HEALTH
The apparent human health risks at Plant 78 appear to be minimal, despite the levels of groundwater
contamination observed. This is due to the foUowing reasons:
• Groundwater is nonpotable without prior treatment due to naturaUy occurring high TDS,
• Distance to nearest homes,
• Distance to nearest surface water drainage (Blue Creek),
• Length of time for plume to reach Blue Creek,
• Low population density in the surrounding area, and
• Lack of bioaccumulative properties for the contaminants at Plant 78.
The time for the plumes from the northern end of Plant 78 and M-585 to reach Blue Creek are uncertain,
ranging at least one order of magnitude; the time for the plumes to actuaUy reach water supply wells wiU exceed
100 years. By not considering biodegradation or other decay processes, groundwater concentrations at Blue
Creek were conservatively modeled. The predicted groundwater concentrations at a specific discharge point at
iBlue Creek, without allowing for surface water dilution, are predicted to be less than the AWQC for aquatic life.
Only TCE appears to exceed the AWQC for human health, although these criteria are likely to be too
| conservative, since Blue Creek is not expected to be utilized for drinking water, recreation, or fishing at any time.
The combined cancer risks for the potential exposure pathways are 4.6 x 10* risk level, and the weight of
evidence is B2. The noncancer hazard quotients are all less than unity, predicting minimal threat to health, based
on noncarcinogenic effects. There are no observed ecological health effects due to observed contamination at
Plant 78.
4-211
5.0 ALTERNATE REMEDIAL MEASURES
F7W14/P785.1
02/18/92
5.0 ALTERNATE REMEDIAL MEASURES
The development of alternative remedial measures is integrated with and dependent upon input from the
Feasibility Study (FS). The process by which the FS is developed is, in turn, integrated with and dependent upon
the findings of both the Remedial Investigation (RI) and Risk Assessment (RA). The RI provides data with
respect to the nature and extent of contamination at the site. The RA identifies the type and level of potential
risk to which human or environmental receptors may be exposed. The FS addresses those exposure pathways
identified in the RA as posing an unacceptable risk to human health or the environment in order to mitigate the
endangerment. Those releases identified in the RI, for which the RA concludes pose no current or potential
future threat, should be eliminated from consideration from the FS.
As presented in Section 4.0, the RA performed for Plant 78 determined that the concentrations of site-related
constituents detected in environmental media at the site do not pose an unacceptable current or future risk to
human health and the environment. The results of the RA support the implementation of the no action
alternative for Plant 78. Therefore, there is no need to determine alternative remedial measures. A decision
document will be prepared to dociunent the implementation of the no action alternative.
5-1
6.0 RECOMMENDATIONS
P78-914/P786.1
02/18/92
6.0 RECOMMENDATIONS
6.1 DIRECTION AND APPROACH OF FUTURE IRP EFFORTS
The Stage 2 investigation at Plant 78 has determined that the levels of site-related constituents detected in
environmental media at the site do not pose an unacceptable current or future risk to human health and the
environment. The results of the investigation support the implementation of a no action or limited action
alternative and as such, the performance of a Feasibility Study (FS) is not necessary or appropriate.
Implementation of the no action or limited action alternative is consistent with current EPA guidance (EPA,
1988). In situations where the results of the baseline risk assessment may indicate that the site poses httle or
no threat to human health or the environment, the FS should be either scaled down as appropriate to that site
and its potential hazard, or eliminated altogether (EPA, 1988). The remote location of Plant 78 and the unique
geological and hydrogeological characteristics of the site allows the appropriateness of the no action or limited
action alternative.
6.2 RECOMMENDATIONS FOR EACH SITE AND/OR OPERABLE UNIT
For purposes of simplifying the discussion of investigation sites at Plant 78, the NDD (including Building E-519),
E-512, and FVD (including Building E-515) are grouped into Operable Unit (OU) No. 1. The M-585 site and
Blue Creek will remain as separate sites.
OU No. 1 is classified as a Category 1 site where no further IRP action (including remedial action) is required.
The M-585 French Drain Site is classified as a Category 1 site where no further IRP action (including remedial
actions) is required.
Blue Creek is classified as a Category 1 site where no further IRP action (including remedial action) is required.
6-1
7.0 REFERENCES
P7W14/P787.1
02/18/92
7.0 REFERENCES
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Bower, H. and R.C. Rice. 1976. A Slug Test for Determining Hydraulic Conductivity of Unconfined Aquifers
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macrochirusl. BuUetin of Environmental Contamination and Toxicology 26:446-452. In: EPA, 1985b.
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