DSHW-2024-008174

CORPORANON
RCRA, I'ACIUITY IIT{TTESTIGATION
voLUME'oi$E - A
TASK r:'DESCRIPTqN OF Cunnnttr CONDITIONS {1
April 1993
T coRPoRAroN
STRATEGIC OPERATIONS
8 April L993
V000: FY93 :59
Dennis R. Downs, Directoroivision of Solid and Hazardous Waste
State of Utah Department of Environmental QualityP.O. Box L44880Satt Lake City, Utah 841-L4-4880
Dear Mr. Downs:
RE: Submittal of Thiokol Corporation RCRA FacilityInvestigation Workplans
Please find enclosed three sets of inserts to ThiokolCorporationrs RCRA Facility Investigation Workplans. Theseinserts contain modifications which have been made to theworkplans as a result of comments received from the DSHW
concerning the draft submittals.
The comments received from the DSHW along with Thiokolts
response to these comments are included as an attachment to thisIetter. The content of the comments and the responses have beenincorporated into the revisions of the workplans.Certification is also included as an attachment.
Plan
If you have any questions in this regard, please contact me at(80L) 853-5928, ot Frank Walker at [phone].
Sincerely,
and Environmental Senrices
. D. Thompson, Director
Thiokol Waste Managenent
PO. Box 689, Brigham Cit14 UT 84302-0689 (801) 863-35 / /
CER.|IIFICAAION OF IIEIOXOIT RCRA PACIITITI INVES:IIGAIIOII rORtrPIrAltg
ttl certify under penalty of Iav, that this document and all
attachments were prepared under my direction or superx/ision in
accordance with a system designed to assure that qualified
personnel properly gather and evaluate the informationsubmitted. Based on my inguiry of the person or persons who
manage the system, or those persons directly responsible forgathering the information, the information submitted is, tothe best of my knowledge and belief, true, accurate, andcomplete. I am aware that there are significant penalties for
submitting false information, including the possibility offine and imprisonment for knowing violations.rl
Signed:
Dated: 7 *7)
J. D. Thompson, Director
Thiokol Waste Managrement and Environmental Serrrices
i
t
I
I_,.-T-:__*- ____:_.
L.The RFI does not follow the guidelines and format outlined in Module Seven of
Thiokol's Post-Closure Permit. This makes the review of the document more time
consuming. laborious and hence. most costly for Thiokol.
Thiokol began the work of preparing the RFI workplans immediately following the
conclusion of the RFA. The RCRA Conective Aaion Plan and RCRA Facility
Investigation Guidance Manuals were used in preparing the Draft RFI submittals.
The Draft RFI Workplans were submitted to the DSHW prior to the issuance of the
Post-Closure Permit, therefore, the plans may not parallel those within the permit.
Thiokol has utilized the Post-Closure Permit as a checklist for developing Phase I,
and believes the submittal accompanying this response includes the essential
elements required by the permit.
The purpose of the RFI is to characterize the nature and extent of contamination
both within the facility boundaries and migrating from the facility. In order to
accomplish these objectives. the RFI Work Plan must include explicit detailed tasls
that are designed to determine the presence. concentration. extent. direction and rate,
of movement of hazardous wastes or hazardous constituents on and off the Thiokol
property. The proposed investigation plans in Volume Four of the RFI Work Plan
are limited in and sDarinqlv describe the rati veloD th
sampling and analysis procedures for characterizing the contamination that may exist.
Among other things. the investigation plans need to be revised to properly evaluate
the hydrogeologic conditions and potential migration pathways in the vicinity of the
SWMUs in order to assess the extent of contamination and to insure that the
necessary data and information will be provided to support a Corrective Measures
Study.
The Data Management Plan for Phase I of the RFI has been modified to describe
the phased approach to investigating those sites which have been prioritized based
on their actual or potential threat to human health and the environment, aud where
a release of hazirdous waste or hazardous waste constituen(s) has'iibt 'been
documented. Phase I of the RFI will concentrate on verification of a release of
hazardous waste or hazardous constituent(s), concentration of contaminants, and a
preliminary evaluation of the extent of contamination. Subsequent phases will be
added as needed to further characterize the extent, direction, and rate of movement
at those sites verified as having a release and exceeding applicable standards during
Phase I. The objective of the workplans in Volume Four is to present site specific ',
plans to obtain data which will allow valid conclusions to be made regarding the sites
in terms of contamination, and identiff those sites which will require further
investigation in Phase II of the RFI. An evaluation for hydrogeologic conditions and
potential migration pathways are beyond the scope of the Phase I Investigation and
are deferred to subsequent phases.
2.
Throughout the RFI Work Plan. Thiokol refers to various soil. groundwater and
other studies as sources of information to partially fulfill the requirements of the
RF[. Many of these studies are presently being conducted pursuant to Compliance
Order and RCRA closure plans. A significant amount of information has been
gathered from those studies which will be useful in conducting the RFI. however. the
status of those investigations underscore the hydrogeologic complexity of the facility
and of investigation. In order to prevent costly and time consuming repetitive
sampling and review. the RFI is to be that plan.
Several sites identified as SWMUs during the RFA have been investigated under
regulatory issued Consent Agreements, DSHW approved Closure Plans, and the
DOD Installation Restoration Program (IRP). Investigation activities at these sites
have been at least equal to, and in most cases, has exceeded the equivalent of a
Phase I, and even a Phase II, RFI. Several of the sites have entered corrective action
by either clean closure or closure in place with monitoring. A new Consent
Agreement is in process which addresses industrial wastewater discharges. These
discharge sites have been identified as SWMUs and are incorporated into the RFI.
Those sites where investigations have previously been conducted by regulatory
requirements, closure plans, and/or the IRP will continue to be addressed as.
SWMUs, but the independent investigations conducted at these sites should be
considered as satisrying the requirements of the initial phases of the RFI.
Current facility investigations that are being conducted outside of the RFI have
identified widespread groundwater contamination beneath the facility. As mentioned
in Task I. Section 5.0. delineation of the contaminant plume is ongoing. Since the
vertical and horizontal extent of groundwater contamination at the facility has not
en defined. anv releases to sroundwater whic
Waste Management Units (SWMUs) identified in the RCRA Facility Assessment
(RFA) will need to be thoroughly delineated to support a Corrective Measures Study.
Ground water contamination is widespread beneath much of the manufacturing areas
where many SWMUs are located. This contamination in many areas is one or more
orders of magnitude above the detection limit for these contaminates. As a regult,
it is often not technically possible to delineate ground water contamination of most
SWMUs from ground water contamination of RCRA "regulated units" or other
SWMUs, unless the contamination is at statistically significant levels or of an
anomalous q/pe. Thiokol believes that for many units the most appropriate ground
water strategy is not to differentiate betrveen individual units, but to group units
areally and treat contamination as one plume system of various constituents and
components.
Some of the proposed investigation plans need to be modified to properly
characterize possible contamination at the sites. Using an abbreviated list of
6.
indicator parameters to determine the oresence and define the extent of
ites w rds of then is inaporooriate at sites where comolete records of the tvoes androDn
amounts of wastes that were disposed of are not available. Thiokol needs to provide
rationale to justiff its selection of analytical parameters for contamination
investiqations wher d of in the Dast unknown.
The constituents of concern and parameters to be monitored during Phase I of the
RFI were selected after a thorough review of the existing data for each of the sites.
Thiokol has proposed constituents and parameters for monitoring based on
knowledge of the processes generating the waste, as well as the composition of the
wastes known or suspected to have been managed at the site. Where analytical data
is available from past sampling activities, constituents were chosen based on
concentrations present when compared to regulatory levels or background. In the
case of the industrial wastewater discharges, these constituents represent those which
were found in previous sampling of the effluent to exceed relevant regulatory health
and risk based standards as well as background criteria. Additional constituents of
concern have been added when they serve as indicators of other chemicals. (See
Section 4.0 of the Proiect Management Plan Volume Two)
The rationale for selecting the constituents and parameters for monitoring is included
with each specific sampling plan in Volume Four.
Each constituent entering the environment will have its own characteristic migration
rate and plume shape because of independent chemical and physical factors that
affect the concentration. extent and rate of movement of a constituent within the
nvtronmen include contaminant solubili ion. I
iokol m ted wi
r than a sinsular contaminant olume at each
Thiokol has revised the sampling stratery to clariff the stepped approach to site
evaluation. Phase I will focus on verification of releases from SWMUs. After a
release has been documented, subsequent phases will expand the charucterization
to include the chemical and physical factors described above.
The majority of the proposed hydrogeologic and soil contamination investigations are
designed on the premise that there is only a remote possibility for contaminants to
reach groundwater. Those conclusions are partly based on climatic conditions at the
facility (low infiltration rates through the soil column because of the relatively small
amount of annual precipitation) or because it has been assumed that there may be
limited mobility of the constituents of concern. Although precipitation amounts may
be small. many of the investigation sites may be influenced by proximal industrial
wastewater discharges. Such discharges could significantly enhance the mobility ofa
Therefore. Thiokol should consider a sampling strate$,that anticipates such diversity.
8.
constituents in the environment.
The investigation plans have been revised to clariff the stepped approach to site
evaluation. Sites where contaminates are mobile, or present at levels that present
significant risk to human health or the environment as determined by initial
sampling, will be further characterized through additional sampling. Thiokol believes
this phased approach wilt be most effective in focusing resources to sites where
mobility or high levels of constituents might pose a significant risk to human health
or the environment. If hazardous constituents are present at levels of concern (of
impact to human health and the environment) at sites proximal to industrial waste
flows, these sites may be candidates for Phase II investigation which may include soil
stratigraphy, chemistry and other characteristics in comment 6. However, an
informed decision cannot be made until the initial investigation has been completed.
The sampling strategy must account for the horizontal and vertical extent of
contamination. Most of the investigation plans are limited to soil sampling at the
surface and at two foot depths. There are no contingent plans for continued
samplingat greater depths or for additional investigations if releases to groundwater
have occurred.
See response to comment no. 2.
As in the A-2 Photographic Processing Drainfield Investigation Plan. In most of the
investigation plans. Thiokol has basically proposed a nvo-dimensional sampling
stratery to evaluate the horizontal extent of contamination. The stratery should
isticallv reDresentative vertical comDonen hof
contamination that may have occurred. Additionally. Thiokol has not discussed the
number of samples that will be collected at the site and has not provided any
rationale for limiting the depth of sampling to two feet below the ground surface.
t}ae Data Collection Oualiry Assurance Plan has been modified to address each of the
items in the sampling section of the Data Collection Stratery, as required by Module
VII of the Post-Closure Permit. This includes the issues raised by the DSHW in
comment no. 9.
losic investisations must also incl methodolow for the
characterization of attenuation mechanisms which may affect contaminant migration.
Such mechanisms mav incl not limit ion exch
9.
L0.
n content. mineral content and alkalini
acterization will
r is the orinci
contaminant transport media at Thiokol. there,fore. a thorough hydrogeologic
contaminant movement.
ntial for rminins th xtent and directi
t 1..
Site investigations will consist of a phased sampling program. Attenuation
mechanisms will be investigated at sites where attenuation plays an important role
in evaluating risk to human health or the environment. Sites that are not
contaminated (as determined by initial investigation), or will be clean closed by
removal of contaminates, or where levels of contaminants are below levels of
concern, will not be investigated for attenuation parameters. Phase II investigation
approach will include evaluation of ground water at sites where initial investigations
indicate the probability of migration of contamination to ground water.
Thiokol must also investigate stratigraphic nature of the soil and rock column
overlying the groundwater system in order to understand the potential migration
pathways. Previous investigations at the facility have identified variable soil
permeabilities and discontinuities which could affect the direction and rate of
movement of hazardous wastes or hazardous constituents. This twe of information
will be particularly useful in the investigation stratery at sites where waste
management practices have been implemented to eliminate the discharge of
hazar tes but industrial wastes have continuallv been disposed o
thorough knowledge of the migration pathways will be important.and it
will be necessary to identiff all potential receptors.
The soil and rock stratigraphy at Thiokol has been investigated at over 75 widely
distributed sites. This material has been previously submitted to the Utah DSHW.
Although the soil and rock strata are very heterogenous, stratigraphy and potential
migration pathways at many sites are fairly well understood. At sites where this
information is not knowq and where contaminant fate is necessary to evaluate risk
to human health or the environment, this data will be collected as part of Phase II
investigation. If hazardous constituents are present at levels of concern (of impact
to human health and the environment) at sites proximal to industrial waste flows,
these sites may be candidates for Phase II investigation including soil stratigraphy,
chemistry, and physical characteristics. However, an informed decision cannot be
made until the initial investigation has been completed.
The potential receptors have not been adequately addressed in the Work Plan.
There are references in reports of investigations at the sites to groundwater users as
potential receptors. however. the DSHW rdcently collected surface water samples
emanating from a natural spring near the junction of State roads 83 and 102. and the
analyilical results from those samples indicate the presence of Trichlorethylene (11.6
l) and 1..1,.l.-Trichloroethane (l.&us,/l). Thi ischarqe is near cattl
grazing areas and within a few miles of a protected water.fowl habitat.
Information concerning potential receptors to contaminated ground water has been
previously submitted to the Utah DSHW in referenced documents, and is
resubmitted in Volume l: Descriotion ol Cunent Corditiow. Section 6.
L2.
L3.
L4,
15.
The data collection strategy must be revised to ensure that all information data and
resultine decisions are technicallv sound. statisticallv valid and prooerlv documented.
Primarily. the revisions must discuss the representativeness of selected analytical
parameters. describe the necessary level of precision and accuracy for analytical data-
ribe the meth ision. accuracv and
completeness of the data. and provide rationale to assure that the data accurately
and precisely represent a characteristic of a population. parameter variations at a
sampling point. a process condition or an environmental condition. Thiokol has not
rovl ional lecti e analvtical Darameters.
The Data Collectbn Quality Assurance Plan contained in Volume Two has been
revised to address these concerns.
Statistically representative soil sample depths are important to determine the spatial
variabilitv of the constituents and the limits of contamination. Also. when collecting
the soil samples. the soils need to be characterized. since the sorptive capacity of
clavs and orsanics mav effect the overall distribution of metals and other constituents
(e.9.. 1007o sand or 1007o clay or an intermediate composition).
A preliminary characterization of the soils wilt made at the time of sampling under
Phase I. The sampler will document basic physical features of the soil and otler
pertinent information in the field log book. A more detailed characterization of the
soils is warranted only following verification of contamination and when the extent
and rate of migration are critical for evaluating potential for inter-media
contamination. Subsequent phases will accommodate the detailed characterization.
Many of the sampling plans state that extensive soil and groundwater sampling at the
Thiokol facility may be used to establish a data base for background values of
naturally occurring inorganic constituents. The DSHW must have access to all
proposed background data for review before the data can be approved for inclusion
in the RFI. Please provide a summary of all data intended for use as background
values.
Thiokol proposes to use the following sources as a background data base:
DSHW approved Closure Plan data:
T-29 Hydrazine Burning Pit
M-224 Shot Pond
M-136 Drum Storage Area
M-39, M-114, M-508, M-636 Photographic Waste Discharge Sites.
The background data for the closure plans has been previously submitted to the
DSHW. The data for the photographic waste sites will be submitted in late Spring,
1993, and will include QA/QC information. The soil background data base which
will be used and amended are summarized in Table 1 in the Data Collection Quality
Assurance Plan in Volume Two.
L6.All numerical information that is used in preparing statistical computations for
molins Drosr r analvsis needs to be Dresented. 'l'his tncludes. but is notThis incl
limited to. the coefficient of variation. the level of precision. the Student's t value.
and anv other information that i verifv the results and lor conclusionsifv th
that are Dresented i w of
anv information con di r amt mav De r if
L7.
L8.
there is insufficient information to document the validity and reliability of any data.
\\e Data Collection Oualin Assurance Plan contained in Volume Two has been
revised to address these concems.
The draft Work Plan addresses the major elements of the RFI. but the level of detail
is inadeguate to satisff the scope of work required to perform the investigation. The
investigation plans should be revised to implement a phased approach to the.
investigation which will identiff the presence and extent of contamination in the soil
and sroundwater.
Ttte Proiect Management Plan contained in Volume Two has been revised to discuss
a phased approach to the RFI.
In the Data Collection Oualitv Assurance Plan Section (Vol. 2). Appendix F Section
6.0. page 4 sites a list of analytical methods to be used in analysis of samples. The
Post-Closure Permit issued to Thiokol lists in Attachment 7. all the approved
methods to be used in anallrtical work. The methods used should come from this list.
Thiokol's Environmental Iaboratory Quality Assurance Plan cites SOP-101 as
containing the list of approved analytical methods performed by the laboratory. The
SOP is the Standard Operating Procedures for the laboratory. The analytical
methods described in this document reference EPA methods and do not deviate from
the methods in the Post-Closure Permit. A copy of SOP-101 has been included as
an attachment to the I-aboratory's Quality Assurance Plan.
All samples collected for laboratory analysis in Phase I will be analyzed using EPA
approved methods. For ground water samples, these methods are specified in Table
E-2 of Thiokol's Post-Closure Permit. Soil samples will be analyzed by methods
described in the most recent available edition of the Test Methods for Evaluating Solid
Waste.
o
L9.In the Photographic Wastewater Discharge Section of Volume 3. Unit Number 20.
the Investisation Plan refers to the Stioulation nsent Order for r n
of this sitb as well as elsewhere throughout the document. The purpose of the RFA
is to outline procedures for approval. This must be done for each SWMU.
See response to comment no. 3.
20.nit Number 1,91.. Investiqation Plans. ref,Ph
2L.
Investigation Plan. The RFI should contain the investigation plan for each SWMU.
for review and possible approval and not refer to another document.
Volume Three of Thiokol's RCRA Facility Investigation contains a brief summary
for each of the identified solid waste management units. This summary describes
location, operational dates, types of waste managed, RFA Recommendations,
Previous Investigations and Proposed Investigation Plans. Under the Investigation
Plans section of this summary, Thiokol states what further action is planned at the
site. If further investigation is warranted for the RFI, this section will refer to a
specific investigation workplan which has been prepared outlining the activities which
will occur. These specific workplans are contained in Volume Four.
The RFA Recommendations for Unit 111. among others suggests that the soils be
sampled around all sumps that have been removed. It is unclear whether or not this
has been or is going to be accomplished.
Regulatory requirements for hazardous waste sumps necessated a regular inspection
and testing program be implemented by Thiokol. Hazardous waste sumps were and
continue to be inspected by an independent engineer for leaks and basic tank
integrity. If a hazardous waste sump was determined to be of questionable integrity
and could not be repaired, or if the sump had been in service for 15 years or had
otherwise reached the regulatory deadline for replacement, the sump was replaced
by a sump meeting applicable design standards. When the old sump was removed
from service, a Thiokol Environmental Engineer inspected the area for signs of
excessive soil moisture or discoloration indicating a potential release from the sump.
If signs of a release were visible, the area of concern was sampled for waste
constituents managed within the sump. If no signs of a release were visible, the new
sump was installed and inspected prior to being placed into service.
Currently, there are no plans for sampling around those sumps which have been
removed. However, beginning in 1991, any sump which is taken out of service and
removed or replaced is sampled according to the sampling plan titled SorT
Investigation Procedures Following Sump Removal included in Volume Four of the
RFI workplans. Analytical data obtained from sampling under this plan to date has
been included with the respective SWMU summary in Volume Three of the RFI.
22.
23.
24.
The Investigation Plan for Unit 46 and for other similar units. states...."appear to be
water tight." What standard method analysis was used to make this determination.
Hazardous waste sumps were and continue to be inspected by an independent
engineer for leaks and basic tank integrity. The inspection is strictly a visual
evaluation (See response to comment no.21).
The operational dates for many of the units located in and near M-136 indicate they
ceased operation prior to November of 1.988. Please provide the specific dates of
cessation.
The operational dates for these units have been changed to reflect best knowledge
of beginning and ending operations.
The Constituent of Concern Section for Unit 251 and in many instances elsewhere
throughout the document. indicates "there are no constituents.....which exceed
relevant regulatory. health and risk based standards." Any units that exceed.
background must meet the clean-up standards of R315-101.
The levels of constituents within the industrial waste discharges were compared to
R448-6-2 Ground Water Quality Standards, R449-103-1 Primary Drink Water
Standards, Proposed National Primary Drinking Water Regulations, Secondary
Maximum Contaminant levels, Health Advisories by the Office of Drinking Water
Regulations and the Proposed Rules for Corrective Action For Solid Waste
Management Units at Hazardous Waste Management Facilities. If the level of any
constituent in the discharge exceeded the minimum value of that constituent in the
mentioned standards, it was then compared to the level in Blue Creek and ground
water considered to be representative of background. If the constituent exceed the
maximum detected value in either Blue Creek or the ground water it was listed as
a constituent of concern for that site and will be included in Phase I of the RFI for
verification of its presence in the soil.
The procedure outlined above is the process used in determining which corrstituents
would be investigated in the soils during Phase I of the RFI. It was not meant to
propose clean-up standards. If subsequent phases determine that corrective action
is required, the clean-up standards will follow the criteria of R315-101-2 which states:
"Subsequent to source elimination, clean-up standards for remaining
contamination which may include numerical, technolory-based or risk-based
standards or any combination of those standards, shall be determined on a
case-by-case basis taking into consideration the following criteria:
(a) The impact or potential impact of the contamination on the public
health;
25.
26.
27.
28.Throu
(b) The impact or potential impact of the contamination on the
environment;
(c) Economic considerations and cost effectiveness of clean-up options;
and
(d) The technolory available for use in clean-up."
Unit Number 257 (M-14N). Constituents of Concern. see Comment Number 18.
See response to comment no. 18.
Unit Number 258 (M-33C) and throughout the document. Investigation Plans. see
Comment Number 20.
See response to comment no. 20.
It is stated for the Units 302. 321 and 322 near M-345. and other units at Air Force
Plant 78. that "...this investigation has determined that levels of constituents detected.
in environmental media at the site do not pose an unacceptable current or future risk
to human health and the environment". The Division of Solid and Hazardous Waste
e determination whether or n f contamination reDresen
a risk. See Comment Number 24.
The cited statement is taken from the lrutaltuion Restoruion Prograrn ilRP) $tage
2 Report. February 1992 submitted to the Utah DSHW as well as U.S. EPA Region
VIII. The results of the IRP investigation concluded that the North Drainage Ditch
did not pose an unacceptable current or future risk to human health and the
environment.
molinq Techni f Volum
change the tapwater rinse and deionized rinse in bucket..." What constitutes a
frequent chanse?
The wording in the Sampling Techniques section of the workplans has been changed
and the phrase "frequently change the tapwater rinse..." has been replaced by "Do not
reuse tap water".
GENERAL COMMENTS
This submittal of Thiokol's RCRA Facility Investigation has been modified to clariff the
phased approach to site evaluation. Emphasis has been placed on assuring that each item
specified in Thiokol's Post-Closure Permit has been addressed.
Several new solid waste management units have been identified since the draft submittal in
Jdy, L992. These sites are included with this submittal as well as any investigation plans
proposed for Phase I.
or{c
H
F
I
TTIIOKOL CORPORATION
RCRA FACILITY II\"VESTIGATION
TASK Iz DESCRIPTION OF CURRENT
CONDITIONS
o
CONTEIYTS
1.0 INIRODUCTION
2.0 FACILIIY BACKGROI'ND2.1 ADMIMSTRATIONAI{DffiAREA2.2 HIGH PERFORMAT{CE PROPELLAIYT DEVELOPMENT AREA (pLAriIT
m)2.3 TEST AREA2.4 AIR FORCE PLAT.IT 78
3.0 MSEI'IING3.1 LAND USE
3.2 CLIMATE3.3 TOPOGRAPHY AND DRAINAGE3.4 GEOLOGY3.5 SITE STRATIGRAPHY
3.6 HYDROLOGY3.6.1 Regional3.6.2 Manufacturing Area3.6.2.L Perched Water System3.6.2.2 Perched Ground Water Tnnes
3.6.2.3 Well lnsallation in Perched Tanes3.6.2.4 Regional Water System
3.6.2.5 Ground Water Flow Directions
3.6.2.6 Regional Ground Water Flow Directions
3.6.2.7 Perched Ground Water Flow Directions
3.6.2.8 Transmissivity, ConductivityandStorativityEstimates3.6.2.9 Vertical Grcund Water Velocity
3.6.3 Plant III
3.6.4 Air Force Plant 78
3.6.5 Test Area
4.0 WELL INSTALLATIONS4.1 ICI{NT]FACTITRING AREA4.2 HIGH PERFORMANCE PROPELI-ATiIT DE\IELOPMENT AREA (PLANT
m)
4.3 TEST AREA4.4 AIR FORCE PLANT 78
5.0 NATT'RE AND ETTEhIT OF CONTATVIINATION
5.1 POTENTIAL POLLI]TANT MIGRATION PATI{WAYS
6.0 POTEIYTIAL RECEPTORS6.1 CI'RRENT AND FUTI]RE USES OF GROTTND WATER
6.1.1 Existing Ouality of Ground Water and Other Possible Sources of
Contamination
6.1.1.1 Existing Water aua[ty
6.1.1.2 Other Possible Sources of Conamination
6.1.2 Potential Health Risks by Human Exposurc
6.1.3 Potential Damage to Wildlife. Crops. Vegetation. and Physical Stmctures
6.L.4 Persistence and Permanence of Potential Adverse Effects6.2 POTENTIAL ADVERSE EEEECTS (SURFACE WATERS)
6.2.1 Hydrological Characteristics (,Surface Waters)
6.2.2 Patterns of Rainfall
6.2.3 Proximity of the Units to Surface Waters
6.2.4 Current and Future Uses of Surface Waters. and Established Water Ouality
Standards
6.2.4.L Current and Future Uses of Surface Waters
6.2.4.2 Established Water Quality Standards
6.2.5 Ouality of Surface Waters. and Other Sources of Contamination
6.2.5.1 Quality of Surface Waters
6.2.5.2 Sotrces of Contamination
6.2.6 Health Risks of Human Exposure
6.2.7 Potential Damage to wildlife, Crops. Vegetation, and Physical Structures
6.2.7.L Upland Habiats
6.2.7.2 Wetlands
6.2.7.3 Streams
6.2.7.4 Physical Structures
Persistence and Permanence of Potential Adverse Effects
PERSISTENCE AND PERI\{ANENCE OF POTENTIAL HAZARDOUS
CONSTITTJENTS
1. 1. l-Trichloroethane
6.3.1.1 Ambient Irvels
6.3.L.2 Healttr Effects
6.3.L.2.1 General
6.3.1.2.2 Ingestion
6.3.L.2.3 Inhalation
6.3.1.2.4 Dermal Toxicity
6.3.1.2.5 Meabolism and Excretion
6.3.1.2.6 Aquatic Ecosystems
6.3.1.3 Environmental Fate
Trichloroethvlene
-
6.3.2.1 Ambient Irrrels
6.3.2.2 Healttr Effects
6.3.2.2.1 General
6.3.2.2.2 Ingestion
6.3.2.2.3 Inhalation
6,2.8
6.3
6.3.1
6.3.2
6.3.2.2.4 Derrnal Toxicity
6.3.2.2.5 Metabolism and Excnetion
6.3.2.2.6 AquaticEcosystems
6.3.2.3 Environmental Fate
6.3.3 l.l-Dichloroethene
6.3.4 Acetone6.4 E)(POSI'RE PATITWAYS
6.4.1 Surface Water Fate
6.4.2 Direct Contact
6.4.3 Inhalation of Vapors and Dusts
6.4.4 Ingestion of Water and Soil
6.4.5 Ingestion of Crops and Livestock
6.4.6 Ingestion of Game Species and Aquatic Organisms
6.5 COMPARTSON TO REQUTREMENTS, STANDARDS, AND CRTTERH
6.5.1 Esablished Criteria
6.5.2 Estimated Criteria
6.5.2.L Aquatic Life
6.5.2.2 Wildlife and Domestic Livestock
6.5.2.2.1 Surface Water Ingestion by Nonhuman Biota
6.5.2.2.2 Inhalation
6.5.2.2.3 Thrcat to Wildlife6.6 NO THREAT TO HEALTII OR ENVIRONMEI{T
7.0 ON.GOING INVESTIGATIONS7.1 SOIL STT]DIES AT PHOIOGRAPHIC WASTE DISCIHRGE SITES7.2 INSTALLA'TION RESTORATION PROGRAI\{7.3 M-136 CLOSI]RE ATiID POST CIJOST]RE PERMIT APPLICATION
CORRECIT\IE ACTIONS7.4 CLOSI'RE ACTTVTUES7.5 M-225 IIIGH PERFORMANCE PROPELI.AI.IT BI]RNING GROI]NDS
IN\IESTIGATION
E.O WASIE MII\IMIZAIION AT IHIOKOL
9.0 IMPLEIVIEDITATION OF INTMIM MF"AST'RES
FIGURE 2.L
FIGURE 2.2
FIGI]RE 2.3
FIGURE 2.4
FIGURE 2.5
FIGURE 2.6
FIGURE 3.1
FIGURE 3.2
FIGURE 3.3
FIGURE 6. 1
FIGURE 6.2
FIGURE 6.3
FIGURE 6.4
FIGURE 6.5
FIGT]RES
Ttriokol Plant Genemal Area Location
Ttriokol Plant Property Boundaries and Adjacent Property Ov,mers
Itdanufacturing Area Site Plan
High Performance Propellant Dwelopment Alea Site Plan
Test Area Site Plan
Air Force Plant 78 Site Plan
Regional Potentiometic Surface lvlap
Well Location and Potentiometric Surface lvlap
Ground Water Flow Net lvlap
Water Quality Trends in Springs
Spring I-ocations and Total Dissolved Solids
Total Dissolved Solids and pH of Monitor Wells
Potential Human and Livestock Receptors
Blue Creek Water Quatity
TABLES
TABLE 3.1 Summary of Aquifer Test Analyses - A, B, and C Series Wells
TABLE 3.2 Summary of Aquifer Test Analyses - E Series Wells
TABLE 6.1 Average Annual Temperatures and Precipiation
TABLE 6.2 Blue Creek Beneficial Use Classifrcation
TABLE 6.3 Common Plant Species
TABLE 6.4 Bird Species Observed
TABLE 6.5 lvlammals Observed or Expected
TABLE 6.6 Summary of Fate of Contaminants in Abiotic Media
TABLE 6.7 Average Values of Environmental Parameters in Estimating Volatilization
Fluxes from Springs
TABLE 6.8 Volatization Rate ConsAnts of Contaminant From Springs
TABLE 6.9 lvlaximum Exlnsure Levels Proposed for Contaminants in SurfaceWaters
TABLE 6.10 Summary of Release Mechanisms and Flux Rates for Springs
TABLE 6.11 Summary of Potential ARAR's
TABLE 6.12 EPA Healft Advisories for 1,1,1-TCA
.,o
APPENDICES
APPENDD( A Monitor \Mell Survey Locations urd Completion Diagrams
APPEI{DD( B Solid Waste lvlanagement Unit Summary Tables
APPENDD( C Solid Waste Itfanagement Unit hcation ]rIaps
APPENDX D Product and Waste Spills
APPEMD( E Relevant Environmenal Documents and Studies Prepard for Ttriokol
1.0
2.0
2.1
II\ITRODUCIION
fire objective of Task I of Thiokol's RCRA Facility Investigation GFD will be
8o present a deAiled description of the cutrent conditions at the Norttrern Utah
plantsite.
FACILMY BACKGROUI\D
Thiokol's Northern Utatr based Operations are located in Box Elder County,
Ud, approximately ttrirty miles northwest of Brigham City. Access to Thiokol
includes Interstate 15 from the north or south, Interstate 84 from the West and
then Utah State Highway 83 to the plantsite. T\e 19,378 acre plantsite is remote
from any major population center and is also reasonably isolated from farms and
ranches located at varying distances from the facility boundaries.
The Thiokol facility comprises four m{or areas wherc manufacturing and testing
activities take place. These areas are designated as the Administration and
lvlanufacturing Area, the High-Performance Propellant Development Area @lant
rrD, Test ArEa, and Air Force Plant 78. Ite general location of the plantsite is
shown in Figure 2.1, md the plant boundaries are delineated and adjacent land
owners shown in Figure 2.2. The four major areas arc shown in Figures 2.3,
2.4,2.5, and 2.6.
Thiokol Corp. owns and operates all of the areas with the exception of Air Force
Plant 78 which is owned by the Unitcd States Air Force. Plant 78 is operated by
Thiokol Corp. under a government contract.
From thebeginning of operations in 1956 to thepresent time, plant activities have
encompassed a wide mnge of programs requiring the production of solid rocket
propellants, rocket motor Bfug, military flareproduction, and indusfial support
necessary to achieve each program's objectives. Solid rocket motrors
manufactured at the plant vary from motors containing 7-9 pounds of propellant
to 1,100,000 pounds. Programs have included Space Shuttle SRIU, Peacekeeper,
Trident, SRAI\{, Harm, Genie, Minuteman, Poseidon, and production of ignitors
for passive restraint systems for automobiles.
ADMIMSTRATION AND NIANI]FACTI]RING AREA
The Administration and Manufacturing Area consists of laboratory, production,
and testing facilities. This site also includes burning areas designated as I-10 and
M-136, for sensitive, high energy waste.
2.2
2.3
2.4
Iaboratory facilities are involved in propellant research, prooEss dwelqlment,
materials dwelqlment, nondestnrctive and destructive Bfug, standards
measurement, X-ray facilities and applied physics research.
Production, mixing and casting facilities comprise the largest area and involve the
greatest number of buildings. The activities conducted in the production facilities
include emply rocket motor chamber preparation, prqrellant ingredient
preparation and handling, propellant mixing, case bonding, motor casting, motor
curing, mold assembly'disassembly, propellant Brinding, storage, final assembly,
and shipment.
Automation, robotics, and remote controls are used where practical, especially
in ingredient preparation and propellant mixing. Closed ingredient handling
systems are used in all possible applications to prevent conamination of the
processes, products, and environment.
HIGH PERFORIVIANCE PROPELLANT DEVELOPMENT AREA (PLAIYT Itr)
Plant Itr conains facilities for the preparation of development prqrcllants. Therc
qrerations include ingredient preparation, mixing, and pilot plant operations. It
also conains a burning area designated as M-225, for Nitroglycerin (NG), test
and development propellant wastes. Gas generate conaining Sodium Azide for
the automobile air bags produced by Morton International is also destroyed in this
arca.
TEST AREA
The Test Area occupies the south west area of the plant and includes test firing
bays. fire facilities here include horizontal and vertical test fuing bays, where
solid rocket motors, such as the Space Shuttle's, are secured in place and fired
!o their maximum thnrst to test the operation and performance of that particular
type of motor. Many different t)"es of computer aided testing, sensing and
recording equipment are included in these firing bays.
AIR FORCE PI-ANT 78
Air Force Plant 78 comprises a large number of major buildings that are used for
the manufacture of large solid propellant rocket motors, such as the Tlident and
Peacekeeper motors. Major p(rcess steps conducted at Plant 78 are similar to
those at the Administration and lvlanufacturing Area and include empty chamber
preparation, propellant ingredient preparation, testing and handling, propellant
3.1
3.0
3.2
mixing, propellant casting, grinding and curing, find assembly, and
WSETTING
This section describes the land use, climate, topography and drainage, regional
geology, local site shatigraphy, and hydrologic conditions that prevail within the
region encompassing the Thiokol property.
LAND USE
Thiokol Corlnration consists of four phts, on alproximately 30 square miles,
near the center of Box Elder County. A brief discussion of the operations
conducted at these facilities is provided in the prwious sections.
Tnning to the north, west, $)uth and farther east of the facility is mostly
agricultural. Much of the land is not suited for any purpose whatsoever, except,
possibly, some marginal grazing, because of the salinity of the land and
groundwater near the Ttriokol facility. Ttris is particularly evident to the south,
southwest, and southeast.
CLIMA'TE
The climate in the vicinity of firiokol is semi-arid with moderately cold to cold
winters and hot summe$. The nearby mountain ranges and the Great Salt kke
to the south exert a modifying influence upon the local climate. Regional
precipiation is generally grcater in winter and spring than in summer and fall and
greater near the mountain peaks of the Wasatch and neighboring ranges than in
the intervening Blue Creek Valley in which the majority of the Thiokol qrerations
is located. Howwer, in the valley, qpring precipitation generally exceeds ttnt of
the winter months. Due to its high satinity the Great Salt kke doe.s not frezn
and thus, moderates valley temperatures somewhat.
The average annual temperature in the thiokol area is in the 45 to 50 degree
range, with generally hot, dry summers. Relative humidity averages betrreen 20
and 30 percent during summer afternoons. Nights are ustrally cool, but daytime
maximums occasionally exceed 100 degrees F. orr clear nights, cold air usually
drains from the slopes of the adjacent ranges and accumulates on thevalley floor,
while the foothills and bench anreas, such as at Thiokol, remain relatively wann.
The average daily temperature ranges from about 11 to 32 degrees F in lanuary
and from about 54 to 9l degrees F in IuIy.
3
3.3
3.4
The average precipitation at the Thiokol facility is 14.88 inches per year.
According to interpreted weather data for the Thiokol facility, the 25 year storm
with a 24 hour duration would result n 2.4 inches of precipiation.
On an annual basis, the winds for the valley tend to prevail from the north during
the eadier morning hours and south to southeast averaging about l0 mph during
the afternoon.
TOPOGRAPHY AND DRAINAGE
fire topography of the site rises gently from an elerration of about 4250 fetabove
mean sea lerrel in the southeastern @rner of the site to approximately 6050 feet
along the eastern border of the site. The surface of the site is generally covered
by a thin veneer of residual and colluvial soils.
fire mafor stream draining the site is Blue Creek, a perennial stream whose
channel has cut through older sheam-channel deposits and lacusrine alluvium
along its course. The site rests upon the west flank of the Blue Spring Hills.
The area of the site was rcworked by the wave action of Iake Bonneville during
the late Pleistocene, eroding many of the pre.existing surficid features at the site
or mantling them with lake sediments. As a result of reworking by kke
Bonneville, continued slope wash, and other erosional processes, the site area is
currently cbarzictrrizrd by gentle topography that slopes out from the mountain
front toward the center of the valley.
Sand and gravel has been deposited in localized areas by a combination of lake
and stream prooesses. These deposits have been excavated in cerain areas of the
site for use as structural fill. As a result, some eqnsures of the once-buried
stratigraphic units have been created.
GEOLOGY
The Thiokol facility is located in the Southern Blue Creek Valley, northwest of
the Salt r ake Valley, which is the eastern most stnrctural valley of the Basin and
Range physiographic province, which includes parts of Utatl, Idaho, Nevada,
Arizona, and New Mexico. The Basin and Range province consists of a number
of north-south aligned mountain ranges and valleys bounded by high-angle normal
faults. The Blue Creek Valley, in which Thiokol is located, is bounded on the
east and west by the Blue Springs Hills and the Engineer and Promontory
Mounain ranges, respectively. Movement along the faults has displaced the
mountains upward relative to the adjacent vatley. Likewirc, ttre mountains
b immediately west of Thiokol are bounded on their eastern margin by one or morc
faults which are partly buried by recent deposits.
Bedrock, composed of Middle Paleozoic shale, sandstone and limestone is
exlnsed in the ranges adjacent to the site. The bdrock is highly fractured with
some folding.
During the Mississippian and Permian Periods, marine sediments consisting of
sand, chy, and calcareous detritus were deposited in shallow marine
environments. In the late Cretaceous Period, compressional forces from the west
resulted in folding and thnrst faulting in conjunction with uplift of the region into
mountain ranges. Extensive jointing and fracturing of the bedrock were caused
by this folding and faulting episode. Tensional stresses in the early to middle
Tertiary Period resulted in north-south trending normal faults that formed a series
of high linear mountain ranges with intervening basins which received sediment
from adjacent highlands. This activity was associated with volcanism and ancient
lake deposition.
In the late fertiary Period, a series of geologic units tentatively identified as the
Salt Irke Group were formed from deposition of sediments in large lakes which
developed within the valleys. These lake deposits are composed primarily of silts
and clays with minor amounts of sand and gravel and are characterized by low
to moderate permeabilities; extensive deposi$ of volcanic ash are also present in
the Salt r ake Group. The alluvial fan deposits werc overlalryed by more recent
lalce sediments of Pleistocene Iake Bonneville, the predecessor to the present
Great Salt Iake. I:ke Bonneville covered much of western Utah and parts of
Idaho and Nevada between about 23,W and 12,000 years 4go. Deposits
associated with the lake consist of lake bed and alluvial materials reworked by
lake bottom and shoreline processes. Iake Bonnerrille sediments thicken
southward.
The most recent sedimentary deposits consist of sueam alluvium and mud and
debris flows. The stream alluvium consist primarily of silty and clayey sand and
gravel. The mud and de.bris flow deposits are characterized by a broad gradation
of sediments from clay-size fines to boulders as large as 3 feet in diameter.
SITE STRATIGRAPHY
The stratigraphic units present at the site can be subdivided into two distinct
groups, Cenozoic and Pdeozoic. The ulpermost group of stratigraphic units
consists of unconsolidated to moderately-consolidated deposits of Tertiary and
Quaternary age. These deposits include moderately to poorly consolidated
Tertiary-age volcanic materials, tentatively identified as part of the Salt kke
3.5
3.6
3.6. 1
Group. Also includd in this group are unconsolidated Quaternary alluvial and
lacusffine deposits and recent alluvium.
fire early Quaternary dluvial materials at the site are composed of poorly-sorted
gravel and cobbles as well as occasional targe boulders in a sitty-sand matrix.
Underlying the deposits of the Salt Id<e Group are Paleozoic limestones, shales
and sandstones. These older rocks are exposed in the mountains west and east
of the site.
Significant amounts of lacustrine sediments were deposited in the Blue Springs
Vdley during all Pleistocene lake cycles. These deposits consist of thick
sequenoes of clay and silt in the center of the valley grading into veneers of sand
and gravel intercalated with clay and silt layers along the valley margins.
HYDROLOGY
The following discussion of the hydrology beneath the Thiokol facility is based
on information from the re,ports Second Interim Report. M-136 Burn Area.
Groundwaer Monitoring Progran, Irctalluion Restorotion Progron Phase II.
Co\frnrution/Owlificaion Stagg 2, ild RCF,d Compliance Plan These
documents are large and have been previously submitted to the Utah Bureau of
Solid and Ilazardous Waste.
Regional
Ground water in Blue Creek Valley occurs under unconfined and confined
conditions. These two conditions exist in fractured and faulted bedrock, lake
clays and gravels, unconsolidated alluvium, gravel and sandy deposits.
Precipitation, surface water infiluation, and plant discharges that infiltrate into
sediments, may migrate slowly, vertically, and horizonally to form perched water
tables above the 50 - 150 foot depth of the regional water z.one. The perched
ground water may errentually migrate to the deeper regional system. The regional
system mnges from 50 - 450 feet in depth depending on the topographical
location. Blue Creek may recharge shallow aquifers in the center of the Blue
Creek Valley. The direction of movement wittrin the faulted and fractured
bedrock will be controlled by the connection of faults and fracturcs. Figure 3.1
shows thepotentiometric surface map of Blue Creek Valley in 1970. Regionally,
the ground water flow trend is from north to south.
Manufacturing Area
The geology at Thiokol is complex, and the subsurface hydrology reflecs this.
3.6.2
3.6,2.t
T$o general hydrogeologic units are recognized wittrin the site area; the valley-
fill and bedrock. The environments of deposition and digenesis of each of these
units results in significant differences in the ability to store and transmit ground
water. Porosity and its influence on permeability is the most significant
difference between the valley-fill and bedrock units. the porosity of the valley-
fill is generally interstitial porosity, while the bedrock porosity is generally
secondary (fractures).
Within the valley-fiI1, ground water occun under confined and unconfined
conditions. fire valley-fill sediments consist of sands and gravels inteftedded
with silts and clays. Generally, the coarser materials are found along the margins
of the valley and as basal sediments above the bedrock. The silts and clays act
as confining units above the coarser materials. Some local perched zones are
found within the silt and clay deposits. Wittrin consolidated sediments, ground
water occurs in fault zones, fracture zones, and solution cavities in the
limestones. The ground water occurs under perched, confined, and unconfined
conditions.
Perched Water System
The perched water system at M-136 is comprised of three known perched water
zones. The uppermost water unit, Zone A, is monitored by wells D-1, A-2, A-
10, B-9, and B-10; the middle water unit, Zone B, is monitored by A-3; and the
lowest unit, Zone C, is monitorcd by well C-4. Installation of well C-9
interconnected zones A and B causing a drop in the water level of B to equal that
of Tnne A, and allowing migration of contaminates. These two zones are now
essentially equivalent. The perched water zones at M-136 are separated from the
regional water zone by a fault which acts as an aquitard. The static water levels
of the perched zones are between 175 and 280 feet above the static water level
of the regiond mne. The perched water zones are found within fractured areas
of medium bedded to massive limestones and quartzites. The zones appear tro be
subhorizontal features, stacked one above the other, and separated verticatly by
ttrin-bedded calcareous siltstones. While the aquitards which separate zones
appear to be at least partially bedding plane controlled, the water zones are
primarily controlled by fracturcs. If a stratum is not foactured in a horizon where
a ground water zone might be expected, water will not be encountered. Ttris is
illustrated in well C-9, where a water zone was drilled at an elevation of 4547
feet, but in C-4, located 12 fer:t northwest of C-9, the strata are unfractured at
this elevation, and the water zone was not observed.
The water zones are strongly controlled by faults. Within the perched system,
at least truo and perhaps four or more faults affect ground water. Based upon the
occurrenoe of a carbonaceous shale and quartzite unit in wells A-3 and C4, and
topographic relief of the bedrock, two or possibly three east-west faults transect
3,6.2.2
3.6.2.3
the area.
Based upon topography of the bedrock and minor variations of the static water
level of water zone A, two north-south fautts are inferred in the area. In
addition, pump test data from wells A-3, C-4, and C-9 indicate the presence of
hydrologic barriers which may atso indicate the presence of these faults.
Perched Ground Water Zones
Wells D-L, A-2, A-10, B-9, B-10, and C-9 are completed wittrin the water zoneA. Tnne A appeans to be bounded on the west by the fault adjacent to the
regional ground water system, and on the north by a fault between D-1 and A-3.
It extends on the south to at least well 810. Tlrc zone extends east of A-10, but
ground water movement may be impeded by a small fault between D-l utd A-2.
This aquitard may be responsible for a significant difference in the static water
level between D-1 and A-2. This difference was approximately nine feet in 1987,
but has diminished to 1.86 feet by December 1991.
TnneB
Water zone B is confined and water rose approximately 200 feet when it was
drilled in well C-4. Itextends north of A-3, south of C-9, and probably eastward
of A-10. It probably does not extend southward to the next canyon, because here
the stream channel intersects the sAtic water lerrel and might drain the zxtne.
Well A-3 monitors the zone. Well C-4 encounterpd the zone, but this was sealed
off with casing.
Tnne C
The extent of zone C is unknown. It is monitored only by well C.4 and is found
between 4477 and 4290 fer;t elerration (within the same interval as the regiond
system to the west). This zone exhibits high head prcssurcs and the water column
rose 166 feet in well C-4.
Well lnstallation in Perched Zones
Well D-l was insalled in October 1985. Ground water zone A wan enoountered
at elevation 4560 feet in a fractued quartzite and the water lerrel rose to 4568
feet.
Well A-2 was drilled in lvlarch and April 1988, and hit zone A at 4555 feet. The
water level rose to 4559 feet (nine feet below the level in D-1).
Well A-10 was installed in lrlay 1988. Tnne A was found at elerration 4548 and
3.6.2.4
rose to 4559 feet.
Well A-3 was insalled in March and April 1988. 7nrc A was not found in well
A-3, and zone B was encountered at elerration 45il n a fractured quartzite. Ttris
quartzite is different from the quartzite observed in D-l and is distinguished by
the presence of a very dark-gray carbonaceous shale above it. The water rose 77
feet to elevation 4il1.
Vlells C-9 and C-4 were dri[ed in August 1988. At C-9, a water zone was
drilled at 4568 feet, but very little water was produced and drilling continued to
4547 fet. At this elevation, zone A produced over 10 gpm of water and the
water lwel quickly rose to 4555 feet. Well C-9 was drilled to a total depth of
elevation 4506 feet.
Wells B-9 and B-10 were drilled in December 1989 and lanuary 1990. Static
water level of zone A in these wells is elevation 4555.9 and 4554.5 feet.
Part of the purpose for drilling C-9 was to try to drill to the elevation of the
regional water zone @elow 4300 feet). When this was not possible with C-9, an
attempt was made with the second well, C-4. Although C-4 is only 12 feet
northwest of C-9, the borchole logs do not correlate well and it appears that a
small fault may exist between the wells. At 4547 feet, where zone A was
expected in C-4, the rocls arp massive and the borehole produced no free water.
At elevation 4530, a large fracture was encountered and circulation and cuttings
were lost to elerration 4568 of well C-9. firis filled well C-9 below this elerration
with cuttings from C-4. Water zone B was drilled at M37 feet and the water
column quickly rose l99 feet to elevation 4636. This zone was sealed to the
surface with an eight inch stel casing and bentonite. Tllne C was drilled at
elevation 4381 and it rose to M79 feet. This zpne was sealed to the surface with
six inch steel casing and bentonite. Trlne C was again encountered at elevation
4310 feet and the well was drilled to a total depttr at elevation 4290 ferlt. The
regional water zone was not encountered in well C-4 and is not believed to be
present east of the burning grounds.
Regional Watpr System
The regional water system is found west of the perched water system. It does not
appear to extend eastward beneath the perched zones.
Installation of well C-4 involved drilling through three perched water zones to
determine if regional water exists east of the M-136 Burning Ground facility.
Instead of regional water, well C4 encountered a highly pressured perched zone
within the elevation interval expected to be occupied by the regional zone
(elevation 4280 through 4350 feeQ.
A perched water zone within the expected regional water intervd was also
observed in well T00z,located 8000 feet south-southeast of C-4. Well TCC2
is a steel-cased eight-inch diameter borehole constnrcted in 1956 as an exploraory
plant process-water well. The static water level in TCC2 is approximately 4235
feet, which is 40 feet below the regional static level in this area. Ilre well was
drilled M2fer;t deep (approximate elerration 4085 feeQ and the regional zone was
not encounterpd. The water quality is tpical of perched zones obserrred east of
the burning ground (312 ppm salinity), and higher $Elity than generally observd
for regional water (1000-8000 me/l TDS).
Piezometer M139-Bl was drilled during the summer of 1988 as part of a UBSIfW
supervised RCRA investigation of heavy metal contamination at M-139
photographic waste site. Well FlO was installed in December 1989 and January
1990 as part of the M-136 drilling program. These wells are located between
wells C4 and TCC2. As expected, both of these wells encountered perched
water zones. East of the plant facility, in areas of recharge, regional water
appears to have been displaced by confined perched water zones.
Ground Water Flow Directions3.6,2.5
3.6.2.6
Static water levels are recorded
Potentiometric surface is illustrated
illustrated on Figure 3.3. Ttese
December 1991.
semi-annually from all monitoring wells.
on Figure 3.2 and ground water flow net is
are based upon water levels compiled in
Regional Ground Water Flow Directions
The major features of the regional ground water system consist of a mound
between wells D-3 and D4, and two prominent channels or troughs to the east.
The first channel extends from well C-2 southward between wells C-3 and C-1.
This channel clearly parallels the structural fends of the basin and range faulting.
The second channel is found east of well A4. This channel probably also
parallels basin and range faulting, although existing daa is inconclusive. Ttris
second channel exhibits steep gradients (0.45% between wells A-5 and A-4) and
is probably the major conduit for ground water moving from M-136 Burning
Areas. The two channels merge south of C-3. Ground water appears to pool
beneath Blue Springs Valley behind the hydrogeologic constriction at Engineering
Mountain and flow east and then southward around the constriction through
fractures, solution channels, and fault breccia in the adjacent carbonate rocks.
This ground water flow pattern has not varied significantly during the time perid
that Thiokol Corporation has monitored static water levels.
The mound at D-3 and D4 may result from the past use of the M-136 facilities,
10
3.6.2.7
3.6,2.8
3.6.2.9
but more likely because it is located at a transition between areas of higher
transmissivity up the canyon and lower transmissivities wittrin the valley
alluvium. Although ground water moves radially from the mound, most of the
ground water is carried east and south through the channel at0-2 and D-6. The
wastewater diqposal qrcrations at M-136 ceased operation in November 1988, but
the mound has not significantly diminished since that time.
Perched Ground Water Flow Directions
The rapidly declining water level of well D-l relative to A-2 and A-10 is
evidence for a possible artificial souroe of ground water at D-1. A possible
recharge source was previous waste management practices at the M-136 burning
areas. Because this water percolation source has ceased, natural recharge areas
from the east are expected to exert greater influence on ground water flow
directions in the future. As in the regional system, the perched water (Zone A)
appears to move eastward, and then to the south.
Tlansmissivity, Conductivity and Storativity Estimates
Pump test data has been evaluated for 23 A, B, and C series wells, to examine
aquitard leakage, unconfined aquifer conditions, fracture flow and dual porosity
behavior, aquifer boundaries, well borc storage, and skin factor. Table 3.1 is a
summary of the A, B, and C series wells, and Table 3.2 is a summary for the E
series wells for the tpe of analysis used for each well and the transmissivity,
conductivity and storativity estimates.
Vertical Ground Water Velocity
Well B-2 is installed as nested piezometers to evaluate vertical ground water
velocities. The well consists of three, two-inch, 316 sainless steel and PVC
piezometers. Each piezometer is completed progressively deeper into the
saturated zone. The screened intervals arc approximately placed between
0-10, 24-34, and 48-58 feet below water level. Static water level variation
between these wells is 0.01 feet. Construction practices for installation of a2ffi
foot long, trno-inch pipe in an eight-inch diameter borehole cannot prevent 0.01
feet of variation in prpe length, due to curvature or spiral of the pipe. As a
result, it appears that ground water flow at the site is essentially horizontal.
West of the Administration area, wells B-6, E-7, and F-5 have been installed at
127 f*t,228 fet, and 318 feet below the surface respectively. Differences in
static water levels between these wells are also very small, indicating essentially
no vertical flow in this area.
North of the Administration area, wells E-l and F-2 were also completed at
11
3.6.3
different levels. Monitor well E-l is a 4 inch completion screened just below the
static water level (105- 125 feet). Well F-2 is a nested peiezometer similar to
well B2 described above. F-2 is screened between 14G'150 fet,2M-214 feet,
and 31G320 f*t. The static water level in E-l and the two upper F-2 well
screens is approximately the same, indicating no vertical flow in the upper 115
feet of saturated ?nne. However, the satic water level of the lower F-2 well is
approximately 10 feet above the upper three wells. This indicates a steep upward
vertical flow gradient from below 310 feet to above 150 feet depth. The lower
zone is a confined aquifer with a leaky uplrer confining layer. This upward flow
gradient would be expected to act as a confining barrier to contamination and
impede downward vertical contaminant flow in this area.
A second area of known upward vertical flow exists south of the Administration
area where ground water flows at springs and flowing wells as surface waters
feeding Blue Creek.
Plant III
The movement and location of ground water beneath the area known as the High
Performance Propellant Development Area (see Figure 2.4) has not been well
defined. T\vo wells, TCC3 and TCC3A, were drilled in this area in 1956 and
1962. Deailed discussion on these two wells can be found rn RCF"/ Compliance
Planprepatd for Thiokol by Underground Resource Management, Inc. in August
1985. Well TCC3 was drilled 350 feet below ground surface and encountered
ground water at approximately 300 and320 feet and static water lerrels measured
n 1962 showed the water to be at an elevation of 4260 feet. This well was later
abandoned and has not been used. IVell TCC3A is currently being used to supply
process water to buildings in the High Performance Propellant Dwelopment
Area. When drilled this well encountered water at a depth of 317 feet and at 395
feet. The surface elevation of the ground water in 1962 was 285 feet.
TWo more wells have been drilled near the M-225 burning grounds. One of these
wells was drilled to a depth of 200 feet, but could not be completed because the
fractures in the limestone formations prohibited further drilling. A second well
was completed and ground water encountered at 618 feet. Ground water appears
to flow south and southeast toward the Great Sdt kke. A report of the
investigations at M-225 will be submittd to ttre Utah DSIIW during Summer
1993.
3.6.4
3.6.5
4.0
4.L
Air Force Plant 78
Ttre ground water movement and direction has been studied at Air Force Plant 78
by the Air Force Insallation Restoration Program (IRP). The IRP program has
installed eight monitoring wells on Air Force Plant 78 at various sotd waste
nranagement units. Deails on these well insallations can be found rnlrctallaion
Resnraion Progran Phase II CortfintwtionlOwlificaion Stage 2 prepared by
Environmental Science and Engineering, Inc. in August 1991. orr plant 78 there
is a westerly comlrcnent of flow. The local direction of ground water flow on
Plant 78 is generally west from the Blue Spring Hills to Blue Creek and then
south along the Blue Creek Valley toward the Great Sdt kke.
Test Area
The ground water is currently being investigated in aleas north and east of Test
Area as part of the M-136 LTTA ground water plume studies. Ground water
flow in Test Area appears to move from north to south, with the piezometric
gradient averaging approximately five feet per mile. The ground water surface
elevation is estimated at 426o fet. Suppoting documents will be submitted to
the Utah DEQ when the studies are completed.
WELL INSTALLAIIONS
Thiokol has insalled monitoring wells at various locations throughout its
Northern Uah facilities to investigate ground water conditions. The discussion
which follows describes the drilling activities which have hken place at the
individual areas of the plant. The completion diagrams for the drilled wells are
included in Section TVo of this report.
MANTJFACTTJRING AREA
In Fall 1985, Engineering Sciences was contracted to install six grcund water
monitoring wells @ Series) to detect if contamination is present in the ground
water beneath the M-136 Burning Grounds. Engineering Science submitted a
report alled Prelimirury Geolrydrologic Evalwtion which contains the data
collected during the insallation of these monitoring wells. The Engineering
Science report is located in the document filed Ground Waer Detection Progran
M-1;!5., dated 15 May 1986.
The information collected from the installation of the six detection wells indicated
13
the subsurface geology to be very complex. Analysis of the grcund water
samples showed the water to have a trace solvent concentration in alt six ground
water monitoring wells. Itwas deterrnined that additional monitoring wells would
need to be insalled to fully understand the subsurface conditions at M-136.
In 1987, ten additional ground water monitoring wells (designated A-1 through
A-10) were installed. Before the ten ground water monitoring wells werc
installed, a geophysical survey was performed to give more detail to the
subsurface geology. Deails of the monitoring wells are reported ti M-136
Burning Area Growd Waer Monitoring Progran Firct Interim Report, submitted
Febnrary 1988, and hereafter referred to simply as Ftrct Intertm REort.
In 1988, nine monitoring wells, C-l through C-9, were insalled to assess the
extent of conamination, rtrd dso to characterize the subsurface geology and
hydrology. These are described in an Addenfi,an to the Ftrct Irueim Report,
submitted May, 1989.
In 1989, ten monitor wells, B-1 through B-10, were insalled to assess the extent
of contamination of ground water south and south-southwest of the M-136
facility. These are deailed rn M-li6 Burning Area Gruund Waer Monitoring
Progran Second Inteim ReWn, fvfay 1990; 1991 Interim Report, April 1991;
1992 Interim Repon, Febnrary 1992.
All nB' monitoring wells were installed with dedicated Gnrndfos stainless steel
submersible purge pumps, and Geogard teflon and stainless steel, bladder t1pe,
sampling pumps.
Ten additional monitor wells, E-l through E-10 were installed in 1990. The
drilling was conducted by Zimmerman Well Service of Salt Lal<e City, Utah, and
supervised by Chen Northern, Inc., of Salt Id<e City, Utah.
The ten "En series monitoring wells were installed with dedicated Gnrndfos
stainless steel submersible purge pumps, and Well Wizard teflon and sainless
steel, bladder t1pe, sampling pumps.
In 1988, Morton lhiokol installed 2 monitoring wells near buildings M-39, and
M-114. These buildings are x-ray facilities which up until 1980, discharged
photographic process waste water into adjacent disposal areas. The wells were
installed to determine the depth to the uppermost aquifer under each site and to
obtain a geologic desctiption of all soil horizons encountered.
A description of the photographic waste site well installations is deailed in the
report Cteolrydrologic Investigation Plntographic Waste Sites, October 1988.
L4
4.2
4.3
4.4
HIGH PERFORMANCE PROPELLANT DE\IELOPMENT AREA (PLANT IIr)
T\ryo wells, TCC3 and TCC3A, were driUed at Plant m in 1956 and 1962.
Well TCC3 was drilld 350 feet below ground surface and encountered ground
water at alryroximately 300 and 320 fer,t and static water lerrels measured n 1962
showed the water to be at an elevation of 426o f*t. Ttris well was later
abandoned and has not been used. Well TCC3A is currently being used to supply
prooess water to buildings in the High Performance Propellant Dwelqrment
Area. When drilled this well encountered water at a depth of 317 feet and at 395
feet. The surface elerration of the ground water n 1962 was 285 feet. Detailed
discussion on these two wells can be found rn RCM Compliance Plan prepared
for Thiokol by Underground Resource Management, Inc. in August 1985.
TVo more wells havebeen drilled near the M-225 burning grounds. One of these
wells was drilled to a depth of 200 feet, but could not be completed because the
fractures in the limestone formations prohibited further drilling. A second well
was completed and ground water encountered at 618 feet. Details of the ground
water at this site will be submitted to the utatr DsIIw in early summetr, 1993.
TEST AREA
In 1956, a well designated as TCCT was drilled within the Test Area facility.
The well depth was advanced to approximately 170 feet ino broken limestone but
did not encounter ground water. The well was abandoned and no additional
drilling has occurred with this area.
A deEiled discussion on this well can be found n RCF/ Conpliance Plan
prepared for Thiokol by Underground Resource I\rlanagement, Inc. in August
1985, and submitted to the Bureau of Solid and Ilazardous Waste in 1985.
AIR FORCE PLANT 78
Nine shallow groundwater monitoring wells @-1 through P-9) havebeen installed
at Plant 78 inconjunction with the Insallation Restoration Program for the United
States Air Force. All monitoring wells were completed in perched water table
zones wittrin lake clays and gravels. The wells were installed in an 8-inch
borehole and consisted of 4-inch inside diameter Schedule 40 PVC.
In 1988, Morton Thiokol insalled 2 monitoring wells near buildings M-508 and
M-636. These buildings are x-ray facilities which up until 1980, discharged
photographic prccess waste water into adjacent disposal arcas. The wells were
15
b insalled to determine the depth to the uppermost aquifer under each site and to
obain a geologic desctiption of all soil horizons encountered.
A description of the photographic waste site well insalations is detailed in the
rqnrt Geolrydrologic Invesfigaion Photographic Waste Sites, October 1988.
NATI'RE AI\D ETTEI|IT OF CONTA]VIINATION
Routine sampling of theground water moniOring wells at theTtriokol facility has
shown probable releases to the ground water from past practices associated with
the M-136 Burning Grounds. A detailed summary of the extent and nature of this
contamination is found in the M-1i6 Burning Area Gromd Water Monitoring
Progran annud interim reports.
5.0
Delineation of the contamination
that is monitoring the plume is
document.
plume is on-going. The groundwater system
described in the Hydrology sections of this
5.1 POTENTIAL POLLUTANT MIGRATION PATIIWAYS
Classes of wastes that are present and handled at the firiokol facility include
metals, solvents, and reactive wastes.
Metal wastes are generated primarily from: (1) the washing of floors and walls
in explosive areas which handle product metal materials @rimarily aluminum) as
propellant ingredients, and (2) from photographic laboratories at ttre facility which
generate wastewater contaminated with metals (primarily silver).
Solvent wastes are generated during various processes but mainly from the
cleaning of parts. 1,1,1- Trichloroethane (methyl chloroform) is currently ttre
most widely used solvent at Thiokol.
Reactive wastes include propellant and explosive materials which have been
scrapped or other materials which have been contaminated with propellant or
explosives. Reactive materials used at Ttriokol include nitroglycerin (NG),
ammonium perchlorate (AP), cyclotehamethyleneteetraniramine (HlvOQ and a
variety of minor and/or experimental explosives.
Potential pollutant migration pathways from many of the solid waste management
units can include soil contamination, releases to groundwater, and air emissions.
Any relearc from a solid waste management unit would depend on the presence
16
and concentration of conaminants in aqueous wastes dircharged to the unit, the
relative evalnration and infiltration rates of aqueous wastes in the unit, the
characteristics of the soils underlying the unit, and tpe of unit which received the
waste.
A major source of pollution was eliminat€d with the cessation in usage of the
unlined M-136 liquid surface impoundments on November 7, 1988, which had
received wastewaters contaminated with explosives and solvents since 1962. I,ow
permeable caps were constnrcted over the impoundment areas in 1991 to
minimize infiltration and conuol any further releases ftom the units.
Soil contamination may result from the release of wastes to the soils surrounding
and underlying the units. As aqueous wastes released from one of the units
infiltrates through or walnrates from the soil, solid particles in the waste may
remain on or near the soil surface. Organics in the waste may be absofted by
soil particles as the water passes through the soil column. This absorption
depends on the ability of the soil to bind the organics present in the discharged
water. Evaporation of water from the unit may also cause nonvolatile
contaminants to remain on the soil surface.
Groundwater contamination may result when a waste is released from a unit and
allowed to infiltrate through the soil column to the underlying aquifer. Ground
water contaminated in this manner would spread through the course of normal
groundwater flow. The contamination of ground water associated with the M-136
Burning Grounds has primarily occuned from wastewater contaminated wittr
dissolved solvent wastes moving thorough the soil column to ground water with
some adsorption of volatile organics onto the soil particles, rather than the waste
solvents being discharged into the units saturating the soils and moving to ground
water. Ttris is supported by the sampling daa indicating a falling trend in
contaminant levels. An exception to this is Pit No. ll (unit No. 8) where waste
solvents were discharged into the unit.
Air emissions can result from the volatilization of organic contaminants contained
in the aqueous waste discharge. These organics could originate from
contaminated water lyrng in the unit or from surface soil contaminated with these
comlrcunds. firis pathway is dependent on the vapor liquid equilibrium
relationship of the waste solvent in the water. Air emissions would be erpected
to occur during or immediately following water discharge or as direct rcsult of
the open burning of hazardous constituents during flashing operations. Flashing
consisted of open burning the residues in the bottom of each unit after the water
had evaporated or percolated away.
An industrial wastewater treatment plant was constnrcted by Thiokol and is now
fully operational. It has the capability of teating explosive conAminated
L7
6.0
6.L
wastewate$ generat€d by Ttriokol prior to discharge to Blue Creek following the
provisions of a Uah Pollutant Discharge Elimination System (UPDES) permit.
The hazardous wastewaters previously managed in many of the SWMUs are now
managed through this treatment system. The waste stneams arc collected in
double lined tanks or sumps and subsequently transported to ttle treatment system.
Therefore, it is expected that the risk for contaminant release from these units has
substantidly decreased.
POTENTIAL RECEPTORS
Potentialreceptors to conAminated ground water and surface waters are described
in the following sections, and includes environmental factors which contributes
or mitigates exposure.
CURRENT AND FUTURE USES OF GROI]ND WATER
Present and future use of ground water downgradient of M-136 areas is limit€d
by the natural salinity of the water. Hood $9n) reports that the total dissolved
solids in ground water east of Ttriokol Administration area is 5,100 mg/l (well
location (8-10-5) Sbab). Saline qprings occur along the south end of Blue Spring
Hills. Figure 6.1 strows the average yeady concentration of toal dissolved solids
at four of these springs during years 1982 through 1985. Shotgun Springs
averages 7,088 mEfr, Pipe Spring 6,803 mEfr, Horse Spring 10,200 mg/I, and
Fish Spring averages 7,381mg/1. These springs are used by wildlife and grazing
livestock.
South of firiokol property, within ttre Blue Creek drainage basin, there are
approximately 800 acres of irrigated agricultural land. This land is located on the
east flank of the Promontory Mountains, and essentially all the irrigation water
is derived from wells and springs upgradient from Blue Creek (Hood, f. W.,
1972). At the mudflats of the Great Salt kke, local gun clubs possess the water
surface rights to Blue Creek and have drilled ground wat€r wells for nonculinary
uses (Battelle-Columbus I:boratories, Rwised 1987).
Figure 6.2 dercribes and locates springs and pre-1985 wells on the plantsite and
on nearby surrounding areas.
Thiokol utilizes approximately one million gallons per month of water from Well
TCC 3A for nonculinary p(rcess uses. TCC wells are exploratory water wells
drilled in the late 1950's and early 1960's. Figures 6.2 and 6.3 illustrates
concenEations of total dissolved solids. No public drinking water system utilizes
1E
l
L ground water from the Blue Creek drainage basin downgradient from the Thiokol
facility.
Following reconnaissance of Blue Creek and Promontory Mountain areall, Bolke
and Price, (1972) and llood (1972) concluded that future ground watcr use in
areas down gradient of Ttriokol is limited because of the poor quality of the
ground water.
Existing Ouality of Ground Water and Other Possible Sources of Contamination
Existing Water Quatity
The ground water quatity in Blue Creek Valley is generally poor due to naturally
occurring chlorides and total dissolved solids. kvels of dissolved solids range
from 400 to over 12,000 mg/I. Figures 6.2 and 6.3 illustrates concentrations of
total dissolved solids adjacent to Thiokol including average levels of toal
dissolved solids for selected springs south of firiokol plantsite.
Quality of ground water depends ulnn the sediments which it has contacted.
Quality is quite gd in local, upgradient areas of water recharge, but degrades
rapidly as it moves from mountain to the valley axis. High lwels of total
dissolved solids in lowland areas are probably due to slow migration through
Tertiary sediments. Down gradient from the firiokol sites, quality deteriorates
rapidly as it enters the mudflats of ttre Great Salt Id(e.
Other Possible Sources of Conamination
There are several potential sour@s of conamination to ground water in the Blue
Creek Valley: disposal of domestic waste by Thiokol Corporation, Morton
International, the small town of Howell, and others, and upstream agricultural
practices, including fertilizer application and irrigation practices. Of these, only
upstream agricultural practices are likely to significantly affect quality of ground
water.
The community of Howell, Utah, five miles to the north of Thiokol, is on septic
tanks. Domestic wastes at Thiokol Corporation and adjacent Morton International
are also treated in septic tanl/drainfield systems. Industrial waste water flows
(non-hazardous) made up of boiler water, treated cooling water, floor wash water,
and some miscellaneous sources are allowed o percolate/evaporat€, and may
potentially influence groundwater. These nonhazardous flows are described in the
document Ground Water Ouality Protection Report, submitted 8o the Utah DEQ,
Division of Water Quality, l0 September 1991.
6.1.1
6.L 1. 1
6.L,L.2
19
6,L.2
6.1.3
Another potential source of contamination is the practice of irrigation in the u1ryer
portion of the valley. Fertilizers and pesticides may percolate to grroundwater,
and natural constituents may also leach from the soil.
Sampling results listed in Appendix l3.D of the Hazardous Waste Permit
Application indicate that irrigation does contribute polluting constituents to Blue
Creek, and can be expected to also affect ground water.
Potential Health Rislcs by Human Exposure
The firiokol facilities are located in a remote area of eastern Box Elder County,
Utatr. Box Elder County occupies an arca of 5,640 square miles. A 1980
population of 33,212 rqnesents a population density of about six individuals per
square mile. The population of the nrral areas of the county (less than 2,500
population) is about 14,000. Family groups living in the area of Ttriokol can be
classified into (l) ranchers and farmers, ild (2) externally employed heads of
households who commute from long distances. There are no schools, hoqpitals,
or churches in the area of the plant. There are no inhabited buildings or ranch
houses (ground water) downgradient of the plant. Adjacent ranch houses are
located on Figure 6.4.
The potential of health risk to humans is limited by lack of access and exp,osure
to waste contaminated areas and ground water. Ground water is deep, between
100 and 600 feet below grade, and use is restricted by naturally occurring
chlorides. Ground water naturally degrades downgradient from firiokol facilities,
and is not considered suihble for drinking water, and only marginally suitable for
irrigation of crops, or grazing animals (Bollc and Price, 1972; Hood, L972).
Potential Damage to Vlildlife. Crops. Vegetation. and Physical Stnrctures
Potential damage to domesticated animals, wildlife, and vegetation is limited by
lack of acoess and ex1rcsure to waste contaminated areas and ground water.
Domesticated animals @rincipally bovines) opn Er:rE in the Blue Springs Hills
and the eastern pafis of Thiokol property. They are restricted from access to
hazardous waste sites by physical barriers. Ground water is between
100 and 600 feet below grade at M-136. Downgradient ground water is rapidly
degraded by naturally occurring chlorides and not considered suitable for grazing
animals (Bolke and Price, 1972). Numerous upgradient and nonconaminated
water sources are available for livestock and wildlife including cattle troughs
provided by Thiokol. To date, there have been no documented cases of sick
20
6.L.4
6.2
6,2.t
animals from drinking ground water.
No commercial crqps (other than open rdnge) arc grown on Thiokol property.
Approximately 8fi) acres of irrigated crcps are grcwn south and west of fitiokol
on the east flank of the Promontory Mountains. Water for irrigation is obained
from Promontory Mounain sour@s. Downgradient surface and ground waters
are considered too saline for sustained agricultural uses. For example, bd
dissolved solids in a well east of Ttriokol Administrative area is 5,100 mg/l
(Ilood, L972), and Ilorse Spring has TDS levels approaching 12,000 mg/l.
Because of the great depth to ground water, native vegetation would not be
impacted by ground water contamination until it emerged and flowed as surface
waters.
There are no subsurface structures adjacent to or downgradient from open burning
areas which might be impacted by waste contaminated ground water.
Persistence and Permanence of Potential Adverse Effects
The major hazardous constituents in ground water at Thiokol consists of
trichloroethene, 1, 1, l-tichloroethane, and brealcdownproduct 1, ldichloroethene.
Minor constituents consist of acetone, l,ldichloroethane, chloroform, ild
bromomethane. Only TCE and TCA are expected to be constituents with possible
exg)sure pathways. These are described in Section 6.3.
PoTENTTAL ADVERSE EFEECTS (SIJRFACE WATERS)
Ilydrological Characteristics (,Surface Waten)
Thiokol's main plantsite is located in the northern end of the Great Salt kke
Basin. In this area, the basin is broadly bounded by the Wasatch Mountains on
the east and the Nerrada Desert on the west.
The plantsite occupies the southern end of the Blue Creek Valley. Ttris valley
lies between the Uah-Idaho border on the north and the Great Salt kke mud flats
on the south. It is also bounded by the north-south nrnning Promontory
Mountains on the west and the Blue Spring Hills and West Hills on the east. The
Blue Creek Valley drainage basin oovers approximately 220 square miles. Total
relief in the basin is about 3,000 feet. The lowestpoint is about 4,270 feet above
mean sea level on the southern end, the highest point is about 7,100 feet above
sea level in the north Promontory Mountains.
2t
6.2.2
Surface waters in the ar€a $urounding the firiokol facility include wetlands,
streams, springs, and lakes. Onsite wetlands are very limited, but include small
areas around springs and the flood plain of Blue Creek which lies at the bottom
of a 15 to 40 foot deep eroded channel. These areas arc characterized by the
sedges and grasses oommon to fresh water wetlands. fitey are ecologically
important to wildlife in the immediate area, but are of limited imlrcrtance to the
area as a whole.
Patterns of Rainfall
Currently, Thiokol has a 10 meter meteorological tower and instnrments to
measure and record air temperature, barometric pressure, relative humidity, solar
radiation, precipitation, vertical and horizonal wind speed and direction.
The climate of the Great Salt kl<e Basin is largely dominated by the Sierra
Nevada Mountains, 500 mi to the west and the Rocky Mountains, 300 mi to the
east. The Sierras and other mountain ranges forming the west coast chain modify
the character of winter storms which move across the Great Sdt Iake Basin.
Most of the moist Pacific air which brings winter precipitation to ttle basin must
move across these mountain barriers with consequent loss of moisture. This
partidly accounts for the aridity of the Salt kke Basin. The Rocky Mountains
to the east also have a marked moderating influence on the climate of the basin.
The mountains prevent the westward penetration of all but exce,ptionally strong
masses of cold continental air.
The Salt r alie Valley is frequently under the influence of the Great Basin high-
pressure area with its characteristic light winds and clear weather. The
circulation and terrain features favor the development of unusual vertical wind
stnrctures in the valleys, in which the increase of wind speed with height is much
less ttran that observed in open, well-ventilated regions. Ihis effect is most
pronounced in the summer months, when Salt I:ke City shows a nearly constant
mean wind in the first 3,000 ft above the surface. Winds aloft dicate a mean
east-southeasterly flow over the arca every month of the year.
fire firiokol plantsite is classified as semiarid, with an average annual total
precipitation of 14.88 inches at the Thiokol meteorology station. During the
winter months, the average toal snowfall amounts to 24 inches. Precipitation
tpically occurs on 95 days out of the year (includes trace precipiation). During
the year, it would be expected that 35 percent of the days would be clear, 30
percent of the days would be partly cloudy, 34 percent would be cloudy, and fog
would be expected to occur about I percent of the time. Table 6.1 provides
average annual precipitation and temperature data for the plant from 1962-1988.
22
6.2,3
Locally, temperatures in the Blue Creek Valley are strongly affected by the Great
Salt Irke. Because of its high salt content, the lake does not fuerze allowing it
to act as a heat sink through the year. firis influence tends to lengthen the
growing seialx)n, lower summer temperatures, ild rairc winter temperaturcs
(URI\{, 1985). December, fanuary, Febnrary, July, and August contribute the
least rain during the year.
Proximity of the Units to Surface Waters
A wetland habitat is formed by deltas of the Bear and lfalad Rivers, irrigation
canals, and Sulphur, Salt, and Blue Creeks. These wetlands are located
approximately 11 miles southeast of Thiokol and include the 100 square mile Bear
River Migratory Bird Refuge administered by the U. S. Fish and Wildlife Service
and Utah State and private gun club waterfowl management arealI. These
wetlands are imporant to both the Pacific and Central Migratory Flyways. In
addition to being used by waterfowl during spdng and fall migrations, the
wetlands are a nesting ground for approximately 60 of the 2fl) species of birds
recorded on the refuge.
Of the five streams which feed the wetlands described above, four of the streams,
Salt Creek, Sulphur Creek, Bear River, and lvlalad River, are well removed (5,
7, l0 and 8 miles, respectively) from the plantsite and should not be affected by
plant activities or contaminated groundwater. The fifth sEeam, Blue Creek, flows
through and along the western edge of the facility.
Blue Creek originates some 15 miles north of ThiokoUAir Force Plant 78. It is
the only perennial strearn in the Blue Creek Drainage Basin and the only sure
source of water throughout the year. The major souroe of water in Blue Creek
is Blue Springs which flows out of the ground approximately selren miles norttr
of Ttriokol. Ttris water has been impounded in a small irrigation reservoir
approximately one mile south of Blue Springs. There are several arroyos and
small catchment basins throughout the Blue Creek Basin which contribute
snowmelt during the spring, but are dry the rest of the year. These can be
considered intermittent tributaries to Blue Creek.
Blue Creek Reservoir is used an a lxluroe of irrigation water for the land above
Thiokol, Inc. Until 1975, flow in the creek was intermittent. Following the
Ivlalad earthquake in 1975, flow from the spring increased and stabilized, ild
water in the creek now flows the entire year at a rate of 4 to 60 cubic feet per
second. Much of the flow during the summer months is irrigation return flow.
Creek water is not used as it flows through and past Thiokol property. firis is
due in part because of its inaccessibility, but mostly because of its poor quality.
Discharge of Blue Creek water into the wetlands below Thiokol is regulated by
23
6.2.4
6.2.4.1
small waterfowl management imlnundments.
Several springs surface on and around the Thiokol plantsite. In most cases the
springs are very low flow and surface as water-filld holes. One group of springs
on the plantsite is used as a souroe of water for firiokol operations (Raikoad
Springs); howwer, springs and wells located serreral miles from the plant are the
source of most water used on plant. Springs which are located below plant
operations include Connors, Fish, Horse, Shotgun, and Pipe Springs. These
springs are delineated on Figure 6.2.
Few lakes exist in the region surrounding fidokol fitis is due to the nrgged
topography of the area and the desert climate. The Great Sdt kke is located
approximately 11 miles south of the plantsite and is the major collection point for
water flowing within the Great Basin region. Because of this, the lake is a
mineral sink and is many times saltier than the oceans. Only a limited number
of life forms can live in the briny water. In addition, the northern half of the
Great Salt Iake (separated from the southern portion by a railroad causeway built
in the late 1950s) which is closest to Thiokol, is fed by less fresh water than the
southern half and is somewhat saltier.
kkes in the area include portions of the Bear River Migratory Bird Refuge,
which contains several low lying dikes to impound Bear River water and the Blue
Creek Reservoir.
Current and Future Uses of Surface Waters, and Established Water Ouality
Standards
Current and Future Uses of Surface Waters
The uses of most surface waters in the Mud Flats and Bear River Migratory Bird
Retuge are deailed in the t RM (1985), NASA $9m, and Battelle-Columbus
(1987) re,ports. Uses consist primarily of irrigation upgradient of Ttiokol, and
wildlife uses downgradient.
The surface water of most imporance is Blue Creek because it is the major
source of water through the Blue Crcek Valley and because it has the highest
potential of being affected by Ttriokol activities (through surface water
contamination). According to Bolke and Price (L972), irrigation in Blue Creek
Valley began in 1904 when Blue Creek Dam was constnrcted. The project
supplies approximately 7,2N acre-feet of water for irrigation each year and was
24
6.2.4.2
6.2,5
6.2.5.1
the only souroe of irrigation water until 1962. Now two wells supply water for
300 additional asres of irrigated land.
There are no irrigation diversions for at lezst ll2 mile above Thiokol prqperty
and the water is exclusively used by wildlife and aquatic biota from that point to
the Great Salt Idie mud flats. To our knowledge, no fishery is supported in Blue
Creek below the Blue Creek Reservoir.
Established Water Quality Strndards
Water quality in the surf,ace waters surrounding Thiokol is generally poor because
of high total dissolved solids and salt concentrations. Blue Creek, in general, has
high total dissolved solids and salt concentrations. Water from Blue Creek has
been classified by the Strte of Utah. It is designated as Class 3D, protected for
water fowl, shore birds, and food chain uses, and Class 4, protected for
agricultural uses in the reach from the mud flats to Blue Creek Reservoir. A
listing of the in-stream water quality concentration limits for these classifications
is given in Table 6.2.
A comparison of the in-stream water quality standards with Blue Creek water
quality rweals several inconsistencies with the sueam classification. Before Blue
Creek reaches Thiokol property, in-stream concentrations exceed the shndards
for BOD, boron, iron, and TDS. At Rocky Point, downstream from Plant 78 and
the M-136 Burning Grounds, in-stream concentrations exceed the sandards for
the same constituentsi i.e., BOD, boron, iron, and TDS. The same is tnre for
samples collected from Blue Creek west of Lampo function. Blue Creek
"naturally' falls below its beneficial use in-stream water quatity standards
established by State classification.
Ouality of Surface Waters. and Other Sources of Contamination
Quality of Surface Waters
Surface water quality measuremens in the Blue Creek Valley arc limited. Most
of the available data have been collected by firiokol. Some Blue Creek water
quality information is also available from the State of Utah Department of Health.
Appendix 13.D of the Hazardous Waste Permit Application lists Blue Creek
water quality measurcments taken by a consulting firm during a recent Thiokol
project. Ttre samples were collected on two occasions in the Spring of 1988.
One sample was collected prior to the irrigation season while the second was
25
6.2.5.2
collected after the irrigation sealpn had commenced. Parameters listed do not
include 'volatiler' "basey'neutral,' 'pesticide,' or 'acid extractable' organic
compounds because none wert detected in the samples. Each sample was a 24-
hour, hand composited sample. Blue Creek water was collected at thee separate
locations each time. The first is labeled 'north' and is found at the State
Highway 83 culvert on the north edge of firiokol property. The second location
is labeled 'middle' and is located at Rocky Point which is the State Highway 83
culvert crossing approximately three miles south of the first. The third location
is labeled "south' and is found at the culvert crossing west of Lampo function
which leads to the Golden Spike National Historical Site west of Thiokol.
Parameters measured were those required for National Pollutant Discharge
Elimination System (IIPDES) permit application, in-stream water quality
constituents, pesticides used at Thiokol, and other selected pammeters.
Blue Creek water quality measurements have been recorded by Thiokol on a
monthly basis since l9Tl. This data is found in the Hazardous Waste Permit
Apolication Appendix 13.E. Constituents measured under this sampling program
are limited to ions associated with the production of rocket motors. The
measurements are talcen to monitor any pollution effects Ttriokol prcoesses may
have on Blue Creek.
Thiokol Corp. also samples Blue Creek in conjunction with the T PDES permit.
These samples are analyzed for parameters stated in the permit. fire samples
have been taken since the Fall of 1989 and results are available for review upon
request.
State sampling of Blue Creek is done on an infrequent basis. TVo Blue Creek
locations are sampled by the State: the first is at Blue Spring, approximately
seven miles to the north of fitiokol, and the second is at the culvert crossing west
of Iampo function. fire "02 Blue Creek at CR504 crossing of Golden Spike
Monumentn location is the southern-most sampling location of firiokol.
Thiokol has collected monthly grab samples from four springs which could be
affected by plant operations. firc springs sampled include Shotgun, Pipe, Fish,
and Horse Springs. Data is available at Thiokol for review.
Sources of ConAmination
There are several potentid souroes of conamination to surface water in the Blue
Creek Valley: Thiokol Corporation and Morton International ITPDES permits,
application of pesticides, herbicides, by Ttriokol and upstream agricultural
practices, upstream fertilizer and irrigation practices, and storm nrnoff.
26
At the present time, Thiokol Corporation and Morton International have one
IIPDES permit each for waste water discharge into Blue Creek. Ttriokol
Corporation has no information concerning the Morton International permit. The
community of Ilowell, Iftah, five miles to the north of firiokol, is on septic
tanks. Domestic wastes at Thiokol are also treated in septic tanl/drainfreld
systems or are treated in a small activated sludge waste water treatment plant and
discharged into Blue Creek under the IIPDES permit. Industrial waste water
flows (non-hazardous) made up of boiler watetr, heated cooling water, floor wash
water, and some miscellaneous sources are all contained on plant.
Thiokol has received a IIPDES permit which includes combined flows of
wastewater discharged from a state-of-the-art, hazardous wastewater treatment
facility, a sanitary treatment facility, and industrial discharges. The wastewater
treatment facility neutralizes, destroys, and/or removes explosive and organic
contaminants from the wastewater. The T PDES frmit establishes discharge
standards for the effluent. These established standards are monitored per the
frequency established by the permit, unless othenvise required by the Bureau of
Water Quality. Water discharged may slightly impact the toal-dissolved-solids
concentration in Blue Crek.
Storm water flows from Thiokol will be permitted under the IIPDES permitting
system as required by sOrm water regulations under the Clean Water Act.
An additional potential souroe of conamination to surface water within the Blue
Creek Basin is through the application of fertilizers and pesticides. Fertilizers are
applied in the upper portion of the basin to increarc crop production; however,
it is not known how much impact this practice has on Blue Creek water quality.
Fertilizer usage, rates of application, times of application, and chemical makeup
can all impact a stream. It is not known how much phosphate, nitrogen,
potassium, or iron may reach Blue Creek as a result of fertilizer usage. Ttriokol
does not use fertilizer.
Herbicides and pesticides arre used for weed and insect control on farms and on
Thiokol property in Blue Creek Valley. The effect of pesticide usage at Thiokol
has been monitorcd and found to be undetecable. Blue Creek water samples
were collected on two se,parate occasions north of the plant, at Rocky Point below
Plant 78, the burn grounds, and west of Lampo Junction. The samples were
analyzed for lvIalathion,2,4-D,2,4,I-T, Divron, Mirex, Guthion, Parathion,
Methoxychlor, Acrolein, Aldrin, Chlordane, DDD, DDE, DDT, Dieldrin,
Endosulfan, Endrin, Heptachlor, Heptachlor Epoxide, Isophorone, Dioxin, and
Toxaphene. These constituents were chosen because they are pesticides which are
included on the priority pollutant list, used at Thiokol (no resuicted pesticides are
used at Thiokol) or included on the instream water quality standards list for Blue
Creek. None of the pesticides were detected in any of the samples. Results of
27
these analyses indicate that pesticides are notpolluting Blue Creek and ttrat weed
and insect control efforts are not impacting surface water quality in Blue Creek
Valley. (Some agricultural pesticides might be affecting Blue Creek, but were
not analyzed.)
Another potential soruoe of contamination to Blue Creek is the practice of
irrigation in the upper portion of the valley. Fertilizer and pesticide usage have
been discussed; howwer, natural constituents leached from the soil as a re.sult of
irrigation are also potential polluters of Blue Creek.
Sampling results indicate that irrigation does contribute polluting constituents to
Blue Creek. Figure 6.5 is a plot of sulfate, chloride ion, and total dissolved
solids concentrations at the sampling locations described above. Ttre x-axis
indicates river miles below Blue Springs. No irrigation takes place below the
sampling locations. firc samples were collected before the irrigation season and
after the irrigation seas)n began. For the three parameters plotted, it is very
evident that concentrations increase in Blue Creek as a result of irrigation.
Effects measured later in the irrigation season, after leaching has taken place for
some time, may be less dramatic. Rainfall and nrnoff could also affect the results
shown.
Another potential source of conamination to Blue Creek is nrnoff from
undisturbed land. There is insufficient data to evaluate the effects this source
could have on Blue Creek water quality, but it is possible that temporary
increases in otal dissolved solids as a result of storms could exceed increases
noted for irrigation. Analysis of Utah Strte Health Department sample results
taken over a four-yearperiod and comparable Thiokol sample rcsults aken during
the same period shows that water quality naturally deteriorates as Blue Creek
flows through the valley due to minerals leaching from the alkaline soils. It also
shows that Thiokol operations have little or no effect on Blue Creek water
quality.
6.2.6 Health Risks of Human Exlpsure
The firiokol facilities are located in a remote area of eastern Box Elder County,
Utatr. Box Elder County occupies an arca of 5,640 square miles. A 1980
population of 33,2L2 represents a population density of about six individuals per
square mile. The population of the nrral areas of the county Qess than 2,5W
population) is about 14,000. Family groups living in the area of Thiokol can be
classifred into (l) ranchers and farmers, and (2) externally employed heads of
households who commute from long distances. There are no schools, hospitals,
or churches in the area of the plant. firere are no inhabited buildings or ranch
houses downgradient of the plant. Adjacent ranch houses are located on Figure
6.4.
2t
6,2.7
6.2.7,L
6.2.7.2
The potential of health risk to humans is limited by lack of access and exposure
to waste oontaminated areas and surface waters. Surface water is of very poor
quality and use is not considered suiable for drinking water or other domestic
uses (Bolke and Price, 19721' Hood, 1972).
Potential Damage to wildlife, Crops. Vegetation. and Physical Structures
Upland Habiats
Ttre Thiokol plantsite is entirely composed of upland habitat, with the following
exceptions: (1) developed areas occupying approximately 25 percent of the 3G
mi2 area afi Q) wetland habitats along Blue Springs Creek occupying less than
one percent of the area.
The semiarid climate and well-drained soils of the area support a vegetation t)?e
dominated by bluebunch wheatgrass (Agropyron spicaw) and sagebnrstr
(Atriplex sp.). Lists of common plant, bird, and mammal species are presented
in Tables 6.3,6.4, and 6.5.
Numerous mammal species inhabit the area. The largest is the mule deer, a small
herd of which inhabits theplantsite. Small mammals, including several rabbitand
small rodent species are fairly oommon. Unimproved rangeland, including the
Thiokol plantsite, is used for grazing domestic beef herds.
Upland bird species may be found on the plantsite, though not in large numbers.
Upland game bird species include sage grcuse (Centrocercus urophasiomr), blue
grouse @endragapus obscurus), sharlrtailed grouse @edioecetes plrosiotulhts)
and Chukar partidge (Alectoris chuclur).
Wetlands
On-site wetlands are very limited. The floodplain of Blue Springs Creek which
flows along the western boundary is occupied by serreral species of sedges and
g nses which rcquire and/or have more tolerance of water. fire classification of
these areas as characteristic wetlands may be questionable because of their limited
extent and the minimal surface water season. Small areas of similar vegetation
occupy the perimeters of the isolated springs found near the plantsite.
Small wetland areas such as these are tpically important to wildlife as they
represent a permanently available souroe of water. Even in low water periods
when surface waters may be nearly or entirely dried up, the more abundant,
29
b lusher vegetation with its inherent increased seed and/or fruit production
continues to provide oover, moisture, and food for small mammals and birds.
The delta of the Bear River, where it empties into Great Salt Lake, is located 11
mi southeast of Ttriokol. The delta is the site of the l0G'miz Bear River
Migratory Bird Refuge, administered by the U.S. Fistr and Wildlife Service.
Additionat areas of ttre dela are committed to waterfowl management through
State lands and private gun clubs. Tlrc Bear River Delta occupies an important
position on both the Pacific and Central Migratory Flyways. Beyond ttre
utilization of the Refuge during spring and fall, migration by approximately 60
species, out of the 200 species of birds recorded on the refuge, nest there
annually. The refuge produces approximately 45,000 ducks and 2,500 geese
annually. Canada geese are the only nesting goose species. Principal nesting
ducks, in order of abundance, are the gadwall, cinnamon teal, mallard, pintail,
and redhead. Egrets, herons, ibises, and numerous shorebird species commonly
nest in the lower marshes and along dikes of the Refuge.
Streams
Only a few streams flow through the area between Brigham City and the
plantsite. The aridity of the climate and the relatively small watersheds of these
streams result in extremely unstable flow conditions. The Bear and h[alad rivers
are the largest streams in the area, but are far removed from the plantsite, no
closer than 19 mi from its eastern boundary. Sulphur Creek and Salt Creek,
smaller streams located between these rivers and the plantsite, arE still well
removed from the plantsite. The only stream in the vicinity is Blue Springs
Creek, which flows to the west and south of the units.
The larger streams which are well removed from the plansite contain flowing
water throughout the year, and have pools which do not frerzn solid during the
winter months.
The smaller streams, including Blue Springs Creek, do not necessarily contain
flowing water throughout the entire year, and may, on occasion, freeze solid
during the winter months. Consequently, the fauna and flora are expected to be
much more depauperate. The only fish which might be expected to inhabit these
streams is the western speckled dace (Rhinichthys oscuhts). Benthic
macroinverte;brates such as stonefly @lecoptera Sp.), mayfly @phemeroptera
Sp.), and dragonfly (Odonaa Sp.) larvae tpicalty inhabit intermittent and small
streams such as these, and are expected to occur. The base of the food chain is
expected to be almost entirely derived from attached filamentous algae and
periphyton.
6.2.7.3
30
6.2.7.4
6.2.8
6.3.L
6.3. 1.1
6.3
Physical Stnrctures
There are no down stream stnrctures which might be affected by contaminates in
surface waters.
Persistence and Permanence of Potential Adverse Effects
Ground water beneath the Thiokol facility is relatively deep: approximately 100
feet at the property boundary adjacent to Space AdminisEation area. To the
south, the topography drops gradually in elerration to ftat of the wetlands adjacent
to the Great Salt kke. Ttre ground water surface dips even more gradtrally, and
the two surfaces intersect in a series of qprings and flowing (artesian) wells
approximatsly two miles south of the facility. surface waters are orpected to be
effected long term, only to ilre extent that conaminates arp introduced to surface
waters from conaminated ground water. Section 6.3 describes persistence of
hazardous constituents in ground water.
PERSISTENCE AND PERMANENCE OF POIENTIAL IHZARDOUS
CONSTITT]ENTS
The major hazardous constituents in ground water at Thiokol consists of
trichloroethene,l,l,l-trichloroethane,andbreakdownproductl,ldichloroethene.
Minor constituents consist of acetone, l,ldichloroethane, chloroform, ild
bromomethane. Only TCE and TCA are expected to be a possible exlpsure
1 . 1, l-Trichloroethane
Ambient Levels
No known natural souroes of 1,1,1-Trichloroethane (l,l,l-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 frequenfly observed in groundwater because
it is fairly mobile through soils; approximately 3.0% of all public drinking water
wells conain levels of 0.5 r/L (ppb) or higher (EPA, 1987a). Public drinking
water supply systems using surface water as their souroe normally contain lower
1,1,1-TCA levels than systems supplied by groundwater (EPA, 1987a).
6.3.1 .2
6.3.L,2,1
6.3.1.2.2
Health Effects
General
fire primary acute health lrazard of TCA relates to its anesthetic properties and
ability to prcduce a narcotic effect (McCarthy and fones, 1983). Narcotic effecb
are induced fairly rapidly (Riihimaki and [Ilfuarson, 1986). Exlnsure to
moderate oonoentrations causes transient systems such as headache, dizziness,
drowsiness and Central Newous System (CNS) dqrression @iihmaki and
Ulfuarson, 1986). At high concentrations, anesthesia and rcspiratory and
circulatory failure may lead to death; the most serious risls to human health are
with the use of 1,1,1-TCA in enclosed qpaces (Riihimaki and Illfuarson, 1980.
1,1,I-TCA is classified as a Group D carcinogen (not classified due to inadequate
animal erridence of carcinogenicity) (EPA, 1987b). Specific symptoms of 1,1,1-
TCA poisoning include unconsciousness, CNS dqnession, trd respiratory
symptoms such as coughing, breathlessness, and chest tightness @arker et al.,
L979). At least 30 faalities have been associated with exposure to 1,1,1-TCA,
mostly due to deliberate inhalation or to accidenal occupational exposures (ARC,
L979). Affected organs include heart, lungs, liver kidneys, and CNS; the heart
is the most vulnerable organ (Nelly and Blau, 1985). For the protection of
human health from oxicity due to ingestion of contaminated water and aquatic
organisms, the anrbient water quality criterion is 18.4 mglL (EPA, 1980a). For
the protection of human health from toxic properties of 1,1,1-TCA ingested
through conaminated aqtratic organisms alone, the AWQC is 1.03 g/L (EPA,
1987a). The long-term healttr advisory for children and adults is 35,000 and
125,000 ug/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 mglL (EPA,
1980a). The ACGIH (1988) TI-V for 1,1,1-TCA is 1,900 mg/m3.
Ingestion
A source of exlrcsure to TCA occurs from the ingestion of contaminated drinking
water. Torkelson et al, (1958) observed LDro values of L2.3 g/S bw (body
weight) for male rats, 10.3 g/kg bw for female rats, 11.2 g/kg bw for female
mice, 5.7 glkg bw for female rabbits, and 11.2 g/kg bw for male guinea pigs.
Studies involving the administration of 1,1,1-TCA by gavage concluded that
concentrations ranging from 250 to 1,500 mg/kg bw will cause diminished growttr
rates and decreased survival in rats @uckner et a1.,1985).
32
b 6.3.L.2,3
6,3.L.2.4
6.3.L.2.5
Inhalation
Inhalation of 1,1,1-TCA vapor is a common route of entry (EPA, 1987a).
Inhaled 1,1,1-TCA rapidly equilibrate wittr afierial 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 tfi 3.25 mglL for up to 450
minutes, whereas at concentrations of 4.95 to 5.5 mg/L for 75 minutes,
lightheadedness, loss of coordination, and loss of equilibrium were reported
(Aviado et al., 1976). It is estimated that a no obsenrable effect lerrel (NOEL)
for short-term exg)sure of human to 1,1,1-TCA is in the range of 350 to 500
ppm (1,890 to 2,7N mg/m) (EPA, 1984). Acute pulmonary congestion and
edema are found in human fatalities resulting from inhalation of 1,1,1-TCA
(Caplan et al. 1976; Bonventne et al., 1977). Inhalation of chloroethanes in
general can lead to liver and/or kidney injury, and pulmonary irritation
(McCarthy and fones, 1983).
Dermal Toxicity
All chloroethanes are irriating to the skin. Absorption of 1,1,I-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 a1.,1979). Other
dermal reactions to 1,1,1-TCA include dryness, cracking, scaliness, and
inflammation @arker et al., 1979).
Metabolism and Excretion
1,1,I-TCA is metabolized to a very limited extent in animals and humans. 1,1,1-
TCA rapidly equilibrates with arterial capillary blood across the lung alveolar
endotheliomas and as a result, most is eliminated by exhalation. 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 tichloroacetic acid. TVo urinary metabolites, trichloroethane
and trichloracetic acid, represented approximately 3.0percent of Orc total exerted
dose. Hake (1960) found Cr1 hbeled 1,1,1-TCA was less than 3.0 percent
metabolized in rats following a single intraperitoneal injection.
Metabolism occurs primarily in the liver, and to an unknown extent in ottrer
tissues (IARC, 1979). The primary metabolites are 2,2,2-trichloroethanol and
trichloroacetic acid (EPA,1984; IARC, 1979). Approximately I percent of the
2,2,2-tichloroethanol 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
33
6.3,L.2.6
6.3. 1 .3
rats as the parent compound as long as 25 hours following an interperitoneal
dose. The blood contained 0.02 percent of the dose, fat contained 0.(D percent
of the dose, and 0.01 percent of the dose was observed in other tissues.
1,1,1-TCA distributes throughout the body, readily crossing the blood-brain
barrier. Holmberg et al. (1977) studied the distribution of 1,1,1-TCA in mice
after inhalation exlpsure and observed similar concentrations in kidney and brain
at a given exposure concenhation, but concentrations in liver were twice those
observed in kidney and brain following exlrosures to 100 ppm or more. 1,1,1-
TCA has not been demonstrated to directly cross the placenal barrier into the
fetus, although it may be expected to do so due to its chemical and physical
properties.
Aquatic Ecosystems
Acute 96-hour ECso tests using chlorophyll a and cell number alr measured
res1lonses were conducted with a green alga, Selenastrum capicomututn (EPA,
1978). The highest concentration of 1,1,I-TCA tested was 669,000 \EL, 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; 96hour LtCe values for the flow-through and
static tests were 52,800 ug/L and 10,500 uglL, respectively. The 48-hr LC5s for
D. magu exceeded the highest exg)sure concentration of 530,000 ug/L (EPA,
1978).
A measured steady-state bioconcentration factor of 9 was observed for bluegill
exposed to 1,1,1-TCA (EPA 1978). Thus, significant bioconcenEation is not
expected to occur.
Environmental Fate
1,1,1-TCA is released by evaporation to the atmoqphere 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 roposphere (EPA, 1984).
The lifetime of 1,1,1-TCA is the ropoqphere is in the range of 5 o 10 years
(EPA, 1984), and the estimated half-life is one or morc years (EPA, 1987a).
Photo-oxidation products of 1, l, I-TCA include hydrogen chloride, calbon oxides,
phosgene, and acetyl chloride. 1,1,1-TCA is sAble in the troposphere, ild
significant amounts of the parent comlrcund are conveyed to the stratosphere
(EPA, 1984).
34
6.3,2
6.3,2.L
6.3.2,2
6.3.2.2.L
1,1,1-TCA is resisant to hydrolysis; the rate conshnt for hydrolysis at 25oC in
unbuffered water at a pH of 7.0 is approximately 4 x ld days (Nelly and Blau,
1985). fire estimated half-life in water is greater than 6 months (EPA, 1987a).
Trichloroethvlene
Ambient Levels
No known natural lpurces for TCE exist (EPA, 1985b). TCE is widely
distributed in the aquatic environment, and has been detected in drinking water
supplies, natural waters, and aquatic organisms (EPA, 1980b; EPA, 1985b).
TCE has been detected in human tissue, food supplies, and in air @earson and
McConnell, 1975). Detectable levels of TCE have been observed in groundwater
used for water supplies from various areas; median levels in finished waters from
these sources were 0.31 ug/L (range 0.ll - 53.0 ug/L) (EPA, 1985b).
Contaminated wells and water supplies with levels as high as 330 ug/L have been
reported (EPA, 1979). Four percent of 330 groundwater wells across the U.S.
had detecable levels of TCE; of these detections, 70 percent ranged from 0.5 to
5 uglL (EPA, 1985b). TCE can increase as a result of chlorination; 32 percent
of finished water from surface water supplies has been found to contain TCE at
levels ranging from 0.006 to 3.2 ug/L (mean levels 0.a7 \gtL) (EPA, 1985b).
Health Effects
General
In humans, TCE has been observed to cause mild eye irritation, nausea,
anesthetic, analgesic, behavioral, ild neurotoxic effects (EPA, 1985b). Most
symptoms are a result of effects on the central nervous system. Gastrointestinal
and respiratory symptoms are frequently reported. Following chronic industrial
exlpsures, central nervous system effects did not cease with termination of
exposure (EPA, 1985b). Embryo toxicity and teratogenicity have been observed
in experimenal 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 ras (EPA, 1985b).
The OSHA standard established in 1972 is 100 ppm (525 mg/nf) in air as a TWA
over a 8-hour workday (EPA, 1985b). National Institute of Occupational Safety
3s
6.3,2,2.2
6.3.2,2,3
and Health (MOSID has determined this la,el to be too high for protection
against carcinogenic effects, and recommends a level of 25 ppm (EPA, 1985b).
ACGIII has established a TI-V of 50 ppm.
To protect human healttr from the carcinogenic effects of TCE ingested as a result
of ingesting water or contaminated aquatic organisms, the recommended lerrel in
water is zero (EPA, 1980b). Because zero may be an unattainable goal, the
levels in water that correspond to lO5, l0{, and 107, risk are 27, 2.7, and 0,27
uglL, respectively (EPA, 1980a).
Aquatic Water Quality Criteria (AWQC) for the protection of freshwater aquatic
life have not been esublished, however, daa indicate ttlat toxicity to freshwater
aquatic life occur at lerrels as low as 45,000 uglL, and might be lower if more
sensitive species were tested (EPA, 1980b).
Ingestion
Because TCE is nonp,olar, uncharged, and lipophilic, it can be expected to cross
the gastrointestinal muoosa by passive diffusion (EPA, 1985b). Tte principal
target organs for orally exposed animals tend to be the liver, kidney, and
immunological system.
Ttrcker et al. (1982) reported an LD,o of 1,161 mgl@ bw @ody weight) for
mice, and a single dose of 750 mg/lqg bw did not kill any mice. Mice acutely
exposed (la days) to240 mglSlbwlday TCE exhibitd 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,&4, or 5,380 mg/m)
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 electroencephalogram (EEG) were observed in workers exposed to 50
to 100 ppm TCE. Ottrer workers exposed to 200 ppm for 7 hourilday for 5 days
exhibited eye irritation, dryness of throat, and other mild symptoms (EPA
1985b).
Exposure to 30,000 ppm (161,000 mg/m3) for 20 minutes was lethal to dogs
(Baker, 1958). Studies detailing behavioral effects indicate activity lerrel in rats
significantly decreases following exg)surp to 1,000 to 1,200 ppm (5354 to 6425
36
6.3.2.2.4
6.3.2.2.5
mg/mr) for a single exg)sure (EPA, 1985b). For multiple exposures over periods
greater ttmn 5 weeks, depressed activity occuned at levels as low as 100 ppm
(538 mg/m3) (EPA, 1985b).
Dermal Toxicity
Dermal absorption o@urs with direct contact; uptake is dependent on the t)?e and
area of skin exposed. The dermal absorption rate in mice ranges from 7.82 to
L2.l uglminlcm2, and in humans the rate is estimated to be slow (EPA, 1985b).
Dermal irriation is observed following exg)surc to TCE. Effects include
reddening, skin burns, and generalized dermatitis on contact with concentrated
solution (EPA, 1985b). Contact with dilute aqueous solutions has not been
reported to cause dermal effects. A hlryersensitive reslpnse was observed in
humans @hoon et al., 1984) as a result of dermal contact through indusnial
exlrosurc to valnr or solution at concentrations estimated between 9 and 169 ppm
and exlnsure durations of 2 to 5 weeks.
Metabolism and Excretion
In rats, approximately 90 to 95 percent of an oral dose of TCE administered in
corn oil was obseryed to appear in urine and expired air; this indicates almost
complete absorption by the oral route, as well as indicating the primary routes of
excretion @aniel, 1963). Rapid absorption from the GI tract is indicated by peak
blood concentrations, which occur within I hour in mice and 3 hours in rats
(EPA, 1985b). Administration of the dose in aqueous vehicle, as opposed to corn
oil, reduces the absorption time significantly (EPA, 1985b).
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, 1985b). TCE then
distributes to all body tissues, but tends to partition to lipids. TCE crosses both
the blood-brain and the placenal barriers.
Biotransformation occurs in the liver to three principle metabolites:
Trichloroethanol, TCE-glucuronide, and trichloroacetic acid (EPA, 1985b).
These metabolites are excreted in urine. However, most TCE is excreted
unchanged in expired air.
Aquatic Ecosystems
TCE is acutely toxic to D. nugrw at levels of 85.2 mg[L in a static 48-hour LC56
6.3,2.2.6
37
6.3.2.3
test (EPA, 1978). Chronic tests indicated no adverse effects on D. magna at 10
mglL, the highest level tested (EPA, 1978). In a natural pond, a single dose of
0.025 and 0.110 uglL decreased D. magtu populations, but increased
phytoplankton population (Lay et al., 1984). fire 96hour LCso in a flow-through
test with fathead minnows was 40.7 mgL (Alexander et a1.,1978). Behavioral
effects have been obserrred in fathead minnows at levels as low as 21,900 u/L
(EPA, 1980a).
TCE does not accumuliate in aquatic organisms to any great extent.
Bioconcentration factors of 17 for bluegill were observed after an exlpsure
duration of 14 days (EPA, 1978). Tlrc biological half-life is less thur one day,
suggesting that residue accumulations is not a concern for aquatic life (EPA,
1980b).
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, ild it is not highly
soluble in water (EPA, 1980b).
In air, vertical and horizonal mixing of TCE occurs, and transport is dependent
on persistence of TCE, which in turn is function of free hydroxyl radicals (EPA,
1985b). Free hydroxyl radicals are the primary scavenging mechanism for TCE
in the atmosphere. fire estimated lifetime for TCE is 54 hours (Edney et al.,
1983), assuming an atmospheric hydroxyl radical concentration of 1tr
moleculedcm3. Other estimates of atmospheric residence times range from 11
to 15 days (EPA, 1985b). Approximately 20 percent of the TCE in air is
expected to be destroyed daily (Singh et a1.,1979). Phosgene and dichloroacetyl
chloride are the two principle degradation products that have been observed in air
as a result of photooxidation (EPA, 1985b).
TCE degrades slowly in water; estimated half-lives are l-l2days in surface water
(EPA, 1985b). Volatilization is the major way TCE is lost from water; rate of
volatilization from water depends on the aeration rate (EPA, 1985b). Smith er
aI. (1980) estimated a half-life of 3 hours in shallow rapidly moving sEeams,
whereas a half-life or 10 days or longer was estimated for ponds and lakes.
1.l-Dichloroethene
No known quantities of DCE have been disposed of at M-136. It is believed to
6.3.3
38
be an abiotic breakdown product of TCA and TCE. DCE is more volatile than
TCA or TCE, and is probably less persistent than TCA or TCE. Howwer, DCE
is replenished in the ground water by the continued breakdown of TCA and TCE.
6.3.4
6.4
6.4.t
Acetone
Acetone does not appear persistent in
below the PQL in all wells except C-l
EXPOSI]RE PATITWAYS
ground water. The plume has dropped
which is adjacent to a major source area.
Exposure is the contact of humans or other organisms with site-related
contaminants. In order for a chemical to produce ur effect, there must be a
pathway from the source to the biologic receptor. The potential exlnsure
pathways considered for humans and nonhuman biota 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 conhminated
game species; and, ingestion of conaminated aquatic organisms.
A complete exposure pathway consists of the following four elements (EPA,
1986a):
. Source and mechanism for chemical release,a Environmental transport medium,o Point of potential biological contact, ando An exposure route (i.e. ingestion, inhalation, dermal absorption)
at the contact point.
All four of these comlnnents are necessary to form a complete exlrosure pathway.
If one or more of the comlnnents is lacking, thene is little possibility of an effect
due to site contamination. The points of biological contact are discussed below
for each potential exposurc route. In general, most human receptors are distant
from the contaminant sources. orrly one pathway is considerpd: a hypothetical
receptor whe,re ground water becomes surface water.
Surface \Mater Fate
Volatilization is expected to be the primary removal mechanism of the indicator
chemicals from surface water in qprings if conaminated by ground water. Based
on available persistence information for each of the indicator chemicals (Iable
6.6), only l,l,l-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 chemical is much lower; the
minimum estimate for TCE is 1 day. Maximum half-life estimate for TCE is 12
days (Iable 6.6).
The flux of a volatilizing chemical (g-) in mg/m2-sec can be calculated from:
(Lo, : k" C-, (1)
where: k" == volatilization rate constant (m/sec), andC* : contaminant concentration in surface water
(mg/m3 or ug/L).
The parameter kv can be evaluated from the trvo-film tr*ry, in which the
volatilization rate constant is given by:
(k")' - (lq)-' + (If kJu Q)
where: k, =! mass transfer coefficient in the liquid pharc
(m/sec),tt : mass transfer coefficient in the gas phase
(m/sec), andH0 = dimensionless Henry's Law constant
Using the vdues in Table 6.7 in the following equations, the oxygen reaeration
coefficient (lq) and oxygen surface transfer rate (k') were obtained:
h' : hz (3)
where: k = oxygen reaeration coefficient (dayr), andz = stream, depth (feeO.
Based on Owens empirical expression (Ihormann, 1972):
lq = 21.6 x Vo'n (4)
zt.t5
where: V = strearn or ditch linear velocity in ff/sec, andz = stream depth in ft.
Substituting the values from Table 6.7 into equation (2), the oxygen reaeration
coefficient becomes:
k : 2L.6 x (p.s)o'o' (5)
(0.751t.4s
40
k'.: {!02} x (0.5ft) x {0J04h} x {-day-} = l.s x l0{
m/sec
day ft 8.64xldsec
k : LV2L7 daYrk' = 1.8 x 10{ m/sec
Once (' is known, the mass transfer coefficient of the chemical in the liquid
phase can be estimated as follows:
k, ={-2.}0'25 x h' (6)
IvfW
where: & and (' have units of (m/sec), and lvIW is the molecular
weight of the contaminant.
Substituting the value for ( into equation (6), the mass transfer coeffrcient in the
liquid phase becomes only a function of the molecular weight of the chemical:
k, :{-2.}o'5 * (1.8x10r) A
lvt\il
To calculate f in equation (2), the following equation was used:
k, :{-16-}0.25 x q' G)
IVTW
The gas phase transfer rate (\') in cm/hr was obtained from an empirical
relationship devel@ by Mills (EPA, 1988), who showed that
q' : Toov'' (9)
where: V, = wind s@ in m/sec.
With a wind s@ of 3 m/sec, \' becomes:
q, = 000X3)= 2100 cm/hr
= 5.80 x ld m/sec.
Substituting { into equation (8), the mass transfer coefficient in the gas phase
becomes only a function of the molecular weight of the chemical:
4L
q :{ tg }o'' x (5.80 x 10')
lYt\M
k :{ lZ }o'' x (1.8x10{)
lvt\M
(10)
Mass transfer coeffrcients were obtained with equations (6) and (8). lhe
equations for the mass transfer coefficient in the liquid phase (h') arc as follows,
respectively:
(1 1)
6,4.2
6.4.3
Substituting the molecular weights of 1,1,1-TCA and TCE into equations (11) and
(10) and using the resulting k1 and \ values in equation (2), the volatilization rate
constants (k") were obtained. The results are presented in Table 6.8.
The maximum surface water concentrations Clable 6.9) were used in equation (1)
(q,* : hC*) to estimate volatilization flux rates Cfable 6.10).
Direct Contact
Dermal absorption is expected to be a rare went, occurring only in individuals
contacting conaminated ground or surface water. Ground water is very deep
below the plant site, but becomes progressively shallower southward, and
becomes surface water in springs located near Lampo function.
Nonhuman bioa may be exposed by direct contact with contaminated surface
water, only if contaminated ground water migrates to springs south of plant. If
migration oocurs, exposure might tata place during feeding, drinking, or
bunowing activities. Dermal absorption is species qpecific and dependent on the
type of activity that results in direct contact. 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 expect to
be less than those resulting from inhalation or ingestion. Aquatic species,
however, may be exposed by direct contact with surface water in springs feeding
Blue Creek. Aquatic life are continually exposed to their environment, and may
be sensitive to certain chemicals.
Inhalation of Vapors and Dusts
Volatilization from surface water, sil, 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 oon@rn. Only if
42
6.4,4
6.4.5
contaminatcd ground water migrates to surface water is inhalation of volatiles a
potential pathway for human and nonhuman biota. Because residences in the
surrounding area are quite distant from the site boundaries, rtrd none of the
contaminated ground water or potentially contaminated surface water is used for
culinary pulposes, human exposurc is not considercd important.
Ingestion of Water and Soil
Ground water and surface waters are not utilized in the Thiokol area as a drinking
water source because of poor water quality due to high TDS. TDS values in
wells and springs directly downgradient of Thiokol is over 7,000 mglL; therefore,
future groundwater use in the area is limited. If these lpuroe were to become a
drinking water source in the future, risk would have to be reevaluated.
Surface water from springs is not utilized immediately downgradient of fitiokol
for drinking water or irrigation puposes. However, livestock and wildlife may
acoess BIue Creek and consume surface water. It is unlikely that children or
other human receptors will contact contaminated surface waters 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.
Ingestion of Cro,ps and Livestock
Crops are not currently irrigated with ground water or surface waters
downgradient of Thiokol and are therefore not expected to be a significant
exposure pathway. At ttlis time, all known actively used irrigation wells are
upgradient from the site. If ground water or potentially contarninated surface
water is used for crop watering activities, due to thevolatility 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 exg)surc
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 (I(-,) for each of the indicator chemicals and equations from
Kenaga (1980) were used to predict bioaccumulation factors (BAF) in livestock:
Iog BAF : (-3.45'l + 0.500 0og K"*)) (L2)
where: BAF :
I(*, :bioaccumulation factor, ?trd
octanol-water partition coefficient.
43
L The estimated I,og BAF and BAF values are as follows:
-
--
Loe BAF
-u-
-2.20
-2.27
BAF
0.0063
0.0054
6.4.6
6,5
6.5. 1
1r 1,I-TCA
TCE
The bioaccumulation factor rqxesents concentration in tissue compared to
concentration in diet. Theprcdicted values are less than one and bioaccumulation
is not indicated for any of the chemicals of concern.
Ingestion of Game Species and Aquatic Organisms
Game species are not expected to be a potential exposure pathway to humans
based on the lack of game organisms and bioaccumulation factorvalues estimated
for the indicator chemicals. Aquatic organisms are also not anticipated as an
exlpsure pathway, beause the tendency for the chemicals of concern to
concentrate in tissue is very low, and the lack of game fish in Blue Creek and
associated springs.
CoMPARTSON TO REQITIREMENTS, STANDARDS, AND CRITERIA
Established Criteria
The maximum expected exposure point concentrations (fable 6.9) were compared
to both established and estimated criteria to determine potential healttr rists.
Potential applicable or rclevant and appropriate criteria (ARARO for the indicator
chemicals arc summarized in Table 6.11. The maximum contaminant levels
(MCLs) for groundwater are defined in the National Primary Drinking Water
Standards (EPA, 1987c).
Other standards and criteria that might apply are the Ambient Water Quality
Criteria (AWQC) for the protection of freshwater aquatic life and its uses and for
the protection of human healttr (EPA, 1986a). fire indicator chemicals are not
regulated under the Clean Air Act (CAA), or by National Ambient Air Qudity
Standards (NAAQ$. The American Council of Governmental Industrial
Hygienists (ACGIII) Threshold Limit Values GLVs) are used to indicate adverse
effects to workers exposed via inhalation. The EPA Health Advisories (IIA$ for
1,1,1-TCA are prcsented in Table 6.12. The IIAs are nonregulatory criteria
u
6.5.2
6.5 ,2.L
6.5 .2.2
6.5 .2.2.r
based on noncarcinogenic human healttr effects from exposure to dri*ing water
and/or consumption of fistt.
Estimated Criteria
Aquatic Life
An aquatic life criterion for l,l,I-TCA was estimated because an AWQC for the
protection of freshwater organisms was unavailable. The LCe for fathead
minnows (10,500 ug/L) was divided by a factor of l0 to convert the acute lethal
value to a chronic nonlethal value. EPA (1986b) uses a conversion factor of 1/10
the LC56 for aquatic organisms, as compared to environmental concentrations, to
assume a no-risk situation. Therefore, the uncertainty factor applied 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
1050 ug/L.
Wildlife and Domestic Livestock
Surface Water Ingestion by Nonhuman Biota
Criteda for ingestion of surface water werp estimated for wildlife and domestic
livestock from the Lowest Observed Adverrc Effect Levels (LOAELs) and No
Observed Effect I-evels (NOELs) from fte toxicity data rwiewed. Ttrese criteria
are intended to sewe as indicator lerrels of risk to nonhuman biota other than
aquatic life. Chronic exlrosure data were considered more appropriate than acute
and subacute effects data were considered preferable to lethal effects data.
The LOAEL for 1,1,1-TCA was 250 mglSlbwlday for rats dosed acutely and
subacutely @uckner et at.,1985). A 200 gm rat oonsumes 25 ml water daily
(Sax, 1984). The LOAEL in drinking water would be:
LOAEL = mg/kg/day = mglL (13)
Water Consumption Ukglday
The LOAEL in drinking water for a 200 gm rat consuming 25 ml drinking water
daily is 2,000 mg/L. Decreased growth rate and decreased survival were
observed at this dose lerrel. An uncertainty factor of 100 was applied because of
45
the limited toxicity daa available (i.e., few species, no avian data, and no
livestock daa, limited chronic and sublethal effects data, converting dietary
values to drinking water values, etc.) and to adjust LOAEL values to NOELs
(results: 20 mgtL.
The LOAEL for TCE is 2.5 mglL for rats orposed to TCE in drinking water
(Iucker et al., L982). Irss uncertainty is involved with ttris estimate, since
drinking water was the souroe of exlnsure for the toxicity study. An uncertainty
factor of 50 was applied for interspecies variation, limited data, and converting
a LOAEL to a NOEL. The resulting estimated acce,ptable lerrel in drinking water
for terrestrial wildlife and livestock is 50 ug/L.
The surface water criteria for livestock and wildlife at which no adverse effecs
are expected are:
6.5,2.2,2
6.5.2.2.3
o lrlrl-TcA :
OTCE:
Inhalation
1r 1r I-TCA
TCE
20 mglL, ?trd
0.050 mElL.
350 ppm (short-term NOEL; EPA 1984)
less than 10 ppm or 538 mg/m3 (subchronic
LOAEL; EPA, 1985b).
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 indicaor chemical was, thetefore, used to indicate
acceptable levels. Chronic data was considercd more apprqlriate than acute, and
sublethal data were considered more appropriate than lethal. The estimated air
concentrations are:
o
o
-
--
Threat to rilildlife
At atl areas of oonoern, pedicted exgrsurc concentrations arc less than the
estimated or established criteria protective of aquatic or terrestrial organisms.
The maximum predicted levels in surface water are orders of magnitude lower
than the AWQC for freshwater aquatic life. Inhalation of site-generated
contamination is not expected to result in adverse effects in nonhuman bioa.
46
L 6,6
7.0
7.1
NO THREAT TO IIEALTII OR ENVIRO}.IMENT
The risls to human healttr and the environment appear to be minimal, despite the
lerrels of groundwater contamination observed. This is due to the following
reasons:
. Groundwater is unpotable without prior treatment due to naturally
occurring high TDS,o Distance to nearest homes,o Distance from conAmination to nearest surface water dischargeo Irngth of time for plume to reach surface waters,o Low population densrty in the surrounding area, ando Iack of bioaccumulative properties for the contaminants.. Blue Creek or associated springs are not expected to be utilized for
drinking water, recreation, or fishing at any time.
The predicted and observed groundwater concentrations at a specific discharge
point at springs, without allowing for surface water dilution, are predicted to be
less than the AWQC for aquatic life.
The combined cancer risks for the potential exposure pathways are less than lff
risk level, and the weight of evidence is 82. The noncancer hazard quotients are
all less than unity, predicting minimal threat to health based on noncarcinogenic
effects. There arc no observed ecologicd heatth effects due to observed
contamination.
ON.GOING IIYVESTIGATIONS
SOL STT]DIES AT PHOTOGRAPIIIC WASTE DISCHARGE SITES
In April 1987, Morton Thiokol entered into a Stipulation and Consent Order with
the Utah Solid and Hazardous Waste Committee (Case Nos. 8502162,8@6402)
in regards to several photographic waste discharge areall. Morton firiokol agreed
to investigate these areas in a 'Soil Study Plann, and to begin closure activities
based on the findings and conclusions of the Committee.
The overall objective of thepresent study is to evaluate whether silver, cadmium,
chromium and lead are likely to migrate from the discharge areas to the
uppermost aquifer at each site. The study is evaluating the present extent of
downward migration of these metals, the potential for future mobility of the
metals in the soil, and soil properties, including soil moisture available to leach
the metals, that will affect the migration potential of these metals.
47
'7 .2
Environmental activities at these sites will proceed as specified in the Stipulation
and Consent Order; thus, no additional investigation studies are planned for the
RCRA Facility Investigation.
INSTALLATION RESTORATION PROGRAM
The area at the Thiokol facility known as Air Force Plant 78, is operated by
Thiokol Corporation but ownership belongs to the United States Government.
The Insallation Restoration Program (IRP) was dwel@ by the Department of
Defense to ensure Ont its facilities comply with legislation governing disposal of
hazardous waste.
fire objectives of the IRP are to identify and fully erraluate suqpected 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 IRP is the basis for response actions on United Sates Air Force insallations
under provisions of the Comprehensive Environmental Resp,onse, Compensation,
and Liability Act (CERCLA) of 1980, as clarifred by E:recutive Order 12316, ard
the Superfund Amendments Reauthorization Act (SARA) of 1986, as clarified by
Executive Order 12580.
Engineering Science, Inc. was retained by the Air Force Engineering and Services
Center to conduct the IRP at Plant 78. Work began on the IRP 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, monitor wells were insalled and sampled. Soil borings were
installed, sampled, and andyzed and an EM-31 geophysical survey was conducted
to accomplish the contamination assessment. Additional soil borings and another
monitor well were installed during the winter of 1988. As a result of the
investigations, five of the eight sites were selected for additional investigation.
fire objectives of the additional investigation were to conduct field investigations
to verify the results, define the magnitude and migration potential of
contaminants, perform a baseline risk assessment, and develop preliminary and
detailed alternatives for remedial action.
The final results and conclusions from the IRP investigations were submitted to
the State of Utah Division of Solid and Hazardous Waste in September 1992.
The reports concluded that based on the current conditions at Plant 78, no
significant risk or threat to public health or the environment exists and no further
action was planned.
48
7.3
'7 ,4
7.5
Region VItr of the U. S. EPA reviewed the IRP reports and incorporated the
findings into an evaluation of the silp utilizing the I{azard Ranking System GnS).
The EPA determined that the site would be classified as Site Evaluation
Accomplished (SEA) with no further evaluation planned.
No additional investigation activities are planned for the RCRA Facility
Investigation at the IRP sites.
M.136 CLOSI]RE AND POST CLOSIJRE PERMIT APPLICATION
CORRECTIVE ACTIONS
Thiokol Corporation is currently involved in studying and modeling the ground
water contamination plume as required in its Closure and Post Closure Permit
Application. Results from modeling the plume and the proposed corrective action
measures based on the results of this modeling were submitted to the Uah
Division of Solid and Hazardous Waste in a report ljrtled M-136 Liquid Thermal
Tfea*nent Area Conective Action Plan, dated December 1992.
CLOSI'RE ACTTVITIES
Thiokol has initiated closure procedures at serreral of its waste management sites.
These sites include the T-29 Hydrazine Burning Pit, the M-224 Shot Pond, the
M-136 Drum Storage Yard, and the M-136 Liquid Thermal Treatment Areas.
With the exception of the M-136 Liquid Ttrermal Treatment Areas, the sites have
all been restored to where there are no statistically significant levels of
contaminants above background. At the M-136 Liquid Thermal Treatment Areas,
low permeable covers were @nstructed over each of the lnnds to effectively
minimize infiluation and to divert run-on/nrn-off.
Closure activities at each of these sites has been completed and a
describing the investigation and closure proceedings has been submitted
regulatory agencies.
M-225 HIGH PERFORMANCE PROPELLANT BI'RNING GROT'NDS
INVESTIGATION
A partial closure plan was submitted to the State of Utah Bureau of Solid and
Hazardous Waste to investigate the burning trenches which are no longer used
within the M-225 Burning Grounds. Investigation activities at this site have
included deep soil borings and the installation of a groundwater monitoring well.
Investigations activities are ongoing at this site as part of the M-225 Partial
report
to the
49
8.0
9.0
Closure Plan and not as part of the RCRA Facility Investigation.
WASTE MIIYIMIZAIION AT TIIIOKOL
Thiokol Corporation is committed to the reduction of both hazardous and non-
hazardous wastes generated at its facilities. In place, is a Waste Minimization
Plan which implements a cost assessment and benefit assessment approach to
waste reduction. The goals of the program are to reduce waste to the
environment, lower environmental compliance costs, reduce operating costs,
increase profit margins, and become more market competitive. The goals arc
being accomplished by various production organizations following a coherent
approach to waste identification, process evaluation, and waste reduction
opportunities.
Several waste minimization teams have been formed and are currently working
to reduce the total volume and toxicity of waste.
IMPLEIVIEI{TATION OF INTERIM MEAST]RES
Thiokol Corporation has taken measures at many of its solid waste management
units to mitigate the threat of harm to human healttr and the environment. The
measures include the replacing of single containment sumps with new sumps
having secondary containment and leak detection equipment. Serreral of the
waste docks for collecting waste in liquid form have been equipped with
secondary containment.
At the M-136 burning grounds, the pits known as the Liquid firermal Treatment
Areas (LTTAO have undergone closure to construct a low-permeable cap over
each site to effectively prevent migration of waste residues further into ttre soil
profile. Closure activities have also taken place at the M-224 shot pond and the
M-136 dnrm storage yard where the soils are being excavated as necessar5r, to
remove contamination.
Closure plans have been prepared and submitted to the Division of Solid and
Hazardous Waste for the I-10 Burn Ground and the sludge burning trays at M-136
Burn Ground. Closure plans are currently under development for the
Photographic Waste Discharge Sites.
50
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American Conference of Government Industrial Hygienists. 2nd printing.
Cincinnati, Ohio
Alexander, H.C., et al. L978. Toxicity of perchloroethylene, trichloroethylene, 1,1,1-
trichloroethane, ild methylene chloride to fathead minnows. Bulletin of
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Aviado, D.M., S. Zaktrari, J. A. Samaan, and A. G. Visamer, 1976. Methyl Chloroform
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Baker, A.B. 1958. The nervous system in trichloroethylene: an experimental study.
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82l006F. Office of Health and Environmental Assessment. Iuly 1985.
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Battelle - Columbus Iaboratories, Revised 1987, Environmental Analysis Repot on Space
Shuttle Solid Rocket Motor Production Program at ThiokolAMasarch Division,
Brigham City, Utah: Vol IV
Bolke, 8.L., Price, P., 1972, Hydrologic Reconnaissance of the Blue Creek Valley Area,
Box Elder County, UAh: U.S. Geological Survey; Dept. of Natural Resources,
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Bonventre, J.,O. Brennan, D. Iason, A. Henderson and M. L. Bastos. 1977. Two deaths
following accidental inhalation of dichloromethane and 1.1.1-trichloroethane.
Iournal of Analytical Toxicology 4:158-160.
Buckner, J.V., S. Muralidhara, W.F. Mackenzie, G.M. Kyle and R. Luthra. 1985. Acute
and subacute oral toxicity studies of 1,1,1-trichloroethane in Bts, The
Toxicologist. 5(l) : 100.
Caplan, Y.f., R.C.Backer and I.Q. Whitaker. 1976. 1,1,1-Trichloroethane: report of
fatal intoxication. Clinical Toxicology . 9:69-74.
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IoxloC\
i
---
r-

,-
o6
-
r-
-uE.
\
o'
;
.
--
LY6bl-
o(o
o(o$t
$t
\r
oC\
Tq
r\r\
o$o)
oo\
ot
sf
co
$I$r
or\
F
vco
rOr\
a)€,
oN
CD
.
t,ooq-ooo5€l--
qn
.-oF-F
.oo(,
(u?
,A
l->f-Govo.-ol--F
1^o-(E-V.9
,o-l-
A->L-GoY.ooo(t
r
-?
Ao-G-Y.ooo(u-
?Fboa-l--l-
,A
la-
bGoYoo?-F
Ao1-(u:o
e
o-SF
A.>L.
(uoY.oooG-
,4
.
o-o-Y.ooC)o?
Iol--F
.ooo(!-
9,o(--F
bo?-bo-J.
f-oo.ooo
f-oFbL-o-J-
oCL
l--ool-
Fb
EE
og
o
?b
5=
fI@so
o1-(u-a13Go-o
-I-
EE
co
g
o
-I-
Eg
€g
o
l--
==
f!
ct
s
o
>oooo(r
o,
qlJ6
aooOoCE
bo.C
t-b-.IJz=o=
,F
I
lt
J
NI
t!
a)IUJ
!r
IUI
to
I
uJ
(o
I
t!
T\I
IT
J
Oi
iI
o TABLE 6.1
AVERAGE ANNUAL TEXTTPERATTIRES AND PRECIPITATTON
Plant 78, 8658
End year - 1988
TT}TPERATURE
Station: Thiokol
Start Year - 1962
2 yearB in 10
will have
PRECIPITATTON
2 Yeare in 10.. r . Av€lraqC!ur,-rr nave Average
-number of-----rllO. Of
l{onth Avg
daily
mErx
Avg Avg
daily
max
Max
temp.
)than
Mj.n
temp.
<than
grow'n
degree
Avg
(in. )
Less
than
( in. )
Hore days with
than 0.10 inch
22 .0
27 .5
36.4
45.0
54. 8
63 .8
72.2
70. 5
59.8
47 .8
35.3
24.2
49
58
69
78
88
97
100
ooJJ
93
82
65
54
1
7
50
178
461
728
975
944
59s
2s9
3s
3
4235
1. 02
1. 10
1. 20
1. 51
1. 58
1.55
0. 80
0.96
1.21
1. 47
1.35
1. 10
0. 46
0. 3g
0. 4g
0. 51
0. 52
0. 48
0.32
0.29
o.2g
0. 54
0.39
0.39
1. 50
1. 70
1.81
2.28
2 .51
2.43
1.38
1. 55
2.O2
2.4t
2 .13
1. 87
or more
3
3
3
4
4
3
2
2
3
3
37
davE
January
February
March
April
o:"
JuIy
August
September
Oetober
November
December
YearIy
Average
YearIy
Extreme
TotaI
32.7 11.2
39 .3 15.7
48. 5 24.2
59.2 30.8
74.6 39.1
80.9 46.7
90.9 53.5
89 . 1 51.9
78. 0 41.6
64.3 31.3
47 .5 23.1
34. 9 13. 5
-21
-12--
2
15
22
26
39
28
24
16
-0
-13
4
3
61,3 31.9 45.5
103 -29 102 r-A-lL
14. 88 8. 53 18. 71
Growing Degree Daye Threshold: 40.0 deg. F
TABLE 6.2
BLIIE C8.E3 BENESICIAL USE
3D ,- P;oE,ected f or sacer f osl , shore blrCs,
1..- ProEect,cd for
PASAI€TE3.
agr:,culcural uses
cIl'SSIilCAIION
and food chain
1g
5.0
6.5 .D 9.0
t5
tt 0.360 ( cslvalcac )
r* 0 .014
il 0.016i* 4.270 '
il 0.050Hr I .000r* 0.33 Lil 0.0024r* 6.251
.IE 0.020r* 0.027n 0.297
il o.azz
pH .& IrEp depencicar
easc-by-case
0.002,
0.01
,- rug/1)
15
3.0ffr* 0. 004 3lZ.ttr*r 0.05610. lg*'rl 0.002310. lg
0.01r*'rr 0.003910.52rtn 0.09 lz.a
0.03
0.001
0.06
D.O. (30 day ave. - 88/1)
pH
f urb ld1cy lacrease (NTU)
Arseslc (ag /L)
Soron (ng / L)
Cadu,itJl!, (ng /L)
Clrrou,luE (tocal 'D tr8/1)
(hexavaleac ,D ug/l)
(c-vaie,ac ,- trg/I)
Copper (ng / L)
Iron (rng / L)'
LeaC (rng /L)
!{crcury (ag /L)
llickel (aS / I)
Seienluc (ng /L)
Sllver (ng /L)
Z!,nc (urg / L)
Cyanide (frec - ES/l)
Ase,onla (unloalzed -, trg / L)
Chiorlac ( eocal restdual - sg/l)
Eycrogea Sulf 1de (uadlssoclac,ed
- ugll)
?heaol (ua:<1aua '|- Eg/l)
?oeal Dtssolved Solids (uaxLsr:n
Gross Alpha (aaxttruu 'D pcl lL)
AldrLn (aa:cluua (- ug/l)
Ciordanc (ug/ 1)
E3dosulfau (ug /L)
E=drla (ug /L)
Gurhlou (uaxl-gtrn - ug/1)
Eepachlor (ug / L)
Llndaue (ug lL)
bcho:q7chlor (uaxluua - uS/I)
!11rax (aaxlnuo .- ug/l)
?zrachloa (uaxlgrra - ug/I)
Pc3 (ug lL)
?escacblorophcuol (ug/l)
ioxapheue (ug /L)
r*n 0.01412.0t:lrH L3lZ0 (pE dcpeadeue)r*rr 0.00021a.73
6.5 (- 9.0
rfr 0.1
(Tocal)
0. 75*** 0.01
ffi 0.10
r** 0.2
rff 0.1
*ffnnqIU O YJ
1200
15
PAR.{I€:E3
Polluclon lndlcacors
Gross Beea (pCi /L)
BOD= (ug /L))
TABLE ,5 .2 CONT.
50(
J
!
50
a
fu-si:eaE rreger qualJ.cy lrust ace!
11s c ad
Aclci solub le ccnceBE:asloas . Uscd
calculace coBcsnElaE1oa h,alcs for
coppcE , lead, Blckel r si.l,vcr, aud
average (acuee goxlelcy) 1r-+ !s.
Ebc Bost sc=lugeat crlterla ot those
300 ag/ ! harriaess as CaCO ? to
caca,1[a, e;i.valeac ehroei.ds,
z1nc. AlL couccnE=acloas are t hour
t**
t**r
Ac:d solubie, aa:chra coEcaEE:at1ou llulgs
Four day avcrage (chroalc toxlelgy) ead I hour avcrage (acugc
cox:e1cy) conccntrasloa llalts tlspecrlvely.
o
TABLE 6.3
COMMON PI.A}TT SPECIES IH TEE VICINTTY OP TEE
TEIO E OI./WASATCE PI.A}fISTTE
Common Name Seientifie Name Esbitst Soil Assoeiations{8)
Eluebuneh wheatgrs,ss'
S ag"-b rrrsh (S hadscale)
B ig Sagebrush (Sagebnsh)
B itterbrnsh (AnteloPe brush)
Sandberg blueg!8ss
Cheatgrass
Juniper
Snourberry
YepowErush (RaOU it bnrsh)
Wiregrass
Sedges
Kenhrelcy bluegrs,stt
Inland sattgrass
Fortail,
Habitat
u = upland
w = wetland
Aeroowon soieeturn
--
Atriolex p.
Artemisia tridentata
--
Purshia tridenteta
P oa seeunda
Bromus teetorurn
Junioenrs osteosDerms,
--
Svmohoriesrt6s sD.
Chrrrsothamnus sD.
Aristida sp.
Gzoenrs p.
Poa Dra,tensis
--Distiehlus so iegta strieta
MrSrEJg
SrE Sp
!4II
S,E
s
s
M
E
w
w
w
w
t{
u
u
:
ur
xt
w
Setaria +
Soil Asoeiations (Classifiegtion by Soil Conservation 5gtryisgl (8)
M = MiddlrBroad Assoeiatlon
S = Sand&ll
E = Hupp-Abela Assoeiation
Sp = SarPete
W = Wood Cross
TABLE 6.4
Bird species observed on or uear Plant 78.
Species Common Name
IJnrs califoraicus
IJrlrs argentatus
Corvus brachwhyuchos
Corrnrs corar(
Pica pica
---Sturnella neslecta
Mimus oolyelottos
Aeelaius ohoeniceu
Charadrius vocifcrus
Recurvi rostra americana
Himantoous mexicanus
Catoptroohorus semioalmatus
Actitis macularia
Limosa fedoa
Ardea herodias
Eeretta thula
Pelecanus ervthrorhnnchos
Falco mexicanu
Hiruudo pvrrhonota
Riparia rioaria
Buteo swainsoni
Circus cvaneus
Aquila chrvsaetos
Hdiaeetus leucoceohalrc
Anas Elawrhnnchos
Anas cvanoptena
Anas discors
Anas crccca
Anas acuta
Anas americana
Anas strcDqa
--Anas clweata
--Avthva americana
A:rthva affinis
Avthva valisineria
Fulica americana
Bucephda clanenrla
Oxnrra ia-'icensis
--Branta canadensis
Cvous coumbianus
Phasianus colchicus
Californis gull *
Hcrring gull *
American crow *
Common raven *
Black-billed magpie +
Westcra meadowlark *
Northern mockingbird +
Rd-winged blackbird +
Killdeer *
Americaa avocet +
Black-nccked stilt +
Vlillet *
Spoacd sandpipcr * '
Marbld godwit +
Grcat blue heron *
Snoury egrct +
American white pelicau +
Prairie fdcon *
Ctitr swallow *
Ba* sndlow #
Swainsg['s hawk t
Northern harrier +
Golden eaglc +
Bald eaglc #
Mallard *
Cinnamon tcal +
Blue-winged arzrl #
Grceo-winged tral #
Northem piuail #. Americatr wigeon #
Gadurall #
Northera shovelet #' Redhead #
Lesscr scaup #
C,anvasback +
Anrerican coot +
Comnon goldeteye #
Ruddy drck #
Camds goose +
Thndra s\yeo +
Ring-ncckcd pheasant +
t - Obse:ved ou Plant 78.+ - Observed within viciniry of Plant 78 (including nearby Refuges).# - Reported in Plant 78 Viciniry.
TABLE 6.5
M"-maJs obscrved or expected Bear Plant 78.
Species Common Na-e
Perosnathus Daffus
--
Microdipodops meeaceph alus
Dipodomrrs gd
Reithrodontomrr meealotis
Perom)rscts crinins
Peromrncus m aniculatns
PeromJrscus bovlei
Neotoma lepida
Ondatra zibethicrs
Onvchomvs leucoeaster
-
Microns pennsylrranicns
Microns longicaudu
Languns curtagus
Eutamias minimts
Marmota flavivenrris
AmmosDernoohilus leucurus
-
Sorex cinereus
Sorex merriami
Sorex vagrans
Sorex oahstris
Syrnlagrs idahoensis
Swrlagus nunallii
kous townseudii
Leous califorinicus
-
Myotis lucifugrs
Mvotis evoris
--
Mt otis thvsanodes
Mlrotis volans
Mvotis subulanus
-
Lasionvcteris noctivasen s
-
Eotesicus fucrs
-
Lasiuns cinereu
Euderma macularum
Conmorhinns townseudii
Odocoileus hemionu
AntilocaDra a-ericana
--
Cads latrans
Taxidea tixus
Mustela frenata
Mtstela ermina
Mephitrs mephitus
Soieole eracilis
-
Procyon lotor
Felis rufus
Great Basin Pocket Moue
Dark Kangaroo Morsc
Ord's lGngaroo Rat
Westeru Hanrest Moue
Canyou Moue
Deer Morse t'
Bruh Morse t*
Desert Wood Rat
Mrskrat
Nonheru Grasshopper Moue
Meadow Vole
Longtail Vole
Sagebnsh Vole
Lcast chipmunk
Yellow-bellied Marurot
White-tailed Antelope Squirrel
Masked Shrew
Merriam's Shrew
Vagrant Shrew
Northeru Water Shrew
BgEY rabbit
Nuttall's Conontail
White -tailcd Jackrabbit
Black-tailed Jachabbit
Little Brown Myotis
Long-eared Myotis
Fringed Myotis
I-oog-legged Myotis
Suall-footed Myotis
Silver Haired Bat
Big Broqm Bat
Hoary Bat
Spotted Bat
Tornnsend's Big-eared Bat
Mule Deer tt
Pronghoru
Coyote t'
Badger t'
Long-tailed Weasel
Ermine
Striped Skunk "
Westeru Sported Skunk
Raccoon
Bobcat tr
t* - Observed on Planr 78.
O Table 6.6 Summary of Fate of Contaminants of Concern in Abiotic Media
Primary RemovalWater Mechanism
1,1,1-TCA >365 > 180 > 180 Volatilization
TCE <10 l-12 Volatilization
Photooxidation
Source: EPA, 1986
Table 6.7 Average values of the environmental parameters used in the astimating of
contaminant volatilization fluxes from springs
Parameter Value
depth
widrh
linear velocity
wind qpeed
0.5 ft
5ft
1.5 ff/sec
9.8 fl/sec (3 m/sec)
I Table 6.8 Volatilization rate constants and mass transfer coefficiens for contaminants from
springs
Contaminant IvI\M
(g/mole)
tt
(m/sec)
k,
(drc)
HO lq
(m/sec)
1,1,1-TCA
TCE
133
131
1.26x104
L.27x104
3.52x10-3
3.53x10-3
1. 19x104
1. 15x104
0.59
0.37
Kr
K,
Kn
Ho
-
-
-
mass fransfer coefficient, liquid phase
mass transfer coefficient, gas phase
volatilization rate constant
Henry's I.aw Constant
Table 6.9 Maximum Exposure kvels Proposed for Conaminants in Surface Waters
Contaminated by Ground Water
MAXIMUM PREDICTED EXPOSIIRE POINT CONCENTRATION (mg/L)
CHEMICAL ffiLE\YEL
1r 1r I-TCA 0.2
TCE 0.027
O Table 6.10 Summary of Release Mechanisms and Flux Rates for springs
Flux
Rate
s
(mg/
m2-
sec)
Area of Release Mechanism 1,1,1-TCA TCE
Concern
Springs volatilization 2.38x1O2 3. 11x10-3
Table 6.11 Summary of Potential ARARs
Ambient Water Ouality Criteria (ug/L)
Chemical MCL Freshwater Life Human Healttr Human Health TLV
(ug/L)Water and Fish Only (mg/M3)
Fish
1,1,1-TCA 200 A: 1.84 x lff 1.03 x lff 1,900 (350)
C:
TCE 5 A: 4.5 x l0 8.07 x l0' 268(50)
C:
'r Values are for the 10{ risk level.
'r* As total trihalomethanes.
'r** Va1ues in parenthesis are in ppm.
No values available.A: Acute values, amy be criteria or lowest effet concentrations (LEC)
r@ommended by EPA.
C: Chronic values, may be criteria or lowest effect concentration (LEC)
recommended by EPA.
Table 6.L2 Summary of EPA Health Advisories for 1,1,,1 TCAI (mg/L).
Exposure Duration 1r 1r I-TCA
1 day (10kg child)
10 day (10 kg child)
Long term (10kg child)
I-ong term (70kg adult)
Lifetime (70 kg adult)
100
4G
40
100
0.2
t EPA, 1987az grre or ten day HA unavailable; EPA recommends the long term valueNA Not Applicable