DWQ-2008-020009

Recapture Reservoir
Limnological Assessment of Water Quality

Prepared for:

Utah Department of Environmental Quality -
Division of Water Quality

Mike Allred - Project Manager
Carl Adams - Project Supervisor

Prepared by:

Cirrus Ecological Solutions, LC

Recapture Reservoir
Limnological Assessment of Water Quality

Prepared for:

Utah Department of Environmental Quality
Division of Water Quality
TMDL Section

Mike Allred – Project Manager
Carl Adams – Project Supervisor
288 North 1460 West
Salt Lake City, Utah 84114-4870

Prepared by:

Cirrus Ecological Solutions, LC.
965 South 100 West, Suite 200
Logan, Utah 84321

Utah Department of Environmental Quality
Division of Water Quality
Watershed Protection Section

Recapture Reservoir

Waterbody ID UT-L-14080201-007
Location San Juan County, Utah
Pollutants of Concern Dissolved Oxygen
Impaired Beneficial Uses Class 3A: Protected for cold water species of game fish and other cold water
aquatic life, including the necessary aquatic organisms in their food chain.
Water Quality Assessment Average in-lake Total Phosphorus concentrations are 0.023–0.033 mg/L and do
not appear to significantly impact Dissolved Oxygen concentrations.

Reservoir profiles of Dissolved Oxygen in the spring season are influenced by
runoff volumes. Low Dissolved Oxygen (<4 mg/l) is evident at depth from June-
October during years of average-low precipitation.

Impairment of Class 3A fishery is evident based on reservoir profiles that
maintain low DO (< 4 mg/L) and elevated temperature (> 20°C).
Water Quality
Targets/Endpoints
Maintain 0.025 mg/l In-Lake Total P.
Maintain 0.05 mg/l Total P concentration in Recapture Creek, Johnson Creek,
Bulldog Creek, and Bullpup Creek.

Average annual TP load = 225 kg/year

Change fisheries beneficial use of reservoir from Class 3A (cold water) to Class
3B (warm water).

Seasonal site specific reservoir DO standard during July and August of 100
percent of DO measurements in the epilimnion of greater than 3 mg/L.

Implementation Strategy Implement CNMPs on agricultural lands adjacent to reservoir tributaries.

Implement and maintain livestock grazing BMPs on public land grazing
allotments.

Eliminate and/or maintain exclusion of livestock grazing below high water line.

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TABLE OF CONTENTS

Table of Contents ............................................................................................................................ ii
List of Tables .............................................................................................................................. iii
List of Figures ............................................................................................................................ iv

1.0 Introduction ............................................................................................................................... 1
1.1 TMDL Program Description ................................................................................................. 1
1.2 Previous Studies .................................................................................................................... 2
1.2.1 Recapture Creek Flow Assessment 1982 ....................................................................... 2
1.2.2 Recapture Reservoir Clean Lakes Study ....................................................................... 2
1.2.3 Utah State Water Plan – Southeast Colorado River Basin (2000) ................................. 3
1.3 Public Participation ............................................................................................................... 3

2.0 Project Area Description ........................................................................................................... 4
2.1 History ................................................................................................................................... 4
2.2 Watershed Description .......................................................................................................... 4
2.3 Climate .................................................................................................................................. 7
2.4 Geology/Soils ........................................................................................................................ 7
2.5 Land Cover and Land Use ..................................................................................................... 7
2.6 Hydrology ............................................................................................................................ 11
2.6.1 Annual Water Budget ................................................................................................... 14

3.0 Water Quality ......................................................................................................................... 15
3.1 Water Quality Standards..................................................................................................... 15
3.2 Water Quality Monitoring ................................................................................................... 16
3.2.1 Water Quality Monitoring Stations .............................................................................. 16
3.3 Existing Water Quality ........................................................................................................ 19
3.3.1 Surface Water Quality .................................................................................................. 20
3.3.1.1 Dissolved Oxygen ................................................................................................. 20
3.3.1.2 Total Phosphorus .................................................................................................. 22
3.3.1.3 Dissolved Phosphorus .......................................................................................... 26
3.3.1.4 pH ......................................................................................................................... 27
3.3.1.5 Total Suspended Solids ........................................................................................ 27
3.3.1.6 Nitrogen - Ammonia ............................................................................................. 27
3.3.1.7 Water Temperature ............................................................................................... 31
3.3.2 Groundwater Quality ................................................................................................... 31
3.3.3 Biological Data ............................................................................................................ 32
3.3.4 Trophic State Index ...................................................................................................... 38
3.4 Summary ............................................................................................................................. 42

4.0 Pollutant Source Characterization ........................................................................................... 43
4.1 Livestock Grazing ............................................................................................................... 43
4.2 Diffuse Runoff .................................................................................................................... 48
4.3 In-stream Pollutant Load Calculation ................................................................................. 53
4.4 Loading Source Summary .................................................................................................. 54

5.0 TMDL Analysis ....................................................................................................................... 56
5.1 Water Quality Targets ........................................................................................................ 60

iii
5.2 Permissible Loadings.......................................................................................................... 60
5.3 Seasonality .......................................................................................................................... 60
5.4 Margin of Safety ................................................................................................................. 60
5.5 TMDL Target Load ............................................................................................................. 61
5.6 Future Growth .................................................................................................................... 61
5.7 Allocation of Pollutant Loads ............................................................................................. 61

References ..................................................................................................................................... 63

LIST OF TABLES
Table 2.1. Subdivisions in Recapture Reservoir Watershed. ......................................................... 6
Table 2.2. Landcover types in the Recapture Reservoir watershed. ............................................... 9
Table 2.3. Land ownership within the Recapture Reservoir watershed. ...................................... 11
Table 2.4. Stream Flow Monitoring Stations in the Recapture TMDL project area. ................... 11
Table 2.5. Recapture reservoir project area daily stream flow by month (cfs). ........................... 13
Table 3.1. Beneficial use and associated water quality standards for impaired waterbodies
located in the Recapture Reservoir TMDL study area. .............................................. 15
Table 3.2. Water quality parameters associated with Class 3A reservoirs and streams. .............. 16
Table 3.3. Water quality monitoring stations identified in the Recapture TMDL project area. ... 17
Table 3.4. Water quality at three Recapture Reservoir monitoring sites. ..................................... 23
Table 3.5. Water quality at two Recapture Reservoir monitoring sites. ....................................... 28
Table 3.5. (cont’d) Water quality at two Recapture Reservoir monitoring sites. ........................ 29
Table 3.6. Groundwater quality data from well stations. ............................................................. 31
Table 3.7. Algae measurements collected from Recapture Reservoir.1........................................ 33
Table 3.8. Summary of habitat needs of Recapture Reservoir fish. ............................................. 34
Table 3.9. Description of lake trophic status based on Carlson TSI values. ................................ 39
Table 3.10. Trophic State Index (TSI) values for monitoring sites located on
Recapture Reservoir. ................................................................................................. 40
Table 4.1. Livestock grazing information associated with public lands in the Recapture
Reservoir TMDL project area. .................................................................................... 45
Table 4.2. Total phosphorus loads associated with livestock grazing in the Recapture
Reservoir TMDL project area..................................................................................... 47
Table 4.3. Total phosphorus loads from grazing to Recapture Reservoir defined by watershed
or by land owner. .......................................................................................................... 48
Table 4.4. Land use distribution in the Recapture Reservoir watershed. ..................................... 49
Table 4.5. Initial coefficients for phosphorus load runoff from land uses used in total
phosphorus runoff model. ............................................................................................ 50
Table 4.6. Incremental contributions and diversions of flow and phosphorus loads from
diffuse sources in the watersheds feeding Recapture Reservoir during an
average precipitation year. ............................................................................................ 51
Table 4.7. Modeled monthly runoff flows and total phosphorus loads to Recapture Reservoir
for average annual precipitation year. .......................................................................... 52
Table 4.8. Modeled monthly runoff flows and total phosphorus loads to Recapture Reservoir
for 2002 and 2005. ........................................................................................................ 52
Table 4.9. Annual total phosphorus loads (kg/year) by land use and landowner to
Recapture Reservoir for average annual precipitation year. ......................................... 53
Table 4.10. Annual total phosphorus loads (kg/year) by subwatershed and landowner
to Recapture Reservoir for average annual precipitation year. .................................... 53
Table 4.11. Measured daily total phosphorus loads from tributaries of Recapture Reservoir. ..... 55

iv
Table 5.1. Water quality at Recapture Reservoir monitoring sites. .............................................. 58
Table 5.2. Total phosphorus loading summary for Recapture Reservoir. ..................................... 62
Table 5.3. Allocation of permissible total phosphorus loadings to Recapture Reservoir by
land ownership............................................................................................................... 62

LIST OF FIGURES
Figure 2.1. Watershed subdivisions within the Recapture Reservoir TMDL project area. ............ 5
Figure 2.2. Land cover types within the Recapture Reservoir TMDL project area. ...................... 8
Figure 2.3. Land ownership within the Recapture Reservoir TMDL project area. ...................... 10
Figure 2.4. Stream flow monitoring stations within the Recapture Reservoir TMDL project
area. ........................................................................................................................... 12
Figure 3.1. Water quality monitoring stations within the Recapture Reservoir TMDL
project area. ............................................................................................................... 18
Figure 3.2. Available DO measurements collected from tributary streams to Recapture Reservoir
including Bulldog Canyon Creek and Johnson Creek. .............................................. 20
Figure 3.3. Selected reservoir DO and temperature profiles measured from monitoring
stations on Recapture Reservoir during 2005. ........................................................... 24
Figure 3.4. DO profiles observed at Recapture Reservoir Above Dam during 2005 and 2006. .. 25
Figure 3.5. Available TP measurements collected from tributary streams to Recapture
Reservoir including Johnson Creek and Bulldog Canyon Creek. ............................. 26
Figure 3.6. Total and Dissolved Phosphorus concentrations measured at Recapture
Reservoir monitoring locations during 2001-2006. .................................................... 30
Figure 3.7. Temperature profiles at three sites in Recapture Reservoir. ....................................... 32
Figure 3.8. Recapture Reservoir profiles measured August 14, 2001. ......................................... 36
Figure 3.9. Recapture Reservoir profiles measured August 31, 2005. ......................................... 37
Figure 3.10. Trophic State Index values calculated for Recapture Reservoir
including Chlorophyll a (Chl-a), Sechi Depth, and Total Phosphorus (TP). ........... 41
Figure 4.1. Livestock grazing allotments in the Recapture Reservoir TMDL project area. ......... 44

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1.0 INTRODUCTION

The Total Maximum Daily Load (TMDL) study for Recapture Reservoir in San Juan County,
Utah has been completed under the direction of the Utah Department of Environmental Quality –
Division of Water Quality (DWQ). This report will be submitted to the U.S. Environmental
Protection Agency (EPA) as specified by section 303(d) of the Clean Water Act (CWA). The
assessment of water quality and flow defines conditions leading to low concentrations of
Dissolved Oxygen (DO) in the reservoir, located in the eastern portion of San Juan County. This
assessment relies upon recent and historic monitoring data collected in the study area and as such,
provides an accurate picture of existing water quality conditions while incorporating the longer-
term climatic influences that affect the greater Recapture Reservoir watershed.

There are many factors influencing water quality in Recapture Reservoir. It is not the intent of
this assessment to place blame or criticism on any individual or group, but to try and provide an
accurate characterization of all conditions that lead to water quality impairment in the study area.

1.1 TMDL PROGRAM DESCRIPTION
The TMDL program was one of several programs established in connection with the 1977
amendments to the Clean Water Act to maintain and restore water quality to waters of the United
States. A specific goal of the TMDL program is to ensure that water quality standards established
by states are achieved and maintained. A critical element of the TMDL process identifies the
maximum amount of pollutant that a water body can receive and still meet water quality
standards. This amount is sometimes called the maximum allowable pollutant load or
“permissible load”. If appropriate, the TMDL can associate the permissible load with a critical
time period including months of low stream flow.

The scientific assessment of water quality included as part of a TMDL incorporates the best
information available to determine the nature and extent of impairment for a given water body.
Pollutant loads are also defined for each significant pollutant source contributing to impairment.
Pollutants can come from point sources, such as water treatment plants and concentrated animal
feeding operations, and nonpoint sources, such as agricultural areas and eroding streambanks.
Following source identification and allocation of pollutant loads, an implementation plan is
provided that will reduce existing pollutant loads and allow water quality standards to be
achieved.

The TMDL process is a shift from the more generalized approaches employed in the past to
implement the CWA. It demands a local focus on the target watershed, from both a scientific and
an applied perspective. Water quality standards that are broadly applied can be carefully
evaluated under this process in terms of restoring and maintaining beneficial uses under actual
conditions that influence water quality. Successful implementation of this assessment will
require cooperation between federal, state, and local entities, and will include local stakeholders
living within the study area.

2

1.2 PREVIOUS STUDIES
Water quality and streamflow in the Recapture Reservoir project area were regularly monitored
by federal and state agencies from 1957-1980 for the Indian Creek Tunnel, from 1965-2006 for a
site on upper Recapture Creek, and from 1975-1993 for a site on lower Recapture Creek (below
the confluence with Johnson Creek). Routine water quality measurements have been made from
1997 to present at a site on Johnson Creek approximately 5.5 miles upstream from the reservoir,
in 1978 where Route 163 crossed Recapture Creek prior to construction of the reservoir, from
1988 to 2000 on Bulldog Creek just above its outfall to the reservoir, and from 1989 to 2006 for
three sites within the reservoir.

Two studies have focused specifically on Recapture Reservoir, including a flow assessment that
was completed on the upper Recapture Creek watershed to fulfill Army Corp of Engineer
permitting requirements prior to construction of the reservoir (UDWR 1981). The other local
study was completed by DWQ on Recapture Reservoir as part of an EPA sponsored Clean Lakes
study that reviewed water quality in all reservoirs and lakes in Utah. (Judd 1997.) Published
studies have more typically incorporated the watershed above Recapture Reservoir as part of
research that examined all or portions of larger river basins including the San Juan River or
Colorado River. A brief review of studies completed to date is included below.

1.2.1 RECAPTURE CREEK FLOW ASSESSMENT 1982
The Utah Division of Water Resources prepared a report in 1982 to support their request to
include the construction of Recapture Reservoir within the category of Nationwide Permits with
respect to Section 404 requirements of the Clean Water Act, as administered by the U.S. Army
Corps of Engineers. In this report, UDWR developed a model for predicting runoff to the
Recapture Reservoir watershed. It included a calculation of “natural flow” to a stream gage on
Recapture Creek Below Johnson Creek that was only three years old by correlating its flows to
those at other, older gage sites on Recapture Creek (within the reservoir’s watershed) and Indian
Creek 15 miles to the north (and outside the reservoir’s watershed). UDWR used an “Elevation-
Precipitation Curve for Abajo Mountain Area” and then a “Precipitation-Runoff Curve for South
and East Colorado Area” to develop “Unit Runoff” factors in acre-feet per square mile for each
1,000 foot elevation band. The result was an estimate of average annual natural flow to the gage
at Recapture Creek Below Johnson Creek of 4,402 acre-feet per year, and flow to the reservoir
site (after accounting for diversions and other tributaries) of 2.3 cfs, or 1,616 acre-feet per year.
New calculations for the watershed indicate that UDWR’s calculations of national flow to the
reservoir site may have underestimated flows by as much as 4,500 acre-feet per year.

1.2.2 RECAPTURE RESERVOIR CLEAN LAKES STUDY
This study provides a brief overview of the history and geology of Recapture Reservoir, and
discusses its characteristics such as area, volume, and retention time. Beneficial uses of the
reservoir are also detailed, as well as recreational opportunities in the area. Some information on
fisheries management in the reservoir is also provided.

STORET water quality data from 1989 and 1991 from the three water quality stations in the
reservoir are summarized. Profile measurements for DO and temperature are also given. DO
results show concentrations of <4 mg/l at depths below 4 meters. Slight exceedances of the total

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phosphorus (TP) indicator value were recorded in 1991. Phytoplankton data shows that green
algae are predominant.

Pollution sources were identified, and sedimentation and nutrient loading from grazing and feed
yards and wastes or litter from recreation were listed. No point sources were identified.

1.2.3 UTAH STATE WATER PLAN – SOUTHEAST COLORADO RIVER BASIN
(2000)
As part of the State of Utah’s goal of providing a framework for state water policy planning, a
detailed water plan was prepared for the Southeast Colorado River Basin, which includes the
Recapture River watershed. This plan discusses the Basin’s water-related resources and the
problems, needs, issues and alternatives for conservation and development measures. While the
plan covers a wide area, useful information on Recapture Reservoir and its tributaries is found
within this document. The main focus of the plan is the conservation and development of water
supplies within the Basin.

The plan declared surface water quality in the Basin to be “generally of suitable chemical quality
for agricultural, municipal and industrial uses.” Total dissolved solids (TDS) were said to
increase with distance downstream due to lower quality groundwater inflow and return flows
from irrigation. Data for TDS and conductivity were provided for selected stations.

1.3 PUBLIC PARTICIPATION
Federal and local agencies were contacted during April 2007 to provide notification that a TMDL
assessment was being completed for Recapture Reservoir. Personnel from each agency were
invited to participate in a stakeholder review process at that time.

Public review of the Draft TMDL report will commence in February 2008. Comments will be
accepted from the public following a 30-day review period and incorporated into the final TMDL
report submitted to the EPA on April 1, 2008.

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2.0 PROJECT AREA DESCRIPTION

2.1 HISTORY
The area around Recapture Reservoir was settled by Mormon pioneers in the late 1800s.
Blanding, two and a half miles southwest of the reservoir, is the closest town and was the last to
be established in San Juan County when it was founded in 1897.

Large-scale cattle ranching came to the area when the LC Cattle Company was established
around 1880. The company grazed about 17,000 head of cattle near the confluence of Recapture
and Johnson Creeks in the south end of the Recapture Reservoir watershed. Several other large
companies also brought cattle to the area. Most of these companies were gone by the late 1890s
as a result of low cattle prices, drought, rustlers, and other factors. (UDWR 2000)

Early settlers used water from streams from the Abajo Mountains north of Blanding for
agricultural irrigation. As the town grew and water demand increased an irrigation company
began a tunnel project to divert yet more water from Indian Creek on the north side of the Abajo
Mountains to Johnson Creek on the south side. Started in 1921, the tunnel was completed in
1952. Another interbasin diversion now part of the Recapture Reservoir watershed includes a
catchment and canal from Dry Wash on the west into Johnson Creek.

Recapture Creek was impounded in the early 1980’s with an earthen dam, which is crossed by
Highway 191 north of Blanding. Most of the water stored in the reservoir is used for agriculture,
although the city of Blanding occasionally withdraws water for municipal use. (Judd 1997,
Thorton 2007)

2.2 WATERSHED DESCRIPTION
The Recapture Reservoir watershed is entirely within the area designated by the USGS as the
Upper Colorado Region, Hydrologic Unit Code (HUC) 14, which eventually flows into the San
Juan River, and thence into the Colorado River. For the purposes of this project, the Recapture
Reservoir watershed is drawn to include two smaller watersheds outside of its natural drainage to
accommodate diversions from Indian Creek to the north and Dry Wash to the west. Other minor
subdivisions within the Recapture Reservoir watershed that feed diversions or stream confluences
were also identified and named for reference in this project. The entire watershed is 64.29 square
miles (41,143 acres) in size. See Figure 2.1 for a map of the watershed and Table 2.1 for
descriptions of the smaller subdivisions.

5

Figure 2.1. Watershed subdivisions within the Recapture Reservoir TMDL project area.

6
The Recapture Reservoir watershed is drained by four streams flowing north to south. The largest
stream is Johnson Creek, which forms at approximately 11,000 feet in elevation just west of
Abajo Peak. Flow from Indian Creek Tunnel comes from a diversion in the upper Indian Creek
watershed at about 9,100 feet above sea level and brings water approximately 1-3/4 mile through
a tunnel in the mountain to enter Johnson Creek at about 8,200 feet elevation. At about 7,700 feet
elevation, a diversion from Johnson Creek feeds the Blanding municipal pipeline. The canal from
Dry Wash enters the western boundary of the watershed at about 8,000 feet elevation and is
collected in a small reservoir at about 7,700 feet before being drained via a natural watercourse to
reach Johnson Creek at about 7,100 feet elevation. At about 6,800 feet elevation, the Upper Canal
diverts Johnson Creek water during the late spring, summer, and early fall. This canal leaves the
southwest corner of the watershed roughly parallel to and 200 feet below the Blanding Pipeline to
feed two small surface reservoirs approximately two miles north of Blanding. Below the Upper
Canal diversion, Johnson Creek flows unimpeded to the confluence with Recapture Creek at
approximately 6,100 feet elevation.

Recapture Creek rises at approximately 10,000 feet elevation from the south side of the Abajo
Mountains as two parallel drainages that form the northeast corner of the watershed. It is not
diverted by canals or pipelines and is joined by Johnson Creek at approximately 6,100 feet
elevation. About 0.3 miles and 50 feet of elevation below the confluence with Johnson Creek, a
diversion to feed the Lower Canal had been built, but is now abandoned. Recapture Creek enters
Recapture Reservoir between the reservoir’s design elevations of 5,940 (0 acre-feet volume) and
6,080 (17,500 acre-feet volume) feet above sea level.

The eastern third of the watershed is drained by two named tributaries, Bulldog and Bullpup
Creeks. Bulldog rises at about 8,000 feet elevation and drains most of the east side of the
watershed. A much smaller Bullpup Creek forms the southeast portion of the watershed. Both
tributaries drain directly into Recapture Reservoir.

Table 2.1. Subdivisions in Recapture Reservoir Watershed.
Subwatershed Area (ac) Watershed Subdivision Area (ac) 8 Digit HUC1
Johnson Creek 17,649 Indian Creek Tunnel2 1,547 14030005
Blanding pipeline 5,275 14080201
Dry Wash2 560 14080201
Upper Johnson Creek 6,546 14080201
Upper canal 1,312 14080201
Lower Johnson Creek 2,408 14080201
Recapture
Creek
8,285 Upper Recapture Creek 2,404 14080201
Lower Recapture Creek 5,881 14080201
Recapture
Reservoir
14,700 Bulldog Creek 10,507 14080201
Bullpup Creek 3,167 14080201
Recapture Reservoir 1,026 14080201
Other 509 Lower canal3 509 14080201
Total 41,143
(64.29 sq mi)

1 May be partial Hydrologic Unit Code. 2 Drainages for interbasin transfers from adjacent watersheds. 3 Assumed entire area drains outside of Recapture Reservoir watershed.

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2.3 CLIMATE
The climate in southeast Utah is arid to semi-arid. Average monthly maximum temperatures in
summer are in the high 90s (oF) and average monthly minimum temperatures in December and
January winter are 3-10oF. Annual average precipitation is approximately 13.3 inches in
Blanding. The average precipitation for 2001-2007, the years of most data on surface water flows,
was 12.95 inches, although rainfall was below average in 2002 (8.0 inches) and above average in
2005 (16.7 inches).

The watershed spans a broad range of precipitation bands, however, from 13 inches per year near
Blanding to over 39 inches at the top of the Abajo Mountains. Precipitation from these higher
elevations generate much of the runoff that feeds into Recapture Reservoir (UDWR 2000).

The monthly Palmer Drought Indices in 2007 put all of southeastern Utah in the mid-range of
moisture (through October), indicating that available moisture in the area is neither deficient nor
abundant.

2.4 GEOLOGY/SOILS
Recapture Reservoir lies within the Paradox Basin, a large depression on the southwest flank of
the Uncompahgre uplift. This basin was repeatedly filled with seawater 300 million years ago,
which deposited carbonate-rich sediments that became limestone and dolomite strata. The
Paradox basin covers approximately 20,000 square miles, including most of San Juan County. As
seawater receded, salt and other saline deposits were left behind and now underlie the Paradox
Basin. Eroded material was transported by prehistoric rivers flowing into the basin, creating
alluvial fans, deltas, and tidal flats that are rich in clay, copper, uranium, vanadium, gold, and
silver as well as oil and gas deposits that formed from decomposed organic matter. The Abajo
Mountains located to the north of Blanding were formed by igneous intrusions nearly 25 million
years ago and exceed 11,000 feet in elevation. This isolated mountain range is comprised of
dramatic granite features that are visible from many miles away. The highest elevation in the
Recapture Reservoir watershed is found along the ridges near Abajo Peak at 11,295 feet above
sea level. The reservoir itself is approximately 6,080 feet above sea level at is inlet, resulting in a
mean surface gradient of approximately 9 percent.

Soils in the Recapture Reservoir drainage are generally very stony and well-drained. These soils
are mainly formed by aeolian deposits or colluvium derived from sandstone. Approximately 2
percent of watershed soils are considered farmland of statewide importance. Such soils typically
consist of very fine sandy loam.

2.5 LAND COVER AND LAND USE
Land cover in the project area was mapped from the dataset provided by the Southwest Regional
Gap Analysis Project, completed in 2005 by the Remote Sensing/Geographic Information
Systems Laboratory at Utah State University (USURS/GISL). Land cover types were then
combined into broader categories for which data was available for phosphorus export coefficients
(Figure 2.2). The land cover types, analysis categories and acreages within the Recapture
Reservoir watershed are summarized in Table 2.2. Forest land covers 18,673 acres, or 45.4
percent of the watershed. Pinyon-juniper was the next largest, covering 16,713 acres, or 40.6
percent of the watershed.

8

Figure 2.2. Land cover types within the Recapture Reservoir TMDL project area.

9

Table 2.2. Landcover types in the Recapture Reservoir watershed.
Analysis
Category
Area
(ac)
% of
Total
SWReGap Landcover Type Area
(ac)
Forest Land 18,673 45.4 Inter-Mountain West Aspen-Mixed Conifer Forest
and Woodland Complex
9,578
Rocky Mountain Aspen Forest and Woodland 2,250
Rocky Mountain Gambel Oak-Mixed Montane
Shrubland
8,294
Rocky Mountain Lower Montane Riparian
Woodland and Shrubland
567
Rocky Mountain Montane Dry-Mesic Mixed
Conifer Forest and Woodland
38
Rocky Mountain Montane Mesic Mixed Conifer
Forest and Woodland
30
Rocky Mountain Ponderosa Pine Woodland 5,674
Rocky Mountain Subalpine Dry-Mesic Spruce-Fir
Forest and Woodland
607
Rocky Mountain Subalpine Mesic Spruce-Fir
Forest and Woodland
256
Pinyon-
Juniper
16,713 40.6 Colorado Plateau Pinyon-Juniper Shrubland 327
Colorado Plateau Pinyon-Juniper Woodland 16,385
Range
Land
3,802 9.2 Inter-Mountain Basins Big Sagebrush Shrubland 2,104
Inter-Mountain Basins Greasewood Flat 0.2
Inter-Mountain Basins Mat Saltbush Shrubland 1
Inter-Mountain Basins Mixed Salt Desert Scrub 0.1
Inter-Mountain Basins Montane Sagebrush Steppe 1,523
Inter-Mountain Basins Semi-Desert Grassland 6
Inter-Mountain Basins Semi-Desert Shrub Steppe 0.8
Rocky Mountain Subalpine Mesic Meadow 167
Agriculture 1,142 2.8 Agriculture 1,142
Barren 611 1.5 Colorado Plateau Mixed Bedrock Canyon and
Tableland
6
Rocky Mountain Alpine Bedrock and Scree 574
Rocky Mountain Cliff and Canyon 31
Water 201 0.5 Open Water 201
Urban 2 0.01 Developed, Medium - High Intensity 1
Developed, Open Space - Low Intensity 1
Total 41,143 41,143

Landownership within the watershed is dominated by federal holdings. The largest landowner is
the US Forest Service, which administers 26,644 acres (65 percent of the watershed). The BLM
administers 7,332 acres (18 percent of the watershed). Only 5,838 acres (14 percent of the
watershed) is privately owned. The primary land use in the watershed is livestock grazing. Other
common uses include agriculture, energy development, and dispersed recreation. Figure 2.3 and
Table 2.3 show land ownership in the Recapture Reservoir watershed.

10

Figure 2.3. Land ownership within the Recapture Reservoir TMDL project area.

11

Table 2.3. Land ownership within the Recapture Reservoir watershed.
Land Ownership Area (ac) Percent of Total
US Forest Service (USFS) 26,644 65
Bureau of Land Management (BLM) 7,332 18
State 1,329 3
Private 5,838 14
Total 41,143 100

2.6 HYDROLOGY

Table 2.4 lists sites where reasonably long term measurements of stream flow have been made in
the Recapture Reservoir watershed. Figure 2.4 shows the locations of these stations.

Table 2.4. Stream Flow Monitoring Stations in the Recapture TMDL project area.
Station Station Name Agency Type Period of Record
9185800 Indian Creek Tunnel near
Monticello, Utah1
USGS Stream October 1957-
September 1980
9378630 Recapture Creek near Blanding,
Utah
USGS Stream October 1965-
September 2006
9378650 Recapture Creek below Johnson
Creek near Blanding, Utah
USGS Stream October 1975-
October 1993
N/A Blanding Pipeline Blanding City Pipeline January 2002-
December 2007
N/A Recapture Reservoir Discharge San Juan Water
Conservancy
District
Stream 2001 - present
1 Station located outside of the natural watershed of Recapture Reservoir but included because entire
runoff of this watershed subdivision is assumed to be diverted into the watershed via a tunnel.

Stream flows in the Recapture Reservoir watershed have been reported by various entities. The
USGS has monitored three sites on a daily basis: Indian Creek Tunnel Station 9185800,
Recapture Creek Near Blanding Station 9378630, and Recapture Creek Below Johnson Creek
Station 9378650. Blanding City reports flows into their pipeline from the diversion on Johnson
Creek. The San Juan Water Conservancy District (SJWCD) reports flows at the Recapture
Reservoir discharge and measures the elevation of the reservoir occasionally during the spring,
summer, and fall, from which a volume can be calculated.

No flow gages are known to exist for interbasin transfers from Dry Wash, nor for diversions into
the Upper Canal. Anecdotal reports on the latter, however, claim a maximum capacity of 10 cfs,
and that seasonal flows are typically 7-9 cfs (Palmer 2008).

12

Figure 2.4. Stream flow monitoring stations within the Recapture Reservoir TMDL project
area.

13

Stream flows are also measured by the Utah Division of Water Quality when taking water quality
measurements, but these are infrequent and were therefore not used for determining temporal
patterns of stream flow in the watershed.

Anecdotal reports are that Bulldog and Bullpup Creeks provide flows to the reservoir only during
runoff events.

Table 2.5 shows a summary of daily stream flows by month for long term gages in the Recapture
Reservoir watershed. All three of the gauged streams are seasonal in nature, with peak flows
between April and June, and lowest (or no) flows from August through February. Indian Creek
peaks slightly earlier than Recapture or Johnson Creeks as expected due to the influence of
snowmelt at higher elevations. Average monthly flows for upper Recapture Creek (Station
9378630) are typically less than 10 cfs, while downstream after the confluence with Johnson
Creek, the gage shows average monthly flows above 30 cfs in late spring. The latter flows would
be even higher if not for the diversions into the Blanding Pipeline and the Upper Canal in the
upper reaches of Johnson Creek. The maximum flow of 57 cfs in Recapture Creek was evidently
due to a major storm that occurred October 19-20, 1972. Maximum flows at the lower Recapture
Creek Below Johnson Creek have peaked at over 212 cfs.

Table 2.5. Recapture reservoir project area daily stream flow by month (cfs).

USGS 9378630 –
Recapture Creek
near Blanding
USGS 9378650 -
Recapture Creek
Below Johnson
Creek Near
Blanding
USGS 9185800 -
Indian Creek
Tunnel near
Monticello
SJWCD - Recapture
Reservoir Discharge
Month Mean Min Max Mean Min Max Mean Min Max Mean Min Max
Jan 0.1 0.0 6.9 0.1 0.0 2.9 0.3 0.0 1.0 0.4 N/A N/A
Feb 0.1 0.0 3.5 1.4 0.0 26.0 0.3 0.0 1.0 0.8 N/A N/A
Mar 1.7 0.0 26.0 10.5 0.0 128.0 0.4 0.0 5.0 0.9 N/A N/A
Apr 4.7 0.0 50.0 35.1 0.0 200.0 1.3 0.0 13.0 2.3 N/A N/A
May 6.0 0.0 46.0 37.9 0.0 212.0 4.7 0.0 21.0 5.7 N/A N/A
Jun 2.0 0.0 31.0 15.3 0.0 129.0 5.9 0.0 18.0 5.4 N/A N/A
Jul 0.2 0.0 4.2 1.5 0.0 27.0 2.2 0.1 18.0 4.8 N/A N/A
Aug 0.1 0.0 6.0 0.2 0.0 18.0 0.9 0.0 7.3 4.3 N/A N/A
Sep 0.0 0.0 1.2 0.2 0.0 15.0 0.6 0.0 3.2 3.0 N/A N/A
Oct 0.1 0.0 57.0 0.4 0.0 24.0 0.8 0.0 7.1 1.7 N/A N/A
Nov 0.1 0.0 19.0 1.0 0.0 80.0 0.6 0.0 5.9 0.4 N/A N/A
Dec 0.0 0.0 7.1 0.1 0.0 2.6 0.3 0.0 3.2 0.3 N/A N/A
Summary 1.3 0.0 57.0 8.6 0.0 212.0 1.5 0.0 21.0 2.5 N/A N/A

Available measurements of Recapture Reservoir discharges were limited to a six year period
since 2001 and generally included one or more measurements per month with the exception of
mid-winter. Monthly discharge from the reservoir is managed, so flows are more even through
the year than the flows in the tributaries, with monthly average flows ranging from 0.3 cfs in
December to 5.7 cfs in May. Since measurements are not made on a daily basis, daily minimum
and maximums are not available.

14

Water in Recapture Reservoir is managed by the San Juan County Water Conservancy District.
Most water stored in the reservoir is ultimately used for agricultural purposes. The city of
Blanding owns a right to 800 acre-feet of the reservoir for municipal use, but only withdraws
water during years of low precipitation. The most recent municipal use of reservoir storage by
Blanding occurred in 2002 when 284 acre-feet were withdrawn during July and August. Blanding
City and the Blanding Irrigation Company also divert water from Recapture Creek and Johnson
Creek before flows can reach Recapture Reservoir. Blanding City has a 1 cfs water right from
Johnson Creek and a 2 cfs water right from Indian Creek which is diverted through the Abajo
Peak tunnel.

2.6.1 ANNUAL WATER BUDGET
In order to understand long term patterns of flow and nutrient loads to Recapture Reservoir, a
model was constructed to estimate present day runoff to the reservoir. This model was based on
an area-altitude approach described in a letter and accompanying analysis produced by the Utah
Division of Water Resources (UDWR) dated January 27, 1982 in support of their request to
include the Recapture Dam construction project under the Nationwide Permits provisions of
Section 404 of the Clean Water Act, administered by the U.S. Environmental Protection Agency.

A present day model faces similar challenges as those encountered by UDWR in 1981.
Specifically, there are few monitoring stations and limited periods of data and, while the lower
Recapture Creek Below Johnson Creek gage has now produced 18 years of data, those data ended
in 1993. The upper Recapture Creek Near Blanding gage also has a longer period of record,
although the most recent data available were recorded in September 2006. Moreover, diversion
flows to the Upper Canal and the contributions of Dry Wash, Bulldog Creek, and Bullpup Creeks
are only anecdotal. On the other hand, actual flow data is now available for the Blanding Pipeline
for the last 7 years, and there is a record of discharge from the reservoir itself back to at least mid-
2001. New Geographic Information Systems (GIS) mapping analysis and spreadsheet tools
cannot recreate actual data on flows, but they help improve the speed and resolution of analysis.

A variation on the area-altitude approach used by UDWR was used for this TMDL analysis (see
Appendix B). The watershed for the Recapture Reservoir was first delineated using GIS layers of
streams superimposed on USGS topographic maps. The watershed subdivisions contributing
interbasin transfers from Indian Creek and Dry Wash were included, as were those areas draining
directly into the reservoir near the dam. The result was a layer of 12 watershed subdivisions (see
Figure 2.1 and Table 2.1).

The original UDWR values for runoff as a function of precipitation were reproduced in a table
and similar normalization steps were taken to generate new “Unit Runoff” values, yielding a
formula for calculating acre-feet per year per square mile as a function of precipitation. These
unit runoff values were then fit to an exponential function which was adjusted by successive
approximation to get the best fit for the upper Recapture Creek Near Blanding watershed because
that smaller watershed has the longest and most recent period of record and no diversions. It was
then adjusted once more to minimize error when applied to the gages at Recapture Creek Below
Johnson Creek and Recapture Reservoir itself. The resulting model still produced some error due
to the limited data available, but proved a more accurate predictor of flows to Recapture
Reservoir than did the earlier work.

15

3.0 WATER QUALITY

The Utah Division of Water Quality (UDWQ) and the United States Geological Survey (USGS)
have been involved with water quality monitoring in the Recapture Reservoir basin. Water
quality data have also been collected by the US Forest Service and the Utah Department of
Health. The record of water quality monitoring data reviewed in this assessment extends from
1950 through 2007. The exact length of the data record varies depending on the monitoring site
and the agency responsible for data collection. Where possible, water quality data collected in
the past 10 years (1998-2007) is used to represent existing conditions. An assessment of existing
conditions has indicated that water quality measurements in the study area violate water quality
criteria designed to protect the beneficial use of Recapture Reservoir and tributaries that flow to
the reservoir. This chapter is a detailed assessment of these measurements and provides the basis
for the Recapture Reservoir TMDL that is presented in Chapter 5.

3.1 WATER QUALITY STANDARDS
The water quality standards and goals are based on the designated use of water bodies adopted by
the state to protect public health and welfare, enhance water quality, and protect those assigned
beneficial uses (e.g. aquatic life, recreation, and agricultural use). The Utah 2006 303(d) list
indicated Recapture Reservoir is impaired for low dissolved oxygen (DO) concentrations. The
beneficial use and associated water quality standards for impaired conditions at Recapture
Reservoir are shown in Table 3.1.

Table 3.1. Beneficial use and associated water quality standards for impaired waterbodies
located in the Recapture Reservoir TMDL study area.
Name Pollutant of
concern
Beneficial Use
Class
Beneficial Use
Support
Standard / Indicator
Value
Recapture
Reservoir
Dissolved
oxygen (DO)
3A – Cold water
aquatic life Non-supporting DO ≥ 4.0 mg/L

In general, impairment to water bodies is based on water quality parameters including
temperature, pH, and DO (Table 3.2). Measurements of these parameters are collected during
routine monitoring by the State of Utah. At stream monitoring stations, full support status is
assigned to the water body if less than 10 percent of measurements for any of these water quality
parameters exceed the established criteria. Non-support status is assigned when exceedance is
greater than 10 percent. Exceptions to these thresholds are made for DO in lakes and reservoirs
where water quality is modified in deep impoundments due to stratification. In these situations,
non-support status is determined if 50 percent of profile measurements are less than 4.0 mg/L.

The total phosphorus (TP) value used by the State of Utah to determine impairment is an
indicator of pollution and is not a numeric criterion or water quality standard. As a result, Utah
does not consider a water body to be impaired based solely on exceedances of the TP indicator
value alone. Desired concentrations of TP applied to reservoirs and streams are 0.025 mg/l and
0.05 mg/l, respectively. These values have been shown to represent threshold values that prevent

16
eutrophication and excessive algae growth. Excessive growth and decomposition of algae and
zooplankton can deplete DO concentrations to levels that are harmful to fish. The acute DO
criteria for early and adult life stages in streams are greater than or equal to 8 mg/L and 4 mg/L,
respectively. The chronic, 30-day average DO criterion is greater than or equal to 6.5 mg/L. In
addition to these parameters, other measures of water quality health are used to support a
beneficial use assessment. Some of these measures include fish surveys, phytoplankton, and
macroinvertebrate assessments. A detailed review of existing water quality measurements in the
project area as well as measurements of fish, algae and macroinvertebrate populations are
provided below.

Table 3.2. Water quality parameters associated with Class 3A reservoirs and streams.
Parameter Standard/Indicator Level
Ammonia pH dependent criteria calculated for individual data points
as per Utah Code R317-2.
Dissolved Oxygen (DO) 4.0 mg/L acute criterion for adult coldwater aquatic species.
pH 6.5 - 9.0
Total Dissolved Solids (TDS) 1,200 mg/L
Total Phosphorus (TP)* 0.05 mg/L
Water Temperature 20 oC
* Pollution indicator value.

3.2 WATER QUALITY MONITORING
Compiling and accurately interpreting water quality and flow data are critical elements of a
TMDL assessment. The concentration of a particular pollutant and flow can be used to calculate
its load equivalent as mass per unit time (e.g., kg/yr). If paired measurements of flow and water
quality are collected at regular intervals and at the appropriate locations, these measurements can
be used to validate loads allocated to different pollutant sources. Available measurements of flow
were presented earlier in Section 2.

Members of the Cirrus team obtained the majority of data from publicly accessible repositories
including the EPA-STORET database, the Utah DWQ database, and the USGS National Water
Information System (NWIS) data archives. In addition, Cirrus contacted all pertinent agencies
and stakeholders within the TMDL study area with the ability to provide additional data and
information that could be used to characterize pollutant sources.

This water quality assessment reviews all available water quality data for the study area. The
assessment relies primarily upon water quality data collected by the Utah DWQ during intensive
monitoring cycles. As this information was collected on a regular basis, it provides a
comprehensive review of water quality conditions in the study area. The most recent data
considered in this assessment was collected during 2007.

3.2.1 WATER QUALITY MONITORING STATIONS
Water quality measurements have been collected at 15 monitoring sites in the project area (Figure
3.1). Summary details for each station are provided in Table 3.3. Information on the period of

17
record and frequency of water quality measurements collected at each station are provided in
Table A1 (Appendix A). Although the USGS has consistently monitored water quality at stream
gage sites dating back to 1971, this data set is primarily limited to measurements of temperature
and specific conductivity. The Utah DWQ has collected a much wider range of surface water
quality measurements to date, extending back to the mid-1970s. The USGS has collected the
only measurements of groundwater quality, including 2 locations near Recapture Reservoir.
Only two stream stations have long-term records that also include recent measurements of water
quality. Station 4953460 is located on Johnson Creek above the upper canal diversion and about
5.5 miles upstream of the reservoir. This station has data from 1997 – 2006. The other station
with a comprehensive data record is Bulldog Canyon Creek above Recapture Reservoir (Station
4953510), near the reservoir high water mark. This station has data from 1988 – 2001.

Table 3.3. Water quality monitoring stations identified in the Recapture TMDL project area.
Station Station Name Agency Type Period of
Record
Number of
sample visits
5958010 Recapture Reservoir above
dam 001.
DWQ Lake 1989 - 2005 19
5958020 Recapture Reservoir 1/4 way
up reservoir 02.
DWQ Lake 1989 - 2005 18
5958030 Recapture Reservoir 1/2 way
up reservoir 03.
DWQ Lake 1989 - 2005 19
4953460
Johnson Creek above
Recapture Reservoir above
diversion.
DWQ Stream 1997 - 2005 23
4953500
Recapture Creek wash at
U163(191) crossing below
reservoir.
DWQ
Stream
1978 - 2000 3
4953510 Bulldog Canyon Creek above
Recapture Reservoir.
DWQ Stream 1998 - 2001 42
1900101 Blanding-Johnson Creek 1. Dept. of
Health
Stream 1977 - 1989 7
1900102 Blanding-Indian Creek. Dept. of
Health
Stream 1981 - 1987 3
1005010522511 Upper Indian Creek. USFS Stream 1980 4
100501251351 Johnson Creek at Blanding
Pipeline inlet.
USFS Stream 1980 3
9185800 Indian Creek Tunnel near
Monticello, Utah
USGS 1971 - 1980 64
9378630 Recapture Creek near
Blanding, Utah
USGS 1971 – 1991 128
9378650 Recapture Creek below
Johnson Creek near Blanding,
Utah
USGS
1977 - 1994 104
373954109270001 (D-36-22)12ccd-1 USGS Well 1982 1
374726109303001 (D-34-22)28caa-1 USGS Well 1977 1
1 Station located outside of the Recapture Reservoir watershed on upper Indian Creek upstream of the Indian Creek
tunnel inlet.

18
Figure 3.1. Water quality monitoring stations within the Recapture Reservoir TMDL
project area.

19
Three monitoring stations are located on the reservoir itself including Station 5958010 –
Recapture Reservoir above dam 001, Station 5958020 – Recapture Reservoir 1/4 way up
reservoir 02, and Station 5958030 – Recapture Reservoir 1/2 way up reservoir 03. For discussion
purposes these stations will be referred to as Station 01, Station 02, and Station 03, respectively.
Water quality records from these stations extend from 1989-2006 with consistent summer season
profile measurements beginning in 2001. All reservoir measurements of water quality were
collected by DWQ and include the parameters of concern addressed in this TMDL. The most
intensely studied year of reservoir monitoring occurred in 2005 when each station was visited
once per month during June, July, August, and October.

3.3 EXISTING WATER QUALITY
An assessment of water quality conditions in the Recapture Reservoir watershed has indicated
that concentrations of DO and TP in the study area generally meet the criteria for the aquatic
wildlife beneficial use (Class 3A), with the exception of some profile measurements of DO at
reservoir monitoring stations. Both DO and TP drive important chemical and biological
processes that support viable aquatic habitat. Dissolved oxygen can be heavily influenced by
temperature, as well as surface reaeration, mixing of the water column, plant photosynthesis and
respiration, and high concentrations of nutrients and organic matter.

In general, the concentration of DO is inversely related to water temperature. Cold water
temperatures increase the solubility of DO and allow a given water volume to contain greater DO
concentrations. Atmospheric oxygen influences aquatic systems through surface reaeration. This
process is induced by turbulence created as water flows across roughened channel surfaces or
from wind moving across the water surface of lakes and reservoirs. Mixing of stratified water
volumes can occur as tributary streams flow into lakes and reservoirs. Additional mixing can
occur when thermal profiles shift during the fall season as reservoir surface layers become colder,
denser and ultimately settle to the bottom to force deep water volumes back to the surface. This
process is commonly referred to as fall turnover.

Oxygen is also introduced to the water column by photosynthesis of aquatic plants. However, if
high levels of light and nutrients are present, algae populations will rapidly increase, resulting in
large diurnal swings of DO concentrations. These diurnal cycles caused by photosynthesis can
exceed saturation levels during daylight hours.

Dissolved oxygen is lost to the atmosphere when water temperatures increase and the solubility of
DO in water is reduced. Dissolved oxygen is also consumed by respiration of animals and
plants. Nighttime respiration, particularly by high concentrations of algae, may reduce DO levels
below the water quality criterion in some water bodies.

Phosphorus and nitrogen provide essential nutrients for plant and animal life. If nutrients are
present in excessive amounts, the growth of algae and other waterborne plants is accelerated.
Nutrient rich water bodies that experience rapid growth of algae are considered eutrophic. Decay
of algae through bacterial decomposition can significantly reduce DO levels. Additional organic
material can be carried into streams and reservoirs through point source discharges or in the form
of nonpoint source runoff. No effluent discharges from point sources have been identified in the
project area.

20
3.3.1 SURFACE WATER QUALITY
The assessment of current water quality conditions in the Recapture Reservoir watershed included
the compilation and summary of available measurements of water quality data that have the
potential to influence reservoir DO concentrations. Stream monitoring stations included in this
assessment were selected based on their location with respect to Recapture Reservoir and length
of data record. In most instances, only water quality measurements collected since 1998 were
considered.

Summary statistics for parameters including DO, TP, Dissolved Phosphorus (DP), Total
Ammonia, Total Suspended Solids (TSS), pH, and Water Temperature (Temperature) for selected
stream monitoring sites are shown in Tables A2 - A13 (Appendix A). These tables provide a
summary of current and historical data collected at each site within the last decade. A complete
statistical summary of water quality parameters is provided in Appendix A. Time series and
seasonal box-and-whisker plots for the selected parameters are also included in Appendix A for
selected monitoring sites in the project area.

3.3.1.1 Dissolved Oxygen
Minimum DO concentration measured in tributary streams to Recapture Reservoir is 2.4 mg/L
(June 2001) above the reservoir in Bulldog Canyon Creek and 5.0 mg/L (August 2005) five miles
upstream of the reservoir in Johnson Creek. Maximum stream DO concentrations are 5.8 mg/L at
Bulldog Canyon Creek and 12.6 mg/L at Johnson Creek. All other stream stations have no DO
data, or have it only for the year 1980. Mean DO in Bulldog Canyon Creek is 4.4 mg/L, and 8.7
mg/L upstream in Johnson Creek. Figure 3.2 shows available DO measurements collected from
each site including 19 measurements (1988-2001) collected from Bulldog Canyon Creek and 20
measurements from Johnson Creek (1998-2006).

Figure 3.2. Available DO measurements collected from tributary streams to Recapture
Reservoir including Bulldog Canyon Creek and Johnson Creek.

A c u te C rite ria (a d u lt) = 4 .0 m g /L
A c u te C rite ria (ju v e n ile ) = 8 .0 m g /L
0
2
4
6
8
10
12
14
16
1 9 9 0 1 9 9 5 2 0 0 0
B u lld o g C an y o n C reek ab o v e R ecap tu re R eserv o ir
S ta tio n 4 9 5 3 5 1 0
O

X

Y

G

E

N

,

D

I

S

S

O

L

V

E

D

M

G

/

L
D a te
A c u te C rite ria (a d u lt) = 4 .0 m g /L
A c u te C rite ria (ju v e n ile ) = 8 .0 m g /L
0
2
4
6
8
10
12
14
16
2 0 0 0 2 0 0 5
Jo h n so n C re e k a b o v e R e c a p tu re R e se rv o ir a b o v e D iv e rsio n
S ta tio n 4 9 5 3 4 6 0
O

X

Y

G

E

N

,

D

I

S

S

O

L

V

E

D

M

G

/

L
D a te
Bulldog Canyon Creek above
Recapture Reservoir Station 4953510
Johnson Creek above Recapture Reservoir above
Diversion Station 4953460

21
Recapture Creek and its tributary streams are classified as 3A streams (cold-water aquatic life
beneficial use) with an acute DO standard for juvenile and adult life stages of 8.0 mg/L and 4.0
mg/L, respectively. This standard also applies to the Reservoir itself. All DO measurements
collected from Johnson Creek and all but one DO measurement from Bulldog Creek met the 4
mg/L criterion.

During the past ten years, minimum DO concentrations in Recapture Reservoir have been
consistently below 0.5 mg/L in the lower portions of the water column. Maximum DO levels in
Recapture Reservoir range from 8.4 to 8.9 mg/L. Recent (1998-2007) mean DO concentrations
observed at reservoir monitoring stations ranged from 4.6 to 6.0 mg/L. DO levels generally
increased with distance upstream from the dam.

Table 3.4 provides water quality information on reservoir profile measurements. Reservoir
profiles have been consistently measured at three monitoring stations since 2001. Greatest water
depths typically occur nearest the Dam and decrease toward the inlet. The percent of DO profile
measurements that violated the 4.0 mg/L criterion in Recapture Reservoir at Stations 01 and 02
ranged from 0 to 75 percent, with many sample dates indicating more than 50 percent of DO
profile measurements below this level. The greatest number of samples violating DO criteria
occur in August of most years when more than 50 percent of the column is below 4 mg/L. The
lowest concentrations were observed on August 14, 2003 when 75 percent of DO profile
measurements were less than 4.0 mg/L. An exception to this seasonal pattern occurred in 2006
when less than 50% of the water column was above 4.0 mg/L in June and July, all of the water
column was above 4.0 mg/L in August, and 26% of the water column was below 4.0 mg/L in
September. However, the number of measurements collected in August 2006 at Station 01
(above Recapture Dam) are very limited and do not appear to represent the entire profile.
Average DO concentrations during August of most years were less than 4.0 mg/L at Station 01
and Station 02 (1/4 way up the reservoir). During July 2005 DO profiles at the two upper-
reservoir locations were low, with most measurements less than 5.0 mg/l.

Full support of DO criteria was typically observed at reservoir monitoring stations in June and
July of each year as well as September and October when measurements were available for these
months. Although water is deepest at Station 01, based on the consistency of violations it does
not appear that support of DO criterion is strongly correlated with water depth at reservoir
monitoring stations.

Figure 3.3 displays profile measurements of DO and temperature at all three reservoir monitoring
stations during June and October of 2005. Note that although the total depth varies at each
station, the shape of the profiles at depth is very similar, even during different times of the year.
These plots indicate a pattern that is typical of other years and provide evidence that stratified
layers are consistent between the three monitoring locations with respect to distance
(approximately 0.4 miles between each station), and season. It is likely these stratified layers
continue upstream of Station 03 (1/2 way up the reservoir). The similarity between profiles at
each station indicates the presence of stratified layers throughout a large portion of the reservoir.
A probable cause for this condition is a lack of mixing due to the absence of tributary inflow
during the summer and fall months, as described above in Section 2.

Most profile measurements show that Recapture Reservoir is stratified in June and continues
throughout the summer and fall season. Figure 3.4 includes reservoir profiles measured at Station
01 during a wet (2005) and relatively dry year (2006), as indicated by monthly precipitation
values shown near the bottom of each plot. Note that total precipitation during January through
June for 2005 was roughly 3 times as great as total precipitation measured during the same period

22
in 2006. DO profile measurements in June 2005 indicate complete mixing to a depth of nearly 30
meters. Stratification was evident for approximately 4 weeks later in July. Water column depth
had decreased substantially over this period, although only 15 percent of measurements were
below 4.0 mg/L. DO concentrations continued to decrease in August to below 2 mg/L at depths
below approximately 7 m. This pattern was reversed in October in the upper water column when
concentrations increased to more than 6 mg/L at depths of nearly 10 m below the water surface.
Note that total precipitation during the winter and spring seasons prior to June 2005 totaled nearly
16 inches. Spring runoff associated with precipitation levels of this magnitude appear to be
capable of complete water column mixing as shown by the June 2005 profile.

Profiles from 2006 indicate the presence of stratified water layers during the measurement period
of June through September. Similar to 2005, upper column DO concentrations increase between
July and September. These increases could be the result of mixing from runoff volumes
generated by intense thunderstorms capable of generating surface runoff and tributary inflow, or
in response to increased DO solubility and thermal mixing as surface water layers begin to cool.
Note that total precipitation (November-May) prior to June 2006 was slightly more than 4 inches
and roughly 25 percent of the total shown for the same time period in 2005. Profile
measurements from both years do not indicate a fall turnover by the time measurements are taken
in October.

3.3.1.2 Total Phosphorus
Within the past eight years, minimum TP concentrations in Recapture Reservoir and its tributaries
have been below detection limits (typically 0.02 mg/L). Maximum TP on stream sites was 0.36
mg/L at Bulldog Canyon Creek and 0.19 mg/L at Johnson Creek. These measures are at or
above the pollution indicator value of 0.05 mg/L TP for streams. Figure 3.5 shows available TP
concentrations measured at each stream monitoring site, including 29 samples (1988-2001) from
Bulldog Canyon Creek and 22 samples (1998-2006) from Johnson Creek. It is noted that 2
samples from Bulldog Canyon Creek and 14 samples from Johnson Creek were below the method
detection limits for TP measurements. Average TP concentration (1998-2007) at stream sites are
0.02 mg/L at the Johnson Creek station and 0.03 mg/L at the Bulldog Canyon Creek station. In
general, TP concentrations were highest during the winter season (January-March) at each stream
station (including Johnson Creek and Bulldog Canyon Creek) but were still below the 0.05 mg/l
indicator value. Exceedance of the TP indicator value at stream stations during 1998-2007 was
4.8 percent at Johnson Creek. All samples from Bulldog Canyon Creek during this time period
were at or below 0.05 mg/L.

Measurements of TP were typically collected from Recapture Reservoir in June through October
during visits when reservoir profiles were measured. Maximum TP concentrations at reservoir
stations ranged from 0.23 mg/L at Station 01 to 0.05 mg/L at Station 03. Mean reservoir TP
concentrations based on available data (1998-2007) were 0.033 mg/L at Station 01, 0.032 mg/L at
Station 02, and 0.023 mg/L at Station 03.

Recapture Reservoir was considered to be in non-support of the TP indicator value in 1996 and
1998, but it has been considered in full support of this parameter since that time. Data from
reservoir stations indicate that 17-44 percent of available TP measurements measured during
1998-2007 have exceeded the 0.025 mg/l indicator value (Table A11-Table A13, Appendix A).
Exceedance of the indicator value is highest at Station 02 and lowest at Station 03.

23
Table 3.4. Water quality at three Recapture Reservoir monitoring sites.
DO pH Temperature
Date Depth
(m) Samples Mean
(mg/L) % <4.0 mg/l Status1 Mean 6.5>%>9.0 Status1 Mean
(oC) % >20 C Status1
Reservoir Station 5958010 – Recapture Reservoir Above Dam 01
6/13/2001 21.8 23 5.37 34.78 FS 7.72 0 FS 12.39 0 FS
8/14/2001 20.4 22 2.52 68.18 NS 7.67 0 FS 15.39 31.81 NS
6/4/2003 15.5 17 5.26 35.29 FS 7.78 0 FS 13.93 29.41 NS
8/14/2003 11.8 12 2.12 75 NS 7.52 0 FS 17.23 41.67 NS
6/7/2005 28.9 28 7.28 0 FS 7.88 0 FS 10.66 0 FS
7/13/2005 18.4 20 4.84 15 FS 8.24 0 FS 13.84 25 NS
8/31/2005 14.6 17 2.91 58.82 NS 7.42 0 FS 15.93 35.29 NS
10/5/2005 14.7 16 4.46 37.5 FS 7.63 0 FS 14.08 0 FS
6/22/2006 21.1 23 5.07 52.17 NS 7.9 0 FS 13.72 21.74 NS
7/19/2006 18.2 19 2.79 52.63 NS 7.58 0 FS 16.6 42.11 NS
8/24/2006 3.5 5 6.19 0 FS 8.14 0 FS 22.42 100 NS
9/22/2006 18 19 6.02 26.32 FS 8.23 0 FS 14.22 0 FS
Reservoir Station 5958020 – Recapture Reservoir ¼ Way Up Reservoir 02
6/13/2001 3.3 5 7.97 0 FS 8.49 0 FS 18.94 0 FS
8/14/2001 14.1 15 3.58 53.33 NS 7.8 0 FS 18.06 46.66 NS
6/4/2003 14 15 5.56 33.33 FS 7.83 0 FS 14.44 26.66 NS
6/7/2005 13.3 14 7.18 0 FS 7.8 0 FS 12.72 0 FS
7/13/2005 20.6 22 4.02 68.18 NS 8.02 0 FS 13.5 22.73 NS
8/31/2005 9.5 11 4.1 36.36 FS 7.57 0 FS 18.67 63.64 NS
10/5/2005 17 18 4.02 38.89 FS 7.61 0 FS 13.49 0 FS
6/22/2006 14.7 17 5.62 29.41 FS 8.1 0 FS 16.27 29.41 NS
7/19/2006 11.8 13 3.66 46.15 FS 7.71 0 FS 20 53.85 NS
8/24/2006 6.2 8 5.06 25.00 FS 8.01 0 FS 22.08 100 NS
Reservoir Station 5958030 – Recapture Reservoir ½ Way Up Reservoir 03
6/13/2001 7 8 7.76 0 FS 8.35 0 FS 17.52 0 FS
8/14/2001 5.2 7 6.70 0 FS 8.41 0 FS 22.65 100 NS
6/4/2003 9.4 11 6.81 18.2 FS 8.02 0 FS 16.50 36.4 NS
6/7/2005 12.1 12 6.96 0 FS 7.89 0 FS 12.57 0 FS
7/13/2005 12.0 14 3.71 66.6 NS 7.90 0 FS 16.35 41.7 NS
8/31/2005 4.1 6 6.11 0 FS 7.84 0 FS 21.78 100 NS
10/5/2005 7.1 9 6.83 0 FS 7.92 0 FS 15.62 0 FS
6/22/2006 9.1 11 6.69 18.2 FS 8.33 0 FS 18.51 45.5 NS
7/19/2006 6.8 8 5.43 25.0 FS 8.00 0 FS 22.88 87.5 NS
8/24/2006 5.3 7 5.51 14.3 FS 8.06 0 FS 22.12 100 NS
FS= full support of beneficial use, NS= non-support of beneficial use.

24

Figure 3.3. Selected reservoir DO and temperature profiles measured from monitoring
stations on Recapture Reservoir during 2005.

Recapture Reservoir
October 5, 2005
0
5
10
15
20
25
30
35
0 2 4 6 8 10 12 14 16 18 20
DO (mg/L) and Water Temperature (C)
De
p
t
h

(
m
)
DO Above Dam DO 1/4 Way Up DO 1/2 Way Up
Temperature Above Dam Temperature 1/4 Way Up Temperature 1/2 Way Up
Acute
criterion -
adult
Recapture Reservoir
June 7, 2005
0
5
10
15
20
25
30
35
0 2 4 6 8 10 12 14 16 18 20
DO (mg/L) and Water Temperature (C)
De
p
t
h

(
m
)
DO Above Dam DO 1/2 Way Up DO 1/4 Way Up
Temperature Above Dam Temperature 1/4 Way Up Temperature 1/2 Way Up
Acute
criterion -
adult

25

Figure 3.4. DO profiles observed at Recapture Reservoir Above Dam during 2005 and 2006.
2005
0
5
10
15
20
25
30
0 2 4 6 8 10
DO (mg/L)
De
p
t
h

(
m
)
Jun 7, 2005
Jul 13, 2005
Aug 31, 2005
Oct 5, 2005
0.00
0.50
1.00
1.50
2.00
2.50
3.00
3.50
4.00
Ja
n
Fe
b
Ma
r
Ap
r
Ma
y
Ju
n
Ju
l
Au
g
Se
p
Oc
t
No
v
De
c
Month
Pr
e
c
i
p
i
t
a
t
i
o
n

(
i
n
)
Acute
criterion -
adult
2006
0
5
10
15
20
25
30
0 2 4 6 8 10
DO (mg/L)
De
p
t
h

(
m
)
Jun 22, 2006
Jul 19, 2006
Aug 24, 2006
Sep 22, 2006
0.00
0.50
1.00
1.50
2.00
2.50
3.00
3.50
4.00
Ja
n
Fe
b
Ma
r
Ap
r
Ma
y
Ju
n Ju
l
Au
g
Se
p
Oc
t
No
v
De
c
Month
Pr
e
c
i
p
i
t
a
t
i
o
n

(
i
n
)
Acute
criterion -
adult

26

Figure 3.5. Available TP measurements collected from tributary streams to Recapture
Reservoir including Johnson Creek and Bulldog Canyon Creek.

Table 3.5 provides information on profile measurements of TP. These measurements are
generally collected at 4 different depths that are representative of the entire water column. Note
that although most dates include samples that exceed 0.025 mg/L, most dates also include
samples that were below the detection limit. Samples with concentrations less than the detection
limit were represented by a value of one-half the detection limit. For each sample date, the
highest TP concentrations were consistently measured from the lowest profile sample which is
collected roughly 1 meter above the reservoir bottom. Figure 3.6 displays all TP measurements
collected during periods when reservoir elevation data is available (2001-2007) and indicates that
higher concentrations are present during times when reservoir levels have increased rapidly.
These time periods are typically associated with the spring runoff period.

3.3.1.3 Dissolved Phosphorus
The availability of phosphorus for growth of algal species is indicated by measurements of DP.
A high DP/TP ratio indicates that much of the phosphorus in water bodies is potentially available
for use by algae and other plant species. Only one measurement of DP is available from stream
monitoring locations in the project area. It was collected in March 2006 at Johnson Creek. The
DP value at this station was 0.030 mg/L, which is below the pollution indicator value of 0.05
mg/L.

Measurements of DP have been routinely collected from reservoir monitoring stations. Table 3.5
indicates mean DP concentrations calculated from reservoir profile samples. Similar to TP
measurements, many of the DP samples had concentrations that were below detection limits as
well as high concentrations collected from samples near the reservoir bottom. Nearly all mean
DP concentrations were below 0.30 mg/L and most were below 0.025 mg/L. DP/TP ratios were
consistently greater than 0.50, indicating that most of the phosphorus is available for plant
growth. Note that for some dates all DP samples had concentrations below detection limits and a
value of 0.020 mg/L was assumed. In these instances, the actual DP/TP ratio is likely
overestimated.
T o ta l P = 0 .0 5 m g /L
0 .0 0 9
0 .0 3 4
0 .0 5 9
0 .0 8 4
0 .1 0 9
0 .1 3 4
0 .1 5 9
0 .1 8 4
1998 1999 2000 2001 2002 2003 2004 2005 2006
Jo h n so n C re e k a b o v e R e c a p tu re R e se rv o ir a b o v e D iv e rsio n
S ta tio n 4 9 5 3 4 6 0
P

H

O

S

P

H

O

R

U

S

,

T

O

T

A

L

(

M

G

/

L

A

S

P

)
D a te
T o ta l P = 0 .0 5 m g /L
0 .0 0
0 .0 5
0 .1 0
0 .1 5
0 .2 0
0 .2 5
0 .3 0
0 .3 5
1 9 9 0 1 9 9 5 2 0 0 0
B u lld o g C an y o n C reek ab o v e R ecap tu re R eserv o ir
S ta tio n 4 9 5 3 5 1 0
P

H

O

S

P

H

O

R

U

S

,

T

O

T

A

L

(

M

G

/

L

A

S

P

)
D a te
Bulldog Canyon Creek above
Recapture Reservoir Station 4953510
Johnson Creek above
Recapture Reservoir above Diversion Station 4953460

27

Figure 3.6 displays all DP measurements collected during periods when reservoir elevation data is
available (2001-2007). DP concentrations generally follow a pattern similar to TP although the
large increases observed during early 2005 are limited in their range. The highest concentrations
were observed in late 2006 on a date when reservoir elevations were not available. It is not
known if the increased concentrations in both TP and DP sample were in response to loading
from tributaries or resuspension of bottom sediments. The highest measured concentration on
this date was collected at the bottom of the water column.

3.3.1.4 pH
Minimum pH measurements throughout the Recapture Reservoir watershed since 1999 have been
essentially neutral, ranging from 6.9 at Station 02 to 7.4 at Bulldog Creek. Maximum values are
neutral to slightly basic, ranging from 8.3 at Bulldog Canyon Creek to 9.6 at Johnson Creek.
Mean pH values were slightly basic and ranged from 7.8 at Stations 01 and 02 to 8.3 at Johnson
Creek.

The pH standard for Class 3A water bodies including Recapture Reservoir and its tributaries is
6.5 - 9.0. This standard was not exceeded in Recapture Reservoir in the past eight years or in
Bulldog Canyon Creek during the entire period of record. The standard was exceeded in 7.1
percent of samples at Johnson Creek. Seasonal patterns of pH levels were not observed in
streams in the project area.

As with other parameters, pH measurements in the reservoir were only taken in June through
October. Table 3.4 provides a summary of pH profile measurements collected during each
sample date. As indicated in this table, no violations of the pH standard were observed in profile
measurements.

3.3.1.5 Total Suspended Solids
Minimum TSS concentrations were below detection limits throughout the watershed including
stream and reservoir sites. Maximum TSS readings in project area streams were 32 mg/L in
Bulldog Canyon Creek and 92.7 mg/L at Johnson Creek. Mean TSS values at these stations were
19.2 and 16.4 mg/L, respectively.

All reservoir TSS readings since 1999 have been below detection limits. This indicates that
suspended material brought into the reservoir by inflowing tributaries settles quickly. It also
provides additional evidence that little or no water column mixing occurs during the summer and
early fall that would resuspend material.

3.3.1.6 Nitrogen - Ammonia
Most ammonia measurements taken in the project area since 1999 were below the detection limit.
The only stream with ammonia concentrations above the detection limit was Johnson Creek
which had a mean concentration of 0.04 mg/L and a maximum value of 0.06 mg/L. No
exceedance of the pH-dependent ammonia standard occurred.

More than 40 percent of reservoir measurements of ammonia were below the detection limit.
Mean concentrations of reservoir measurements above the detection limit ranged from 0.047 to
0.054 mg/L. Maximum values ranged from 0.23 mg/L at Station 01 to 0.08 mg/L at Station 03
While mean values show little variance, maximum values are generally higher at Station 01 and
Station 02. Similar to stream monitoring stations, no exceedance of the ammonia standard was
observed at reservoir monitoring stations.

28
Table 3.5. Water quality at two Recapture Reservoir monitoring sites.
Total P (mg/L) Dissolved P (mg/L)
Date Depth
(m) Samples
Below
Detection
Limit
Mean
Samples
>0.025
mg/l
Samples
Below
Detection
Limit
Mean
Samples
>0.025
mg/l
DP/TP
Ratio
Reservoir Station 5958010 - RECAPTURE RES AB DAM 001
6/13/2001 21.8 4 1 0.024 1 4 3 0.021 0 0.88
8/14/2001 20.4 4 2 0.034 2 4 2 0.029 1 0.85
6/4/2003 15.5 4 4 0.020 0 4 4 0.020 0 1.00
8/14/2003 11.8 4 1 0.028 1 4 3 0.024 1 0.86
6/7/2005 28.9 4 2 0.026 1 4 4 0.020 0 0.77
7/13/2005 18.4 4 3 0.038 1 4 3 0.023 1 0.61
8/31/2005 14.6 4 3 0.032 1 4 3 0.023 1 0.72
10/5/2005 14.7 4 3 0.038 1 4 3 0.025 1 0.66
6/22/2006 21.1 4 3 0.028 1 4 4 0.020 0 0.71
7/19/2006 18.2 4 4 0.020 0 4 4 0.020 0 1.00
8/24/2006 3.5 2 2 0.020 0 2 2 0.020 0 1.00
9/22/2006 18 4 1 0.106 3 4 1 0.108 3 1.02
Reservoir Station 5958020 - RECAPTURE RES 1/4 WAY UP RES 02
6/13/2001 3.3 2 0 0.028 2 2 2 0.020 0 0.71
8/14/2001 14.1 2 1 0.036 1 2 0 0.046 2 1.28
6/4/2003 14 2 2 0.020 0 2 1 0.016 0 0.80
6/7/2005 13.3 2 1 0.045 1 2 1 0.024 1 0.53
7/13/2005 20.6 2 1 0.068 1 2 1 0.026 1 0.38
8/31/2005 9.5 2 1 0.064 1 2 1 0.023 0 0.36
10/5/2005 17 2 1 0.034 1 2 1 0.030 1 0.88
6/22/2006 14.7 2 2 0.020 0 2 2 0.020 0 1.00
7/19/2006 11.8 2 2 0.020 0 2 2 0.020 0 1.00
8/24/2006 6.2 2 2 0.020 0 2 2 0.020 0 1.00
Reservoir Station 5958030 - RECAPTURE RES 1/2WAY UP RES 03
6/13/2001 7 2 1 0.027 1 2 2 0.020 0 0.74
8/14/2001 5.2 2 2 0.020 0 2 2 0.020 0 1.00

29
Table 3.5. (cont’d) Water quality at two Recapture Reservoir monitoring sites.
TP (mg/L) DP (mg/L)
Date Depth (m) Samples
Below
Detection
Limit
Mean
Samples
>0.025
mg/l
Samples
Below
Detection
Limit
Mean
Samples
>0.025
mg/l
DP/TP
Ratio
6/4/2003 9.4 2 2 0.020 0 2 2 0.020 0 1.00
6/7/2005 12.1 2 1 0.037 1 2 1 0.020 0 0.54
7/13/2005 12.0 2 1 0.036 1 2 1 0.021 0 0.57
8/31/2005 4.1 2 1 0.025 1 2 2 0.020 0 0.80
10/5/2005 7.1 2 2 0.020 0 2 2 0.020 0 1.00
6/22/2006 9.1 2 2 0.020 0 2 2 0.020 0 1.00
7/19/2006 6.8 2 2 0.020 0 2 2 0.020 0 1.00
8/24/2006 5.3 2 2 0.020 0 2 2 0.020 0 1.00

30

Figure 3.6. Total and Dissolved Phosphorus concentrations measured at Recapture
Reservoir monitoring locations during 2001-2006. Data points represent individual
measurements collected at approximately 2-4 depths in the water column for a given sample date.

Total Phosphorus
(2001-2006)
0
0.05
0.1
0.15
0.2
0.25
2
0
0
1
2
0
0
2
2
0
0
3
2
0
0
4
2
0
0
4
2
0
0
6
Date
To
t
a
l

P

(
m
g
/
L
)
6015
6020
6025
6030
6035
6040
6045
6050
6055
6060
Re
s
e
r
v
o
i
r

E
l
e
v
a
t
i
o
n

(
f
t

a
b
o
v
e

s
e
a

l
e
v
e
l
)
At Dam 1/4 Way Up 1/2 Way Up Indicator Value Reservoir Elevation
0.025 mg/L indicator value
Dissolved Phosphorus
(2001-2006)
0
0.05
0.1
0.15
0.2
0.25
Jan-01 May-02 Sep-03 Feb-05 Jun-06
Date
Dis
s
o
l
v
e
d

P

(
m
g
/
L
)

.
6015
6020
6025
6030
6035
6040
6045
6050
6055
6060
Re
s
e
r
v
o
i
r

E
l
e
v
a
t
i
o
n

(
f
t

a
b
o
v
e

s
e
a

l
e
v
e
l
)

.
At Dam 01 1/4 Way Up 1/2 Way Up Indicator Value Reservoir Elevation
0.025 mg/L indicator value

31
3.3.1.7 Water Temperature
Since 1999, maximum stream temperatures were 23.5 oC on Johnson Creek, upstream of the
reservoir, and 27.5 oC at Bulldog Canyon Creek, just above the reservoir. Mean temperature at
Johnson Creek was 9.9 oC, and much higher at 23.2 oC on Bulldog Canyon Creek which exceeds
the 20 oC Class 3A standard. Exceedance of the temperature standard was recorded in 20 percent
of measurements from Johnson Creek samples and 33.3 percent of samples collected from
Bulldog Canyon Creek.

Maximum temperatures in reservoir profiles ranged from 24.7 to 24.9 oC. Mean temperatures
increased with distance from the dam, ranging from 14.1 oC at Station 01 to 16.9 oC at Station 03.
The criterion for supporting the 3A beneficial use in reservoirs is based on the same temperature
threshold of 20 oC as in streams, but the standard is in terms of the percentage of samples taken
from a single location on the reservoir that exceed that criterion temperature. Table 3.4 shows the
results of water temperature measurements for the three monitoring sites in the reservoir between
early June and October for several of the last six years. Until early June and after early
September, temperature does not exceed 20 oC. However, some percentage of the samples always
exceed the 20 oC standard during late June through August.

The percentage of reservoir samples that exceed the standard is substantially higher at the Station
03 site because it is much shallower. Figure 3.7 shows temperature profiles of all three sites on a
typical day in August. All three profiles were measured from the surface to the bottom. Note first
that the site immediately above the dam is deepest (~15 m) and the site half way up the reservoir
is much shallower (~4 m). Surface water temperatures are slightly lower at the dam where the
water is deepest. However, all three sites show a similar temperature profile with respect to actual
depth. At the site furthest from the dam, and the shallowest location, all of the profile
measurements exceed the 20 oC criterion. Since the same number of measurements is spread out
through the entire water column, deeper sites, such as near the dam, will register a smaller
percentage of samples that fail the temperature criterion. As with DO, this suggests that water
quality in the reservoir needs to be assessed with respect to actual depths of habitable water by
the designated fishery.

3.3.2 GROUNDWATER QUALITY
Two groundwater monitoring stations were identified in the watershed, with one visit to each
station. One station is 10 miles upstream of Recapture Reservoir (374726109303001), and one is
near the reservoir (373954109270001). Table 3.6 contains a summary of parameters at each
station. No measurements of nutrients were identified at these locations. Measurements of
temperature and TDS appeared to be representative of good groundwater quality conditions.

Table 3.6. Groundwater quality data from well stations.
Station Station Name Year Specific
Conductance
(umhos/cm
@ 25oC)
pH Solids,
Dissolved
(mg/l)
Water
Temperature
(oC)
373954109270001 (D-36-22)12ccd-1 1982 510 9.2 130 16.5
374726109303001 (D-34-22)28caa-1 1977 - 7.6 251 -

32

Figure 3.7. Temperature profiles at three sites in Recapture Reservoir.

3.3.3 BIOLOGICAL DATA
The available measurements of algae in the Recapture Reservoir watershed were limited to the
period 1995-2001 at Station 01 (Recapture Reservoir Above Dam). Phytoplankton data collected
about 15 years ago showed one species of green algae, Sphaerocystis schroeteri, to be highly
dominant, representing almost 98 percent of algal cell volume (Judd 1997). A review of the
DWQ algae monitoring data from STORET shows a more balanced species distribution. Sixteen
different species were identified from samples collected during this time period, with no species
representing more than 21 percent of the total composition. Most of these species are green algae
species, which are indicative of good water quality and moderate production. Table 3.7 shows
algae data from Recapture Reservoir.

Macroinvertebrate data was also collected on Johnson Creek above Recapture Reservoir in
October 2004. An O:E score of 0.881 was recorded. An O:E score is the ratio of observed over
expected for macroinvertebrate populations. Therefore, a score of 1.0 would indicate that all
species expected were observed. Anything above the threshold value of 0.74 is considered to be
in full support. Based on macroinvertebrate samples, Johnson Creek was found to be in full
support of its beneficial uses.

Recapture Reservoir is reported to have supported populations of cold water fish including brook
trout, rainbow trout, and bullheads (Judd 1997). The reservoir was initially treated in the fall of
1983 for elimination of non-game fish prior to filling the impoundment to capacity level. A
limnological assessment completed by Utah DWR at that time indicated the reservoir could
support a cold water fishery. As a result, rainbow trout were initially stocked by DWR to
establish in the reservoir. Fish stocking was discontinued in 2001 because illegally introduced
northern pike were found to be eating the fingerlings.
Recapture Reservoir
August 31, 2005
0
5
10
15
20
25
30
0 5 10 15 20 25
Temperature (deg C)
De
p
t
h

(
m
)
Above Dam 1/4 Way Up 1/2 Way Up
Cold water
fisheries
criterion

33

A recent gillnetting survey was conducted on Recapture Reservoir by DWR on April 26, 2007.
This survey collected numerous pike that were 18-24 inches and one large 8 lb, 31 inch adult.
Other fish that were identified included many robust 11-14 inch largemouth bass as well as good
numbers of black bullhead roughly 2 lbs each (DWR 2007). Most of these species are considered
warmwater fish and likely have adapted to higher temperatures and low DO conditions that are
sometimes observed in the reservoir. All warmwater species have been illegally stocked. No
coldwater species were identified in the survey results.

Table 3.7. Algae measurements collected from Recapture Reservoir.1
Species Value2 % of Total Type
August 23, 1995
Chlorophyta sp. 1 5,560 11.10 Green
Melosira granulate 5,560 11.10 Diatom
Oocystis sp. 1 16,680 33.30 Green
Phacus 5,560 11.10 Green
Sphaerocystis schroeteri 11,120 22.20 Green
Bacillariophyta sp. 1 5,560 11.10 Green
TOTAL 50,040 100
August 4, 1999
Pteromonas 16,700 15.80 Green
Chlorophyta sp. 1 22,200 21.00 Green
Ceratium hirundinella 5,600 5.30 Dinoflagellate
Ankistrodesmus falcatus 50,000 47.30 Green
Oocystis sp. 1 11,100 10.5 Green
TOTAL 105,600 100
August 14, 2001
Bacillariophyta sp. 1 31,300 31.20 Diatom
Fragilaria crotonensis 18,800 18.80 Diatom
Bacillariophyta sp. 2 3,100 3.10 Diatom
Tabellaria fenestrata 18,800 18.80 Diatom
Oocystis borgei 6,300 6.30 Green
Pteromonas 21,900 21.90 Green
TOTAL 100,200 100
1 Biological data included algae measurements at Station 5958010 Recapture Reservoir above Dam 01. 2 Units #/L.

Table 3.8 indicates habitat needs of fish species stocked by DWR following reservoir
construction as well as those species later identified in surveys of Recapture Reservoir.

Based on the available data, it is quite likely that every summer cold water species of fish would
be under severe stress. Figure 3.8 shows a condition in August of 2001 where the entire water
column at Station 03 is warmer than 20 °C, and at Station 01, water below 20 °C is only present
where DO levels are less than 4.0 mg/L. This situation may occur in most of the reservoir every
year, for even in a year of very high precipitation, such as 2005, Figure 3.9 shows that fish would
have encountered the same situation. Based on 2007 gill netting, it appears there are no cold
water species that survived. Warm water fish, are much less constrained by temperature and DO
levels in comparison to cold water species. Water temperatures have never exceeded the Class
3B warm water criterion of 27 °C during monitoring visits to Recapture Reservoir.

34
Table 3.8. Summary of habitat needs of Recapture Reservoir fish.
Species
Optimum Temperatures
(deg C) DO Requirements
(mg/L)* Habitat Type Diet Spawning
Season Substrate
Egg Adult Spawning
Black
Bullhead
22.2 -
23.9 21–24 18.9–22.2

Optimum > 7,
Lethal <3
(summer), 0.3
(winter)

50–80% of total stream area
with low velocity pools or
backwaters and also riffle-
run areas.
Omnivores, mainly
crustaceans
Late spring–
summer Silt
Bluegill 20.0 15–25 19.4–20.0 Optimum >5,
Lethal <1
Weedy, shallow, clear,
warm water.
Insects, small fishes,
frogs, crayfish, and
snails, plankton
Spring Sand or
gravel
Cutthroat
Trout 10.0 12–15 5.5–8.9 Optimum >9 Clear, cold lakes and
streams.
Adults carnivorous,
young eat plankton and
insects
Early spring Silt-free,
rocky
Brook Trout 4.5-
11.5 11-16 4.5-10.0 Optimum >7
Clear, cold water with 1:1
pool:riffle ratio and stable
flow and vegetated banks.
Macroinvertebrates,
terrestrial insects Fall Silt-free,
rocky
Green
Sunfish 23.3 18–32 18.9–27.7 Optimum >5,
Lethal <1.5
Small, warm, streams,
ponds, and shallow areas of
lakes.
Insects, mollusks, and
small fish Spring
Largemouth
Bass
16.7–
18.3 26.7 14.4–15.0 Optimum >8,
Lethal <1
Small, shallow lakes and
ponds and large, slow rivers.
Fish and small
mammals; plankton,
insects
Spring
Rainbow
Trout >5.6 12–18 10.0 Optimum >9,
Lethal <3
Clear, cold lakes and
streams with 1:1 pool:riffle
ratio.
Fish, invertebrates,
algae, vascular plants Early spring
Silt-free
rocky
substrate
Northern
Pike 16-20 19-21 8-12 Optimum >4,
Lethal <1.5
Shallow, vegetated areas in
lakes and reservoirs Fish, insects Spring Dense
vegetation
*The term “optimum” can be misleading, as some species can survive DO levels well below their optimum, while others are more sensitive. When considered
with the lethal limit, this information provides an indication of the relative ranges of requirements across species.
Sources: Petrovsky and Magnuson 1973, Matthews and Berg 1997, Stuber et. al 1982a, Hickman and Raleigh 1982, Stuber et. al 1982b, Sigler and Sigler
1996, Inskip 1982, Raleigh 1982, Casselman and Lewis 1996.

35

Depth DO Temp
0.1 7.05 24.52
1.2 6.98 24.35
2.2 7.15 22.71
3.1 7.05 22.53
4.3 6.94 22.14
5 5.88 21.2
5.2 5.84 21.13
Depth DO Temp
0 7.24 23.26
1.1 7.18 23.1
2 7.16 22.76
3 7.07 22.58
4 6.75 22.46
5 6.32 22.12
6.1 5.01 21.55
7 2.85 19.71
7.9 1.33 17.49
9.1 0.8 16.09
10.1 0.58 14.44
11.1 0.45 12.99
12.1 0.38 12.25
Recapture Reservoir Profile
Station 03 1/2 Way - August 14, 2001
0
5
10
15
20
25
30
35
0 5 10 15 20 25
DO (mg/L) and Water Temperature (ºC)
De
p
t
h

(
m
)
DO Temperature
Recapture Reservoir Profile
Station 01 at Dam - August 14, 2001
0
5
10
15
20
25
30
35
0 5 10 15 20 25
DO (mg/L) and Water Temperature (ºC)
De
p
t
h

(
m
)
DO Temperature

36

Figure 3.8. Recapture Reservoir profiles measured August 14, 2001. Shaded cells in tables
indicate measurements that comply with Class 3A criterion for DO (> 4 mg/L) or temperature (20
ºC). Note that both criterion are never met at the same depth.
13.1 0.32 11.38
14.1 0.3 10.63
15 0.26 9.86
16 0.27 9.77
17 0.26 9.5
18.1 0.25 9.28
19.3 0.25 9.16
20.2 0.24 9.05
20.4 0.23 9.05

37

Figure 3.9. Recapture Reservoir profiles measured August 31, 2005. Shaded cells in tables
indicate measurements that comply with Class 3A criterion for DO (> 4 mg/L) or temperature (20
ºC). Note that both criterion are met at a depth of 6 m.
Depth DO Temp
0 6.24 22.31
1 6.33 22.31
1.9 6.16 22.12
3.1 6.2 21.69
4 5.72 21.02
4.1 5.99 21.23
Depth DO Temp
0 6.45 20.36
1.9 6.19 21.03
2.8 6.1 20.89
3.1 5.76 20.79
4.7 5.31 20.62
5.1 4.95 20.34
6 4.01 19.92
6.4 3.52 19.88
7.1 1.28 18.74
8 0.39 13.52
9.1 0.1 12.25
10 0.12 11.27
11 0.31 10.7
12 0.66 10.48
13 0.91 10.19
14.1 1.61 9.94
14.6 1.75 9.85
Recapture Reservoir Profile
Station 03 1/2 Way - August 31, 2005
0
5
10
15
20
25
30
35
0 5 10 15 20 25
DO (mg/L) and Water Temperature (ºC)
De
p
t
h

(
m
)
DO Temperature
Recapture Reservoir Profile
Station 01 At Dam - August 31, 2005
0
5
10
15
20
25
30
35
0 5 10 15 20 25
DO (mg/L) and Water Temperature (ºC)
De
p
t
h

(
m
)
DO Temperature

38
3.3.4 TROPHIC STATE INDEX
The trophic state of a lake or reservoir is an indicator of the total weight of all living biological
material or biomass found within the waterbody at a given point in time (Carlson and Simpson
1996). The specific trophic state of a water body can be influenced by nutrient additions, as well
as other factors such as season, zooplankton grazing, mixing depth, etc. (Carlson and Simpson
1996). Trophic status is generally considered to respond to nutrient inputs over time, and will
reflect the biological condition of a waterbody. The trophic state index (TSI) is based on
measurements of nutrient-related parameters that are believed to characterize biomass. Carlson
(1977) has developed trophic state indices based on measurements of chlorophyll a (Chl-a), TP,
and Sechi disk (SD) depth, each of which can independently provide an estimate of algal
biomass.

Chlorophyll a is a green pigment produced by all plants (including algae) during photosynthesis
and generally accounts for 1-2% of total algal biomass. Concentrations of nutrients such as
phosphorus and nitrogen greatly influence the growth and production of algal species.
Measurements of water clarity are represented by SD depth and indicate the maximum depth that
a 8-inch diameter disk can be observed from the water surface. High levels of turbidity would
result in low SD readings and indicate high amounts of suspended material, such as algae.

For the purpose of classification, priority is given to chlorophyll because this variable is generally
considered to be the most accurate of the three indicators at predicting algal biomass. According
to Carlson (1977), TP may be better than Chl-a at predicting summer trophic state from winter
samples, and transparency should only be used if there are no better methods available.

Carlson’s TSI values typically range from 0 to 100, although theoretically, the range of values
could exceed these bounds (Carlson and Simpson 1996). An increase of 10 units in the TSI scale
is equivalent to doubling the concentration of TP or halving water transparency as measured by
SD depth. Calculations for determining TSI values based on TP, Chl-a, and SD depth are
provided below.

TSI (TP) = 14.42 ln (TP in g/l) + 4.15 (3-1)

TSI (Chl–a) = 9.81 ln (chlorophyll a in g/l) + 30.6 (3-2)

TSI (SD) = 60 – 14.41 ln (Sechi disk in meters) (3-3)

where:
TSI = Carlson trophic state index
ln = natural logarithm

Information relating Carlson TSI values to trophic state characteristics is provided in Table 3.9.
Lakes and reservoirs that exhibit an oligotrophic state are considered to have good water quality.
While a mesotrophic state is considered good for some aquatic species, it can include seasonal
conditions that are detrimental to salmonids and other cold water aquatic species. A trophic
status of eutrophic or hypereutrophic is considered to represent poor water quality conditions.
TSI values calculated for three monitoring sites on Recapture Reservoir are included in Table
3.10. Most TSI values at each site were associated with a mesotrophic state although some TSI
values for Chl-a and SD were in the oligotrophic or eutrophic state, respectively. In general, TSI
values for Chl-a and TP increased with distance above the dam and were typically observed in the

39
upper range of the mesotrophic state. A few TSI values for TP and SD at upper reservoir sites
were observed at levels considered to represent eutrophic conditions.

TSI values calculated for the site above Recapture Dam are displayed in Figure 3.10 and indicate
that trophic status degrades slightly over the summer with the poorest conditions observed in
September. TSI values for Chl-a, which are considered to best represent algal populations, were
near the threshold between an oligotrophic and mesotrophic state. Annual average TSI values
were generally mesotrophic and indicated that TSI values for Chl-a were not well correlated with
TP. TSI values for SD were consistently higher than values for Chl-a and TP. High TSI values
for SD likely reflect the lack of mixing observed in Recapture Reservoir.

Based on the TSI assessment, Recapture Reservoir is generally mesotrophic, although TSI values
for SD and TP are in the eutrophic range during some time periods. TSI values for TP are
generally higher than Chl-a and therefore do not appear to limit algal growth. However, this
could be a response to typical differences in sampling depth including surface measurements of
Chl-a while TP samples were collected at 2-4 depths in the water column.

Table 3.9. Description of lake trophic status based on Carlson TSI values (Carlson and
Simpson 1996).
TSI Trophic statusa Description
< 35 Oligotrophic Clear water, high oxygen levels throughout the year although shallow
lakes/reservoirs may develop low dissolved oxygen concentrations in
the hypolimnion. Salmonid fisheries dominate aquatic populations.
Water may be suitable for unfiltered drinking in some cases.
35 - 50 Mesotrophic Water is moderately clear, greater chance of low dissolved oxygen
concentrations in the hypolimnion during the summer season. Low
dissolved oxygen levels result in salmonid losses, walleye may
predominate. Water requires filtration for drinking purposes.
50 - 70 Eutrophic Low dissolved oxygen levels predominate, heavy algal growth
dominated by blue-green algae. Warm water fisheries only. High
biomass may discourage boating, swimming.
> 70 Hypereutrophic Dense algal growth, heavy algal scums present at surface. Rough fish
dominate; summer fish kills possible.
a Oligotrophy, mesotrophy, and eutrophy are used in the context of the amount of algae in the entire water
column and are not based on oxygen concentrations observed at depth.

40
Table 3.10. Trophic State Index (TSI) values for monitoring sites located on Recapture
Reservoir. Values shown are based on averages of measured parameters collected in
each year.
Station Year TSI Chl-a TSI TP TSI SD
Recapture Reservoir Above Dam

1989 36 49 56
1991 38 49 54
1993 35 46 55
1995 34 34 45
1997 35 - 48
1999 34 45 48
2001 15 49 46
2003 19 43 47
2005 31 48 52
2006 32 57 49
Recapture Reservoir 1/4 way up

1989 38 48 55
1991 38 43 54
1993 38 46 58
1995 31 40 44
1997 37 - 49
1999 35 42 49
2001 15 52 47
2003 15 41 47
2005 34 55 49
2006 30 37 50
Recapture Reservoir 1/2 way up

1989 42 41 62
1991 45 47 66
1993 31 47 58
1995 32 34 46
1997 31 - 48
1999 33 42 50
2001 15 42 50
2003 15 37 48
2005 31 46 52
2006 35 37 50

41

Figure 3.10. Trophic State Index values calculated for Recapture Reservoir including
Chlorophyll a (Chl-a), Sechi Depth, and Total Phosphorus (TP).

Monthly Average Trophic State Index (1995-2006)
Recapture Reservoir above Dam
0
10
20
30
40
50
60
70
80
90
100
June July August September October
Month
TS
I
Chl-a Sechi depth TP
Hypereutrophic
Eutrophic
Mesotrophic
Oligotrophic
Annual Average Trophic State Index (1989-2006)
Recapture Reservoir above Dam
0
10
20
30
40
50
60
70
80
90
100
1989 1991 1993 1995 1997 1999 2001 2003 2005 2006
Year
TS
I
Chl-a Sechi Depth TP
Hypereutrophic
Eutrophic
Mesotrophic
Oligotrophic

42
3.4 SUMMARY
This water quality assessment reviewed data collected from both streams and reservoirs located in
the project area. Concentrations measured at stream monitoring locations generally represented
good water quality. Additional information defining loading from tributaries to Recapture
Reservoir will be reviewed in Chapter 4.

Water column measurements collected at three reservoir monitoring sites were only available
between June through October. A comparison of profiles at all sampling locations indicates
similar patterns and indicates that a majority of the reservoir is stratified. Profile measurements
from late June through early September show that DO concentrations in the reservoir generally
fall to a non-supporting status (DO is above 4.0 mg/L in less than 50% of the water column). The
reservoir fails to reach a fully-supporting status every year. The duration and timing of DO
impairment appears related most closely to periods of low surface water inflows observed during
the summer and fall months in the project area.

Complete mixing of the water column appears to occur following periods of high precipitation
that produce heavy spring snowmelt or short-term runoff during summer and fall storm events.
Restratification occurs within weeks during periods of low precipitation.

Mean reservoir TP concentrations based on available data (1998-2007) were 0.033 mg/L at
Station 01, 0.032 mg/L at Station 02, and 0.023 mg/L at Station 03. Each of these mean values
exceed the 0.025 mg/L pollution indicator value. Although some individual measurements of TP
and DP exceed the pollution indicator value, these samples are typically collected from the
bottom of the reservoir. Based on the phosphorus measurements reviewed in this assessment, it is
likely that existing concentrations do not produce excessive growth of algae that subsequently
decompose and consume DO to the low levels observed in reservoir profiles.

Temperatures during the warmest months of the summer result in portions of the reservoir where
no part of the water column is below the 20 °C criterion recommended for a Class 3A cold water
fishery. Measured profile temperatures have all been below the 27 °C criterion recommended for
Class 3B warm water fisheries.

43
4.0 POLLUTANT SOURCE
CHARACTERIZATION

Based on observations made during two field surveys conducted in the spring and fall of 2007, a
review of GIS information, and discussions with various state and local agencies, the following
pollutant categories have been identified in the Recapture Reservoir watershed.

1. Livestock Grazing
2. Diffuse Loads from Runoff

The human population in the watershed is relatively small and dispersed in nature. There are
point sources of pollution within the watershed. There is very limited industry in the watershed,
and agricultural activities are predominantly related to ranching with the majority of crops in the
watershed being raised for animal forage. Because of this, the pollutant contributions from
sources such as urban runoff, industrial activity, and agricultural chemicals (pesticides and
fertilizers) are nonexistent or insignificant. The following sections describe each of the
significant pollutant sources in more detail.

4.1 LIVESTOCK GRAZING
Cattle grazing can be a significant pollutant source in many western watersheds where historic
grazing has taken place. This is especially true when cattle are concentrated in or near the
riparian zone surrounding streams, water courses, and other water bodies. This is quite often the
case in watersheds where perennial streams provide a water source on a year-round basis.
Although this does happen to a limited degree in the project area, field observations indicate that
many corridors of tributary streams to Recapture Reservoir do not support abundant riparian
vegetation or the opportunities for shade, forage, and livestock watering. As a result, watering
needs for livestock in the project area are met by dispersed developed water sources including
troughs and pipeline systems fed by spring boxes or wells.

Review of grazing allotment information obtained from the U.S. Forest Service and BLM
indicates the potential for livestock grazing throughout the watershed. Figure 4.1 shows the
grazing allotment boundaries associated with public lands in the project area. Grazing allotments
are found on nearly all public land within the TMDL study area. It is estimated that over 64
percent of the Recapture Reservoir watershed is within grazing allotments permitted by the Forest
Service or the BLM. These allotments have varying numbers of permitted animals and seasons of
use which have changed substantially from year to year as a result of drought conditions (High
2007). Some grazing allotments are rested entirely during some years, while most allotments
have ranged between 100 percent and 50 percent of the permitted level. Table 4.1 indicates the
level of authorized and actual use associated with livestock grazing on federal lands.

44

Figure 4.1. Livestock grazing allotments in the Recapture Reservoir TMDL project area.

45

Table 4.1. Livestock grazing information associated with public lands in the Recapture Reservoir
TMDL project area.
Agency Allotment Pasture Total
Pasture
Area (ac)
Authorized
(AU)
Actual
(AU)
AU/ac Unit area
load
(kg/ac/day)
BLM Bulldog 5,621 62 62 0.011 0.0006
BLM 300 300 0.053 0.0029
SITLA SITLA-2 SITLA-2 204 15 15 0.074 0.0040
SITLA SITLA-32 SITLA-32 644 23 23 0.036 0.0019
SITLA SITLA-36 SITLA-36 468 30 30 0.064 0.0035
USFS Bulldog Bulldog 1,016 26 26 0.026 0.0014
USFS Bulldog Dry Canyon 1,166 28 31 0.027 0.0014
USFS Bulldog Recapture 1,571 26 29 0.018 0.0010
USFS Camp Jackson Brushy Basin 1,942 215 237 0.122 0.0066
USFS Camp Jackson Johnson
Creek
6,007 219 181 0.030 0.0016
USFS Camp Jackson Recapture 5,398 270 232 0.043 0.0023
USFS Lakes-S Peak Bulldog 2,376 87 87 0.037 0.0020
USFS Lakes-S Peak Lakes 220 197 0.083 0.0045
USFS Lakes-S Peak South Peak 84 95 0.040 0.0022
TOTAL 26,414 1,605 1,546

Livestock grazing also occurs on state and privately-owned land. Grazing allotments on state
land are managed by SITLA and are located primarily at lower elevations of the watershed.
Authorized grazing levels were obtained from SITLA personnel. No records of actual use are
currently maintained for these allotments.

Periodic livestock grazing also occurs on private land. However, no information on livestock
numbers was obtained for these areas. Field surveys completed in April 2007 observed no
livestock on private lands, and less than 10 animals were identified on private land areas during
October 2007.

The timing of grazing activities within the watershed is also important. Grazing allotment
information has indicated that grazing practices occur on high elevation public lands during the
summer and fall seasons. In some areas of the state, livestock numbers in lower elevations of the
watershed can increase during the late fall, winter, and spring months as animals are moved from
public lands to privately owned pastures. Field surveys confirm that little or no animals were
held on private lands during 2007. Therefore, it is anticipated that actual use numbers of
livestock grazing on federal and state allotments represent annual loads associated with this
source.

The following assumptions were made so that loads from livestock grazing could be calculated.

1. Grazing allotments are used at the average actual use reported from 1997-2006.
Allotment data provided by federal agencies included some years where only the
authorized or actual number was reported. During these years the same number was used
to represent both categories and incorporated into the mean value.

46

2. Livestock are distributed equally over the area of each grazing allotment and can be
accounted for in a density of animal units/acre and translated into a unit area load of
TP/acre/day.

Table 4.1 lists all grazing allotments that intersect the project area. Additional descriptive
information such as the number of permitted animals and the days of use in each allotment is also
provided. Animal densities were calculated by dividing the total allotment area by the average
actual use reported for each allotment by federal and state agencies. Grazing allotments were
then clipped to the project area using a GIS. The total number of cattle were determined by
multiplying animal density by the acreage of livestock grazing areas.

The process that delivers loading due to livestock grazing includes direct deposition in existing
water bodies and surface runoff from areas where cattle have grazed. Given the dispersed nature
of grazing activities, it is assumed that only animal waste deposited in the area within 100 meters
(about 300 feet) of an existing water body contributes to loading.

In considering the two mechanisms by which loading occurs, it is also assumed that 100 percent
of the TP associated with manure deposited within 10 meters (about 30 feet) of an existing water
body contributes to loading (delivery ratio = 100 percent simulating direct deposition) and that
approximately 10 percent of manure deposited between 10 and 100 meters from an existing water
body contributes to loading (delivery ratio = 10 percent). Table 4.2 lists the contributing area
associated with these two zones. These areas were calculated by buffering the streams and
reservoirs using GIS.

According to the Agricultural Waste Management Handbook (NRCS 1992) the average weight of
a grazing cow is approximately 1,000 pounds and the average TP production rate is
approximately 0.12 pounds of TP/1,000 pound animal/day. Based on these numbers, the unit area
loads were calculated for each allotment by multiplying the animal density (number of animals
per square mile) by the TP production rate. The unit area loads were then adjusted based on
information regarding actual use of each allotment. Table 4.2 indicates the total loads associated
with each grazing allotment, as well as for the entire watershed and the portion of that load
delivered to Recapture Reservoir. The load to the reservoir has been adjusted to account for
diversions that remove flow and loading from the study area. Table 4.3 indicates the annual TP
loads generated by livestock grazing in each major tributary watershed flowing to Recapture
Reservoir and how this load is distributed among federal and state agencies.

As mentioned previously, no information is recorded on the exact distribution of livestock
grazing. Field observations indicate the lack of riparian corridors that would typically serve to
concentrate animals seeking forage, shade, and water. It is not certain at this time exactly how
much of the TP load generated by livestock grazing is delivered to Recapture Reservoir by
tributary streams. The assumptions used to calculate loads have been conservative and reflect
some indication of the relative magnitude this source could contribute to project area streams and
ultimately to Recapture Reservoir. Loads from livestock grazing do not account for processes
that remove TP from flowing waters in streams such as adsorption, settling, and uptake by aquatic
vegetation.

47

Table 4.2. Total phosphorus loads associated with livestock grazing in the Recapture Reservoir TMDL project area.
Agency Allotment Pasture Area 0-10m
(ac)
Area 10-
100m (ac)
Days of
use
Unit area load
(kg/ac/day)
TP Load 0-
10m (kg/yr)
TP Load 10-
100m (kg/yr)
Total Load
(kg/yr)
USFS Camp
Jackson
Brushy Basin 91 717 32 0.0066 19.2 15.2 34.4
USFS Bulldog Dry Canyon 59 541 26 0.0014 2.3 2.1 4.3
USFS Camp
Jackson
Johnson
Creek
264 2196 28 0.0016 12.2 10.2 22.4
USFS Lakes-S Peak Bulldog 91 836 32 0.0020 5.8 5.3 11.2
USFS Lakes-S Peak South Peak 91 836 100 0.0022 19.7 18.1 37.8
USFS Lakes-S Peak Lakes 91 836 107 0.0045 43.6 40.2 83.7
SITLA SITLA SITLA-2 8 63 57 0.0040 1.9 1.4 3.3
SITLA SITLA SITLA-32 31 272 57 0.0019 3.4 3.0 6.4
SITLA SITLA SITLA-36 13 112 57 0.0035 2.7 2.2 4.9
USFS Bulldog Bulldog 54 476 26 0.0014 2.0 1.7 3.7
BLM Bulldog-
BLM
Bulldog 317 2462 122 0.0006 23.2 18.0 41.2
BLM Bulldog-
BLM
Bulldog 317 2462 23 0.0029 21.1 16.4 37.6
USFS Camp
Jackson
Recapture 281 2326 48 0.0023 31.8 26.3 58.1
USFS Bulldog Recapture 96 810 27 0.0010 2.6 2.2 4.8
Total Load to Stream (kg/yr) 191.5 162.4 353.9
Total Load to Reservoir
(kg/yr)
171.6 145.6 317.3

48
Pollutant loads from diffuse runoff are discussed below and include a detailed discussion of the
methodology used to calculate loads. Diffuse runoff loads account for the effect of surface runoff
by landcover type and are assumed to incorporate loading from livestock grazing.

Table 4.3. Total phosphorus loads from grazing to Recapture Reservoir defined by
watershed or by land owner.
Watershed BLM SITLA USFS Total (kg/yr)
Johnson Creek 5.8 0.8 24.8 31.5
Recapture Creek 16.1 1.8 61.9 79.7
Bulldog Creek 36.7 4.9 138.8 180.5
Bullpup Creek 5.2 6.4 0.4 12.1
Recapture Reservoir 12.9 0.6 - 13.5
Total 76.8 14.5 225.9 317.3

4.2 DIFFUSE RUNOFF
In the Recapture Reservoir watershed, the major source of pollutant loading to surface water is
runoff of precipitation moving phosphorus from diffuse sources into streams and reservoirs.
Examples of diffuse sources include the following:

 Phosphorus in compounds bound to naturally occurring soils and minerals running
off from different landcover (vegetation) types.

 Nutrients and other constituents associated with erosion from upslope areas disturbed
by grazing or forestry activities.

 Surface runoff from developed agricultural and urban areas that contains agricultural
chemicals including fertilizers and pesticides.

 Nutrients and other constituents associated with erosion from other human disturbed
areas (including trails, roads, and dispersed camping sites).

All of these sources are related to land use. Urban and intensive agricultural land uses make up a
small percentage of the land uses in the watershed. Because the region experiences relatively low
precipitation – 13.3 inches annually in nearby Blanding – the more intensive agricultural uses are
thought to be a minor contributor to phosphorus runoff to surface water. The only agricultural use
existing over substantial portions of the watershed is dispersed livestock grazing, on both private
and public lands. Low precipitation results in generally low stream flows, which in turn
concentrates animals around artificial water sources and away from natural streams. This gives
vegetation and soils an opportunity to reabsorb any phosphorus in surface runoff.

Factors such as soil type, slope, and riparian conditions, also influence the amount of nutrient
loading to surface waters but given that phosphorus does not seem to be a major pollutant in the
watershed’s streams or the reservoir itself, it was felt that an adequate TP runoff model could be
developed based on just a few characteristics, including: patterns of hydrologic flow based on
precipitation; spatial runoff patterns based on relationships between subwatersheds, diversions
and interbasin transfers; and spatial patterns and types of land uses and their associated
phosphorus loads.

49

Flow for the TP runoff model was taken from stream flow estimates that were developed in the
water budget model (see Section 2.6.1). Near the top of the watershed (see Figure 2.1), an
interbasin transfer brings water from Indian Creek north of the natural Recapture Reservoir
watershed via a tunnel through the Abajo Mountains into Johnson Creek. Blanding City takes
advantage of the increased flow in Johnson Creek and diverts some of that water via a pipeline.
Further downstream a canal transfers water from the adjacent Dry Wash watershed west of the
natural Recapture Reservoir watershed to Johnson Creek, after holding back the first 185 acre-
feet for livestock in a small reservoir. Several miles below, a Utah DWQ water quality station
monitors phosphorus and other parameters on Johnson Creek just above a point where most of the
creek is diverted in the summer into the Upper Canal for transfer out of the basin into two
reservoirs above Blanding City for irrigation. Johnson Creek then joins Recapture Creek, which
has collected water from high altitude areas to the east. The combined streams then flow
unimpeded into Recapture Reservoir. (Johnson Creek is no longer diverted into the Lower Canal.)
Further to the east two other tributaries, Bulldog Creek and Bullpup Creek drain lower elevations
into the reservoir directly. Lands immediately around the reservoir drain into the reservoir
directly.

The water budget model calculated runoff by first determining the 12 watershed subdivisions
within the Recapture Reservoir drainage based on the locations of stream gages, water quality
monitoring stations, and diversion points. These were then further divided based on bands of
annual precipitation to yield a total of 61 areas for analysis. The water budget model then
calculated runoff as acre-feet per square mile using an exponential function that was fit initially to
the upper Recapture Creek watershed, which has no diversions, and then adjusted slightly to
minimize error when applied to the only other two subwatersheds within the watershed where
some long-term stream gage data was available for calibration, Recapture Creek Below Johnson
Creek and Recapture Reservoirs’ discharge itself.

Different land uses generate different loads of phosphorus for transport by runoff. Export
coefficients, in the form of kilograms/hectare/year, have been successfully applied to these
different land uses in other TMDL studies. Table 4.4 lists the land use distributions in the
Recapture Reservoir watershed in terms of acres and percent. Over 95 percent of the land use in
the Recapture Reservoir watershed is forest and range land, with smaller areas of agriculture in
the south and southeast portions of the watershed. The spatial distribution of these land uses is
displayed visually in Figure 2.3. Based on results in basins with similar landcover and hydrology,
a table of initial loading coefficients was developed, shown in Table 4.5.

Table 4.4. Land use distribution in the Recapture Reservoir watershed.
Area
Land Use Category Acres Square Miles Percent
Agriculture 1,142 1.78 2.78
Urban 2 0.00 0.01
Forest Land 18,673 29.18 45.38
Pinyon-Juniper 16,713 26.11 40.62
Range Land 3,802 5.94 9.24
Barren 611 0.95 1.48
Water 201 0.31 0.49
Total 41,143 64.29 100

50

Table 4.5. Initial coefficients for phosphorus load runoff from land uses used in total
phosphorus runoff model.
Land Use Category Export Coefficients (kg/ha/yr)
Agriculture 1.00
Urban 1.00
Forest Land 0.05
Pinyon-Juniper 0.25
Range Land 0.10
Barren 0.20
Water 0.00

In order to calculate diffuse runoff loads, a map of landcover, acquired from the Southwest
ReGap project (USURS/GISL), was overlain on the 61 areas from the water budget model to
create a table of almost 3,100 polygons. Twenty-six detailed landcover types were summarized
into the seven land uses above. Each polygon therefore had properties of runoff (based on the
area within a particular polygon and the exponential function of precipitation), phosphorus loads
(based on the export coefficient for each land use), as well as ownership (BLM, USFS, Utah
SITLA, and private) and subwatershed location for purposes of summary for the load
calculations. The mass load of phosphorus was then calculated by finding the ratio of modeled
precipitation runoff to total expected precipitation for each polygon and applying this ratio to the
loads determined by multiplying the phosphorus export coefficient by the area of each polygon.
These load values could then be summed in various combinations to yield loads for each
landowner, land use, and subwatershed.

Calculating the load expected to enter Recapture Reservoir required processing these flows and
loads from the top of the watershed to the reservoir itself, taking into consideration the
contributions of flows and loads from each watershed subdivision, and the diversions of flows
and loads out of the watershed via a pipeline or canal. This incremental approach was necessary
because concentrations of phosphorus varied as precipitation and patterns of land use changed
through the watershed.

An application of this model is shown in Table 4.6 for average annual TP loads to Recapture
Reservoir that illustrates how each tributary or diversion contributes or removes different
combinations of flow and phosphorus load. The model was calibrated by increasing the export
coefficients by a factor of 3.0 to achieve a TP concentration similar to that measured at the
UDWQ Water Quality Station 4953460 on Johnson Creek of approximately 0.025 mg/L (see
Residual in Johnson Creek - at UDWQ monitoring station value of 0.029 mg/L in the table
below). The model predicted a concentration of 0.046 mg/L which is very similar to the value at
the monitoring site 1/4 way up the reservoir (0.030 mg/L at Station 5958020; see Section 3, Table
11). The 0.046 value of TP would be expected to drop significantly as phosphorus settles out, so
it was considered a reasonable estimate for reservoir concentrations measured at the dam (0.024
mg/L at Station 5958010).

51
Table 4.6. Incremental contributions and diversions of flow and phosphorus loads from diffuse sources in
the watersheds feeding Recapture Reservoir during an average precipitation year.
Source of Flow and Load and Diversion
Modeled
Runoff
(acre-feet)
Modeled Load
TP (mg/L) (pounds) (kg)
Interbasin Transfer from upper Indian Creek
watershed 2,047 155.8 70.7 0.028
Upper Johnson Creek watershed above the
Blanding Pipeline 4,019 284.9 129.2 0.026
Less diversion to the Blanding Pipeline (976) (71.7) (32.5) 0.027
Residual in Johnson Creek 5,091 369.0 167.4 0.027
Dry Wash runoff 133 9.3 4.2 0.026
Dry Wash flow held back in small reservoir (first
185 acre-feet) (133) (9.3) (4.2) 0.026
Residual in Johnson Creek 5,091 369.0 167.4 0.027
Johnson Creek watershed below the Blanding
Pipeline diversion but above the UDWQ water
quality monitoring station 907 97.8 44.4 0.040
Residual in Johnson Creek 5,998 466.8 211.7 0.029
Upper Canal diversion - -
Provided by the watershed captured by canal 31 9.6 4.4 0.113
Diversion from Johnson Creek to supply balance
of canal flow estimated at 9 cfs for 6 months (3,227) (251.1) (113.9) 0.029
Residual in Johnson Creek - at UDWQ
monitoring station 2,771 215.7 97.8 0.029
Add in other watersheds - -
Lower Johnson Creek (low elevation runoff
pattern) 35 15.7 7.1 0.164
Upper Recapture Creek above USGS gage 908 68.6 31.1 0.028
Upper Recapture Creek below USGS gage 412 51.0 23.1 0.045
Lower Recapture Creek (low elevation runoff
pattern) 32 14.9 6.8 0.172
Upper Bulldog Creek 287 47.0 21.3 0.060
Lower Bulldog Creek (low elevation runoff
pattern) 96 60.9 27.6 0.232
Bullpup Creek 30 19.9 9.0 0.245
Watershed flowing directly into Recapture
Reservoir 6 2.9 1.3 0.169
Total Flow into Recapture Reservoir 4,577 496.5 225.2 0.040
Evaporative effects on phosphorus concentrations (606) - - 0.000
Effective balance of flows and loads into
Recapture Reservoir 3,972 496.5 225.2 0.046

These annual flows and loads can also be distributed monthly for different water years. The tables
below apply the monthly pattern of the USGS stream gage in upper Recapture Creek Near
Blanding to flows from the higher elevation subdivisions of the watershed. The monthly pattern
of the USGS stream gage on lower Recapture Creek Below Johnson Creek was used to calculate
flows from lower elevation subdivisions of the watershed. Table 4.7 shows monthly flows and

52
loads for an average year, before evaporation effects at the reservoir, based on flows of 2001-
2007 (when average annual precipitation was 12.95 inches at Blanding, compared with the long-
term precipitation average of 13.3 inches).

Table 4.7. Modeled monthly runoff flows and total phosphorus loads to Recapture
Reservoir for average annual precipitation year.
Month Flow (acre-feet)
TP Load
(pounds) (kg)
Jan 4 0.4 0.2
Feb 55 6.0 2.7
Mar 471 51.1 23.2
Apr 1,528 165.8 75.2
May 1,704 184.9 83.9
Jun 666 72.3 32.8
Jul 66 7.2 3.3
Aug 10 1.1 0.5
Sep 7 0.8 0.4
Oct 18 1.9 0.9
Nov 44 4.7 2.1
Dec 3 0.3 0.1
Total 4,576 496.5 225.2

The model also allows estimates for flows and TP loads to the reservoir based on years of greater
or lesser precipitation. Table 4.8 shows estimates of flows and loads for 2002 and 2005,
respectively dry and wet years in Blanding. These were obtained by adjusting average annual
runoff as a ratio of that year’s precipitation to the average precipitation of 2001-2007, and then
applying monthly patterns to the annual results as above.

Table 4.8. Modeled monthly runoff flows and total phosphorus loads to Recapture
Reservoir for 2002 and 2005.

Month
2002 - Dry 2005 - Wet
Flow (acre-feet) TP Load (kg) Flow (acre-feet) TP Load (kg)
Jan 1 0.1 5 0.2
Feb 23 1.3 76 3.7
Mar 199 11.1 647 31.4
Apr 647 35.9 2,102 101.9
May 722 40.1 2,344 113.7
Jun 282 15.7 916 44.4
Jul 28 1.6 91 4.4
Aug 4 0.2 14 0.7
Sep 3 0.2 10 0.5
Oct 7 0.4 24 1.2
Nov 18 1.0 60 2.9
Dec 1 0.1 3 0.2
Total 1,937 107.6 6,293 305.2

53
Tables 4.9 and 4.10 show modeled TP loads for the Recapture Reservoir watershed by
landowner, land use, and subwatershed. The largest loads to the reservoir are contributed by
USFS lands, as expected because these account for the largest areal extent of the watershed. For
similar reasons, forest, pinyon-juniper, and range land uses account for the largest loads to the
reservoir. Among the tributaries, Johnson Creek contributes the highest loads.

Table 4.9. Annual total phosphorus loads (kg/year) by land use and landowner to
Recapture Reservoir for average annual precipitation year.
Land Use
Landowner
BLM USFS SITLA Private Total
Percent of
Total
Agriculture 0.2 0.2 0.3 14.3 15.0 7
Urban 0.0 0.0 0.0 0.0 0.0 0
Forest Land 0.1 76.4 0.0 0.4 76.9 34
Range Land 0.2 34.9 0.0 1.8 37.0 16
Pinyon-Juniper 15.6 46.6 2.0 7.1 71.4 32
Barren 0.0 24.8 0.0 0.1 24.9 11
Water 0.0 0.0 0.0 0.0 0.0 0
Total 16.2 182.9 2.3 23.8 225.2 100
Percent of total 7% 81% 1% 11% 100%

Table 4.10. Annual total phosphorus loads (kg/year) by subwatershed and landowner to
Recapture Reservoir for average annual precipitation year.
Subwatershed
Landowner
BLM USFS SITLA Private Total
Percent of
Total
Johnson Creek 4.3 98.6 0.1 2.0 104.9 47
Recapture Creek 3.9 56.3 0.2 0.6 61.0 27
Bulldog Creek 6.2 27.8 0.7 14.3 48.9 22
Bullpup Creek 0.8 0.2 1.2 6.8 9.0 4
Recapture
Reservoir Direct 1.1 0.0 0.1 0.1 1.3 1
Total 16.2 182.9 2.3 23.8 225.2 100
Percent of Total 7% 81% 1% 11% 100%

4.3 IN-STREAM POLLUTANT LOAD CALCULATION
Based on the data available for the Recapture Reservoir watershed, pollutant loads can be
calculated at two monitoring locations where flow and water quality concentrations have been
measured. Loads calculated in this manner are considered to be most accurate if measurements
are collected at the same time (i.e. paired measurements) and represent the full range of flow
conditions at a given monitoring location. Error can be introduced into the calculation of
pollutant loads when measurements of flow and water quality are measured independent of each
other.

54

A review of the original data set, including the number of samples and sample dates should
accompany any assessment of pollutant load calculations. This is particularly important when
attempting to characterize loads from nonpoint pollutant sources, which are highly dependent
upon surface runoff generated during storm events or rapid snowmelt. Pollutant loads should be
based on measurements collected across a representative time period that include both drought
and high flow conditions as well as all seasons of the year. Such a comprehensive data set allows
calculation of meaningful monthly and annual loads.

A review of the data available at stream monitoring stations in the Recapture Reservoir watershed
indicated that measurements were insufficient to calculate more than daily loads. Table 4.11
shows the few actual measurements of tributary TP loads in the Recapture Reservoir watershed.
In each case, a flow (in cfs) was measured at the same time as a concentration of TP (“non-
detect” values were assigned a concentration of 0.01 mg/L). The daily load is calculated from
these two values. Of interest are the concentrations for Johnson Creek that help to validate the
concentrations generated by the TP runoff model.

4.4 LOADING SOURCE SUMMARY
Pollutant loads were calculated for livestock grazing and diffuse runoff. Loads from livestock
grazing indicate the relative contributions to Recapture Reservoir from tributary watersheds and,
based on management responsibility for these watersheds, relative contributions by land
management agencies. The loads resulting from this calculation were not calibrated with
monitoring data and likely overestimate actual loads delivered to the reservoir (because they do
not account for the processes of adsorption, settling, and other factors that are present and serve to
remove phosphorus loads as they are transported through stream systems). To account for other
sources including grazing, and to more accurately project loads delivered to the Reservoir, a
diffuse runoff model was developed.

Pollutant loads from diffuse runoff were adjusted to meet a concentration measured at the stream
monitoring station on Johnson Creek. Loads shown for Recapture Reservoir from diffuse runoff
were adjusted for diversions on Johnson Creek that remove flow and pollutant loads from the
study area. As indicated in Table 4.7, the annual average TP load to Recapture Reservoir is 225.2
kg/yr. This load is significantly less than the load indicated by the livestock-based calculation
discussed above, for the reasons indicated. Therefore, the results of the diffuse runoff model
provide the most accurate indicator of actual load, and the results of the livestock based
calculation provide the most accurate breakdown of livestock’s contribution by watershed and
land ownership. Similarities between the two profiles indicate that livestock is an important
contributor; differences indicate that other loading processes are also at work.

Using available data, daily loads were calculated at the two stream monitoring stations in the area
including Johnson Creek and Bulldog Creek. Annual and monthly loads were not calculated for
these sites due to the high seasonal variability in flow that occurs at these locations which was not
reflected in the limited data available. TP concentrations measured at Johnson Creek helped to
validate the TP runoff model.

55
Table 4.11. Measured daily total phosphorus loads from tributaries of Recapture
Reservoir.
Activity Start
TP Concentration
(mg/L) Stream Flow (cfs) Daily Load (kg)
Bulldog Creek UDWQ Station 4953510
12/14/1988 0.034 0.1 0.002
2/22/1989 0.030 0.4 0.122
12/6/1989 0.017 0.1 0.002
1/24/1990 0.030 0.1 0.006
2/12/1992 0.020 0.3 0.266
4/1/1992 0.048 6.2 0.728
5/14/1992 0.363 0.1 0.005
3/31/1993 0.024 32.8 2.407
6/9/1993 0.009 0.4 0.017
6/28/1995 0.125 0.3 0.022
6/23/1999 0.007 5 0.416
Johnson Creek Above Recapture Reservoir UDWQ Station 4953460
4/1/1998 0.010 11 0.269
5/20/1998 0.010 28 0.685
6/3/1998 0.010 25 0.611
6/23/1998 0.010 13 0.318
3/26/2003 0.037 2.4 0.217
4/16/2003 0.042 7.9 0.812
5/7/2003 0.010 11.6 0.284
5/21/2003 0.024 3.5 0.205
6/4/2003 0.010 3 0.073
6/18/2003 0.010 1 0.024
6/7/2005 0.010 5 0.122
8/31/2005 0.010 5 0.122
11/30/2005 0.010 1 0.024
3/29/2006 0.010 3.5 0.086
5/10/2006 0.192 3 1.409
7/19/2006 0.010 0 0.000

56
5.0 TMDL ANALYSIS

Recapture Reservoir is included on the Utah 2006 303(d) list as impaired for low dissolved
oxygen (DO). The level of impairment is defined by minimum DO requirements designed to
protect cold water fish species. The purpose of this TMDL is to restore full support to the
beneficial uses assigned to the reservoir. A standard approach to completing a TMDL is to
recommend a water quality endpoint that will support designated beneficial uses followed by a
target load for the pollutant of concern that will allow the endpoint to be met. The target load and
necessary load reductions are allocated among the pollutant sources.

This TMDL assessment has gone through the process of defining existing water quality
conditions as well as processes that might contribute to low DO in Recapture Reservoir. The
results indicate that the typical approach of defining and implementing load reductions would
likely not restore support to assigned beneficial uses of Recapture Reservoir. The reasons for this
argument are outlined below, followed by recommendations to preserve water quality in the
reservoir.

As discussed previously, DO is known to be consumed following oxidation of organic matter
which can include algal material in eutrophic reservoirs. Measurements of Chl-a in Recapture
Reservoir have been used in a TSI assessment that was presented in Chapter 3. The results of this
assessment indicate that Chl-a concentrations are generally at levels representing oligotrophic to
mestrophic conditions. Growth of algae is influenced by the presence of nutrients including
phosphorus and nitrogen. TSI results indicate that TP concentrations are primarily mesotrophic
but sometimes observed at levels representing eutrophic conditions. A threshold used to prevent
excessive algae growth in reservoirs is a TP concentration of less than 0.025 mg/L. Average
levels of TP since 1999 in Recapture Reservoir are around 0.030 mg/L, only marginally higher
than the 0.025 pollution indicator level. The highest TP concentrations were consistently
measured at greater depths with less light penetration, making it unlikely that TP levels are a
major contributor to an algal problem, if it exists, and thus the cause of DO impairment.

The existing data indicate that the major factor in low DO levels is a low mixing rate from
inflowing oxygenated water. The reservoir is located in a region of low annual rainfall (13.3
inches in nearby Blanding). Although part of the reservoir’s watershed is found in the Abajo
Mountains, with summits over 11,000 feet, much of the runoff from the mountain streams is
diverted into pipelines or canals for culinary or irrigation use. Low tributary inflows therefore
reduce the opportunity for high-oxygen runoff to mix into the reservoir layers.

The reservoir is capable of becoming well mixed with respect to DO after periods of abnormally
high precipitation, however. The last time the reservoir is known to have been thoroughly mixed
was in early summer of 2005, after more than 11 inches of precipitation fell after January 1 in
Blanding. Most of this precipitation likely occurred in the form of snow and probably didn’t
contribute runoff until March or April (no stream gage information was available for Johnson
Creek, the main tributary to the Reservoir). Within weeks of being fully mixed, however, the
reservoir returned to a stratified pattern. Other periods of reduced stratification documented in the
4 years for which data is available also seem to follow months of above average precipitation.

Reservoir depth profiles measured in 2001, 2003, 2005, and 2006 show that the surface layers of
the reservoir are typically higher in DO than deeper layers. In late summer the reservoir routinely

57
exhibits a clear and sharply stratified boundary between layers of high and low concentrations of
DO. Water temperatures in the reservoir also show a gradient during those periods of critically
low DO, with surface temperatures in the upper 2 meters of the reservoir as high as 25°C and
decreasing to less than 10°C in 10–15 meters of depth.

As indicated in Table 3.8, cold water fish need temperatures less than 20°C. In the shallower
upper reaches of the reservoir there is no depth with temperatures less than 20°C, so cold water
species are forced to migrate to areas of the reservoir near the dam where the water is deeper and
colder. However, at depths with sufficiently low water temperatures, DO concentrations are only
marginally above 4.0 mg/L. During some years profile measurements indicate no water depths at
any of the three monitoring sites in the reservoir with temperatures less than 20°C and DO
concentrations above 4.0 mg/L, which are needed to support a viable cold water fishery.

Beneficial use of Recapture Reservoir was initially defined following consultation with Utah
DWR and a review of information that characterized the physical, chemical, and biological
properties of the water body. Following this assessment it was determined that the reservoir
would be capable of supporting cold water fish species. As indicated in Section 3.3.3, Biological
Data, Utah DWR discontinued stocking the reservoir with cold water fish species in 2001 due to
predation by invasive warm water species including Northern Pike. Utah DWR has indicated that
they plan to continue to manage the reservoir as suitable habitat for warm water fish (Birdsey
2008).

Based on the analysis of existing data and knowledge of local reservoir conditions, it is unlikely
that DO levels can be restored through lowering nutrient concentrations. However, it is important
that nutrient concentrations do not increase beyond existing levels. Increased tributary inflow
would improve mixing of stratified layers and provide a source of DO that is higher than
concentrations observed at depth for the three reservoir monitoring stations. However,
implementation of TMDLs in Utah does not rely upon flow modification. Mechanical reaeration
of the reservoir would also serve to restore DO to the necessary levels but would be cost-
prohibitive.

Monitoring data indicate that it is possible for the reservoir to support a beneficial use associated
with Class 3B criteria. Late summer DO concentrations are typically greater than 4 mg/L for at
least 5–7 meters of depth as shown by reservoir profiles, and maximum temperatures are all less
than 27°C. Table 5.1 indicates the percent of samples that violate Class 3B criteria for DO,
temperature, and pH as shown by measurements of reservoir profiles from 2001 through 2006.

58
Table 5.1. Water quality at Recapture Reservoir monitoring sites.
DO pH Temperature
Date Depth
(m) Samples Mean
(mg/L)
Total
column
% <3.0 mg/l
Status1 Mean 6.5>%>9.0 Status
1
Mean
(oC) % >27 C Status1
Reservoir Station 5958010 – Recapture Reservoir Above Dam 01
6/13/2001 21.8 23 5.37 4.34 FS 7.72 0 FS 12.39 0 FS
8/14/2001 20.4 22 2.52 68.18 NS 7.67 0 FS 15.39 0 FS
6/4/2003 15.5 17 5.26 29.41 FS 7.78 0 FS 13.93 0 FS
8/14/2003 11.8 12 2.12 75 NS 7.52 0 FS 17.23 0 FS
6/7/2005 28.9 28 7.28 0 FS 7.88 0 FS 10.66 0 FS
7/13/2005 18.4 20 4.84 0 FS 8.24 0 FS 13.84 0 FS
8/31/2005 14.6 17 2.91 52.94 NS 7.42 0 FS 15.93 0 FS
10/5/2005 14.7 16 4.46 37.5 FS 7.63 0 FS 14.08 0 FS
6/22/2006 21.1 23 5.07 13.04 FS 7.9 0 FS 13.72 0 FS
7/19/2006 18.2 19 2.79 57.89 NS 7.58 0 FS 16.6 0 FS
8/24/2006 3.5 5 6.19 0 FS 8.14 0 FS 22.42 0 FS
9/22/2006 18 19 6.02 21.05 FS 8.23 0 FS 14.22 0 FS
Reservoir Station 5958020 – Recapture Reservoir ¼ Way Up Reservoir 02
6/13/2001 3.3 5 7.97 0 FS 8.49 0 FS 18.94 0 FS
8/14/2001 14.1 15 3.58 53.33 NS 7.8 0 FS 18.06 0 FS
6/4/2003 14 15 5.56 26.67 FS 7.83 0 FS 14.44 0 FS
6/7/2005 13.3 14 7.18 0 FS 7.8 0 FS 12.72 0 FS
7/13/2005 20.6 22 4.02 0 FS 8.02 0 FS 13.5 0 FS
8/31/2005 9.5 11 4.1 36.36 FS 7.57 0 FS 18.67 0 FS
10/5/2005 17 18 4.02 38.89 FS 7.61 0 FS 13.49 0 FS
6/22/2006 14.7 17 5.62 15.79 FS 8.1 0 FS 16.27 0 FS

59
Table 5.1. (cont’d) Water quality at Recapture Reservoir monitoring sites.
DO pH Temperature
Date Depth
(m) Samples Mean
(mg/L)
Total
column
% <3.0 mg/l
Status1 Mean 6.5>%>9.0 Status1
Mean
(oC) % >27 C Status1
7/19/2006 11.8 13 3.66 46.15 FS 7.71 0 FS 20 0 FS
8/24/2006 6.2 8 5.06 12.50 FS 8.01 0 FS 22.08 0 FS
Reservoir Station 5958030 – Recapture Reservoir ½ Way Up Reservoir 03
6/13/2001 7 8 7.76 0 FS 8.35 0 FS 17.52 0 FS
8/14/2001 5.2 7 6.70 0 FS 8.41 0 FS 22.65 0 FS
6/4/2003 9.4 11 6.81 0 FS 8.02 0 FS 16.50 0 FS
6/7/2005 12.1 12 6.96 0 FS 7.89 0 FS 12.57 0 FS
7/13/2005 12.0 14 3.71 30.77 FS 7.90 0 FS 16.35 0 FS
8/31/2005 4.1 6 6.11 0 FS 7.84 0 FS 21.78 0 FS
10/5/2005 7.1 9 6.83 0 FS 7.92 0 FS 15.62 0 FS
6/22/2006 9.1 11 6.69 12.5 FS 8.33 0 FS 18.51 0 FS
7/19/2006 6.8 8 5.43 14.29 FS 8.00 0 FS 22.88 0 FS
8/24/2006 5.3 7 5.51 14.3 FS 8.06 0 FS 22.12 0 FS
1 FS= full support of beneficial use, NS= non-support of beneficial use.

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5.1 WATER QUALITY TARGETS
The water quality targets selected by this TMDL assessment include the following:

 Average TP concentration calculated from TP profile measurements at three reservoir
monitoring stations not to exceed 0.025 mg/L.

 TP concentration not to exceed 0.05 mg/L at tributary inflow monitoring stations.

 Change beneficial use of reservoir from Class 3A, cold water aquatic life, to Class 3B,
warm water aquatic life, including recommended criteria for DO (3 mg/L) and
temperature (27°C).

 Site specific reservoir DO standard during July and August of 100 percent of DO
measurements in the water column epilimnion greater than 3 mg/L.

5.2 PERMISSIBLE LOADINGS
Permissible loadings are typically used to represent a mass that will produce a desired water
quality concentration. Recommendations can then be made to reduce existing loads to meet the
permissible load. The monitoring data presented in Chapter 3 indicate low concentrations of TP
that are close to the threshold of 0.025 mg/L used to limit algae growth and subsequent
decomposition and consumption of DO. Based on the measured concentrations of TP, the low
DO conditions observed in Recapture Reservoir are not a response to excessive algae growth and
decomposition. Low DO conditions are more likely due to a lack of tributary inflow and mixing
observed in reservoir profiles. Therefore no recommendations are provided for decreasing the
existing TP loading. However, it is recognized that TP loads and concentrations should not be
permitted to increase above existing levels.

5.3 SEASONALITY
The Clean Water Act requires that TMDLs include seasonality. Seasonality is addressed in this
TMDL by modeled loads to Recapture Reservoir on an annual and monthly basis. The
distribution of modeled loads was based on available data records that incorporate periods of wet
and dry years as well as months during which there is little or no tributary inflow to the reservoir.
Although reservoir water quality data is primarily limited to 1989–2006, monthly loads to the
reservoir are based on the distribution of monthly average flows shown by gage records that span
longer time periods including lower Johnson Creek (1975–1993) and upper Recapture Creek
(1965–2006). Annual variation in loading was based on annual precipitation records and the
long-term annual average for Blanding. The long-term average precipitation value is based on
the entire period of record that spans 1957-2006.

5.4 MARGIN OF SAFETY
The Clean Water Act also requires that TMDLs include a Margin of Safety (MOS). Generally,
the MOS is incorporated into the TMDL through the use of conservative assumptions or is

A - 61
specified explicitly by reserving a particular amount of the permissible loading. This TMDL uses
conservative assumptions to address the MOS.

Conservative assumptions have been made in some of the loading calculations and are discussed,
where applicable, in the text of this report. It should be noted that some degree of uncertainty is
associated with using the State of Utah's TP pollution indicator values of 0.05 mg/L for streams
and 0.025 mg/L for the reservoirs as the endpoints for this TMDL analysis. It is believed these
values are conservative, and future monitoring of the reservoir may show that TP endpoint values
could be higher than pollution indicator values. The loads specified in this report will be
evaluated in the future as additional water quality data is acquired. Follow-up monitoring will be
executed to ensure that the reservoirs appropriate beneficial uses as a warm water fishery are
being supported.

5.5 TMDL TARGET LOAD
The TMDL target load is defined by the existing TP load to Recapture Reservoir of 225 kg/yr
based on an annual average precipitation year. The method used to calculate loading to the
reservoir is described in detail in Section 4.2 and was calibrated using available monitoring data
from Johnson Creek. This load incorporates contributions from all pollutant sources including
livestock grazing. As additional monitoring data becomes available through future monitoring
efforts, this target load may be adjusted. However, without additional information, the TP water
quality endpoints of 0.025 mg/L and 0.05 mg/L should remain in place. Any change to the target
load must continue to meet these endpoints unless they are changed.

5.6 FUTURE GROWTH
It is estimated at this time that minimal change will occur in the tributary watersheds to Recapture
Reservoir in the future. Information obtained from population census as well as anecdotal
information from local agencies and stakeholders indicates that rural populations and land use
practices in the TMDL study area will remain fairly constant. However, recreational use of the
public lands managed by the Manti-LaSal National Forest will likely continue to increase.
Recreational use of the reservoir will likely mirror long-term statewide trends in use of resources
of this type and show slight increases over time. It is not anticipated that these changes will result
in significant load increases to the reservoir.

5.7 ALLOCATION OF POLLUTANT LOADS
It is recommended that pollutant loads remain allocated by land ownership, as the vast majority of
land contributing flow to Recapture Reservoir is managed by federal and state agencies.
Agricultural land practices that occur on private land are also significant due to their proximity to
tributary streams as well as the reservoir. Table 5.2 summarizes TP loading. The distribution of
loads by land ownership is presented in Table 5.3.

The TMDL allocation of pollutant loads is defined by modeled loads reflecting current
conditions. TP concentrations observed in reservoir profiles are low and very close to the desired
level of 0.025 mg/L used to control algal growth. Therefore, this TMDL will not include a
reduction in existing loads but will require that loads not increase beyond the current levels
defined in this assessment. BMPs that can be used to maintain existing loads are presented in

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Appendix C. It is recommended that these practices be implemented and maintained in order to
ensure that the TP water quality endpoint is met.

Table 5.2. Total phosphorus loading summary for Recapture Reservoir.
Loading Category Annual load (kg/yr)
Existing Loads 225
Permissible Loads 225
Reserve for Future Growth 0
Load Allocation 225
Necessary Reduction 0
Total 225

Table 5.3. Allocation of permissible total phosphorus loadings to Recapture Reservoir by land
ownership.
Agency Annual load (kg/yr) Percent of total
BLM 16 7
USFS 183 81
SITLA 2 1
Private 24 11
Total 225 100

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REFERENCES

Birdsey, P. 2008. Southeast Regional manager - Utah Division of Wildlife Resources. Personal
communication with Eric Duffin, Hydrologist, Cirrus Ecological Solutions, LC.
regarding management of Recapture Reservoir. February 2008.

Carlson, R.E. 1977. A trophic state index for lakes. Limnology and Oceanography. 22:361-369.

Carlson, R.E. and J. Simpson. 1996. A coordinator’s guide to volunteer lake monitoring methods.
North American lake Management Society. 96pp.

Casselman, J.M. and C.A. Lewis. 1996. Habitat requirements of northern pike (Essox lucius).
Canadian Journal of Fisheries and Aquatic Science 53(S1): 161-174.

DWR. (Utah Division of Wildlife Resources). 2007. Fish survey results conducted April 26,
2007 at Recapture Reservoir. http://wildlife.utah.gov/news/07-04/recapture.php

Hickman, T., and R.F. Raleigh. 1982. Habitat suitability index models: Cutthroat trout. U.S.
Department of Interior Fish and Wildlife Service FWS/OBS-82/10.5

High, J. 2007. Range Specialist, Manti LaSal National Forest. Personal communication with
Craig Limesand, Rangeland Ecologist, Cirrus Ecological Solutions LC, Logan, UT,
regarding municipal use of Recapture Reservoir water.

Inskip, P.D. 1982. Habitat suitability index models: northern pike. US Dept. of Interior, Fish &
Wildlife Service. FWS/OBS-82/10.17.

Judd, H.L. 1997. Utah's Lakes and Reservoirs: An Inventory and Classification of Utah's
Priority Lakes and Reservoirs. Utah Department of Environmental Quality, Division of
Water Quality, Salt Lake City, UT. January.

Matthews, K.R. and N. H. Berg 1997. Rainbow trout responses to water temperature and
dissolved oxygen stress in two southern California stream pools. Journal of Fish Biology
50 (1).

NRCS (Natural Resources Conservation Service). 1992. Agricultural waste management field
handbook. National Engineering Handbook. 210-AWMFH. United States Department
of Agriculture. Natural Resources Conservation Service, Washington, D.C.

Palmer, Curtis. 2008. Watermaster, Blanding Irrigation Company. Personal communication
with Eric Duffin, Hydrologist, Cirrus Ecological Solutions, LC. regarding flow and
diversions to Upper Canal. January 18, 2008.

Petrosky, B.R.; J. J. Magnuson. 1973. Behavioral Responses of Northern Pike, Yellow Perch and
Bluegill to Oxygen Concentrations under Simulated Winterkill Conditions. Copeia, Vol.
1973, No. 1.

A - 64
Raleigh, R.F. 1982. Habitat suitability index models: brook trout. US Dept. of Interior, Fish &
Wildlife Service. FWS/OBS-82/10.24.

Sigler, W.F. and J.W. Sigler. 1996. Fishes of Utah: A Natural History. University of Utah Press.

Stuber, R.J., G. Gebhart, and O.E. Maughan. 1982a. Habitat suitability index models:
Largemouth bass. U.S. Department of Interior Fish and Wildlife Service FWS/OBS-
82/10.16.

Stuber, R.J., G. Gebhart, and O.E. Maughan. 1982b. Habitat suitability index models: Green
sunfish. U.S. Department of Interior Fish and Wildlife Service FWS/OBS-82/10.15.

Thorton, J.L. 2007. Manager, San Juan Water Conservancy District. Personal communication
with Craig Limesand, Rangeland Ecologist, Cirrus Ecological Solutions LC, Logan, UT,
regarding municipal use of Recapture Reservoir water. January 2007.

USURS/GISL. SWReGap data acquired from Utah State University’s Remote
Sensing/Geographic Information Systems Laboratory, at: http://leupold.gis.usu.edu.

UDWR (Utah Division of Water Resources). 2000. Utah State Water Plan – Southeast Colorado
River Basin. <http://www.water.utah.gov/planning/SWP/SEastcol/swp_sc02.pdf>.
Accessed April 2007.

UDWR (Utah Division of Water Resources) 1981. Letter from D. Larry Anderson, Utah Division
of Water Resources, to Tom Skordal, U.S. Army Corps of Engineers, dated January 27,
1981.

A - 65

APPENDIX A - DATA

A - 66
LIST OF TABLES
Table A1. Measurement Frequency of Water Quality Stations in the Recapture Reservoir
Watershed…………………………………………………...……………….…..… A-4
Table A2. Summary Statistics for Station 4953440 - Recapture Creek at U262 Crossing. ..... A -5
Table A3. Summary Statistics for Station 4953460 - Johnson Creek Above Recapture
Reservoir Above Diversion . .................................................................................... A -6
Table A4. Summary Statistics for Station 4953500 - Recapture Creek Wash at U163 (191)
Crossing Below Reservoir. ....................................................................................... A -7
Table A5. Summary Statistics for Station 4953510 - Bulldog Canyon Creek Above
Recapture Reservoir. ................................................................................................. A -8
Table A6. Summary Statistics for Station 1900101 - Blanding-Johnson Creek. ...................... A -9
Table A7. Summary Statistics for Station 1900102 - Blanding-Indian Creek. ......................... A -9
Table A8. Summary Statistics for Station 100501052251 - Upper Indian Creek ..................... A -9
Table A9. Summary Statistics for Station 100501052451 - Lower Indian Creek. .................. A -10
Table A10. Summary Statistics for Station 100501251351 - Johnson Creek at Blanding
Pipeline Inlet. ........................................................................................................ A -10
Table A11. Summary Statistics for Station 5958010 - Recapture Reservoir Above
Dam 01 ................................................................................................................ A -75
Table A12. Summary Statistics for Station 5958020 - Recapture Reservoir 1/4 Way Up
Reservoir 02.......................................................................................................... A -76
Table A13. Summary Statistics for Station 5958030 - Recapture Reservoir 1/2 Way Up
Reservoir 03.......................................................................................................... A -77

LIST OF FIGURES
Figure A1. Seasonal parameter plots for station 4953440 from 1977-2000, including
dissolved oxygen, total phosphorus, and water temperature. ................................ A -78
Figure A2. Seasonal parameter plots for station 4953460 from 1997-2006, including
dissolved oxygen, total phosphorus, and water temperature. ................................. A -79
Figure A3. Seasonal parameter plots for station 4953500 from 1978, including water
temperature. ........................................................................................................... A -80
Figure A4. Seasonal parameter plots for station 4953510 from 1988-2001, including
dissolved oxygen, total phosphorus, and water temperature. ................................. A -81
Figure A5. Monthly parameter plots for station 5958010 from 1989-2006, including
dissolved oxygen and water temperature. ............................................................. A -82
Figure A6. Monthly parameter plots for station 5958020 from 1989-2006, including
dissolved oxygen and water temperature. ............................................................. A -83
Figure A7. Monthly parameter plots for station 5958030 from 1989-2006, including
dissolved oxygen and water temperature. ............................................................. A -84
Figure A8. Time series plots for station 4953440. ................................................................... A -85
Figure A9. Time series plots for station 4953460. .................................................................. A -86
Figure A10. Time series plots for station 4953500. ................................................................ A -87
Figure A11. Time series plots for station 4953510. ................................................................ A -88
Figure A12. Time series plots for station 1900101. ................................................................ A -89
Figure A13. Time series plots for station 1900102. ................................................................ A -89
Figure A14. Time series plots for station 100501052251. ...................................................... A -90

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Figure A15. Time series plots for station 5958010……………….……….……………..…. A -27
Figure A16. Time series plots for station 5958020………………………….….................... A -28
Figure A17. Time series plots for station 5958030……..…………………….…………….. A -29
Figure A18. Time series plots for station 1900101….………………………….................... A -29
Figure A19. Time series plots for station 1900102….……………………………………… A -30
Figure A20. Time series plots for station 100501052251….……………………………..… A -31

A - 68

.

Type 19
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100501052251 River/Stream 4
100501052451 River/Stream 5
100501251351 River/Stream 3
1900101 River/Stream 1 1 2 1 1 1
1900102 River/Stream 1 1 1
373954109270001 Well 1
374726109303001 Well 1
4953440 River/Stream 1 2 1 6 7 4 4 1 1
4953460 River/Stream 3 5 3 8 4
4953500 River/Stream 1 1 1
4953510 River/Stream 1 10 7 6 7 3 2 3 2 1
5958010 Lake 2 2 2 2 1 2 2 2 4
5958020 Lake 2 2 2 2 1 2 2 1 4
5958030 Lake 2 2 2 2 2 2 2 1 4
9185800 River/Stream 1 6 4 6 6 9 9 8 9 6
9378630 River/Stream 3 9 6 4 5 2 3 12 10 6 7 7 9 5 3 8 5 9 9 6
9378650 River/Stream 3 11 3 9 7 9 13 6 3 8 5 10 9 7 1
9378700 River/Stream 12 15 10 9 9 8 7 9 7 6 9 3 8 7 8 11 4 3 8
TABLE A1. MEASUREMENT FREQUENCY OF WATER QUALITY STATIONS IN THE RECAPTURE RESERVOIR WATERSHED. Shaded
cells indicate years during which monitoring occurred and numbers within shaded cells indicate the number of visits to each site that occurred during a given
year.

A - 69

TABLE A2. SUMMARY STATISTICS FOR STATION 4953440 - RECAPTURE CREEK AT U262 CROSSING.
Parameter n BDL1 Date Mean Median SD Geo. Mean Min Max Exceedance2 (%)
Ammonia (mgN/L) 5 4 1980 - 1997 - - - - - -
BOD (mg/L) 2 0 1977 - 1980 2.5 2.5 2.1 2 1 4 0
DO (mg/L) 5 0 1980 - 1997 7.8 7.7 1.4 7.7 6.6 10.2 0
1 0 2000-2000 7.73 - - - - -
Fecal Coliform (#/100 mL) 3 0 1977 - 1980 4,547 4,300 4,635 1,170 40 9,300 66.7
pH 11 0 1977 - 1997 8.3 8 0.6 8.2 7.7 9.5 18.2
2 0 2000 - 2000 8.4 8.4 0.1 8.4 8.4 8.5 0
Total Coliform (#/100 mL) 3 0 1977 - 1980 6,550 4,500 7,634 2,163 150 15,000 33.3
TDS (mg/L) 7 0 1977 - 1997 1,659 1,160 2,408 746.2 126 6,966 50
TP (mg/L) 4 0 1980 - 1988 0.12 0.06 0.17 0.04 0.01 0.37 50
TSS (mg/L) 7 2 1977 - 1997 3,122 2376 3679 1,247 <BDL> 9999 75
Water Temperature (oC) 8 0 1977 - 1997 14.7 14.4 7.8 12.7 5.5 24.5 0
Flow (cfs) 25 18 1977 - 1997 2.4 0.2 8.0 0.16 <BDL> 40 -
Specific Conductivity (umhos/cm@25oC) 12 0 1977 - 1997 1,033 1,011 718.7 746.1 180 1,870 -
2 0 2000 - 2000 419 419 31.1 418.4 397 441 -
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams:
Ammonia: pH dependent criteria calculated for individual data points as per Utah Code R317-2; Biochemical Oxygen Demand (BOD): <5 mg/L; Dissolved Oxygen (DO): (3a) >4.0; Fecal
Coliform: <200 colonies/100 mL; pH: >6.5 and <9.0; Total Coliform: <5,000 colonies/100 mL; Total Dissolved Solids (TDS): <1,200 mg/L; Total Phosphorus (TP): <0.05 mg/L; Total
Suspended Solids (TSS): <35 mg/L; Water Temperature: (3a) <20. 3 Value of the single sample.

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TABLE A3. SUMMARY STATISTICS FOR STATION 4953460 - JOHNSON CREEK ABOVE RECAPTURE RESERVOIR ABOVE
DIVERSION.
Parameter n BDL1 Date Mean Median SD Geo. Mean Min Max Exceedance2 (%)
Ammonia (mgN/l) 3 3 1997 - 1997 - - - - - -
17 14 1998 - 2006 0.04 0.04 0.01 0.04 <BDL> 0.06
DO (mg/L) 3 0 1997 - 1997 8.9 9.2 1.6 8.8 7.16 10.3 0
17 0 1998 - 2006 8.7 8.9 2.2 8.4 5 12.6 0
DP (mg/L) 1 0 2006 - 2006 0.033 - - - - -
pH 6 0 1997 - 1997 8.2 8.2 0.2 8.2 8.04 8.6 0
28 0 1998 - 2006 8.3 8.3 0.5 8.2 7.14 9.6 7.1
TDS (mg/L) 3 0 1997 - 1997 255.3 262 24.7 254.5 228 276 0
15 0 1998 - 2005 155.6 144 41.3 151.1 110 242 0
TP (mg/L) 1 0 1997 - 1997 0.0183 - - - - -
21 14 1998 - 2006 0.022 0.009 0.041 0.009 <BDL> 0.19 4.8
TSS (mg/L) 3 0 1997 - 1997 9.5 6 7.8 7.6 4 18.4 0
15 4 1998 - 2005 16.4 8.4 23.2 8.7 <BDL> 92.7 6.7
Water Temperature (oC) 3 0 1997 - 1997 9.5 10 8.4 5.3 0.86 17.7 0
15 1 1998 - 2006 9.9 6.79 8.6 4.6 <BDL> 23.5 20
Flow (cfs) 3 0 1997 - 1997 1.1 1 0.9 0.8 0.3 2
18 5 1998 - 2005 6.7 3.3 8.3 2.9 <BDL> 28
Salinity (mg/l@ 25oC) 12 1 2003 - 2006 0.14 0.14 0.04 0.13 <BDL> 0.2
Specific Conductivity
(umhos/cm@25oC)
6 0 1997 - 1997 426.3 427 35.9 425.1 369 479
26 0 1998 - 2006 238.1 226 79.6 225.3 95 391
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams:
Ammonia: pH dependent criteria calculated for individual data points as per Utah Code R317-2; Dissolved Oxygen (DO): (3a) >4.0; Dissolved Phosphorus (DP): <0.05 mg/L;
pH: >6.5 and <9.0; Total Dissolved Solids (TDS): <1,200 mg/L; Total Phosphorus (TP): <0.05 mg/L; Total Suspended Solids (TSS): <35 mg/L; Water Temperature: (3a)
<20 oC. 3 Value of the single sample.

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TABLE A4. SUMMARY STATISTICS FOR STATION 4953500 - RECAPTURE CREEK WASH AT U163(191) CROSSING BELOW
RESERVOIR.
Parameter n BDL1 Date Mean Median SD Geo. Mean Min Max
Exceedance2
(%)
Fecal Coliform (#/100 mL) 1 0 1978 - 1978 2,4003 - - - - - 100
pH 1 0 1978 - 1978 8.33 - - - - - 0
Total Coliform (#/100 mL) 1 0 1978 - 1978 903 - - - - - 0
TDS (mg/L) 1 0 1978 - 1978 2103 - - - - - 0
TSS (mg/L) 1 0 1978 - 1978 2,0003 - - - - - 100
Water Temperature (oC) 1 0 1978 - 1978 6.53 - - - - - 0
Specific Conductivity (umhos/cm@25oC) 1 0 1978 - 1978 2503 - - - - - -
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams:
Fecal Coliform: <200 colonies/100 mL; pH: >6.5 and <9.0; Total Coliform: <5,000 colonies/100 mL; Total Dissolved Solids (TDS): <1,200 mg/L; Total Suspended Solids
(TSS): <35 mg/L; Water Temperature: (3a) <20 oC. 3 Value of the single sample.

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TABLE A5. SUMMARY STATISTICS FOR STATION 4953510 - BULLDOG CANYON CREEK ABOVE RECAPTURE RESERVOIR.
Parameter n BDL1 Date Mean Median SD Geo. Mean Min Max Exceedance2 (%)
Ammonia (mgN/l) 16 16 1988 - 1997 - - - - - -
2 2 1999 - 2001 - - - - - -
DO (mg/L) 16 0 1988 - 1997 9.4 9.3 2.4 9.1 5.6 14.9 0
3 0 1999 - 2001 4.4 4.9 1.7 4.1 2.4 5.8 33.3
Fecal Coliform (#/100 mL) 1 1 1990 - 1990
pH 26 0 1988 - 1997 8.0 8.1 0.29 8.0 7.4 8.5 0
3 0 1999 - 2001 7.9 7.9 0.46 7.9 7.4 8.3 0
Total Coliform (#/100 mL) 1 0 1990 - 1990 240,0003 - - - - - 100
TDS (mg/L) 15 0 1988 - 1997 411.2 472 157.1 364.2 82 562 0
3 0 1999 - 2001 513.3 360 434.8 399.2 176 1004 0
TP (mg/L) 24 1 1988 - 1995 0.05 0.03 0.07 0.030 <BDL> 0.36 20.8
5 1 1999 - 2001 0.03 0.03 0.013 0.027 <BDL> 0.05 0
TSS (mg/L) 15 2 1988 - 1997 203.3 29 453.2 30.4 <BDL> 1700 40
3 1 1999 - 2001 19.2 16.8 11.8 16.8 <BDL> 32 0
Water Temperature (oC) 15 1 1988 - 1997 10.5 9.8 8.4 6.2 <BDL> 23.5 20
3 0 1999 - 2001 23.2 24.6 4.9 22.9 17.8 27.3 66.6
Fecal Strep (#/100 mL) 1 0 1990 - 1990 5003 - - - - -
Flow (cfs) 36 25 1988 - 1997 1.1 0.0 5.5 0.01 <BDL> 32.8
2 0 1999 - 1999 2.6 2.6 3.5 0.7 0.1 5
Salinity (mg/l@ 25oC) 1 0 2001 - 2001 0.13 - - - - -
Specific Conductivity
(umhos/cm@25oC)
26 0 1988 - 1997 764.7 770 445.2 664.5 125 2690
3 0 1999 - 2001 721.7 538 560.5 585.4 276 1351
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams:
Ammonia: pH dependent criteria calculated for individual data points as per Utah Code R317-2; Dissolved Oxygen (DO): (3a) >4.0; Fecal Coliform: <200 colonies/100 mL; pH: >6.5 and
<9.0; Total Coliform: <5,000 colonies/100 mL; Total Dissolved Solids (TDS): <1,200 mg/L; Total Phosphorus (TP): <0.05 mg/L; Total Suspended Solids (TSS): <35 mg/L; Water
Temperature: (3a) <20 oC. 3 Value of the single sample.

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TABLE A6. SUMMARY STATISTICS FOR STATION 1900101 - BLANDING-JOHNSON CREEK 1.
Parameter n BDL1 Range of Dates Mean Median SD Geo. Mean Min Max Exceedance2 (%)
Ammonia (mgN/l) 3 0 1981 - 1989 0.10 0.10 0.00 0.10 0.1 0.1 0
pH, lab 5 0 1977 - 1989 7.82 7.80 0.19 7.82 7.6 8.1 0
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams: Ammonia: pH
dependent criteria calculated for individual data points as per Utah Code R317-2; pH: >6.5 and <9.0.

TABLE A7. SUMMARY STATISTICS FOR STATION 1900102 - BLANDING-INDIAN CREEK.
Parameter n BDL1 Range of Dates Mean Median SD Geo. Mean Min Max Exceedance2 (%)
Ammonia (mgN/l) 1 0 1987 - 1987 0.23 - - - - -
pH, lab 1 0 1987 - 1987 8.23 - - - - -
Specific Conductivity (umhos/cm@25oC) 1 0 1987 - 1987 2303 - - - - -
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams: Ammonia: pH
dependent criteria calculated for individual data points as per Utah Code R317-2; pH: >6.5 and <9.0. 3 Value of the single sample.

TABLE A8. SUMMARY STATISTICS FOR STATION 100501052251 - UPPER INDIAN CREEK.
Parameter n BDL1 Range of Dates Mean Median SD Geo. Mean Min Max Exceedance2 (%)
DO (mg/L) 4 0 1980 - 1980 8.75 9.5 1.89 8.57 6 10 0
pH 4 0 1980 - 1980 7.88 7.4 1.1 7.82 7.2 9.5 25
TSS (mg/L) 4 0 1980 - 1980 1 1 0 1 1 1 0
Water Temperature (oC) 4 0 1980 - 1980 4.72 4.44 2.29 4.29 2.22 7.77 0
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams:
Dissolved Oxygen (DO): [standard used is dependent upon the respective site specific criteria] (3a) >4.0; pH: >6.5 and <9.0; Total Suspended Solids (TSS):
<35 mg/L; Water Temperature: (3a) <20 oC.

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TABLE A9. SUMMARY STATISTICS FOR STATION 100501052451 - LOWER INDIAN CREEK.
Parameter n BDL1 Range of Dates Mean Median SD Geo. Mean Min Max Exceedance2 (%)
DO (mg/L) 6 0 1980 - 1980 9.00 9.00 1.10 8.94 7 10 0
pH 4 0 1980 - 1980 8.03 7.60 0.99 7.98 7.4 9.5 25
TSS (mg/L) 5 0 1980 - 1980 23.30 14.00 23.94 12.33 3 56.5 40
Water Temperature (oC) 6 0 1980 - 1980 12.13 10.83 6.30 10.84 6.11 22.22 6.3
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams:
Dissolved Oxygen (DO): [standard used is dependent upon the respective site specific criteria] (3a) >4.0; pH: >6.5 and <9.0; Total Suspended Solids (TSS): <35
mg/L;Water Temperature: (3a) <20 oC.

TABLE A10. SUMMARY STATISTICS FOR STATION 100501251351 - JOHNSON CREEK AT BLANDING PIPELINE INLET.
Parameter n BDL1 Range of Dates Mean Median SD Geo. Mean Min Max Exceedance2 (%)
DO (mg/L) 3 0 1980 - 1980 8.67 9.00 0.58 8.65 8 9 0
pH 2 0 1980 - 1980 9.50 9.50 0.00 9.50 9.5 9.5 100
TSS (mg/L) 3 0 1980 - 1980 5.33 3.00 4.93 4.04 2 11 0
Water Temperature (oC) 3 0 1980 - 1980 10.18 11.11 4.24 9.49 5.55 13.88 0
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams:
Dissolved Oxygen (DO): [standard used is dependent upon the respective site specific criteria] (3a) >4.0; pH: >6.5 and <9.0; Total Suspended Solids (TSS):
<35 mg/L; Water Temperature: (3a) <20 oC.

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TABLE A11. SUMMARY STATISTICS FOR STATION 5958010 - RECAPTURE RESERVOIR ABOVE DAM 01.
Parameter n BDL1 Date Mean Median SD Geo. Mean Min Max Exceedance2 (%)
Ammonia (mgN/l) 36 28 1989 - 1997 0.042 0.016 0.07 0.016 <BDL> 0.33 0
39 24 1999 - 2006 0.054 0.043 0.04 0.043 <BDL> 0.23 0
DP (mg/L) 24 13 1991 - 1995 0.012 0.005 0.010 0.009 <BDL> 0.041 12.5
54 42 1999 - 2006 0.028 0.020 0.030 0.022 <BDL> 0.198 14.8
DO (mg/L) 36 0 1989 - 1997 4.8 5.8 2.7 3.4 0.1 8.4 44.4
189 1 1999 - 2006 4.6 5.1 2.8 2.8 <BDL> 8.9 37.0
Fecal Coliform (#/100 mL) 2 2 1991 - 1991 - - - - - - 0
pH 46 0 1989 - 1997 8.0 8 0.52 8.0 7.1 9.3 4.3
175 0 1999 - 2006 7.8 7.8 0.48 7.8 7.0 8.7 0
Total Coliform (#/100 mL) 2 1 1991 - 1991 - - - - - - 50
TDS (mg/L) 12 0 1989 - 1997 211.8 225 53.5 205.2 124 282 0
10 0 1999 - 2005 169.6 162 52.7 162.3 86 280 0
TP (mg/L) 32 0 1989 - 1995 0.020 0.018 0.012 0.017 0.005 0.048 37.5
54 32 1999 - 2006 0.033 0.020 0.035 0.025 <BDL> 0.231 25.9
TSS (mg/L) 11 7 1989 - 1997 3.5 2.5 3.0 2.5 <BDL> 10 0
10 9 1999 - 2005 - - - - - - 0
Water Temperature (oC) 36 0 1989 - 1997 14.3 13.8 5.4 13.3 7.3 23.2 22.2
181 0 1999 - 2005 14.1 11.8 5.2 13.2 8.2 24.8 22.1
Fecal Strep (#/100 mL) 1 1 1991 - 1991 - - - - - -
Salinity (mg/l@ 25oC) 19 0 2001 - 2006 0.12 0.11 0.05 0.11 0.01 0.2
Specific Conductivity (umhos/cm@25oC) 36 0 1989 - 1997 322.3 325.5 82.9 311.4 190 452
139 0 1999 - 2005 269.6 276 67.9 260.8 173 374
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams:
Ammonia: pH dependent criteria calculated for individual data points as per Utah Code R317-2; Dissolved Phosphorus (DP): <0.025 mg/L; Dissolved Oxygen (DO): (3a) >4.0; Fecal
Coliform: <200 colonies/100 mL; pH: >6.5 and <9.0; Total Coliform: <5,000 colonies/100 mL; Total Dissolved Solids (TDS): <1,200 mg/L; Total Phosphorus (TP): <0.025 mg/L;
Total Suspended Solids (TSS): <35 mg/L; Water Temperature: (3a) <20 oC.

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TABLE A12. SUMMARY STATISTICS FOR STATION 5958020 - RECAPTURE RESERVOIR 1/4 WAY UP RESERVOIR 02.
Parameter n BDL1 Date Mean Median SD Geo. Mean Min Max
Exceedance2
(%)
Ammonia (mgN/l) 18 16 1989 - 1997 0.065 0.06 0.03 0.06 <BDL> 0.13 0
18 13 1999 - 2005 0.047 0.04 0.03 0.04 <BDL> 0.11 0
DP (mg/L) 12 10 1991 - 1995 0.009 0.005 0.006 0.007 <BDL> 0.02 0
24 17 1999 - 2006 0.022 0.020 0.011 0.020 <BDL> 0.058 20.8
DO (mg/L) 16 0 1989 - 1997 4.76 6.0 3.1 3.0 0.1 8.5 43.8
114 0 1999 - 2006 4.83 6.1 2.7 2.8 0.01 8.5 39.5
Fecal Coliform (#/100 mL) 2 1 1991 - 1991 - - - - - - 0
pH 16 0 1989 - 1997 8.0 8.1 0.56 8.0 7.1 8.9 0
107 0 1999 - 2006 7.8 7.8 0.44 7.8 6.9 8.6 0
Total Coliform (#/100 mL) 2 1 1991 - 1991 50
TP (mg/L) 16 0 1989 - 1995 0.021 0.015 0.015 0.016 0.005 0.052 37.5
24 13 1999 - 2005 0.032 0.020 0.028 0.026 <BDL> 0.116 33.3
TSS (mg/L) 5 4 1993 - 1997 - - - - - - 0
9 9 1999 - 2005 - - - - - - 0
Water Temperature (oC) 16 0 1989 - 1997 14.8 14 6.2 13.6 7.3 23.6 37.5
114 0 1999 - 2005 15.1 15.4 5.0 14.3 8.4 24.9 24.6
Fecal Strep (#/100 mL) 2 1 1991 - 1991 - - - - - -
Salinity (mg/l@ 25oC) 15 0 2001 - 2006 0.13 0.12 0.04 0.12 0.08 0.21
Specific Conductivity (umhos/cm@25oC) 16 0 1989 - 1997 320.9 308.5 87.1 309.6 190 448
68 0 1999 - 2005 251.6 222.5 65.2 243.6 175 376
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams:
Ammonia: pH dependent criteria calculated for individual data points as per Utah Code R317-2; Dissolved Phosphorus (DP): <0.025 mg/L; Dissolved Oxygen (DO): (3a) >4.0; Fecal
Coliform: <200 colonies/100 mL; pH: >6.5 and <9.0; Total Coliform: <5,000 colonies/100 mL; Total Phosphorus (TP): <0.025 mg/L; Total Suspended Solids (TSS): <35 mg/L;
Water Temperature: (3a) <20 oC. 3 Value of the single sample.

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TABLE A13. SUMMARY STATISTICS FOR STATION 5958030 - RECAPTURE RESERVOIR 1/2 WAY UP RESERVOIR 03.
Parameter n BDL1 Date Mean Median SD Geo. Mean Min Max
Exceedance2
(%)
Ammonia (mgN/l) 20 19 1989 - 1997 - - - - - -
16 7 1999 - 2005 0.05 0.05 0.012 0.05 <BDL> 0.08 0
DP (mg/L) 12 9 1991 – 1995 0.019 0.020 0.003 0.018 <BDL> 0.02 0
24 23 1999 - 2006 0.020 0.020 0.000 0.020 <BDL> 0.021 0
DO (mg/L) 20 0 1989 - 1997 5.4 6.4 2.6 4.2 0.4 8.2 30
79 0 1999 - 2006 6.0 6.7 1.8 5.6 0.5 8.4 20.3
Fecal Coliform (#/100 mL) 2 2 1991 - 1991 - - - - - - 0
pH 20 0 1989 - 1997 8.1 8.3 0.49 8.1 7.1 8.7 0
73 0 1999 - 2006 8.0 7.9 0.33 8.0 7.1 8.6 0
Total Coliform (#/100 mL) 2 0 1991 - 1991 120000 120000 169700 3464 50 240000 50
TP (mg/L) 16 0 1989 - 1995 0.020 0.016 0.014 0.015 0.005 0.049 31.3
24 18 1999 - 2005 0.023 0.020 0.010 0.022 <BDL> 0.054 16.7
TSS (mg/L) 6 6 1993 - 1997 - - - - - - 0
9 9 1999 - 2005 - - - - - - 0
Water Temperature (oC) 20 0 1989 - 1997 16.9 17.3 5.5 15.9 7.5 23.7 40
76 0 1999 - 2005 16.9 16.7 4.8 16.2 9.3 24.7 35.5
Fecal Strep (#/100 mL) 2 0 1991 - 1991 30 30 14.14 28.28 20 40
Salinity (mg/l@ 25oC) 10 0 2001 - 2006 0.12 0.11 0.034 0.12 0.08 0.2
Specific Conductivity (umhos/cm@25oC) 19 0 1989 - 1997 311.1 288 77.5 301.9 192 437
55 0 1999 - 2005 247.2 222 60.4 240.3 176 368
1 Number of samples below detection limit (BDL). 2 Percent exceedance values calculated using the following numeric criteria and narrative standards associated with Class 2B and 3A streams:
Ammonia: pH dependent criteria calculated for individual data points as per Utah Code R317-2; Dissolved Phosphorus (DP): <0.025 mg/L; Dissolved Oxygen (DO): (3a) >4.0; Fecal
Coliform: <200 colonies/100 mL; pH: >6.5 and <9.0; Total Coliform: <5,000 colonies/100 mL; Total Dissolved Solids (TDS): <1,200 mg/L; Total Phosphorus (TP): <0.025 mg/L;
Total Suspended Solids (TSS): <35 mg/L; Water Temperature: (3a) <20 oC. 3 Value of the single sample.

A - 78
6.5
7.0
7.5
8.0
8.5
9.0
9.5
10.0
W inter S pring S um m er Fall
4 9 5 3 4 4 0 - R E C A P T U R E C K A T U 2 6 2 X IN G
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-0.10
-0.05
0.00
0.05
0.10
0.15
0.20
0.25
0.30
0.35
W inter S pring S um m er Fall
4 9 5 3 4 4 0 - R E C A P T U R E C K A T U 2 6 2 X IN G
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Season
5.0
7.5
10.0
12.5
15.0
17.5
20.0
22.5
25.0
W inter S pring S um m er Fall
4 9 5 3 4 4 0 - R E C A P T U R E C K A T U 2 6 2 X IN G
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Season
Figure A1. Seasonal parameter plots for station 4953440 from 1977-2000, including
dissolved oxygen (6 samples), total phosphorus (4 samples), and water temperature (9
samples).

A - 79
4
5
6
7
8
9
10
11
12
13
W inter Spring Sum m er Fall
4953460 - JOHNSON CK AB RECAPTURE RES AB DIVERSION
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-0 .0 5 0
-0 .0 2 5
-0 .0 0 0
0 .0 2 5
0 .0 5 0
0 .0 7 5
0 .1 0 0
0 .1 2 5
W inter Spring Sum m er Fall
4953460 - JOHNSON CK AB RECAPTURE RES AB DIVERSION
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-0 .0 5
0 .0 0
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W inter Spring Sum m er Fall
4953460 - JOHNSON CK AB RECAPTURE RES AB DIVERSION
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25
W inter Spring Sum m er Fall
4953460 - JOHNSON CK AB RECAPTURE RES AB DIVERSION
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S e a s o n
Figure A2. Seasonal parameter plots for station 4953460 from 1997-2006, including
dissolved oxygen (20 samples), total phosphorus (22 samples), and water temperature (18
samples).

A - 80

6 .4 0 0
6 .4 2 5
6 .4 5 0
6 .4 7 5
6 .5 0 0
6 .5 2 5
6 .5 5 0
6 .5 7 5
6 .6 0 0
W inter Spring Sum m er Fall
4953500 - R EC A P TU R E C R EEK W A S H A T U 163(191) X IN G B L R ES
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S e a s o n
Figure A3. Seasonal parameter plots for station 4953500 from 1978, including water
temperature (1 sample).

A - 81

2 .5
5 .0
7 .5
1 0 .0
1 2 .5
1 5 .0
W inter Spring Sum m er Fall
4 9 5 3 5 1 0 - B U L L D O G C A N Y O N C K A B R E C A P T U R E R E S
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-0 .0 5
-0 .0 0
0 .0 5
0 .1 0
0 .1 5
0 .2 0
0 .2 5
0 .3 0
0 .3 5
W inter Spring Sum m er Fall
4 9 5 3 5 1 0 - B U L L D O G C A N Y O N C K A B R E C A P T U R E R E S
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S e a s o n
0
5
10
15
20
25
W inter Spring Sum m er Fall
4 9 5 3 5 1 0 - B U L L D O G C A N Y O N C K A B R E C A P T U R E R E S
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S e a s o n
Figure A4. Seasonal parameter plots for station 4953510 from 1988-2001, including
dissolved oxygen (19 samples), total phosphorus (29 samples), and water temperature (18
samples).

A - 82
0
1
2
3
4
5
6
7
8
9
J anuary February Marc h A pril May J une J uly A ugus t S eptem ber Oc tober N ovem berD ec em ber
5 9 5 8 0 1 0 - R E C A P T U R E R E S A B D A M 0 0 1
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Month
7.5
10.0
12.5
15.0
17.5
20.0
22.5
25.0
J anuary February Marc h A pril May J une J uly A ugus t S eptem ber Oc tober N ovem berD ec em ber
5 9 5 8 0 1 0 - R E C A P T U R E R E S A B D A M 0 0 1
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Month

Figure A5. Monthly parameter plots for station 5958010 from 1989-2006, including
dissolved oxygen (225 samples) and water temperature (217 samples).

A - 83
-0
1
2
3
4
5
6
7
8
9
10
11
J anuary February Marc h A pril May J une J uly A ugus t S eptem ber Oc tober N ovem berD ec em ber
5 9 5 8 0 2 0 - R E C A P T U R E R E S 1 /4 W A Y U P R E S 0 2
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Month
5.0
7.5
10.0
12.5
15.0
17.5
20.0
22.5
25.0
J anuary February Marc h A pril May J une J uly A ugus t S eptem berOc tober N ovem berD ec em ber
5 9 5 8 0 2 0 - R E C A P T U R E R E S 1 /4 W A Y U P R E S 0 2
T

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Month

Figure A6. Monthly parameter plots for station 5958020 from 1989-2006, including
dissolved oxygen (130 samples) and water temperature (130 samples).

A - 84
1
2
3
4
5
6
7
8
J anuary February Marc h A pril May J une J uly A ugus t S eptem ber Oc tober N ovem berD ec em ber
5 9 5 8 0 3 0 - R E C A P T U R E R E S 1 /2 W A Y U P R E S 0 3
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Month
7.5
10.0
12.5
15.0
17.5
20.0
22.5
25.0
J anuary February Marc h A pril May J une J uly A ugus t S eptem berOc tober N ovem berD ec em ber
5 9 5 8 0 3 0 - R E C A P T U R E R E S 1 /2 W A Y U P R E S 0 3
T

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Month
Figure A7. Monthly parameter plots for station 5958030 from 1989-2006, including
dissolved oxygen (99 samples) and water temperature (96 samples).

A - 85
7/30/97 22:50, 0.107
0 .0 9 7 5
0 .1 0 0 0
0 .1 0 2 5
0 .1 0 5 0
0 .1 0 7 5
0 .1 1 0 0
0 .1 1 2 5
0 .1 1 5 0
0 .1 1 7 5
1990 1995 2000 2005
4953440 - RECAPTURE CK AT U262 XING
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D a te
4/17/80 8:45, 10.200
4/7/87 22:05, 7.700 5/27/87 11:10, 7.900
5/11/88 18:45, 6.600 7/30/97 22:50, 6.800
11/1/2000 12:00, 7.660
6 .5
7 .0
7 .5
8 .0
8 .5
9 .0
9 .5
1 0 .0
1980 1985 1990 1995 2000
4953440 - RECAPTURE CK AT U262 XING
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D a te
4/17/80 8:45, 0.370
4/7/87 22:05, 0.100
5/27/87 11:10, 0.010
5/11/88 18:45, 0.0100 .0 0
0 .0 5
0 .1 0
0 .1 5
0 .2 0
0 .2 5
0 .3 0
0 .3 5
198 0 198 1 198 2 198 3 198 4 198 5 198 6 198 7 198 8
4953440 - RECAPTURE CK AT U262 XING
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D a te
8/24/77 13:00, 23.300
2/8/78 14:00, 8.000
5/24/78 11:00, 6.000
4/17/80 8:45, 5.500
4/7/87 22:05, 13.200
5/27/87 11:10, 15.600
5/11/88 18:45, 24.500
7/30/97 22:50, 21.600
11/1/2000 12:00, 8.300
5 .0
7 .5
1 0 .0
1 2 .5
1 5 .0
1 7 .5
2 0 .0
2 2 .5
2 5 .0
1980 1990 2000
4953440 - RECAPTURE CK AT U262 XING
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D a te
8/24/77 13:00, 9999.000
2/8/78 14:00, 6040.000
4/17/80 8:45, 2660.000
4/7/87 22:05, 340.000
7/30/97 22:50, 2376.000
11/1/2000 12:00, 3730.000
0
1000
2000
3000
4000
5000
6000
7000
8000
9000
10000
1980 1990 2000
4953440 - RECAPTURE CK AT U262 XING
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D a te
Figure A8. Time series plots for station 4953440.

A - 86
7/13/2005 19:15, 0.050
3/29/2006 15:35, 0.060
5/10/2006 18:15, 0.0500 .0 5 0
0 .0 5 1
0 .0 5 2
0 .0 5 3
0 .0 5 4
0 .0 5 5
0 .0 5 6
0 .0 5 7
0 .0 5 8
0 .0 5 9
0 .0 6 0
J ul
2005
A ug S ep O c t Nov Dec J an 2006 F eb M ar A pr M ay
4953460 - JOHNSON CK AB RECAPTURE RES AB DIVERSION
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5
6
7
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9
10
11
12
13
1 9 9 8 1 9 9 9 2 0 0 0 2 0 0 1 2 0 0 2 2 0 0 3 2 0 0 4 2 0 0 5 2 0 0 6
4953460 - JOHNSON CK AB RECAPTURE RES AB DIVERSION
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0 .0 2 5
0 .0 5 0
0 .0 7 5
0 .1 0 0
0 .1 2 5
0 .1 5 0
0 .1 7 5
0 .2 0 0
1 9 9 8 1 9 9 9 2 0 0 0 2 0 0 1 2 0 0 2 2 0 0 3 2 0 0 4 2 0 0 5 2 0 0 6
4953460 - JOHNSON CK AB RECAPTURE RES AB DIVERSION
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0 .0
2 .5
5 .0
7 .5
1 0 .0
1 2 .5
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1 7 .5
2 0 .0
2 2 .5
1 9 9 8 1 9 9 9 2 0 0 0 2 0 0 1 2 0 0 2 2 0 0 3 2 0 0 4 2 0 0 5 2 0 0 6
4953460 - JOHNSON CK AB RECAPTURE RES AB DIVERSION
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0
10
20
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50
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80
90
1998 1999 2000 2001 2002 2003 2004 2005 2006
4953460 - JOHNSON CK AB RECAPTURE RES AB DIVERSION
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Figure A9. Time series plots for station 4953460.

A - 87
3/6/78 15:30, 2000.000
1800
1850
1900
1950
2000
2050
2100
2150
2200
1970 1975 1980 1985
4953500 - R EC A P TU R E C R EEK W A S H A T U 163(191) X IN G B L R ES
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D a te
3/6/78 15:30, 8.300
7.50
7.75
8.00
8.25
8.50
8.75
9.00
1970 1975 1980 1985
4953500 - R E C A P T U R E C R E E K W A S H A T U 163(191) X IN G B L R E S
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Date
3/6/78 15:30, 6.500
6 .0 0
6 .2 5
6 .5 0
6 .7 5
7 .0 0
1970 1975 1980 1985
4953500 - R EC A P TU R E C R EEK W A S H A T U 163(191) X IN G B L R ES
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D a te
Figure A10. Time series plots for station 4953500.

A - 88
2 .5
5 .0
7 .5
1 0 .0
1 2 .5
1 5 .0
1990 1995 2000
4 9 5 3 5 1 0 - B U L L D O G C A N Y O N C K A B R E C A P T U R E R E S
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D a te
0 .0 0
0 .0 5
0 .1 0
0 .1 5
0 .2 0
0 .2 5
0 .3 0
0 .3 5
1990 1995 2000
4 9 5 3 5 1 0 - B U L L D O G C A N Y O N C K A B R E C A P T U R E R E S
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D a te

0
5
10
15
20
25
1990 1995 2000
4 9 5 3 5 1 0 - B U L L D O G C A N Y O N C K A B R E C A P T U R E R E S
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D a te
0
250
500
750
1000
1250
1500
1750
1990 1995 2000
4 9 5 3 5 1 0 - B U L L D O G C A N Y O N C K A B R E C A P T U R E R E S
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D a te
Figure A11. Time series plots for station 4953510.

A - 89
0.180
0.185
0.190
0.195
0.200
0.205
0.210
0.215
0.220
1980 1985 1990 1995
1 9 0 0 1 0 2 - B L A N D IN G - IN D IA N C R E E K
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Date
0.0900
0.0925
0.0950
0.0975
0.1000
0.1025
0.1050
0.1075
0.1100
198 2 198 3 198 4 198 5 198 6 198 7 198 8 198 9 199 0
1 9 0 0 1 0 1 - B L A N D IN G - J O H N S O N C R E E K 1
N

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Date
Figure A12. Time series plots for station 1900101.

Figure A13. Time series plots for station 1900102.

A - 90
7/21/80 0:00, 10.000
8/25/80 0:00, 9.000
9/30/80 0:00, 10.000
10/14/80 0:00, 6.0006 .0
6 .5
7 .0
7 .5
8 .0
8 .5
9 .0
9 .5
1 0 .0
2 2 T u e
J u l 8 0
1 A u g 8 Fri 1 5 Fri 2 2 Fri 1 S e p 8 Mo n 1 5 Mo n 2 2 Mo n 1 O c t 8 W e d 1 5 W e d
1 0 0 5 0 1 0 5 2 2 5 1 - U P P E R IN D IA N C R E E K
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D a te
7/21/80 0:00, 4.440
8/25/80 0:00, 7.770
9/30/80 0:00, 2.220
10/14/80 0:00, 4.440
2 .0
2 .5
3 .0
3 .5
4 .0
4 .5
5 .0
5 .5
6 .0
6 .5
7 .0
7 .5
8 .0
2 2 T u e
J u l 8 0
1 A u g 8 Fri 1 5 Fri 2 2 Fri 1 S e p 8 Mo n 1 5 Mo n 2 2 Mo n 1 O c t 8 W e d 1 5 W e d
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Figure A14. Time series plots for station 100501052251.

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Figure A15. Time series plots for station 5958010.

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Figure A16. Time series plots for station 5958020.

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Figure A17. Time series plots for station 5958030.

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Figure A18. Time series plots for station 1900101.

A - 94
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Figure A19. Time series plots for station 1900102.

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A - 96

APPENDIX B –
WATERSHED BUDGET MODEL

A - 97
Table of Contents

Introduction ..............................................................................................................................B - 98

UDWR 1981 Model .............................................................................................................B - 98

Current Water Budget Model .............................................................................................B - 100

LIST OF TABLES
Table B.1. UDWR 1981 Area altitude method based on natural flow of Recapture Creek
Below Johnson Creek - based on mean annual runoff of 4,400 acre-feet
calculated from correlations to other gages. ...........................................................B - 99
Table B.2. Comparison of 1981 DWR Correlations and Current Data for Recapture Creek
Below Johnson Creek Gage (Adjusted) (all values in acre-feet). .........................B - 100
Table B.3. Reconciliation of average annual flows predicted by model with actual gage
data. ......................................................................................................................B - 101

LIST OF FIGURES
Figure B.1. Modeled functions for unit runoff in acre-feet per square mile per year as a
function of precipitation in the Recapture Reservoir watershed. ........................B - 102

A - 98
INTRODUCTION

A new model was needed to estimate present day runoff and pollutant loads to the reservoir. This
model was based on the area-altitude approach described in a letter and accompanying analysis
produced by the Utah Division of Water Resources (UDWR) dated January 27, 1982 in support
of their request to include the Recapture Dam construction project under the Nationwide Permits
provisions of Section 404 of the Clean Water Act, administered by the U.S. Environmental
Protection Agency.

UDWR 1981 MODEL

UDWR faced the challenge of forecasting “natural” runoff to the reservoir site from only two
stream gages in the watershed and limited data on flows into diversions. Their data were even
more limited than today, however, because the lower Recapture Creek Below Johnson Creek
gage was only three years old, and the watershed at the time was subject to three diversions
(Blanding Pipeline, Upper Canal, and Lower Canal). UDWR therefore initially had to construct a
theoretical historical flow for the lower Recapture Creek gage by correlating the available data,
first to the upper – and non-diverted – Recapture Creek Near Blanding gage (for which data had
been collected for 13 years), and then to a gage on Indian Creek 15 miles to the north (USGS
Indian Creek Above Cottonwood Creek, Near Monticello, UT, Station 9186500) for which data
had been collected for 22 years (but not entirely overlapping in time and from which diversions
existed above the gage). They concluded that the average annual flow at the Recapture Creek
Below Johnson Creek gage was 4,402 acre-feet.

Having constructed a model of annual and monthly average flow at the lower Recapture Creek
Below Johnson Creek gage, UDWR then constructed a model to predict runoff to the proposed
reservoir site. They approached this task by developing coefficients of acre-feet of runoff per year
per square mile for 1,000 foot elevation bands in the watershed. They first used an “Elevation-
Precipitation Curve for Abajo Mountain Area” and then a “Precipitation-Runoff Curve for South
and East Colorado Area” to predict runoff in inches from each elevation band. They then
produced a “Runoff Factor” for each elevation band by normalizing the resulting theoretical
runoff amounts (in inches) to the runoff in the highest elevation band. Applying this normalized
Runoff Factor to the measured area in each elevation band yielded an “Equivalent Area” in each
elevation band. Each Equivalent Area was then taken as a percent of the total Equivalent Area,
and the resulting fraction was multiplied by the total annual runoff for the lower Recapture Creek
Below Johnson Creek calculated from their correlations with other gages. The result was a list of
“Unit Runoff” factors in acre-feet per square mile for each elevation band. Their table showing
their calculations is reproduced below in Table B.1 (with some very small errors due to
rounding).

A - 99

Table B.1. UDWR 1981 Area altitude method based on natural flow of Recapture Creek
Below Johnson Creek - based on mean annual runoff of 4,400 acre-feet calculated from
correlations to other gages.
Elevation
(feet above
sea level)
Area
(sq mi)
Precip
(in)
Runoff
(in)
Runoff
Factor
Equiv
Area
(sq mi)
Unit Runoff
(ac-ft/sq-mi)
Runoff
(ac-ft)
10-11,000 1.547 32.5 14.5 1.000 1.547 433 669
9-10,000 4.828 27.0 8.5 0.586 2.830 254 1,225
8-9,000 7.672 22.5 5.0 0.345 2.646 149 1,145
7-8,000 14.719 17.5 2.4 0.166 2.436 72 1,054
6-7,000 7.953 14.0 1.3 0.090 0.713 39 309
Total 36.719 10.172 4,402

UDWR attempted to validate this approach to modeling watersheds by developing new unit
runoff factors for the smaller watershed feeding the upper Recapture Creek Near Blanding gage,
above which there were no diversions. This yielded slightly different Unit Runoff coefficients
which, when applied back to the larger watershed above the Recapture Creek Below Johnson
Creek gage produced an estimate of 4,650 acre-feet of “natural flow”, only slightly higher than
their value of 4,402 acre-feet from their correlations.

From this point, UDWR made assumptions in calculating the flow expected at the Recapture
Reservoir Dam site. These included:

1. Applying the original Unit Runoff Factors to the rest of the watershed, including Bulldog
and Bullpup Creeks to generate a modeled “natural flow” to the reservoir;

2. Blanding would always divert up to, but no more than, 30 acre-feet per month;

3. The Upper Canal would divert up to, but no more than, 20 cfs (~1,200 acre-feet per
month) from April through October; and

4. The Lower Canal would divert whatever was available (up to 1,130 acre-feet per month
in their summary) from April through October.

UDWR thus calculated that the average annual flow to the Recapture Reservoir Dam site would
be 2.3 cfs, or 1,616 acre-feet (See UDWR 1981, Article C).

Table B.2 compares UDWR’s 1981 calculations of the natural flow at the gage at Recapture
Creek Below Johnson Creek, based on correlations with other gauges, to the longer period of
record now available from this gage, adjusted for diversions and interbasin inflows. Between
1976 and 1993, this gage measured an annual mean of 6,260 acre-feet (median of 4,168 acre-
feet). Assuming that the mean annual flow now is similar to the flow in the years of record, and
calculating a “natural flow” by adding back flows measured by Blanding City for the Blanding
Pipeline of 976 acre-feet per year (average 2002-2007) and the Upper Canal diversion of 2,715
acre-feet (assuming average of 9 cfs for 5 months) as well as the net flows from Dry Wash, and
deducting the annual average interbasin contribution from Indian Creek Tunnel, we would expect
the natural flow at this gage to be approximately 8,917 acre-feet per year. UDWR’s correlations

A - 100
for this gage yielded 4,402 acre-feet per year, a discrepancy of approximately 4,500 acre-feet per
year.

Table B.2. Comparison of 1981 DWR Correlations and Current Data for Recapture
Creek Below Johnson Creek Gage (Adjusted) (all values in acre-feet).
UDWR 1981 Calculation of "Natural Flow" (no diversions or
interbasin transfers) based on correlations to other stations 4,402

Present Day Estimates
Actual mean annual flow at gage 6,260
Add back average annual upstream diversions
Blanding Pipeline 976
Upper Canal 2,715
Deduct average annual upstream inflow Indian Creek Tunnel (1,034)
Dry Wash flow net of 185 acre-feet held back (flow net of “hold
back” is typically zero) -
Total adjustments 2,657
Present day "Natural Flow" 8,917

UDWR 1981 Underestimate (4,515)

The longer period of record for the stream gage on Recapture Creek Below Johnson Creek would
probably have resulted in different conclusions with respect to the USEPA Section 404 Permit
process in 1981. The underestimated stream flow at the stream gage on Recapture Creek Below
Johnson Creek would have flowed to Recapture Reservoir site, adding to UDWR’s estimate of
1,616 acre-feet per year at that site, for an annual total of 6,116 acre-feet, or an average of 8.44
cfs, well above the limit of 5 cfs for a Nationwide Permit at the time.

CURRENT WATER BUDGET MODEL

Not only are there more years of gage data today, but newer information is available for
precipitation bands at different elevations in the Recapture Reservoir watershed. A data layer of
average annual precipitation for 1961-1990, in two inch precipitation bands, was acquired from
the U.S. Department of Agriculture, Service Center Agencies, NRCS - National Cartography &
Geospatial Center (based on data from PRISM, Parameter-elevation Regressions on Independent
Slopes Model, at Oregon State University, http://www.prismclimate.org, created August 2006).
Using GIS software, this precipitation data was clipped to the watershed boundaries, and a
“union” operation produced 61 separate polygons for the unique combinations of watershed
subdivision and precipitation value. These polygons were then grouped for flow modeling
purposes based on where they came together at a diversion or major confluence. Areal extents for
each precipitation-watershed subdivision were exported to spreadsheets for further analysis.

The first new adjusted exponential function was then tested on the watersheds of the other two
gage sites, Recapture Creek Below Johnson Creek and the Recapture Reservoir itself based on the
following assumptions:

A - 101
1. The equation for unit runoff as a function of precipitation is exponential with zero offset
(i.e., some runoff occurs at every precipitation amount).

2. Average annual flow at the upper Recapture Creek Near Blanding gage is 895 acre-feet
per year (from actual gage data).

3. Diversions to the Blanding Pipeline for 2002-2007 equaled 976 acre-feet per year, as
reported by Blanding City officials.

4. Diversions to the Upper Canal averaged 9 cfs for 6 months, based on personal
communications with personnel from the SJWCD.

5. The first 185 acre-feet from the Dry Wash subdivision is retained in the Dry Wash
reservoir, based on personal communications with personnel from the SJWCD.

6. Reservoir losses to evaporation are 48.5 inches of water per year, less 13 inches of
average annual precipitation, times the average areal extent of the reservoir, yielding
evaporative losses of 500-870 acre-feet per year.

This first approximation yielded significant errors when applied to these two other watersheds, so
the coefficient and exponent of the model were adjusted once more to minimize the total error
among all three gage sites. A graph of the unit runoff equation is reproduced in Figure B.1.

A reconciliation of the modeled flows against the flows actually measured at the stream gages is
presented in Table B.3. The model was used to calculate annual average flows for the watershed
areas that fed each of the stream or reservoir discharge gages. Deductions were made for
diversions, based on estimates from local sources, and evaporation from Recapture Reservoir,
based on estimates relying on average evaporation in the region and the average areal extent of
the reservoir each year. Deductions were not made for water withdrawn by Blanding City or the
SJWCD from the reservoir itself.
5.
Table B.3. Reconciliation of average annual flows predicted by model with actual gage data.

Recapture
Creek Near
Blanding
(ac-ft)
Recapture
Creek Below
Johnson Creek
(ac-ft)
Recapture
Reservoir At Dam
(ac-ft)
Modeled Natural Runoff 907 8,332 8,913
Deduct Blanding Pipeline diversion N/A (976) (976)1
Deduct Upper Canal diversion2 N/A (2,715) (2,715)
Deduct Dry Wash held water N/A (185) (185)
Deduct evaporation losses3 N/A N/A (605)
Actual Average Annual Gage Flows 895 6,260 1,668
“Error” - Other unknown inflows
(losses) (13) 1,804 (2,763)
1From average measurements from Blanding 2002-2007.
2Assumes 9 cfs for 5 months. 3Assumes evaporative loss of 47.5” per year for free water surfaces, from UWRL Water Atlas for Utah, and
based on the average areal extent of the reservoir for that year, based on reservoir capacity tables provided by
UDWR.

A - 102

Unit Runoff Per Square Mile
Recapture Reservoir Watershed and Subdivisions
-
100
200
300
400
500
600
700
800
0 5 10 15 20 25 30 35 40
Annual Precipitation (inches)
Ac
-
f
t
/
m
i
l
e
²
/
y
e
a
r
Area-Altitude Method from DWR 1981 Adj'd Model to Recap Nr Bldg=f(Precip)
Adj'd Model For All Subdivisions
Final function adjusted for all
watershed subdivisions
y = 0.0000058x^5.23
Original UDWR trendline
y = 0.000342x^3.0554
R^2 = 1

6. Figure B.1. Modeled functions for unit runoff in acre-feet per square mile per year
as a function of precipitation in the Recapture Reservoir watershed.

The error for Recapture Creek Near Blanding is the smallest, because the model was originally
created based on data from that station and because that watershed is relatively small with no
diversions within it. The positive error for Recapture Creek Below Johnson Creek implies that the
model has either underestimated runoff from lower elevations or not adequately accounted for
ground water discharge to the stream. The negative unknown discrepancy for Recapture
Reservoir implies that the model has overestimated flows from lower elevation land areas, or
underestimated other losses, such as withdrawals from canals, Blanding City, or the SJWCD, or
not adequately taken into account losses of natural seepage to ground water. With respect to this
latter error, representatives from the SJWCD have confirmed that a clay layer was incorporated
into the bottom of the reservoir during construction to minimize seepage. An independent
assessment of the underlying geology and hydrogeology was not undertaken for this report.

A - 103
In all, however, this model predicts flows better than the area-altitude model used in 1981 by
UDWR. It would benefit by taking into consideration additional factors such as slope, vegetation
cover, and soil characteristics. More stream gaging stations, especially at diversions and closer to
the reservoir, would help with future studies.

A - 104

APPENDIX C - PIP
PROJECT IMPLEMENTATION PLAN

A - 105
TABLE OF CONTENTS

Table of Contents .....................................................................................................................C-105
List of Tables .......................................................................................................................C-105

Introduction ..............................................................................................................................C-106

Livestock grazing and diffuse runoff .......................................................................................C-107
Recommendations ................................................................................................................C-109

Recreation .................................................................................................................................C-111
Recommendations ................................................................................................................C-112

Summary ..................................................................................................................................C-112

References ................................................................................................................................C-113

LIST OF TABLES
Table C1. Allocation of permissible total phosphorus loadings to Recapture
Reservoir by land ownership. .................................................................... C-107
Table C2. Total phosphorus loads (kg/yr) from grazing to Recapture Reservoir
defined by watershed or by land owner. .................................................... C-108
TableC 3. Total phosphorus loads (kg/yr) by land use and landowner to Recapture
Reservoir for average annual precipitation year. ......................................... C-108
Table C4. Recommended BMPs for reducing loads from grazing and diffuse runoff. ... C-
109
Table C5. Proper Use Criteria for grazing in the Manti-La Sal National Forest. ...... C-111
Table C6. Recommended BMPs for reducing loads from grazing and diffuse runoff. ... C-
112

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INTRODUCTION

To achieve water quality targets and TMDL endpoints, it is necessary to implement practices that
are commonly known as Best Management Practices (BMPs) or Best Available Technologies
(BATs). BMPs are practices used to protect the physical and biological integrity of surface and
groundwater, primarily from nonpoint sources of pollution. BMPs are most effective when
combined to create a BMP system that will comprehensively reduce or eliminate pollution from a
single source. It should be noted that no single BMP system is considered to be the most
effective way of controlling a particular pollutant in all situations. Rather, the design of a BMP
system should consider local conditions that are known to influence the production and delivery
of nonpoint source pollutants. The design of a BMP system should not only account for the type
and source of pollutant, but should also consider background factors such as the physical,
climatic, biological, social, and economic setting. BATs are used to treat effluent from a facility
or operation before it is discharged through a single location to a receiving water body. Since no
point sources of pollution have been identified in the project area, no BATs will be
recommended.

The following pollutant loading sources were identified during the assessment of water quality
conditions in the TMDL study area:

 Livestock grazing
 Diffuse loads from runoff

Although recreational use of public lands was not defined specifically as a pollutant source in the
TMDL assessment, this Project Implementation Plan (PIP) also includes recommendations for
minimizing impacts from recreational activities. Given the long-term trends observed on public
lands, it is recognized that these activities are an integral part of land use and should be addressed
with regards to the potential for generating nonpoint source pollution.

Recapture Reservoir is currently impaired for Dissolved Oxygen (DO), and has been listed as
such as far back as 1996. Recapture Reservoir was also listed as impaired for Temperature, pH,
and Total Phosphorus (TP) in 1996 and 1998. The TP listing was removed in 1998 when the
state determined that TP data could not be used by itself as a means for determining beneficial
use support.

Existing total watershed loads, and the recommended pollutant load allocations by land owner
and watershed are provided below in Table C1. The target load associated with the TMDL is
reflected by existing conditions. The selection of the target load was based on an assessment of
existing reservoir TP concentrations and a review of potential impacts to reservoir DO levels. It
was determined that existing reservoir TP concentrations are marginally above the 0.025 mg/L
pollution indicator value and likely not responsible for the low DO levels observed in Recapture
Reservoir. Therefore the existing loading to Recapture Reservoir was selected as the target load.
However, all sources identified in the TMDL assessment and those discussed in this PIP are
considered significant in terms of their influence on water quality conditions in Recapture
Reservoir. The remainder of this document will include recommendations for maintaining
existing loads from each source and the unit cost associated activities that can be used to maintain
or reduce loading.

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As pollutant loads are transferred through the TMDL study area, they are influenced by a number
of different processes that reduce the mass of TP delivered to the Recapture Reservoir. Some of
these processes can include adsorption, algal uptake, settling, and flow diversion for municipal or
irrigation purposes. The exact level that each of these processes influence TP loading to the
reservoir is not known at this time. Therefore it is recommended that implementation of BMPs
follow a phased approach that focuses on areas where recommended BMPs are not currently in
place as well as maintaining those areas where BMPs are in place. Additional monitoring of
water quality can then be used to determine if additional BMPs are needed above the level
described in this document.

Table C1. Allocation of permissible total phosphorus loadings to Recapture Reservoir by
land ownership.
Agency Annual TP load (kg/yr) Percent of total
BLM 16 7
USFS 183 81
SITLA 2 1
Private 24 11
Total 225 100

LIVESTOCK GRAZING AND DIFFUSE
RUNOFF

Loads included in this category are related primarily to manure loading from livestock grazing on
public and private lands. Also included are loads from diffuse runoff, which are related to land
use. Specific sources within this category including runoff from agricultural lands,
urban/residential areas, rangeland, forest land, and other land cover types. The TMDL
recommends that total loads from livestock grazing and diffuse runoff be maintained at their
existing level or reduced where possible as opportunities arise to improve management practices.

Livestock grazing is one of the primary land uses in the Recapture Reservoir watershed and as a
result, occurs on many of the areas that contribute seasonal runoff to tributaries of the reservoir.
Nearly all of the BLM and National Forest System lands in the watershed are associated with
public grazing allotments. BLM lands, located in the southern portion of the watershed, are
primarily grazed from mid-May through late September each year. Forest Service allotments are
located in the northern part of the watershed and are grazed slightly later in the season. Areas of
private and state owned lands are also scattered throughout the southern part of the watershed.
Although no animals were observed grazing on private lands during field visits to the TMDL
study area, it is likely that periodic grazing of private land does occur. There are no AFO/CAFO
operations in the watershed. The primary loading mechanisms from grazing animals include the
direct deposition of manure to water bodies and surface runoff from areas where livestock have
grazed. TP loads to Recapture Reservoir resulting from livestock grazing are shown in Table
C2.

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Table C2. Total phosphorus loads (kg/yr) from grazing to Recapture Reservoir defined
by watershed or by land owner.
Watershed BLM SITLA USFS Total (kg/yr)
Johnson Creek 5.8 0.8 24.8 31.5
Recapture Creek 16.1 1.8 61.9 79.7
Bulldog Creek 36.7 4.9 138.8 180.5
Bullpup Creek 5.2 6.4 0.4 12.1
Recapture Reservoir 12.9 0.6 - 13.5
Total 76.8 14.5 225.9 317.3

Land cover in the Recapture Reservoir watershed is primarily pinyon-juniper (approximately 43
percent), followed by rangeland (approximately 29 percent) and forest (24 percent). The amount
of agriculture areas are small (3 percent), but are located near tributary streams on private land in
the lower-elevation part of the watershed. Although agricultural lands comprise only a small
portion of the watershed, they are believed to be significant due to their location as well as
practices that occur in these areas which may include land application of manure or chemical
fertilizers, and tillage of cropped areas. Barren lands are located mostly in the upper elevations of
the watershed are generally considered to have minimal impacts to reservoir loads. TP loads to
Recapture Reservoir from diffuse runoff are shown in Table C3.

Table C3. Total phosphorus loads (kg/yr) by land use and landowner to Recapture
Reservoir for average annual precipitation year.
Land Use
Landowner
BLM USFS SITLA Private
Total Load
(kg/yr)
Percent of
Total
Agriculture 0.2 0.2 0.3 14.3 15.0 7
Urban 0.0 0.0 0.0 0.0 0.0 0
Forest Land 0.1 76.4 0.0 0.4 76.9 34
Range Land 0.2 34.9 0.0 1.8 37.0 16
Pinyon-
Juniper 15.6 46.6 2.0 7.1 71.4 32
Barren 0.0 24.8 0.0 0.1 24.9 11
Water 0.0 0.0 0.0 0.0 0.0 0
Total Load
(kg/yr) 16.2 182.9 2.3 23.8 225.2 100
Percent of total 7% 81% 1% 11% 100%

The following discussion will address BMP recommendations to reduce loading contributed to
streams in the Recapture Reservoir watershed from grazing and diffuse runoff.

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RECOMMENDATIONS

A list of BMPs that are appropriate for reducing loads from grazing and diffuse runoff are
included in Table C4. Recommended management practices include exclusion of cattle from
streams (via the installation of fences), filter strips, range planting, and revegetation of stream
banks.

Table C4. Recommended BMPs for reducing loads from grazing and diffuse runoff.
NRCS Conservation
Practice ID
(where applicable)
Description Cost
382 Fence $2 / linear foot
614 Offsite watering system $1.50 / gallon
393 Filter Strip $250/acre
390 Riparian Herbaceous Cover $160/acre
550 Range Planting $170/acre
Maintain a minimum herbage stubble height of 4-6 inches
within riparian areas. Allow adequate time for regrowth of
plants in these areas before reuse.
Non-structural
Limit springtime grazing of herbaceous vegetation to not
exceed 60 percent. Limit livestock use from riparian areas
when primary forage plants are still in the vegetative state
(early growth stage).
Non-structural
Rest-Rotation grazing. Allow adequate rest for vegetation
recovery in pastures and allotments. Consider limiting
grazing in pastures containing riparian areas during hot
periods when livestock use of riparian areas typically
increases.
Non-structural
Ensure all livestock are removed from each pasture at the
end of the specified use period. Recovery of riparian areas
is reduced if some animals remain following use period.
Non-structural
Implement streambank disturbance standards that require a
percentage of stream channels to be in a stable condition
before grazing is allowed within pastures adjacent to water.
Non-structural
Manage winter feeding to avoid pastures that contribute
direct snowmelt runoff to streams. Non-structural

Along with direct deposition of manure, cattle can damage streams by trampling and eroding the
banks, which serve to widen stream channels, and by removing bank vegetation. This damage
leads to shallower flows, increased water temperature, and poorer water quality. Exclusion of
cattle from streams prevents such damage. Sheffield et al. (1997) and Line et al. (2000) indicated
measured reductions in TP loading of 98 percent and 75 percent, respectively, when livestock
were excluded from streams. Line et al. (2000) indicated that some of the reduction in TP
loading was likely due to reduced erosion from channel banks and upslope areas as well as
filtering of surface runoff by vegetation. Similar conclusions were reached by Sheffield et al
(1997) and Owens et al. (1996) who observed reductions in sediment loss of 70 percent and 40

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percent, respectively, following livestock exclusion from channel corridors. Exclusion of cattle
from streams would require the installation of alternate watering systems, if they are not already
in place.

Filter strips, or buffer strips, allow TP loads contributed from runoff to be reduced as it flows
though surface vegetation. The amount of TP removed by vegetation is dependent upon the
density of vegetation, time of travel, infiltration capacity, and size of soil particles transported by
runoff (Allaway 2003). Higher density vegetation (e.g. grass and forb species) serve to increase
the time required for surface flows to pass through buffer strips. The infiltration capacity of
buffer strips is dependent on vegetation type. Lee et al. (2000) reported that buffers consisting of
forbs and large woody plants trapped 21 percent more TP than did buffers comprised of grass
species alone. It was assumed that woody plant species provided a greater infiltration capacity
than grass species due to their relatively deeper root structure. The larger biomass of woody
species in comparison to grass covers is also thought to maintain a greater capacity for uptake of
TP. However, Schmitt et al. (1999) found few differences between grass and woody species
buffer strips.

It is difficult to make a meaningful comparison between different types of buffer strips due to the
many factors that influence removal efficiency, including slope, strip width, and runoff volume.
Allaway (2003) presented a summary of buffer strip efficiency and found that one of the most
significant factors is buffer strip width. His review noted that buffer strips between 18 feet and
30 feet trap roughly 67 percent of TP and buffers greater than 33 feet or more remove 74 percent
TP, on average, from surface runoff volumes.

Closely related to these two practices is restoration of riparian herbaceous cover. Trampling by
cattle and removal of riparian vegetation can lead to erosion of stream banks. Estimates of the
contribution of stream bank erosion to phosphorus loads vary from 2 percent for non-incised
streams (Sonzogni et al. 1980) to 55 percent for incised streams (Zaimes et al. 2004). Excluding
cattle, planting buffer strips, and restoring riparian vegetation can stabilize banks, thus reducing
phosphorus loads and reducing erosion. As indicated above, some of the TP load reductions
realized from exclusion of cattle from streams is likely due to reduced erosion from channel
banks.

Diffuse loads from surface runoff can also be reduced by completing activities that promote
infiltration and decrease runoff volumes. Vegetation that provides good ground cover, such as
bunchgrasses, slows down runoff water, allowing more of it to infiltrate into the ground.
Overgrazed land also allows more runoff than properly managed rangeland. Overstocking of
grazing allotments can lead to increased soil compaction, which impedes infiltration (McGinty et
al. 2000). Consequently managing livestock use in the Recapture Reservoir TMDL study area is
important. A Manti-La Sal Forest Plan amendment (US Forest Service 1990) defines Proper Use
Criteria for percent use of key species. Meeting these criteria, shown in Table C5, would help
maintain adequate vegetative cover on Forest Service allotments in the watershed.

Range planting would allow for the reintroduction or increase of native and desired forage species
in grazing allotments. Species that are adapted to grazing, as well as the dry conditions prevalent
in San Juan County and much of southern Utah, would be good candidates for this method. A
proper mix of forage species would satisfy the needs of cattle while helping to increase
infiltration of runoff and filtration of sediments while maintaining adequate ground cover.

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Table C5. Proper Use Criteria for grazing in the Manti-La Sal National Forest.
Uplands (Management System) Percent Use of Key Species
Season Long Use 40-55
Deferred Rotation 45-60
Rest Rotation 55-65
Riparian Areas (Season)
Spring 50-60
Summer 45-50
Fall 30-40
Source: 1990 Manti-La Sal Forest Plan Amendment.

It is anticipated that implementation of BMPs designed to remove TP loads from grazing and
diffuse runoff (Table C5), will help to maintain or possibly reduce nonpoint source loading. If
some of these practices are currently in place, they should maintained. It is recommended that
additional efforts be made to apply these practices in all areas of the watershed. Areas that are
known to contribute direct surface runoff to Recapture Reservoir as well as segments near the
reservoir should be emphasized. In general, the TP removal rate of BMPs listed in Table C4 is
considered to be 60 percent from areas where they are not currently in effect , if BMPs are
properly implemented and maintained.

Current practices used by the Forest Service which reduce the amount of TP loading caused by
grazing include (1) the use of deferred rotation, through which areas are prevented from being
grazed in consecutive years, and (2) the creation of a Watershed Protection Area in the northern
part of the watershed, above the grazing allotments where Johnson and Recapture Creeks, as well
as several of their tributaries, originate. In addition, tree planting activities have taken place in
the area affected by the Nizhoni fire in 2002. These efforts will help to reduce processes that
contribute TP loads to Recapture Reservoir.

RECREATION

There are several types of recreation that are common in the Recapture Reservoir project area.
The reservoir itself offers swimming, boating, and fishing. Other locations in the project area
offer camping, hunting, and off-road vehicle use. There is a network of gravel and dirt roads
throughout the area. Primitive camping is available, and a USFS campground, Devil’s Canyon, is
on the eastern boundary of the watershed off of Highway 191. Since most of the land in the
project area is publicly owned, access for recreational purposes is open in many places.

There are many road crossings of streams in the watershed, providing an avenue for runoff from
roads to enter the system. Road networks serve to concentrate sediment from a large area into
one place and can result in a large amount of sediment entering a small, seasonal tributary.
Recreation can also decrease vegetation density and diversity, decrease soil infiltration, and
increase erosion through dispersed camping and ATV use.

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RECOMMENDATIONS

A list of BMPs that are appropriate for maintaining or reducing loading from recreational
activities are included in Table C6. Recommended management practices include constructing
proper crossings where roads intersect streams and upgrading access roads according to USFS
and NRCS standards.

Properly constructed stream crossings would provide for travel needs while not impeding stream
flow. Such crossings, with the proper dimensions of width and slope, could reduce erosion and
sediment deposition. Since stream crossings are already in place throughout the watershed, this
BMP would consist mainly of modifying existing crossings where it is determined to be feasible
and beneficial. Runoff water can also be diverted away from streams using diversion ditches. In
conjunction with improving stream crossings, upgrading roads in the watershed to meet federal
standards for access roads can reduce loading by minimizing erosion and providing proper
drainage. Road upgrade methods include building water bars and roadside ditches.

It has been estimated in some watersheds that roads and stream crossings are responsible for 5 –
90 percent of all sediment from forest lands (Sheridan and Noske 2007)(Chang 2006). The
ultimate level of sediment loading is dependent upon local factors including flow, soil type,
intensity of use. Forest lands comprise about 45 percent of major land cover types in the
Recapture Reservoir project area. Few evaluations of the effects of road restoration on TP
loading have been published, but it has been determined that increasing the thickness of surface
material can reduce surface erosion, as can reducing the amount of road surface draining directly
to streams (Roni et al. 2002). Since phosphorus is carried in sediment, reducing the amount of
erosion at and near stream crossings can reduce the amount of TP introduced into streams from
roads.

Table C6. Recommended BMPs for reducing loads from grazing and diffuse runoff.
NRCS Conservation Practice ID Description Cost
578 Stream Crossing $7/sq. yd.
560 Access Roads $8/sq. yd.

SUMMARY

The objective of the BMPs recommended in this plan is to reduce or remove those processes that
contribute TP loading to Recapture Reservoir. Unit costs have been provided for BMP measures
that are applicable to each pollutant source. The total cost of implementation will be dependent
upon site specific factors that can be obtained through communication with individual
stakeholders. The results of this TMDL assessment indicate that existing loads are marginally
above the 0.025 mg/L TP threshold that limits algae growth. Therefore, no load reductions are
recommended at this time. However, it is critical that loadings do not increase in order to
maintain the existing TP concentrations observed in the Reservoir. It is recommended that a
coordinated effort between local stakeholders and agencies responsible for managing public lands
take place. This effort should focus on identifying locations where existing BMPS are in place
and extend efforts to maintain these practices. It is reasonable to assume that pollutant sources

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with the most direct influence on existing water quality conditions should be addressed first,
followed by those with a lesser influence. A prioritized list of BMPs and water quality
improvement measures includes the following:

 Eliminate any existing routes providing direct animal access to the area immediately
surrounding Recapture Reservoir including areas below the high water mark. Livestock
access to degraded segments of tributary streams should also be eliminated or restricted
until viable riparian vegetation communities are established. Utilize offsite watering
structures where necessary, to satisfy livestock water demand.

 Implement riparian buffer strips along portions of Recapture Reservoir tributaries.
Emphasis should be placed on those areas where grazing and winter feeding has
occurred.

 Conduct range planting in sensitive areas to promote forage plants that intercept runoff
and promote infiltration. This method should focus on grazed areas where vegetative
cover is low and areas of bare ground exist.

This list of BMPs is designed to eliminate or reduce TP loading from areas that significantly
contribute direct surface runoff to Recapture Reservoir. Other BMPs recommended in this PIP
but not included on this list need to be implemented as well in order to support TMDL endpoints.
It is anticipated that by maintaining or implementing the BMPs recommended in this document,
that TP loads to Recapture Reservoir will not increase and provide a means for achieving the
water quality endpoint and load allocations established by the TMDL for Recapture Reservoir.

REFERENCES

Allaway, C. 2003. Phosphorous Loading Algorithms for the South Nation River. South Nation
Conservation Authority Clean Water Committee. Berwick, Ontario, Canada.

Chang, M. 2006. Forest hydrology: an introduction to water and forests. 2nd edition. P. 226.
CRC Press, Boca Raton, Florida. 474 pages.

Lee, K.H., T.M. Isenhard, R.C. Schultz, and S.L. Mickelson. 2000. Multispecies riparian buffers
trap sediment and nutrients during rainfall simulations. J. Environmental Quality
29:1200-1205.

Line, D.E., W.A. Harman, G.D. Jennings, E.J. Thompson, and D.L. Osmond. 2000. Nonpoint-
source pollutant load reductions associated with livestock exclusion. J. Environmental
Quality. 29(6):1882-1890.

McGinty, A., T.L. Thurow, and C.A. Taylor. 2000. Improving rainfall effectiveness on
rangeland. Texas Agricultural Extension Service. Publication E-155.
<http://agrilifebookstore.org/publications_details.cfm?whichpublication=423>. Accessed
January 22, 2008.

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Owens, L.B., W.M. Edwards, and R.W. Keuran. 1996. Sediment losses from a pastured
watershed before and after stream fencing. J. Soil and Water Conservation 51(1):90-94.

Roni, P., T.J. Beechie, R.E. Bilby, F.E. Leonetti, M.M. Pollock, and G.R. Pess. 2002. A review
of stream restoration techniques and a hierarchical strategy for prioritizing restoration in
Pacific Northwest watersheds. North American Journal of Fisheries Management 22:1-
20.

Schmitt, T.J., M.G. Dosskey, and K.D. Hoagland. 1999. Filter strip performance and processes
for different vegetation, widths, and contaminants. J. Environment Quality 22:661-665.

Sheffield, R.E., S. Mostaghimi, D.H. Vaughan, E.R. Collins Jr., V.G. Allen. 1997. Off-stream
water resources for grazing cattle as a streambank stabilization and water quality BMP.
Transactions of the ASAE 40(3):595-604.

Sheridan, G.J. and P.J. Noske. 2007. Catchment-scale contribution of forest roads to stream
exports of sediment, phosphorus and nitrogen. Hydrological Processes 21(23):3107-
3122.

US Forest Service. 1990. Forest Plan Amendment: Forest wide range proper use criteria. Manti-
La Sal National Forest. September 1990.
<http://www.fs.fed.us/r4/mantilasal/projects/forest_plan_1986/forest_plan_amendments/
amend_05_proper_use_criteria.pdf>. Accessed January 21, 2008.

Zaimes, G.N., Schultz, R.C., Isenhart, T.M., Mickelson, S.K., Kovar, J.L., Russell, J.R., Powers,
W.P. 2004. Influence of Land-use Practices on Stream Bank Erosion in Iowa. In: ASA-
CSSA-SSSA Annual Meeting Abstracts, Oct. 31-Nov. 4, 2004, Seattle, WA.