Characterization of dissolved solids in water resources of agricultural lands near Manila, Utah 2004-05

The agricultural lands surrounding Manila, Utah have been identified by the NRCS as areas contributing dissolved solids to Flaming Gorge Reservoir (FGR). Estimates of the amount of dissolved solids discharged to FGR that are attributable to agricultural lands in the area are needed by resource managers to assess the benefits that may be realized from irrigation system improvements. During 2004-05, the U.S. Geological Survey (USGS) investigated the occurrence and distribution of dissolved solids in water from the agricultural lands near Manila, Utah, to determine the amount of dissolved solids being discharged to FGR.Scientific Investigations Report 2006- 5211 Version 2.0, June 2007 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 U. S. Department of the Interior U. S. Geological Survey Prepared in cooperation with the NATURAL RESOURCES CONSERVATION SERVICE Cover photo: Birch Spring Draw outflow to Flaming Gorge Reservoir near Manila, Utah. ( Photograph by Steven Gerner.) Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 By S. J. Gerner, L. E. Spangler, B. A. Kimball, and D. L. Naftz U. S. Geological Survey Prepared in cooperation with the NATURAL RESOURCES CONSERVATION SERVICE U. S. Department of the Interior Scientific Investigations Report 2006- 5211 Version 2.0, June 2007 U. S. Department of the Interior Dirk Kempthorne, Secretary U. S. Geological Survey Mark D. Myers, Director Reston, Virginia: 2006 For additional information write to: U. S. Geological Survey Director, USGS Utah Water Science Center 2329 W. Orton Circle Salt Lake City, UT 84119- 2047 Email: GS- W- UTpublic- info@ usgs. gov URL: http:// ut. water. usgs. gov/ For more information about the USGS and its products: Telephone: 1- 888- ASK- USGS World Wide Web: http:// www. usgs. gov/ Any use of trade, firm, or product names is for descriptive purposes only and does not imply endorsement by the U. S. Government. Although this report is in the public domain, permission must be secured from the individual copyright owners to reproduce any copyrighted materials contained within this report. Scientific Investigations Report 2006- 5211 iii Contents Abstract....................................................................................................................... .................................... 1 Introduction................................................................................................................... .................................. 1 Purpose and Scope.......................................................................................................................... .. 1 Environmental Setting ........................................................................................................................ 3 Geology and Soils ......................................................................................................................... 3 Land Cover/ Use ............................................................................................................................ 3 Climate ............................................................................................................................... ........... 5 Hydrology ............................................................................................................................... ...... 5 Previous Studies and Data- Collection Efforts................................................................................ 5 Acknowledgments .............................................................................................................................. 6 Methods of Investigation.................................................................................................................. ............ 6 Data Collection ............................................................................................................................... .... 8 Daily Discharge and Specific Conductance ............................................................................ 8 Water- Quality Sample Collection, Processing, and Analysis................................................ 8 Quality Control........................................................................................................................ ...... 8 Data Analysis ............................................................................................................................... ...... 9 Dissolved- Solids Concentration Estimates .............................................................................. 9 Dissolved- Solids Load Calculations ........................................................................................ 10 Calculation of Salt- Loading Factor ......................................................................................... 11 Characterization of Dissolved Solids in Water Resources .................................................................... 11 Occurrence and Distribution of Dissolved Solids........................................................................ 11 Discharge of Dissolved Solids into Flaming Gorge Reservoir ................................................... 12 Salt- Loading Factor......................................................................................................................... . 16 Differentiation of Dissolved- Solids Sources ................................................................................ 17 Summary........................................................................................................................ ................................ 22 References Cited.......................................................................................................................... ................ 22 Figures Figure 1. Geographic features and water- quality monitoring sites in the study area near Manila, Utah........................................................................................................................... ........... 2 Figure 2. Geology of the study area near Manila, Utah............................................................................... 4 Figure 3. Land cover/ use in the study area near Manila, Utah.................................................................. 6 Figure 4. Relation of total adjusted dissolved- solids load at synoptic sites and total dissolved-solids load at fixed outflow- monitoring sites near Manila, Utah ............................................ 10 Figure 5. Relative composition of water in the study area near Manila, Utah ...................................... 13 Figure 6. Distribution of dissolved- solids concentration and load, and discharge at water-quality monitoring sites near Manila, Utah................................................................................. 14 Figure 7. Estimated daily total adjusted dissolved- solids load discharged from the study area near Manila, Utah, July 1, 2004, through June 30, 2005 ............................................................ 16 Figure 8. Cumulative total adjusted dissolved- solids load discharged from the study area near Manila, Utah, July 1, 2004, through June 30, 2005 ..................................................................... 17 iv Figure 9. Variation of 􀀃 􀁇 87Sr with strontium concentration in samples collected from selected sites near Manila, Utah. ................................................................................................................. 21 Figure 10. Variation of 􀁇 11B with boron concentration in samples collected from selected sites near Manila, Utah........................................................................................................................... 21 Tables Table 1. Site characteristics and summary of dissolved- solids concentration and load for water- quality monitoring sites near Manila, Utah ....................................................................... 7 Table 2. Instantaneous discharge and properties of water samples collected from water-quality monitoring sites near Manila, Utah................................................................................. 24 Table 3. Concentration of major ions in water samples collected from water- quality monitoring sites near Manila, Utah.............................................................................................. 34 Table 4. Field and analytical methods and minimum reporting levels for water- quality field measurements and constituent concentrations in samples collected from water-quality monitoring sites near Manila, Utah................................................................................... 9 Table 5. Relative percentage of major ions in selected water samples collected at water-quality monitoring sites near Manila, Utah................................................................................. 12 Table 6. Estimated dissolved- solids load in Sheep Creek Canal and Peoples Canal near Manila, Utah, April- October 2004 ................................................................................................ 15 Table 7. Dissolved- solids load at inflow, outflow, and fixed outflow- monitoring sites in the study area near Manila, Utah ....................................................................................................... 15 Table 8. Precipitation at Manila, Utah, and streamflow in Henrys Fork near Manila, Utah, July 2004 through June 2005 ......................................................................................................... 18 Table 9. Discharge and water- quality characteristics for selected water- quality monitoring sites used in the calculation of salt- loading factors for the study area near Manila, Utah ............................................................................................................................... .... 19 Table 10. Site identification and characteristics, chemical concentration, isotope ratio, and specific conductance of samples collected from selected water- quality monitoring sites near Manila, Utah .................................................................................................................. 20 v Conversion Factors, Datums, and Abbreviated Water- Quality Units Multiply By To obtain Length foot ( ft) 0.3048 meter ( m) mile ( mi) 1.609 kilometer ( km) inch ( in.) 2.54 centimeter ( cm) Area acre 0.4047 hectare ( ha) acre 0.004047 square kilometer ( km2) square mile ( mi2) 2.590 square kilometer ( km2) Volume acre- foot ( acre- ft) 1,233 cubic meter ( m3) Rate cubic foot per second ( ft3/ s) 0.02832 cubic meter per second ( m3/ s) gallon per minute ( gal/ min) 3.785 liter per minute ( L/ m) inch per year ( in/ yr) 2.54 centimeter per year ( cm/ yr) Mass ton per day ( ton/ d) 0.9072 metric ton per day ( ton/ d) Temperature in degrees Celsius (° C) may be converted to degrees Fahrenheit (° F) as follows: ° F = ( 1.8 × ° C) + 32. Temperature in degrees Fahrenheit (° F) may be converted to degrees Celsius (° C) as follows: ° C = (° F - 32) / 1.8. Horizontal coordinate information is referenced to the North American Datum of 1983 ( NAD 83). Vertical coordinate information is referenced to the National Geodetic Vertical Datum of 1929 ( NGVD 29). Altitude, as used in this report, refers to distance above the vertical datum. Specific conductance is reported in microsiemens per centimeter at 25 degrees Celsius ( μS/ cm at 25° C). Concentrations of chemical constituents in water are reported either in milligrams per liter ( mg/ L), micrograms per liter ( μg/ L), or nanograms per liter ( ng/ L). Isotopic ratios are reported in units of permil ( per thousand). vi Abstract Agricultural lands near Manila, Utah, have been identi-fied as contributing dissolved solids to Flaming Gorge Reser-voir. Concentrations of dissolved solids in water resources of agricultural lands near Manila, Utah, ranged from 35 to 7,410 milligrams per liter. The dissolved- solids load in seeps and drains in the study area that discharge to Flaming Gorge Res-ervoir ranged from less than 0.1 to 113 tons per day. The most substantial source of dissolved solids discharging from the study area to the reservoir was Birch Spring Draw. The mean daily dissolved- solids load near the mouth of Birch Spring Draw was 65 tons per day. The estimated annual dissolved- solids load imported to the study area by Sheep Creek and Peoples Canals is 1,330 and 13,200 tons, respectively. Daily dissolved- solid loads dis-charging to the reservoir from the study area, less the amount of dissolved solids imported by canals, for the period July 1, 2004, to June 30, 2005, ranged from 72 to 241 tons per day with a mean of 110 tons per day. The estimated annual dis-solved- solids load discharging to the reservoir from the study area, less the amount of dissolved solids imported by canals, for the same period was 40,200 tons. Of this 40,200 tons of dissolved solids, about 9,000 tons may be from a regional source that is not associated with agricultural activities. The salt- loading factor is 3,670 milligrams per liter or about 5.0 tons of dissolved solids per acre- foot of deep percolation in Lucerne Valley and 1,620 milligrams per liter or 2.2 tons per acre- foot in South Valley. The variation of 􀄯 87Sr with strontium concentration indicates some general patterns that help to define a concep-tual model of the processes affecting the concentration of strontium and the 􀄯 87Sr isotopic ratio in area waters. As excess irrigation water percolates through soils derived from Mancos Shale, the 􀄯 87Sr isotopic ratio ( 0.21 to 0.69 permil) approaches one that is typical of deep percolation from irrigation on Mancos Shale. The boron concentration and 􀄯 11B value for the water sample from Antelope Wash, being distinctly different from water samples from other sites, is evidence that water in Antelope Wash may contain a substantial component of regional ground- water flow. Introduction Water from the Colorado River and its tributaries is used for municipal and industrial purposes by about 27 million peo-ple and irrigates nearly 4 million acres of land in the Western United States ( U. S. Department of the Interior, 2003). Water users in the Upper Colorado River Basin consume water from the Colorado River and its tributaries, reducing the amount of water in the river suitable for domestic use and crop irrigation. In addition, application of water to agricultural land within the basin in excess of crop needs can increase the transport of dissolved solids to the river. As a result, the dissolved- solids concentration in the Colorado River has increased, affecting downstream water users. In this report, the term " dissolved solids" refers to the sum of the individual dissolved constitu-ents present in water, and it is synonymous with " salinity." In 1974, Congress enacted the Colorado River Basin Salinity Control Act, which authorizes the construction, operation, and maintenance of salinity control works in the Colorado River Basin. The U. S. Department of Agriculture ( USDA) is a partner in the Colorado River Salinity Control Program, directing offices of the Natural Resources Conserva-tion Service ( NRCS) in the Upper Colorado River Basin to make reductions, where possible, in the dissolved- solids load discharging to the Colorado River from agricultural lands. The NRCS has been actively working to reduce these dissolved-solid loads through promotion of improved irrigation methods. The agricultural lands surrounding Manila, Utah ( fig. 1), have been identified by the NRCS as areas contributing dissolved solids to Flaming Gorge Reservoir ( FGR). Estimates of the amount of dissolved solids discharged to FGR that are attributable to agricultural lands in the area are needed by resource managers to assess the benefits that may be realized from irrigation system improvements. During 2004- 05, the U. S. Geological Survey ( USGS) investigated the occurrence and distribution of dissolved solids in water from the agri-cultural lands near Manila, Utah, to determine the amount of dissolved solids being discharged to FGR. Purpose and Scope This report documents the methods used in, and results of, an investigation to determine the amount of dissolved solids contributed to FGR from Lucerne Valley, South Valley, Antelope Hollow, and a portion of Henrys Fork near Manila, Utah. The report includes a description of the occurrence and distribution of dissolved solids in water resources in or near the agricultural lands near Manila. The report also includes a discussion of the use of isotopes to evaluate the relative contri-butions of dissolved solids from irrigation and non- irrigation sources. Measurements of specific conductance and surface- water discharge made at 23 water- quality monitoring sites from Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 By S. J. Gerner, L. E. Spangler, B. A. Kimball, and D. L. Naftz EXPLANATION Agricultural lands Study area boundary Water- quality sampling site Inflow synoptic Outflow synoptic Fixed outflow monitoring Manila WYOMING UTAH SWEETWATER COUNTY DAGGETT COUNTY AW- 1 BSD- 1 CC- 1 HFK- 1 PC- 1 SCC- 1 SVC- 1 SVC- 2 SPG- 1 Long Park Reservoir Lodgepole Henrys Fork Sheep Creek Canal Sheep Creek Creek 􀀓 􀀔 􀀐 􀀎 􀀍 􀀏 􀀋 􀀒 􀀑 􀀊 􀀌 Wash Antelope Canal Peoples Cottonwood Creek Lucerne Valley South Valley Birch Spring Draw Jessen Butte 44 43 43 414 530 Study area 0 1 3 5 Miles 0 2 4 5 Kilometers 2 1 3 4 􀀅 􀀃 􀀖 􀀂 􀀈 􀀁 􀀁 􀀅 􀀆 􀀖 􀀉 􀀂 􀀃 􀀁 􀀇 􀀄 􀀖 􀀉 􀀂 􀀃 􀀅 􀀂 􀀖 􀀆 􀀁 Antelope Hollow Antelope Spring Sheep Creek Flaming Gorge Reservoir Sheep Creek Canal Sheep Creek Canal HFK- 3 SCC- 1 BSD- 1 Flaming Gorge Reservoir Inset Inset enlarged 500 percent HFK- 3 PC- 2 BSD- 2 DRN- 2 DRN- 3 DRN- 8 SP- 3 SP- 1 6000 DRN- 1a DRN- 1 SP- 4 LAT- 1 DRN- 4 SP- 5 DRN- 5 Figure 1. Geographic features and water- quality monitoring sites in the study area near Manila, Utah. 2 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 May 2004 to June 2005, and results from chemical analysis of water samples collected at those sites, are presented in this report. Estimates of the dissolved- solids load discharging from the study area were determined from these data and also are presented in this report. Environmental Setting The study area is located near the small farming com-munity of Manila, just west of FGR along the border between Utah and Wyoming, and covers about 100 mi2. The northern part of the study area is located in Sweetwater County, Wyo-ming, and the southern part is located in Daggett County, Utah ( fig. 1). The study area includes the watersheds of Antelope Hollow, Birch Spring Draw, South Valley, and the lower part of Henrys Fork. Water discharged from these watersheds is impounded in FGR in the eastern part of the study area. The southern border of the study area is defined by a prominent, steeply dipping ridge that includes Jessen Butte. Altitudes range from about 6,000 ft in the eastern part of the study area along FGR, to as much as 8,600 ft on Jessen Butte, in the southwestern part of the area. Vegetation in the study area consists of willows and cottonwoods along the rivers, sage-brush and rabbit brush along the valley bottoms, and evergreen forests at the higher altitudes. Dispersed settlement in the Manila area began in the mid to late 1800s with the establishment of small cattle and horse ranches. In the fall of 1890, the agricultural possibilities of Dry Valley ( later changed to Lucerne Valley) were recog-nized by Adolph Jessen, an engineer, who, along with others, incorporated the Lucerne Land and Water Company in 1892. In 1894, construction began on the 14.5- mi- long Sheep Creek Canal to the head of Lucerne Valley. The main canal was rated at 50 ft3/ sec and was divided into two 20 ft3/ sec laterals. One lateral flowed 6 mi along the northern slope of the valley and the other followed the south slope for 3 mi. The overall canal system irrigated several thousand acres mostly in the central and western sections of the valley ( Johnson and others, 1998). In 1899, the Lucerne Land and Water Company divested itself of the Sheep Creek Canal, and the Sheep Creek Irriga-tion Company was created and controlled by local irrigators. In response to a need to obtain more economical water, the Peoples Canal Company was formed by a group of home-steaders in 1899 to irrigate 2,000 acres at the eastern end of the valley by diverting water from Henrys Fork. The diversion ditch and Peoples Canal were completed in 1902 and water was delivered the following spring. A century later, water from Henrys Fork and Sheep Creek are still diverted into Lucerne Valley for irrigation ( fig. 1). Geology and Soils The geology of the study area consists of a sequence of Jurassic, Cretaceous, and Tertiary- age sedimentary rocks of marine and terrestrial origin that generally dip to the north away from the Uinta Mountains. As a result, the youngest rocks are located in the northern part of the study area. Closer to the mountain front, the dip of the rocks is steeper and ridges of more- resistant sandstone separate intervening valleys of less- resistant rocks such as shales. Jurassic- age sandstones, shales, and mudstones border and underlie most of South Valley ( fig. 2). These units include the Navajo Sandstone and the Curtis, Entrada, Carmel, and Morrison Formations. The Cretaceous- age Dakota and Cedar Mountain Formations form the ridges that divide South Valley from Lucerne Valley and consist of interbedded fluvial sandstones, siltstones, and shales. The Mancos Shale underlies most of Lucerne Valley, including the area around the community of Manila, and con-sists primarily of silts and clays that tend to form low undulat-ing hills. Streamflow from rainfall and irrigation runoff and from springs and seeps in these areas can have high dissolved-solids concentrations ( Mason and Miller, 2004). The northern part of the study area is underlain by early Tertiary- age sediments that make up the Wasatch, Green River, and Bridger Formations. These units consist of vari-able amounts of limestone ( marls), shales, sandstones ( partly tuffaceous), and mudstones that were deposited in lacustrine ( Green River Formation) and fluvial ( Wasatch and Bridger Formations) environments. Most of the land in the Wyoming part of the study area is underlain by the Eocene- age Bridger Formation, which weathers into badlands in some areas. Irrigated lands adjacent to the floodplain of Henrys Fork are underlain by the Laney Member of the Green River Formation ( Mason and Miller, 2004). Quaternary- age alluvium and col-luvial deposits also are present along the floodplain of Henrys Fork as well as along smaller tributary drainages throughout the study area. These deposits consist primarily of sands and gravels that have been transported downstream from the Uinta Mountains. Soils in the study area are derived from a variety of rock types, including shale, sandstone, and mudstone. Soils in the irrigated areas of Lucerne Valley, which are derived primar-ily from the Mancos Shale, are mostly classified as Rhoamett silty clays, Poposhia loams, and McFadden fine sandy loams ( Schwarz and Alexander, 1995). In parts of Lucerne Valley, particularly those south and east of Manila, salt or alkali flats also develop from near- surface evaporation and concentration of minerals in the shaly soils. In contrast, soils developed from the Green River Formation along Henrys Fork are primarily classified as Luhon channery loams. In the northern part of the area where the Bridger Formation crops out, the soils are classified within the Roto- Rockinchair- Rencot complex and Blazon thin solum- Blazon- Lilsnake complex. Along the flood-plain of Henrys Fork, soils derived from the alluvial sediments are part of the Hagga- Cowestglen association. Land Cover/ Use Land- cover and - use data were obtained from the National Land Cover Dataset ( NLCD) ( U. S. Geological Introduction 3 Tb Tgl Tb Tgl Tgl Tb Twm Twm Kba Kba Qa Qao T3 T3 T3 Qao Qao J1 J1 Qao Qao Qa Qa Qa Qa Jg Jg Jg K2 K2 K1 J2 Qls K2 K2 K2 K3 T1 J2 Quaternary Surficial deposits- Older alluvium and colluvium Quaternary Surficial deposits- Landslides Quaternary Surficial deposits- Alluvium and colluvium Paleocene- Eocene Uinta Mountains- Wasatch/ Colton Formation, Flagstaff Limestone Eocene Green River Formation- Evacuation Creek, Parachute Creek ( oil shale), Garden Gulch, Douglas Creek, Laney Formation Eocene- Oligocene Uinta Mountains- Duchesne River Formation, Uinta Formation- south of Uinta Mountains, Bridger Formation- north of Uinta Mountains Cretaceous Uinta Mountains- Mesaverde Group ( coal) Cretaceous Mancos Shale ( Hilliard Shale and Blair Formation north of Uinta Mountains), Frontier Sandstone, Mowry Shale Cretaceous Dakota and Cedar Mountain Formations Jurassic Uinta Mountains- Morrison Formation Jurassic Uinta Mountains- Curtis Formation, Entrada Sandstone, Carmel Formation Jurassic Nugget ( Navajo) Sandstone Water Jg J2 J1 K1 K2 Qa Qao Qls/ Kba T1/ Twm Tgl T3/ Tb K3 EXPLANATION 0 1 3 5 MILES 0 2 4 5 KILOMETERS 2 1 3 4 41 􀁳 07' 109 􀁳 36' 109 􀁳 54' 40 􀁳 57' WYOMING UTAH Base from U. S. Geological Survey digital line graph data, 1: 100,000 scale, 1979- 84 and 1986- 87, 1989 Universal Transverse Mercator projection, Zone 12. National Elevation Data set 1: 24,000 scale, 1999 Geological data from Love and Christiansen, 1985 Hintze and others, 2000 Figure 2. Geology of the study area near Manila, Utah. 4 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 Survey, 2006). This data set provides a consistent land- cover data layer for the conterminous United States and represents conditions in the early to mid- 1990s. Land cover in the study area consists primarily of shrublands that are used for grazing; about 41,000 acres of shrublands are distributed across the study area. Agricultural lands in Lucerne Valley, South Valley, Antelope Hollow, and along Henrys Fork amount to about 9,800 acres ( fig. 3). Alfalfa and hay are the primary crops with about 7,700 acres of pasture lands and 1,900 acres of alfalfa. Fallow areas, row crops, and small grains occupy less than 100 acres of land, collectively. Forest and grasslands cover about 4,500 and 4,900 acres, respectively. Forests are primar-ily located at higher altitudes along the southern margin of the area and along ridgelines within Lucerne Valley; however, grasslands are fairly evenly distributed throughout the study area. Urban lands make up about 930 acres in the vicinity of Manila. Climate Climate in the study area consists of mild summers and cold winters. For 1952 through 2005, mean annual tempera-ture was 45.3oF ( Western Regional Climate Center, 2005). Extremes have ranged from a low of - 33oF to a high of 99oF. Mean annual precipitation in the study area is 9.14 in., with the precipitation distributed through the spring ( 2.94 in.), summer ( 2.96 in.), fall ( 2.24 in.), and winter ( 1.00 in.). Mean annual snowfall in the study area is about 38 in/ yr, with higher quantities on the ridges and mountains along the southern boundary of the area. The pan evaporation rate ( May- October) in the study area is about 33 in/ yr ( Hemphill, 2005), substan-tially exceeding precipitation. Hydrology Site characteristics of water- quality monitoring sites are listed in table 1. Most of the surface water in the study area originates in the Uinta Mountains immediately to the west and southwest, and flows generally west to east through the area to eventually discharge into FGR. Henrys Fork has the most flow of any perennial stream in the study area, originat-ing from streams that flow north from the Uinta Mountains. Sheep Creek and Lodgepole Creek also originate in the Uinta Mountains and flow along the southern border of the study area, eventually discharging into FGR. Other smaller peren-nial streams in the study area include Birch Spring Draw in the center of Lucerne Valley, and Antelope Wash in the north-western part of the study area ( fig. 1). The stream in Antelope Wash originates from springs that discharge within the study area and then flow to the northeast to merge with Henrys Fork. Numerous ephemeral streams are located in the study area. The need to divert water for irrigation use was recognized early, prompting the construction of canal systems. Water for irrigation is obtained from drainages to the southwest along the flank of the Uinta Mountains and from Henrys Fork, and then diverted through canals into the valley. Peoples and Sheep Creek Canals are the principal diversions in the study area ( fig. 1). Sheep Creek Canal diverts water for use in Lucerne Valley, South Valley, and Antelope Hollow. Water is gener-ally discharged from Long Park Reservoir into Sheep Creek Canal from May to September. Discharge in the canal at the head of Lucerne Valley ( site SCC- 1) varied during this study. For example, the discharge measured in May 2004 was 100 ft3/ s and the discharge measured in September 2004 was 34 ft3/ s ( table 2, located at back of report). The highest discharge measured was 126 ft3/ s in June 2005. Peoples Canal distributes water to irrigate lands in the lower part of Lucerne Valley. Water is generally diverted from Henrys Fork into Peoples Canal from April to November. Discharge at the head of the canal ( site PC- 1) varied during this study. For example, the discharge measured in June 2004 was 50 ft3/ s and the dis-charge measured in October 2004 was 24 ft3/ s ( table 2). Ground- water quality is highly variable among the aqui-fers present in the study area, even within the same hydrogeo-logic unit, and tends to increase in dissolved- solids concentra-tion downgradient from recharge areas and with depth ( Mason and Miller, 2004). Yields from wells in unconsolidated depos-its along the floodplain of Henrys Fork are typically less than 10 gal/ min. Ground water is present in the Bridger aquifer in the Bridger Formation, where most of the sediments are of volcanic origin ( Koenig, 1960). As a result, sulfate, fluoride, boron, iron, and manganese contribute to high dissolved- solids concentrations in ground water. The Laney aquifer ( Green River Formation) has potential yields of as much as 75 gal/ min and dissolved- solids concentrations ranging from 650 to 4,200 mg/ L. Water in the Laney tends to be a sodium sulfate type. Ground- water discharge from the Green River Formation ( fig. 2) is a substantial contributor to base- flow dissolved- solids loads in Henrys Fork ( Mason and Miller, 2004). The Wasatch aquifer typically produces as much as 500 gal/ min. Water within the aquifer is quite variable and is typi-cally a sodium bicarbonate or sodium sulfate type. Sulfate concentrations tend to be high in many areas, which can interfere with plant growth. Locally high concentrations of boron and fluoride also are present in ground water. Aquifers that yield small to moderate quantities of water suitable for domestic or agricultural use are contained within the Nugget ( Navajo), Entrada, Morrison, and Dakota Formations. Previous Studies and Data- Collection Efforts Many studies of water resources and water chemistry have been completed in the upper Green River basin. A good synopsis of these is available in Mason and Miller ( 2004). Most of these studies have been regional in nature and do not provide much water- quality data specific to the agricultural lands near Manila. Hence, dissolved- solids data from sur-face- and ground- water resources in the agricultural lands near Manila are generally sparse prior to this study. However, about 500 samples from Henrys Fork near Manila ( USGS station Introduction 5 EXPLANATION Rangeland Forest Agriculture Urban Wetland Water Barren land 41 􀁳 07' 109 􀁳 36' 109 􀁳 54' 40 􀁳 57' 0 1 3 5 Miles 0 2 4 5 Kilometers 2 1 3 4 WYOMING UTAH Lucerne Valley South Valley Antelope Hollow Henrys Fork Figure 3. Land cover/ use in the study area near Manila, Utah. 09229500), were collected by USGS personnel from 1954 to 1989 and analyzed for dissolved- solids concentration. These data are available from the USGS National Water Information System ( NWIS) database. The U. S. Forest Service collected water samples from Birch Spring Draw at the Flaming Gorge National Recreation Area boundary from 2000 to 2003. Sample analyses included dissolved- solids concentration and results are available from the U. S. Environmental Protection Agency STORET database. A preliminary investigation of dis-solved solids in water resources in the agricultural areas near Manila was conducted by the NRCS and the Daggett County Soil Conservation District from 1991 to 1994. Water conduc-tivity and discharge were measured periodically at eight sites. These data are unpublished. Acknowledgments Landowners in the agricultural areas near Manila who provided access to sampling sites and cooperated in the process of sample collection are gratefully acknowledged. Jerry Steglich, Manila area landowner, is acknowledged for his considerable assistance with data collection and project coordination. NRCS personnel are acknowledged for provid-ing insight into salinity problems and agricultural practices in the study area. Methods of Investigation Drains, seeps, and streams transport dissolved solids from the study area into FGR. To estimate the total dissolved- sol-ids load from these sources, a study approach was followed that included the periodic ( synoptic) field measurement of discharge and water quality at all measurable flows from the study area ( as many as 23 sites), and the regular or continuous field measurement of discharge and water quality at three fixed monitoring sites. Continuous determination of dissolved- solids load at all sites discharging to FGR was not practical. Thus, regular and, during some time periods, continuous field measurements at the three largest drains in the study area were made to capture daily variability in dissolved- solids concentration and load and to provide a basis for estimating daily and annual dissolved-solid loads discharging to FGR from the study area. 6 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 Table 1. Site characteristics and summary of dissolved- solids concentration and load for water- quality monitoring sites near Manila, Utah [ ddmmss, degrees, minutes, seconds; e, estimated; <, less than] Site identifier Site name U. S. Geological Survey site-identification number Latitude ( ddmmss) Longitude ( dddmmss) Site type Dissolved- solids concen-tration, in milligrams per liter Dissolved- solids load, in tons per day Num-ber of measure- Mini- ments mum Mean Maxi-mum Mini-mum Mean Maxi-mum HFK- 1 Henrys Fork at Peoples Canal, near Manila, Utah 410233109440902 410233 1094409 Stream 602 779 1,120 e1.2 74.9 110 6 HFK- 3 Henrys Fork at mouth, near Manila, Utah 410000109390401 410000 1093904 Stream 364 952 1,520 17.6 101 e215 8 SCC- 1 Sheep Creek Canal at head, near Manila, Utah 405800109494601 405800 1094946 Canal 35 338 1,390 e .4 6.4 12.6 7 PC- 1 Peoples Canal at Henrys Fork, near Manila, Utah 410233109440901 410233 1094409 Canal 265 776 1,210 <. 1 51.0 109 8 AW- 1 Antelope Wash at Co. Rd. 13, near Manila, Utah 410244109454901 410244 1094549 Drain 3,580 4,173 4,560 15.2 31.9 45.8 8 CC- 1 Cottonwood Creek at County Road 13, near Manila, Utah 410104109412001 410104 1094120 Drain 2,980 3,540 4,070 .4 3.0 7.3 7 PC- 2 Peoples Canal near mouth, near Manila, Utah 405902109381801 405902 1093818 Drain 963 1,760 3,140 .6 30 96.2 1186 BSD- 1 Birch Spring Draw near Manila, Utah 405908109400201 405908 1094002 Drain 894 2,520 5,880 12.4 35.8 157 1233 BSD- 2 Birch Spring Draw at mouth, near Manila, Utah 405925109383901 405925 1093839 Drain 1,550 3,160 5,940 29.5 65.0 113 10 LAT- 1 Lateral 1 near Manila, Utah 405926109382801 405926 1093828 Drain 1,600 3,140 5,870 .2 1.1 3.2 5 SV- 2 South Valley Canal near mouth 405832109381401 405832 1093814 Drain 639 1,240 1,740 2.2 12.1 30.0 8 SV- 1 South Valley Canal near Manila, Utah 405804109402101 405804 1094021 Drain 485 948 2,960 .4 6.6 33.6 1224 DRN- 1 Drain 1 near Manila, Utah 405945109390001 405945 1093900 Drain 2,070 3,920 7,410 <. 2 < 2.8 15.1 9 DRN- 1a Drain 1a near Manila, Utah 405945109390002 405945 1093900 Drain 2,820 4,200 6,320 .2 1.1 2.1 7 DRN- 2 Drain 2 near Manila, Utah 405938109385301 405938 1093853 Drain 1,830 3,830 5,300 .8 6.9 28.6 9 DRN- 3 Drain 3 near Manila, Utah 405923109383601 405923 1093836 Drain 1,700 2,860 3,560 < .1 < 2.3 8.8 9 DRN- 4 Drain 4 near Manila, Utah 405921109382801 405920 1093828 Drain 900 2,400 3,090 <. 1 < 0.8 2.7 8 DRN- 5 Drain 5 near Manila, Utah 405919109382001 405919 1093820 Drain 2,120 2,610 2,920 <. 1 <. 1 e .8 5 DRN- 8 Drain 8 near Manila, Utah 405937109385501 405937 1093855 Drain 4,360 4,890 5,760 <. 2 <. 2 .4 7 SP- 1 Seep 1 near Manila, Utah 405936109384501 405936 1093845 Seep 3,650 3,710 3,850 .1 .3 .5 5 SP- 3 Seep 3 near Manila, Utah 405922109383501 405922 1093835 Seep 2,790 3,410 3,660 <. 1 <. 1 .1 5 SP- 4 Seep 4 near Manila, Utah 405936109385101 405936 1093851 Seep 5,190 5,510 5,950 <. 2 <. 2 .3 3 SPG- 1 Unnamed Spring near Manila, Utah 405828109512101 405828 1095121 Spring 638 654 671 <. 1 <. 1 <. 1 2 1Includes dissolved- solids concentration and load values determined from daily measurements of discharge and specific conductivity. Methods of Investigation 7 Data Collection Daily Discharge and Specific Conductance Periodic measurements of discharge, specific conduc-tance, and water temperature were made on canals and streams importing dissolved solids to the study area ( three sites) and at all identifiable sites discharging dissolved solids to the reser-voir ( as many as 16 sites) during nine field trips between June 2004 and June 2005 ( fig. 1, tables 1 and 2). To capture the daily variability in discharge and dis-solved- solids load, three fixed outflow- monitoring sites were established where measurements of stream stage and specific conductance were taken at more frequent intervals. These sites were established on the largest drains in the study area ( Birch Spring Draw ( BSD- 1), Peoples Canal ( PC- 2), and South Valley ( SV- 1)) as near their outflow to FGR as practi-cal. From July 1 to September 30, 2004, daily measurements of gage height and specific conductance were made at the fixed sites. Periodic measurements ( averaging once every two weeks) of gage height and specific conductance were made from October 2004 to February 2005; however, as a result of field conditions and personnel and equipment constraints, there were no measurements of stage or specific conductance made for many of the days in this period. Continuous mea-surements ( 15- minute interval) of stage and specific conduc-tance were made at BSD- 1 and SV- 1 from February 25 to June 30, 2005; however, daily measurements of gage height and specific conductance were made at PC- 2 during this period. Stage- discharge relations for the three fixed sites were defined by making instantaneous discharge and stage measure-ments on about a monthly basis. The shifting control method was applied to the stream stage ( water- surface altitude relative to an arbitrary datum) record from the three sites to calculate discharge. This method of determining stream discharge is described in detail in Buchanan and Somers ( 1969) and Ken-nedy ( 1983). Data- collection frequency at these sites varied as a result of changing field conditions and the availability of equipment and personnel. The number of stage measurements that the mean daily discharge at the three monitoring sites was based on varied from 1 to 96 depending on whether the data were collected by a field observer or a field instrument with data- logging capabilities. Water- Quality Sample Collection, Processing, and Analysis Water- quality measurements were made at synoptic and fixed outflow- monitoring sites in the study area from May 2004 through June 2005. All site visits included on- site field measurement of discharge, specific conductance, and water temperature. Samples were collected at selected sites and analyzed for dissolved major ions ( table 3, located at back of report) so that water types within the study area and their distribution could be determined. Water- quality samples from selected sites were analyzed for residue on evaporation at 180oC ( ROE) so that subsequent calculations of dissolved- sol-ids load could be made. Surface- water samples were collected with a depth- integrated, isokinetic sampler and applying the equal- width- increment ( EWI) method when appropriate ( Webb and others, 1999); however, samples from shallow or slow moving streams were collected from the center of flow into an open- mouth 1- liter polyethylene bottle. Water samples collected for analysis of dissolved constituents were filtered through a disposable 0.45- micron capsule filter by using a peristaltic pump. Sample filtering and preservation were com-pleted in the field. Water samples were analyzed for the concentration of major ions at the USGS National Water Quality Laboratory ( NWQL) in Lakewood, Colorado, with the standard analytical techniques described in Fishman and Friedman ( 1989). All data are stored in the USGS NWIS database. Analytical meth-ods and minimum reporting limits for the analyzed properties and constituents are listed in table 4. Water samples were collected from selected sites, filtered through a disposable 0.45- micron capsule filter, and ana-lyzed in the USGS stable isotope laboratory in Menlo Park, California, for strontium and boron, and the isotopic ratios of naturally occurring 87Sr and 86Sr; and naturally occurring 10B and 11B. Quality Control Quality- control samples were collected at selected sites to determine if data quality associated with water samples col-lected for this study is sufficient for water- quality assessments. Two types of quality- control samples were collected and analyzed: ( 1) field blanks to determine sample bias, and ( 2) concurrent replicates to determine sample variability. Results from analysis of these samples are available from the USGS NWIS database. Field blanks were collected once each at sites BSD- 2 and PC- 2 and analyzed for alkalinity and the major ions listed in table 4. None of the major ions were detected in amounts higher than the minimum reporting levels. The alkalinities of these samples, 3 and 5 mg/ L, were above the minimum reporting level but less than 5 percent of the amount detected in all of the environmental samples collected except those from site SCC- 1. The alkalinity measured in water samples from site SCC- 1 ranged from 16 to 26 mg/ L; consequently, if the alkalinity measured in the two field blanks was associ-ated with systemic contamination, the results from analysis of water samples collected at SCC- 1 could have a positive bias, that in turn, would result in a positive bias in the determination of dissolved- solid loads at site SCC- 1. However, the poten-tial contamination would have resulted in a relatively small increase in the dissolved- solids load calculated to be imported to the study area and in the subsequent calculation of the dis-solved- solids load discharging to FGR. 8 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 A concurrent replicate sample was collected at site AW- 1 and analyzed for alkalinity and the major ions listed in table 4. The difference in the concentration of those parameters between the two samples was less than 5 percent. Addition-ally, concurrent replicate ROE samples were collected once at sites PC- 1, BSD- 1, and SV- 1. The difference in ROE between each of the two samples was less than 3 percent. Results from the concurrent replicate samples collected during this study indicate that field and laboratory methods did not significantly affect the variability of results from water- quality sampling. Data Analysis Dissolved- Solids Concentration Estimates Specific conductance is a measure of the capacity of water to conduct an electrical current and is a function of the types and quantities of dissolved solids in water ( Radke and others, 2005). The USGS reports specific conductance in microsiemens per centimeter at 25° C ( μS/ cm at 25° C). As the concentration of dissolved solids increases, the specific- con-ductance value of the water increases; hence, specific- conduc-tance measurements provide a good indication of dissolved-solids concentration. A relation between specific conductance and dissolved- solids concentration generally exists in many water sources. This allows specific conductance to be used in conjunction with chemical analyses to estimate dissolved-solids concentration and load. This relation, expressed as the ratio of dissolved- solids concentration ( from ROE) to specific conductance, was established at all sites. Sites were grouped by type ( stream, canal, drain, seep, or spring) and an average dissolved- solids/ specific- conductance ratio was determined for each type so that this average ratio could be used to estimate dissolved- solids concentration at sites with no chemical data. The relation between dissolved- solids concentration and spe-cific conductance at water- quality monitoring sites in the study area varied spatially and temporally. For example, the mean dissolved- solids/ specific- conductance ratio at site BSD- 2 was 0.82 ( table 2), but the mean dissolved- solids/ specific- conduc-tance ratio at site AW- 1 was 1.0. The dissolved- solids/ specific conductance ratio at site BSD- 2 ranged from 0.75 to 0.89. Higher dissolved- solids/ specific- conductance ratios were gen-erally associated with water containing higher concentrations of sodium and sulfate and lower ratios were associated with calcium bicarbonate type water. Table 4. Field and analytical methods and minimum reporting levels for water- quality field measurements and constituent concentra-tions in samples collected from water- quality monitoring sites near Manila, Utah [ ft3/ s, cubic feet per second; μS/ cm, microsiemens per centimeter; ° C, degrees Celsius; mg/ L, milligrams per liter; ICP, inductively coupled plasma; IC, ion chromatography] Measurement or constituent Unit Field method Analytical method Minimum reporting level Physical Properties Discharge, instantaneous ft3/ s Mid- interval - Variable Specific conductance μS/ cm at 25 ° C Point - 1 Water temperature ° C Point - .1 Alkalinity mg/ L - Titration 1 Major Ions Calcium, dissolved, as Ca mg/ L - ICP .1 Chloride, dissolved, as Cl mg/ L - IC .1 Fluoride, dissolved, as F mg/ L - Ion- selective electrode .1 Hardness, total, as CaCO 3 mg/ L - Calculated 1 Magnesium, dissolved, as Mg mg/ L - ICP .1 Potassium, dissolved, as K mg/ L - ICP .1 Silica, dissolved, as Si mg/ L - ICP .1 Sodium, dissolved, as Na mg/ L - ICP .1 Sulfate, dissolved, as SO 4 mg/ L - IC .1 Solids, dissolved, sum of constituents mg/ L - Calculated 1 Solids, dissolved, residue on evaporation ( ROE) at 180° C mg/ L - Gravimetric 10 Methods of Investigation 9 Dissolved- Solids Load Calculations The approach to calculating the dissolved- solids load discharged from the study area between July 1, 2004, and June 30, 2005, involved a multiple- step process. First, dissolved-solids loads being transported into the study area and being discharged from the study area to FGR were calculated for each of nine periodic visits to the study area. The dissolved-solids load imported to the study area through Sheep Creek Canal and in Henrys Fork was calculated and subtracted from the total load calculated for the 15 sites that were identified as discharging water to FGR. This resulted in a total adjusted dissolved- solids load ( TADSL) that could be attributed to agricultural activities in the Manila area. Concurrently, the dissolved- solids load at the three fixed outflow- monitoring sites on the main drains discharging to FGR was determined. The relation between the load calculated for the fixed outflow-monitoring sites and the TADSL discharging from the Manila study area was determined. For each day that data were col-lected at the three fixed outflow- monitoring sites, a daily mean dissolved- solids load was calculated. For days when no data were collected at the fixed outflow- monitoring sites, no daily mean dissolved- solid loads were estimated. The daily dis-solved- solids load values at the fixed outflow- monitoring sites and the relation between the dissolved- solids load at the fixed outflow- monitoring sites and the TADSL ( fig. 4) were used to estimate the daily TADSL discharged from the study area. The TADSL discharged from the study area has a predict-able relation to the dissolved- solids load at the three fixed outflow- monitoring sites. A regression model that was used to describe the relation of the TADSL and the dissolved- solids load at the fixed outflow- monitoring sites is shown in equation 1: TADSL = 59.4854+ 0.8394ML+ e ( 1) where: TADSL is the total measured dissolved- solids load ( less the dissolved- solids load in inflow to the study area), discharged from the study area, in tons/ d; ML is the monitored dissolved- solids load at fixed outflow- monitoring sites, in tons/ d; and e is the residual error. On the right side of the equation, the variable ML accounts for variability in TADSL relative to the load at fixed outflow- monitoring sites. The overall F- test statistic ( 27.83 on 1 and 7 degrees of freedom) for this model has a p- value of 0.001. This indicates that the apparent relation of the explana-tory variable and TADSL was not likely to arise by chance alone. The coefficient of determination ( R- squared) for this model is 0.80. 50 100 150 TOTAL DISSOLVED- SOLIDS LOAD AT FIXED LOAD- MONITORING SITES, IN TONS PER DAY 0 50 100 150 200 250 TOTAL ADJUSTED DISSOLVED- SOLIDS LOAD AT SYNOPTIC SITES, IN TONS PER DAY 0 200 Figure 4. Relation of total adjusted dissolved- solids load at synoptic sites and total dissolved- solids load at fixed outflow-monitoring sites near Manila, Utah. 10 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 Daily mean dissolved- solids load calculated for the fixed outflow- monitoring sites was applied to equation 1 to deter-mine daily TADSL. For periods with missing data at the fixed outflow- monitoring sites, the daily TADSL was estimated by projecting the calculated daily TADSL at the beginning and end of those periods to the midpoint of the period. Estimates of daily TADSL were summed to calculate an estimated annual TADSL. Calculation of Salt- Loading Factor One measure of the potential for movement of dissolved solids from the agricultural lands near Manila to FGR is the difference between the amount of dissolved solids in water distributed for irrigation and the amount of dissolved solids in ground water discharging into FGR. The difference is the amount of salt accumulated in ground water that could pos-sibly be attributed to deep percolation of unconsumed irriga-tion water. This measure was termed a " salt- loading factor" by Hedlund ( 1994) and is reported in units of tons of dissolved solids per acre- foot ( acre- ft) of deep percolation. Deep per-colation is defined as water that has been applied to irrigated fields but has seeped below the root zone and is unconsumed by crops, or water that has seeped from irrigation delivery systems and is likewise not consumed or evaporated. The salt-loading factor assumes that all the ground water discharging from seeps and drains entered the aquifer from deep percola-tion of unconsumed irrigation water. A salt- loading factor for the study area was determined by subtracting the flow- weighted mean dissolved- solids con-centration in canals from the mean dissolved- solids concen-tration in seeps and drains discharging to FGR. Because the dissolved- solids concentration of water distributed in canals changes throughout the irrigation season, a flow- weighted mean dissolved- solids concentration was used as a descriptive statistic for the water applied to fields. Measurements in seeps and drains that were used in the calculation of the mean dis-solved- solids concentration were from samples collected dur-ing the non- irrigation period, November to April, when nearly all the flow was from ground- water discharge. Characterization of Dissolved Solids in Water Resources Occurrence and Distribution of Dissolved Solids The major- ion composition of study area waters var-ies substantially, with much of the surface inflow to the area being calcium bicarbonate type water ( fig. 5, group A) and most of the surface outflow being calcium sulfate type water ( fig. 5, group B). Water imported to the Manila agricultural area canal system in Sheep Creek Canal is generally calcium bicarbonate type water; however, the water imported through Peoples Canal varies from calcium bicarbonate type water early in the irrigation season when snowmelt is a substan-tial component of flow, to calcium magnesium sulfate type water later in the irrigation season when irrigation return and ground- water discharge in upstream basins of Henrys Fork are the dominant flow components. Water discharged from drains and seeps near the FGR shoreline is generally more mineralized than water imported to the study area by the canal system and is probably derived primarily from irrigation return flow. Deep percolation of irrigation water applied in excess of crop consumptive use results in dissolution of salts from soils derived from the Mancos Shale underlying Lucerne Valley. Sulfate is the predominant anion in water from most of the drains and seeps discharging to FGR from the study area ( table 5, fig. 5). Cations in water from these drains and seeps are predominantly calcium, magnesium, and sodium. Water discharging from South Valley to FGR is generally less mineralized than that discharging from Lucerne Valley and is more of a mixed type. The difference in water types discharg-ing from South Valley and Lucerne Valley is probably a result of the difference in underlying geologic units and soil types. Although the dissolved- solids concentration in water samples collected at the mouth of Henrys Fork was higher than that in water samples collected in the upper part of the valley at the Peoples Canal diversion, the relative major- ion composition of the water was similar. Antelope Wash, at site AW- 1, had the largest relative amount of sulfate of any water sampled in the study area. Discharge, dissolved- solids concentration, and relative composition of major ions in the water at the mouth of Antelope Wash were fairly stable during the study period, probably because of the influence of numerous springs in this subbasin. In the study area, concentrations of dissolved solids ( measured or estimated from specific- conductance measure-ments) ranged from 35 to 7,410 mg/ L ( tables 1 and 2, fig. 6). The dilute water diverted into Sheep Creek Canal transports a relatively small amount of dissolved solids into the study area; about 13 tons/ d at peak discharge. Concentrations of dissolved solids in Sheep Creek Canal ( at site SCC- 1) were generally less than 100 mg/ L during periods when water was being diverted into the canal from Long Park Reservoir ( fig. 1). Two measurements of specific conductance were made in Sheep Creek Canal ( at site SCC- 1) when all flow was from seepage in the vicinity of site SCC- 1. The dissolved- solids concentra-tion based on specific conductance in the canal at the time of these measurements was 770 and 1,390 mg/ L; however, the discharge associated with both measurements was less than 0.3 ft3/ s. Water diverted into Peoples Canal ( at site PC- 1) trans-ports a substantial amount of salt into the agricultural lands near Manila, as much as 109 tons/ d. Concentrations of dis-solved solids in water diverted from Henrys Fork into Peoples Canal ( at site PC- 1) ranged from 265 to 1,210 mg/ L. The dissolved- solids concentration at the mouth of Birch Spring Draw ( site BSD- 2) varied from 1,550 to 5,940 mg/ L. The higher concentrations occurred during base flow when Characterization of Dissolved Solids in Water Resources 11 ground water was the principal component of flow; lower concentrations were the result of more dilute canal tailwa-ter making up a substantial component of flow. Calculated dissolved- solids loads discharging from Birch Spring Draw ( at site BSD- 1) were as much as 157 tons/ d. Calculations of the dissolved- solids load in Birch Spring Draw show that on average the dissolved- solids load increases about 32 percent from site BSD- 1 to site BSD- 2. Field observations indicate that there is little surface inflow but substantial ground- water discharge to Birch Spring Draw in the reach between BSD- 1 and BSD- 2. Water samples from all measured drains discharging to Henrys Fork or FGR had dissolved- solids concentrations rang-ing from 555 to 7,410 mg/ L ( fig. 6). The dissolved- solids load in these drains at the time of sample collection ranged from less than 0.1 ton/ d to 113 tons/ d. Seeps that were measured near the FGR shoreline generally discharged less than 0.1 ft3/ s and had concentrations of dissolved solids ranging from 2,790 to 5,950 mg/ L. The dissolved- solids load discharging from individual seeps was generally less than 0.5 ton/ d. Discharge of Dissolved Solids into Flaming Gorge Reservoir The dissolved- solids load discharging to FGR from seeps and drains in the study area ranged from 157 tons/ d at Birch Spring Draw to less than 0.1 ton/ d at several seeps. During the study period, the water- surface altitude of FGR rose from 6,009 ft to 6,026 ft ( Bureau of Reclamation, written com-mun., 2005); the water- surface altitude when the reservoir has a full pool is 6,040 ft. The unusually low water- surface altitude of FGR during most of the study period made observa-tions of seeps on the reservoir shoreline below the full- pool altitude possible. The dissolved- solids load discharging from seeps that were visited was generally less than 0.5 ton/ d. The dissolved- solids load discharging into FGR from Henrys Fork ranged from 18 to 215 tons/ d; however, no loads were determined for the period of snowmelt runoff when dissolved-solid loads would be much higher, but generally from sources outside the study area. The most substantial source of dissolved solids discharg-ing from the study area to FGR was Birch Spring Draw. The dissolved- solids load at site BSD- 2, at the mouth of Birch Spring Draw, ranged from 29.5 to 113 tons/ d with a mean of 65 tons/ d ( table 1). Loads discharged from Birch Springs Draw were more variable than those at other sites ( standard deviation equals 30 tons/ d), probably because of the numerous irrigation diversions affecting flow in the drain. The second most substantial source of dissolved solids was Antelope Wash. Flow components in this drain include discharge from numerous springs and return flow from irrigation in Antelope Hollow. Dissolved- solid loads near the mouth of Antelope Wash ( site AW- 1) ranged from 15.2 to 45.8 tons/ d. Dissolved- Table 5. Relative percentage of major ions in selected water samples collected at water- quality monitoring sites near Manila, Utah [<, less than] Site identifier ( see table 1) Site type Date of sample collec-tion Dissolved-solids concentration, in milliequiva-lents per liter Ion concentration as percentage of dissolved- solids concentration, in milliequivalents per liter ( from sum of constituents) Calcium Magne-sium Sodium Potas-sium Chloride Fluoride Bicar-bonate Sulfate SCC- 1 canal 08/ 10/ 04 1.3 30 11 4 1 1 < 1 41 11 PC- 1 canal 06/ 01/ 05 8.1 29 16 5 1 1 < 1 30 17 PC- 1 canal 09/ 14/ 04 35.9 22 21 7 1 1 < 1 11 37 HFK- 3 stream 09/ 14/ 04 43.8 24 18 8 1 1 < 1 11 36 BSD- 2 drain 09/ 15/ 04 66.7 18 16 15 < 1 4 < 1 9 37 PC- 2 drain 09/ 16/ 04 53.4 25 15 10 < 1 2 < 1 9 38 SV- 2 drain 09/ 16/ 04 24.7 16 17 16 1 3 < 1 24 23 DRN- 1 drain 06/ 29/ 04 61.3 22 17 12 1 2 < 1 11 35 DRN- 1a drain 06/ 01/ 05 110 15 17 19 < 1 4 < 1 6 39 DRN- 2 drain 09/ 15/ 04 86.3 21 15 15 < 1 3 < 1 7 39 DRN- 4 drain 06/ 01/ 05 26.5 21 15 15 1 3 < 1 13 32 AW- 1 drain 09/ 14/ 04 118 21 22 7 1 1 < 1 5 43 CC- 1 drain 07/ 01/ 04 89.2 21 21 8 1 1 < 1 6 41 SP- 1 seep 06/ 30/ 04 110 21 12 18 < 1 3 < 1 6 38 SPG- 1 spring 06/ 01/ 05 23.3 18 25 9 < 1 3 < 1 27 18 12 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 B A Calcium plus Magnesium EXPLANATION Sheep Creek Canal Peoples Canal Streams Drains Seeps Spring Percent Sulfate plus Chloride Percent Bicarbonate Magnesium Sulfate Sodium plus Potassium Calcium Chloride + Fluoride Percent 100 80 60 40 20 0 80 100 60 40 20 0 80 100 60 40 20 0 100 80 60 40 20 0 100 80 60 40 20 0 100 80 60 40 20 0 100 80 60 40 20 0 80 100 60 40 20 0 100 80 60 40 20 0 80 100 60 40 20 0 Figure 5. Relative composition of water in the study area near Manila, Utah solid loads from Antelope Wash and South Valley ( site SV- 2) were relatively constant, having a mean of 31.9 and 12.1 tons/ d, respectively, and a standard deviation of 11 and 10 tons/ d, respectively. The dissolved- solid loads at site PC- 2 at the tail of Peoples Canal ranged from 0.6 to 96.2 tons/ d with a mean of 30 tons/ d. Dissolved- solid loads at this site were vari-able; the standard deviation being 20 tons/ d. Smaller drains, in particular those at sites DRN- 1 and DRN- 2, discharged a sub-stantial amount of dissolved solids to FGR, as much as 28.6 tons/ d. Dissolved- solid loads in these drains were extremely variable; however, they were generally greatest during June through August. A substantial amount of dissolved solids is transported into, and distributed throughout, the study area by Sheep Creek Canal and Peoples Canal. An estimate was determined of the amount of dissolved solids diverted into these canals during the 2004 irrigation season ( table 6). These estimates are based on instantaneous measurements of flow and dissolved-solids concentration and assume there was flow in Sheep Creek Canal from May 1 to September 30 and in Peoples Canal from April 1 to October 31. The total estimated dis-solved- solids load in Sheep Creek Canal and Peoples Canal was 1,330 and 13,200 tons, respectively. The water diverted into Sheep Creek Canal from Long Park Reservoir is mainly composed of snowmelt and has a low concentration of dis-solved solids. As a result, the dissolved- solids load in Sheep Creek Canal is relatively small compared to that in Peoples Canal even though Sheep Creek Canal generally has more flow. The water diverted into Peoples Canal has a substantial snowmelt component in the spring, but ground- water dis-charge and irrigation return flow, which have high dissolved-solid concentrations, are the major components in summer. Characterization of Dissolved Solids in Water Resources 13 DISCHARGE, IN CUBIC FEET PER SECOND Streams Canals Drains Seeps 13 16 128 20 30 Schematic boxplot Streams Canals Drains Seeps 60 80 100 120 140 160 13 16 128 20 x Streams Canals Drains Seeps 0 2,000 4,000 6,000 8,000 10,000 40 20 0 13 16 128 20 60 80 100 120 140 40 20 0 DISSOLVED- SOLIDS CONCENTRATION, IN MILLIGRAMS PER LITER DISSOLVED- SOLIDS LOAD, IN TONS PER DAY EXPLANATION Number of samples Upper detached Upper outside Upper adjacent 75th percentile Median 25th percentile Lower adjacent Lower outside Lower detached Figure 6. Distribution of dissolved- solids concentration and load, and discharge at water- quality monitoring sites near Manila, Utah. Hence, the water diverted from Henrys Fork through Peoples Canal is a substantial source of dissolved solids to agricultural lands in the study area. The dissolved- solids load in inflow to the study area, outflow to FGR, and at three fixed outflow- monitoring sites is listed in table 7. As previously described, these data were used to determine daily TADSLs, which were then aggregated to determine an annual TADSL. A time- series plot of daily TADSL, with a locally weighted scatter plot smooth ( LOW-ESS), shows the variation in daily TADSL as well as the seasonal changes. Substantial daily variability is evident by the scatter in data points shown on figure 7 for those periods when data were collected at the fixed outflow- monitoring sites. Linear changes are shown for those periods that daily TADSLs were estimated. Daily TADSLs were greatest during July and early August 2004, stayed relatively high through January 2005, and then declined February through early April ( fig. 7). Loads began increasing in mid- April and by June had returned to near the level noted during the previous July. Daily TADSL ranged from 72 to 241 tons/ d with a mean of 110 tons/ d. A time- series plot of the cumulative TADSL shows that dis-charge from the study area during this period was relatively constant ( fig. 8). The aggregate of the daily TADSLs calculated from equa-tion 1 for July 1, 2004, to June 30, 2005, is 40,200 tons. This aggregate value represents the measurable dissolved solids discharging from the study area, less the dissolved solids that were imported to the study area in Sheep Creek Canal and in Henrys Fork. Included in the aggregated TADSL are dissolved solids that may have been imported in atmospheric deposition, or are associated with ground water or surface runoff whose origin was something other than irrigation flow. Not included in the TADSLs are dissolved solids that may have been in ground water discharged below the surface of FGR. The aggregated TADSL should be considered an upper bound to the total dissolved- solids load that was ( 1) discharged to FGR, ( 2) from those sources that were measured, ( 3) during the stated period, and ( 4) that could be associated with agricultural activities in the study area. 14 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 The chemistry, discharge, and consistent nature of flow measured in Antelope Wash indicate that Antelope Spring, the principal source of flow in the wash, could be discharg-ing from a regional ground- water source, possibly from the Bridger aquifer. A more conservative estimate of the dissolved solids discharging to FGR that are associated with agricultural activities in the study area might be derived if the dissolved solids in base flow from Antelope Wash were not included. The mean dissolved- solids load in Antelope Wash ( at site AW- 1) during the non- irrigation period was 24.7 tons/ d. Assuming this is the mean base- flow dissolved- solids load and that it is associated with discharge from a regional ground- water source such as the Bridger aquifer, extrapolating that load to an annual basis results in an estimated annual discharge of 9,000 tons of dissolved solids from a regional source. Subtracting the 9,000 tons of dissolved solids from the aggregate TADSL results in a more conservative estimate of 31,200 tons of dis-solved solids discharging to FGR from the study area ( fig. 8). The dissolved- solids load estimates derived here were determined for the specific period July 1, 2004, through June 30, 2005. The dissolved- solids load discharging to FGR from the study area for other periods may be substantially differ- Table 6. Estimated dissolved- solids load in Sheep Creek Canal and Peoples Canal near Manila, Utah, April- October 2004 [-, no estimate] Period Estimated daily dissolved-solids load, in tons per day1 Estimated dis-solved- solids load, total for period for both canals, in tons Sheep Creek Canal Peoples Canal April - 229 870 May 10.2 229 1,220 June 212.6 109 3,650 July 9.2 86.6 2,970 August 6.3 49.7 1,740 September 5.3 78.3 2,510 October - 51 1,580 Estimated total dissolved- solids load, in tons April- October 1,330 13,200 14,500 1Estimated daily dissolved- solids load is based on a calculated instanta-neous dissolved- solids load. 2Estimated daily dissolved- solids load is based on an instantaneous dis-solved- solids load calculated for June 2005. Table 7. Dissolved- solids load at inflow, outflow, and fixed outflow- monitoring sites in the study area near Manila, Utah [ Data are from table 2 and are instantaneous measurements made in the month indicated; -, no measurement; e, estimated value] Site identifier ( see table 1) Load, in tons per day 2004 2005 June/ July August September October November January February April May/ June Dissolved- solids load at inflow sites HFK- 11 149 8.8 46.5 89.5 68.4 79.8 27.1 72.8 e203 SCC- 1 9.2 6.3 5.3 .5 0 0 0 .4 12.6 Dissolved- solids load at outflow sites BSD- 2 113 39.1 57.1 88.0 45.8 37.8 54.5 29.5 102 PC- 2 68.8 14.2 22.7 19.2 3.6 1.8 1.0 .6 32.5 SV- 2 26.7 11.2 1.3 29.9 8.3 5.2 e 7.5 2.8 2.2 HFK- 3 e100 17.6 21.8 125 108 142 64.8 113 e215 DRN- 1 15.1 1.8 .3 1.1 1.0 <. 1 1.0 e2.1 e. 5 DRN- 1a - 2.0 .8 1.2 .9 .2 .1 .3 2.1 DRN- 2 28.6 11.1 4.7 2.4 1.6 .8 .9 1.0 11.3 DRN- 3 8.8 .7 7.8 2.1 .5 <. 1 e. 1 e. 5 <. 1 DRN- 4 2.7 <. 1 .5 e2.2 .2 <. 1 <. 1 0 .8 DRN- 5 .1 <. 1 <. 1 e. 8 <. 1 0 0 0 <. 1 DRN- 8 <. 2 .1 .2 .4 .1 .2 0 0 .3 LAT- 1 - .3 3.2 e1.4 .2 0 0 0 .6 AW- 1 e37.0 41.5 33.0 45.8 45.6 29.1 25.3 19.7 15.2 SP- 1 .1 .4 .4 .5 .1 - - - .1 SP- 3 <. 1 <. 1 <. 1 .1 <. 1 - - - - SP- 4 <. 2 - <. 1 .3 - - - - - Dissolved- solids load at fixed outflow- monitoring sites BSD- 1 94.8 26.7 33.9 62.3 33.5 41.0 28.6 12.4 60.8 PC- 2 68.8 14.2 22.7 19.2 3.5 1.8 1.0 .6 32.5 SV- 1 22.2 9.6 9.4 33.0 4.9 5.0 7.5 2.4 1.3 1Values are calculated by summing dissolved- solids loads at the head of Peoples Canal and in Henrys Fork directly below the Peoples Canal diversion, then subtracting the load that was discharged to Henrys Fork from Antelope Wash ( site AW- 1). Characterization of Dissolved Solids in Water Resources 15 July Aug Sept Oct Nov Dec Jan Feb Mar April May June 0 100 200 300 2004 ESTIMATED TOTAL ADJUSTED DISSOLVED- SOLIDS LOAD, IN TONS PER DAY 2005 Figure 7. Estimated daily total adjusted dissolved- solids load discharged from the study area near Manila, Utah, July 1, 2004, through June 30, 2005. Points are daily total adjusted dissolved- solids load and line is locally weighted scatter plot smooth ( LOWESS). ent depending upon dispersement of irrigation water, annual precipitation, and other climatic factors. Precipitation in the study area was slightly greater than normal during this period ( 9.5 in., Western Regional Climate Center, 2005); however, precipitation during most of the irrigation season, May through September, was near or less than normal ( table 8). Precipitation in October 2004 was substantially greater than normal and may have helped sustain the amount of dissolved solids discharging to FGR through February 2005. Flow in Peoples Canal is dependent upon flow in Henrys Fork and can be limited in years with less- than- normal precipitation. Flow in Peoples Canal may have been limited by less- than- normal streamflow in Henrys Fork during July- October 2004 and June 2005 ( table 8). Discharge measurements from July 1, 2004, through June 30, 2005 ( table 2), indicate that flow in the Sheep Creek Canal system was probably adequate for normal opera-tion. On the basis of precipitation, canal flow, and streamflow in the study area from July 1, 2004, through June 30, 2005, the dissolved- solids load discharging to FGR during this period is likely normal to slightly less than normal. Salt- Loading Factor The flow- weighted mean concentration of dissolved solids distributed to Lucerne Valley by Sheep Creek and Peoples Canals was 268 mg/ L. This concentration is based on measurements of discharge and specific conductance or dissolved solids at the head of the canals during the irrigation season ( table 9). The concentration of dissolved solids in water samples collected from seeps and drains from November 2004 through April 2005 is representative of ground- water discharge that is assumed to result from deep percolation of unconsumed irrigation water. The mean dissolved- solids concentration in water collected from seeps and drains in Lucerne Valley during this period was 3,940 mg/ L. The increase in dissolved-solids concentration, as a result of processes occurring along the flow paths followed by deep percolation, is 3,670 mg/ L or about 5 tons of dissolved solids per acre- ft of deep percolation in Lucerne Valley. Because the underlying geology and soils in South Valley are less saline than those in Lucerne Valley ( fig. 2), the salt- loading factor associated with deep percola- 16 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 tion in South Valley is much lower than in Lucerne Valley. The flow- weighted mean concentration of dissolved solids in applied irrigation water was 39 mg/ L and the mean dissolved-solids concentration in water collected near the mouth of the South Valley drain during this period was 1,660 mg/ L. The increase in dissolved solids, as a result of processes occurring along flow paths followed by deep percolation in South Valley, is 1,620 mg/ L or 2.2 tons per acre- ft. A water/ salt budget that takes into consideration such factors as canal inflow and seepage, water consumption by crops and phreatophytes, tailwater runoff, and evaporation is a frequently applied method of determining the amount of dissolved- solids discharge associated with agricultural activi-ties in an area. Determining a water/ salt budget is beyond the scope of this report, but the salt- loading factor determined here should be useful for these calculations. Differentiation of Dissolved- Solids Sources Naturally occurring isotopes of strontium and boron in the water are a useful tool for differentiating salinity sources. The delta strontium- 87 ( 􀄯 87Sr) value is a measure of the isotopic ratio of naturally occurring 87Sr and 86Sr. Unlike other isotopes, Sr isotopes do not measurably fractionate in nature. Instead, 􀄯 87Sr values give insight into water- rock interaction processes. In similar lithologies, a water sample representing a shorter hydrologic flow path ( irrigation return flow) will likely have a different isotopic signal than a water sample represent-ing a longer hydrologic flow path ( regional aquifer salinity source; Barbieri and Morotti, 2003). For example, in research conducted by Nimz and others ( 1992), shallow ground water contained positive 􀄯 87Sr values as a result of short- term water-rock interaction, and the deeper regional ground water con-tained negative 􀄯 87Sr values as a result of increased residence time for interaction with more chemically resistant mineral phases. Strontium isotopes have been used successfully to Daily instantaneous specific conductance and gage height Linear interpolation of daily load Instantaneous specific conductance and gage height, daily instantaneous specific conductance and gage height, linear interpolation of daily load 0 10,000 20,000 30,000 40,000 60,000 TOTAL ADJUSTED DISSOLVED- SOLIDS LOAD, IN TONS 50,000 2004 2005 July Aug Sept Oct Nov Dec Jan Feb Mar April May June Total adjusted dissolved- solids load Total adjusted dissolved- solids load less the dissolved- solids load in base flow from Antelope Wash Data source- Color of point indicates type of data or method used in derivation of daily load 40,200 tons 31,200 tons Figure 8. Cumulative total adjusted dissolved- solids load discharged from the study area near Manila, Utah, July 1, 2004, through June 30, 2005. Symbol indicates type of data included in derivation of the daily total adjusted dissolved- solids load estimate. Characterization of Dissolved Solids in Water Resources 17 Table 8. Precipitation at Manila, Utah, and streamflow in Henrys Fork near Manila, Utah, July 2004 through June 2005 [ ft3/ s, cubic feet per second] Month Precipitation at Manila, Utah1 Streamflow in Henrys Fork near Manila, Utah2 Monthly total, in inches Departure from average3, in inches Monthly mean, in ft3/ s Departure from aver-age monthly mean4, in ft3/ s 2004 Jul 0.81 - 0.15 15.9 - 74.3 Aug .93 .04 7.2 - 41.7 Sep 1.05 .18 5.3 - 27.7 Oct 2.45 1.62 31 - 14.4 Nov .76 .23 65.1 10.4 Dec .1 -. 22 76.3 28.3 2005 Jan .35 .03 73.2 30.2 Feb .08 -. 28 55.4 9.2 Mar .35 -. 28 56.6 - 12.4 Apr .87 -. 15 31.2 - 50.6 May 1.04 -. 24 154 3 Jun .72 -. 37 168 - 98 1Data from Western Regional Climate Center ( 2005). 2Data from Watson and others ( 2005 and 2006). 3Average of monthly data, 1952- 2005. 4Average of monthly data, 1929- 2005. differentiate salinity sources in water from southeastern Utah ( Spangler and others, 1996; Naftz and others, 1997). The second isotopic tool of interest for differentiating salinity sources is boron. The delta boron- 11 ( 􀄯 11B) value is a measure of the isotopic ratio of naturally occurring 11B and 10B. Natural water has a wide range of 􀄯 11B values ranging from - 16 to + 59 permil ( Vengosh and others, 1994). Examples of values for several end- member waters include: - 0.9 to + 10.2 permil for non- marine sodium borate minerals; + 2 to + 12.9 permil for treated sewage effluent; + 30 permil for uncontami-nated ground water; - 2.0 to + 0.7 permil for nitrogen fertilizers; + 7.2 to + 11.2 permil for manure- based fertilizers; and + 39 permil for seawater ( Vengosh and others, 1994; Komor, 1997; Barth, 1998). Because of the application of fertilizers on irri-gated lands, as well as other processes, it is likely that water from irrigation- return flow would have a distinctly different isotopic composition than other water sources in a particular area. The combination of both 􀄯 11B and 􀄯 87Sr values in water can be a powerful dual isotopic source- identification technique that may differentiate salinity sources better than the use of each isotope independently. Water samples were collected from selected sites in the study area and analyzed for boron, strontium, 􀄯 11B, and 􀄯 87Sr ( table 10). Some water samples were collected from what might be considered an end member in a mixing model. For example, the water samples from sites SCC- 1 and PC- 1 represent the imported irrigation water. The water sample from spring SPG- 1 ( fig. 1) represents regional ground water that does not have an irrigation return- flow component. Water samples from drains don't likely represent an end member but a mixture of flow components that includes irrigation return flow and possibly regional ground water. Among these sample types there was a wide range in concentrations of strontium and boron as well as in the isotope ratios. The variation of 􀄯 87Sr with strontium concentration indi-cates some general patterns that help to define a conceptual model of the processes affecting the concentration of stron-tium and the 􀄯 87Sr isotopic ratio in study- area waters ( fig. 9). Water samples collected from canals ( from sites SCC- 1 and PC- 1) had relatively low concentrations of strontium ( less than 3,000 􀁐 g/ L) and more positive ( heavier) 􀄯 87Sr isotopic ratios ( greater than 1 permil). Water samples collected from drains had strontium concentrations ranging from 3,350 to 7,380 􀁐 g/ L and lighter 􀄯 87Sr isotopic ratios. As irrigation water from the canals, which may be applied to fields in excess of crop consumptive needs, percolates through soils derived from the Mancos Shale, the 􀄯 87Sr isotopic ratio of that water approaches one that is typical of deep percolation from irrigation on Mancos Shale. In this case, that value is in the range of 0.21 to 0.69 permil. At the same time, strontium is being leached from Mancos Shale and concentrated by evapotranspiration so that the concentration of strontium in water samples collected from drains is much higher relative to that in water samples collected from canals. The water sample collected from site SPG- 1, a small spring upgradient of the agricultural lands, had a negative 􀄯 87Sr isotope ratio and a relatively low strontium concentration. The strontium concentration and 􀄯 87Sr isotope ratio data collected during this study are insufficient to develop a complete mixing model; however, the distribution of the data in figure 9 indicates that there probably is no strong regional ground- water component affecting these constituents in water samples collected from drains. Boron stable- isotope ratios do not vary systematically as do strontium ratios. Instead, values of 􀄯 11B may more likely represent sources of the boron. Few distinctions in boron isotope values from the study area seem clear relative to reported ranges in the literature. However, the value of 􀄯 11B in the sample collected from Antelope Wash falls in the range reported for hydrothermal fluids ( fig. 10; see Vengosh and oth-ers, 1994; Komor, 1997; Barth, 1998). The boron concentra-tion and 􀄯 11B value for the water sample from Antelope Wash being distinctly different from water samples from other sites is further evidence that water in Antelope Wash may have a substantial component of regional ground- water flow from the Bridger aquifer. The variation in strontium and boron concentrations and isotope ratios provide a means to distinguish end members within the study area. The isotope ratios potentially provide some information that may lead to distinguishing a regional component of mixing from irrigation return flow; however, the 18 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 Table 9. Discharge and water- quality characteristics for selected water- quality monitoring sites used in the calculation of salt- loading factors for the study area near Manila, Utah - Continued Site identifier ( see table 1) Site type Date Discharge, in ft3/ s Dissolved-solids concentration from residue on evapora-tion at 180° C, in mg/ L Lucerne Valley inflow SCC- 1 canal 07/ 01/ 04 97 35 SCC- 1 canal 08/ 10/ 04 60 39 SCC- 1 canal 09/ 14/ 04 34 58 SCC- 1 canal 06/ 01/ 05 126 37 PC- 1 canal 06/ 29/ 04 50 808 PC- 1 canal 08/ 10/ 04 23 802 PC- 1 canal 09/ 14/ 04 24 1,210 PC- 1 canal 06/ 01/ 05 41 265 Lucerne Valley outflow BSD- 2 drain 11/ 23/ 04 3.5 4,850 BSD- 2 drain 01/ 20/ 05 2.9 4,840 BSD- 2 drain 02/ 24/ 05 3.4 5,940 BSD- 2 drain 04/ 06/ 05 2.2 4,970 CC- 1 drain 01/ 19/ 05 .6 4,070 CC- 1 drain 04/ 05/ 05 .2 3,910 DRN- 1 drain 11/ 23/ 04 .1 3,740 DRN- 1 drain 01/ 19/ 05 <. 1 4,060 DRN- 1 drain 04/ 05/ 05 .2 3,890 DRN- 1A drain 11/ 23/ 04 .1 4,680 DRN- 1A drain 01/ 19/ 05 <. 1 4,200 DRN- 1A drain 04/ 05/ 05 <. 1 6,320 DRN- 2 drain 11/ 23/ 04 .1 4,780 DRN- 2 drain 01/ 19/ 05 .1 4,930 DRN- 2 drain 02/ 25/ 05 .1 5,000 DRN- 2 drain 04/ 06/ 05 .1 5,300 DRN- 3 drain 11/ 23/ 04 .1 3,510 DRN- 3 drain 01/ 20/ 05 <. 1 3,320 DRN- 3 drain 02/ 24/ 05 <. 1 3,340 DRN- 3 drain 04/ 06/ 05 .1 3,360 DRN- 4 drain 11/ 23/ 04 <. 1 3,090 DRN- 4 drain 01/ 20/ 05 <. 1 2,860 DRN- 4 drain 02/ 24/ 05 <. 1 1,760 DRN- 5 drain 11/ 23/ 04 <. 1 2,840 Table 9. Discharge and water- quality characteristics for selected water- quality monitoring sites used in the calculation of salt- load-ing factors for the study area near Manila, Utah [ ft3/ s, cubic feet per second; ° C, degrees Celsius; mg/ L, milligrams per liter; <, less than; -, no data] Table 9. Discharge and water- quality characteristics for selected water- quality monitoring sites used in the calculation of salt- loading factors for the study area near Manila, Utah - Continued Site identifier ( see table 1) Site type Date Discharge, in ft3/ s Dissolved-solids concentration from residue on evapora-tion at 180° C, in mg/ L Lucerne Valley outflow- Continued PC- 2 drain 11/ 23/ 04 .5 2,800 PC- 2 drain 01/ 20/ 05 .3 2,740 PC- 2 drain 02/ 24/ 05 .1 2,840 PC- 2 drain 04/ 06/ 05 .1 2,880 SP- 3 seep 11/ 23/ 04 <. 1 3,660 SP- 1 seep 11/ 23/ 04 <. 1 3,860 South Valley inflow SCC- 1 canal 05/ 27/ 04 - 38 SCC- 1 canal 07/ 01/ 04 - 35 SCC- 1 canal 08/ 10/ 04 - 39 SCC- 1 canal 09/ 14/ 04 - 58 SCC- 1 canal 06/ 01/ 05 - 37 South Valley outflow SV- 2 drain 11/ 24/ 04 2.1 1,460 SV- 2 drain 01/ 20/ 05 1.1 1,740 SV- 1 drain 02/ 24/ 05 1.4 1,980 SV- 2 drain 04/ 06/ 05 .7 1,450 Characterization of Dissolved Solids in Water Resources 19 Table 10. Site identification and characteristics, chemical concentration, isotope ratio, and specific conductance of samples collected from selected water- quality monitoring sites near Manila, Utah [ μg/ L, micrograms per liter; permil, per thousand; ng/ L, nanograms per liter; μS/ cm, microsiemens per centimeter; ° C, degrees Celsius] Site identifier ( see table 1) Site type Date of sample Description of major flow components Strontium concentra-tion, in μg/ L 􀁇 87Sr, in permil Boron concen-tration, in ng/ L 􀁇 11B, in permil Specific conductance, in μS/ cm at 25° C AW- 1 drain 08/ 10/ 04 Ground- water and surface- water discharge principally derived from Antelope Spring and irrigation return flow 5,960 0.69 890 - 11.0 3,640 PC- 1 canal 08/ 10/ 04 Surface runoff derived from snowmelt and ground- water discharge 2,450 1.16 170 - 1.62 1,110 SPG- 1 spring 11/ 24/ 04 Ground- water discharge principally derived from snowmelt and precipitation recharge 1,250 - 1.24 286 1.25 796 HFK- 3 drain 08/ 10/ 04 Surface runoff derived from ground- water discharge 3,020 1.68 320 4.00 1,680 BSD- 2 drain 08/ 11/ 04 Ground- water and surface- water discharge principally derived from deep percolation of irrigation and irrigation tailwater 3,350 .49 440 4.50 2,340 DRN- 4 drain 08/ 11/ 04 Surface runoff derived from snowmelt and ground- water discharge 5,890 .21 77 8.37 2,960 SCC- 1 canal 08/ 10/ 04 Surface runoff derived from snowmelt 55 3.31 11 10.6 66 DRN- 1a drain 11/ 23/ 04 Ground- water discharge and surface water which may have a treated sewage component 7,380 .55 65 20.7 3,100 20 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 􀁉 87Sr, IN PERMIL DRN- 1a SCC- 1 DRN- 4 HFK- 3 SPG- 1 PC- 1 BSD- 2 AW- 1 Site identifier, refer to table 1 for site designation - 2 - 1 0 1 2 3 4 0 1,000 2,000 3,000 4,000 5,000 6,000 7,000 8,000 STRONTIUM CONCENTRATION, IN MICROGRAMS PER LITER 􀁉 11B, IN PERMIL BORON CONCENTRATION, IN NANOGRAMS PER LITER DRN- 1a SCC- 1 DRN- 4 HFK- 3 SPG- 1 PC- 1 BSD- 2 AW- 1 Site identifier, refer to table 1 for site designation - 15 - 10 - 5 0 5 10 15 20 0 100 200 300 400 500 600 700 800 900 1,000 25 Figure 9. Variation of 􀁇 87Sr with strontium concentration in samples collected from selected sites near Manila, Utah. Figure 10. Variation of 􀁇 11B with boron concentration in samples collected from selected sites near Manila, Utah Characterization of Dissolved Solids in Water Resources 21 results from isotope data collected during this study are incon-clusive. Sampling spatially along drains as well as additional end- member sampling, such as water from shallow and deep wells, Antelope Springs, the Manila sewage- treatment ponds, and Henrys Fork upstream of the Antelope Wash inflow, could provide additional data that would help quantify the dissolved solids contributed to FGR from these components of flow. Summary Water users in the Upper Colorado River Basin consume water from the Colorado River and its tributaries, reducing the amount of water in the river that is suitable for domestic use and crop irrigation. At the same time, the application of water to agricultural land within the basin, in excess of crop needs, can increase the transport of dissolved solids to the river. The U. S. Department of Agriculture ( USDA) is a partner in the Colorado River Salinity Control Program, directing offices of the Natural Resources Conservation Service ( NRCS) in the Upper Colorado River Basin to make reductions, where pos-sible, in the dissolved- solids load discharging to the Colorado River from agricultural lands. The agricultural lands near Manila, Utah, have been identified by the NRCS as areas con-tributing dissolved solids to Flaming Gorge Reservoir ( FGR), in which the Green River - a tributary of the Colorado River - is impounded. This report documents the methods used in, and results of, an evaluation to determine the amount of dis-solved solids contributed to FGR from Lucerne Valley, South Valley, Antelope Hollow, and a portion of Henrys Fork near Manila, Utah. The major- ion composition of study area waters varies substantially. For example, much of the surface inflow to the study area is calcium bicarbonate type water and most of the outflow is calcium sulfate type water. Water discharged from drains and seeps near the FGR shoreline is generally more mineralized than water imported to the study area by Peoples and Sheep Creek Canals. In the study area, concentrations of dissolved solids ranged from 35 to 7,410 mg/ L. The dis-solved- solids load in seeps and drains in the study area, which discharge to FGR, ranged from less than 0.1 to 157 tons/ d. The most substantial source of dissolved- solids discharging from the study area to FGR was Birch Spring Draw. The mean dis-solved- solids load near the mouth of Birch Spring Draw was 65 tons/ d. The estimated annual dissolved- solids load imported to the study area by Sheep Creek and Peoples Canals is 1,330 and 13,200 tons, respectively. The daily dissolved- solids load discharging to FGR from the study area, less the amount of dissolved solids imported by canals, for July 1, 2004, to June 30, 2005, ranged from 72 to 241 tons/ d with a mean of 110 tons/ d. The estimated annual dissolved- solids load discharging to FGR from the study area, less the amount of dissolved sol-ids imported by canals, for the same period, was 40,200 tons; however, of this 40,200 tons of dissolved solids, about 9,000 tons discharging from Antelope Wash may be attributed to a regional source that is not associated with agricultural activi-ties in the study area. The difference in concentration between dissolved solids in water applied to fields in the study area for irrigation and ground water discharging to FGR is termed the dissolved- sol-ids ( salt) loading factor. This value is useful for estimating the amount of dissolved solids discharged to FGR that is associ-ated with each acre- ft of deep percolation. The salt- loading factor is 3,670 mg/ L or about 5.0 tons of dissolved solids per acre- ft of deep percolation in Lucerne Valley and 1,620 mg/ L or 2.2 tons per acre- ft in South Valley. Water samples from selected sites in the Manila area were collected and analyzed for boron, 􀄯 11B, strontium, and 􀄯 87Sr. Water samples collected from canals had relatively low con-centrations of strontium ( less than 3,000 􀁐 g/ L) and more posi-tive 􀄯 87Sr isotopic ratios ( greater than 1 permil). Water samples collected from drains had strontium concentrations ranging from 3,350 to 7,380 􀁐 g/ L, and lighter 􀄯 87Sr isotopic ratios. The water sample from site SPG- 1, a small spring upgradient of the agricultural lands, had a negative 􀄯 87Sr isotope ratio and a relatively low strontium concentration. As irrigation water from the canals, which may be applied to fields in excess of crop consumptive needs, perco-lates through soils derived from Mancos Shale, it appears the 􀄯 87Sr isotopic ratio of that water approaches one that is typical of deep percolation from irrigation on Mancos Shale ( 0.21 to 0.69 permil). At the same time, strontium is being leached from Mancos Shale and concentrated by evapotranspiration so that the concentration of strontium in water samples collected from drains is much higher relative to that in water samples collected from canals. The boron concentration and 􀄯 11B value for the water sample collected from Antelope Wash was distinctly different from water samples collected from other sites. This provides some evidence that water in Antelope Wash may have a sub-stantial component of regional ground- water flow. References Cited Barbieri, M., and Morotti, M., 2003, Hydrogeochemistry and strontium isotopes of spring and mineral waters from Monte Vulture volcano, Italy: Applied Geochemistry, v. 18, p. 117- 125. Barth, S., 1998, Application of boron isotopes for tracing sources of anthropogenic contamination in groundwater: Water Resources, v. 32, p. 685- 690. Buchanan, T. J., and Somers, W. P., 1969, Discharge measure-ments at gaging stations: U. S. Geological Survey Tech-niques of Water- Resources Investigations, book 3, chap. A8, 65 p. 22 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 Fishman, M. J., and Friedman, L. C., 1989, Methods for determination of inorganic substances in water and fluvial sediments: U. S. Geological Survey Techniques of Water- Resources Investigations, book 5, chap. A1, 545 p. Hedlund, J. D., 1994, Salt primer - Water and salt budgets: Portland, Oregon, Soil Conservation Service, West National Technical Center, 60 p. Hemphill, L. S., Water atlas of Utah, Class A pan evaporation for Utah, May - October, 1956- 1970, accessed May 2005 at http:// www. engineering. usu. edu/ uwrl/ atlas/ ch3/ index. html Hintze, L. F., Willis, G. C., Laes, D. Y. M., Sprinkel, D. A., and Brown, K. D., 2000, Digital geologic map of Utah: Utah Geological Survey Map 179DM, scale 1: 500,000 Johnson, M. W., Parson, R. E Stebbins, D. A, 1998, A history of Daggett County: A modern frontier: Salt Lake City, Utah, Utah State Historical Society [ and] Daggett County Com-mission, 315 p. Kennedy, E. J., 1983, Computation of continuous records of streamflow: U. S. Geological Survey Techniques of Water- Resources Investigations, book 3, chap. A13, 53 p. Koenig, K. J., 1960, Bridger Formation in the Bridger Basin, Wyoming, in McGookey, D. P., and Miller, D. N., Jr., eds., Overthrust belt of southwestern Wyoming and adjacent areas: Wyoming Geological Association, 15th Annual Field Conference Guidebook, p. 195- 209. Komor, S. C., 1997, Boron contents and isotopic composition of hog manure, selected fertilizers, and water in Minnesota: Journal of Environmental Quality, v. 26, p. 1212- 1222. Love, J. D., and Christiansen, A. C., 1985, Geologic map of Wyoming: U. S. Geological Survey Map, scale 1: 500,000. Mason, J. P., and Miller, K. A., 2004, Water resources of Sweet-water County, Wyoming: U. S. Geological Survey Scientific Investigations Report 2004- 5214, 188 p. Naftz, D. L., Peterman, Z. E., and Spangler, L. E., 1997, Using 􀁇 87Sr values to identify sources of salinity to a freshwater aquifer, Greater Aneth Oil Field, Utah, U. S. A.: Chemical Geology, v. 141, p. 195- 209. Nimz, G. J., Smith, D. K., Caffee, M. W., Finkel, R. C., Hudson, G. B., Borchers, J. W., and Nimz, K. P., 1992, Isotope char-acterization of hydrologic structure and chemical interac-tion between groundwater and granitic rock in the Wawona Basin, Yosemite National Park: Eos, Transaction, American Geophysical Union, v. 73, p. 170. Radtke, D. B., Davis, J. B., and Wilde, F. D, eds., August 2005, Specific electrical conductance field measurement: U. S. Geological Survey Techniques of Water- Resources Inves-tigations, book 9, chap. A6.3, accessed January 2006 at http:// water. usgs. gov/ owq/ FieldManual/ Chapter6/ 6.3_ con-tents. html Schwarz, G. E., and Alexander, R. B, 1995, State Soil Geo-graphic ( STATSGO) data base for the conterminous United States: U. S. Geological Survey Open- File Report 95- 449, digital map, scale 1: 250,000, online version at http:// water. usgs. gov/ lookup/ getspatial? ussoils Spangler, L. E., Naftz, D. L., and Peterman, Z. E., 1996, Hydrol-ogy, chemical quality, and characterization of salinity in the Navajo aquifer in and near the Greater Aneth Oil Field, San Juan County, Utah: U. S. Geological Survey Water- Resources Investigations Report 96- 4155, 90 p. U. S. Department of the Interior, 2003, Quality of water- Col-orado River Basin: Bureau of Reclamation, Upper Colorado Region, Salt Lake City, Utah, Progress report no. 21, 83 p. plus appendix. U. S. Geological Survey, 2006, National Land Cover Dataset, accessed January 2006 at http:// landcover. usgs. gov/ natl-landcover. php Vengosh, A., Heumann, K. G., Juraske, S., and Kasher, R., 1994, Boron isotope application for tracing sources of contamination in groundwater: Environmental Science and Technology, v. 28, p. 1968- 1974. Watson, K. R., Woodruff, R. E., Laidlaw, G. A., Clark, M. L., and Miller, K. A., 2005, Water resources data, Wyoming, water year 2004; Volume 1. Surface water: U. S. Geological Survey Water- Data Report WY- 04- 1, 591 p. Watson, K. R., Woodruff, R. E., Laidlaw, G. A., Clark, M. L., and Miller, K. A., 2006, Water resources data, Wyoming, water year 2005; Volume 1. Surface water: U. S. Geological Survey Water- Data Report WY- 05- 1, 592 p. Webb, W. E., Radtke, D. B., and Iwatsubo, R. T., September 1999, Surface- water sampling: collection methods at flow-ing- water and still- water sites: U. S. Geological Survey Techniques of Water- Resources Investigations, book 9, chap. A4.1, accessed January 2006 at http:// water. usgs. gov/ owq/ FieldManual/ chapter4/ html/ 4.1_ contents. html Western Regional Climate Center, 2005, Period of record monthly climate summary, Manila, Utah: accessed Octo-ber 14, 2005, at http:// www. wrcc. dri. edu/ cgi- bin/ cliMAIN. pl? utmani References Cited 23 Table 2. Instantaneous discharge and properties of water samples collected from water- quality monitoring sites near Manila, Utah - Continued Site identifier ( see table 1) Site type Sample date Sample time Discharge, instanta-neous ( ft3/ s) pH, water, unfiltered, laboratory ( standard units) Specific conductance, water, unfiltered, laboratory ( μS/ cm at 25° C) Specific conductance, water, field, unfiltered ( μS/ cm at 25° C) Temper-ature, water (° C) HFK- 3 stream 08/ 10/ 04 1700 4.3 - - 1,680 24.3 09/ 14/ 04 1840 5.5 7.9 1,730 1,850 12.5 10/ 26/ 04 1750 46 - - 1,230 6.9 11/ 22/ 04 1635 42 - - 1,240 - 01/ 19/ 05 1530 68 - - 945 .5 02/ 25/ 05 0900 30 - - 977 .1 04/ 05/ 05 1710 58 - - 880 11.1 06/ 01/ 05 1250 e219 - - 444 12.9 HFK- 1 stream 09/ 14/ 04 1600 e. 4 - - 1,540 15.9 10/ 26/ 04 1520 40 - - 1,070 10.1 11/ 22/ 04 1520 47 - - 1,190 1.5 01/ 19/ 05 1240 64 - - 864 - 02/ 25/ 05 0710 29 - - 918 2.3 04/ 05/ 05 1400 57 - - 824 8.8 SCC- 1 canal 05/ 27/ 04 1300 e100 - - 62 10.9 07/ 01/ 04 1225 97 7.5 64 60 13.5 08/ 10/ 04 1125 60 7.2 63 66 15.8 09/ 14/ 04 1250 34 - - 90 15.0 10/ 26/ 04 1140 .22 - - 1,070 4.6 04/ 05/ 05 1130 e. 1 - - 1,930 7.7 06/ 01/ 05 1750 126 - - 61 9.1 PC- 1 canal 06/ 29/ 04 1400 50 8 1,080 1,130 17.6 07/ 22/ 04 0900 40 - - 1,100 16.5 08/ 10/ 04 1330 23 - - 1,110 21.0 09/ 14/ 04 1430 24 8 1,480 1,540 15.5 10/ 26/ 04 1435 24 - - 1,080 10.0 11/ 22/ 04 1445 1.6 - - 1,210 1.4 01/ 19/ 05 1315 .01 - - 864 - 06/ 01/ 05 0840 41 7.9 362 390 11.4 DRN- 1 drain 06/ 29/ 04 1635 2.7 8.1 2,290 2,400 17.6 08/ 11/ 04 1650 .25 - - 2,910 20.5 09/ 15/ 04 1800 .03 - - 3,870 12.5 10/ 27/ 04 1535 .11 - - 4,340 9.7 11/ 23/ 04 1500 .1 - - 3,800 .3 01/ 19/ 05 1610 <. 01 - - 4,320 .3 Table 2. Instantaneous discharge and properties of water samples collected from water- quality monitoring sites near Manila, Utah [ ft3/ s, cubic feet per second; μS/ cm, microsiemens per centimeter; ° C, degrees Celsius; mg/ L, milligrams per liter; ROE, residue on evaporation at 180 ° C; -, no data; e, estimated; <, less than] 24 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 Table 2. Instantaneous discharge and properties of water samples collected from water- quality monitoring sites near Manila, Utah- Continued Site identifier ( see table 1) Hardness, water ( mg/ L as CaCO 3 ) Alkalinity, water, filtered, incremental titration, lab ( mg/ L) Dissolved-solids concentration, sum of constituents, water, filtered ( mg/ L) Dissolved-solids concentration, ROE, water, filtered ( mg/ L) ROE/ Specific-conductance ratio Dissolved-solids concentration from ROE/ Specific-conductance ratio ( mg/ L) Dissolved-solids load ( tons per day) HFK- 3 - - - 1,520 0.90 1,520 17.6 930 242 1,360 1,470 .79 1,470 21.8 - - - - 1.82 1,010 125 - - - 955 .77 955 108 - - - - 1.82 775 142 - - - - 1.82 801 64.8 - - - - 1.82 722 113 - - - - 1.82 364 e215 HFK- 1 - - - - 1.73 1,120 e1.21 - - - - 1.73 781 84.3 - - - - 1.73 869 110 - - - - 1.73 631 109 - - - - 1.73 670 52.4 - - - - 1.73 602 92.5 SCC- 1 - - - - 1.61 38 e10.2 25 16 32 35 .58 35 9.16 26 26 38 39 .59 39 6.31 - - - 58 .64 58 5.32 - - - - 1.72 770 .46 - - - - 1.72 1,390 e. 37 - - - - 1.61 37 12.6 PC- 1 600 255 802 808 .72 808 109 - - - 1.73 803 86.6 - - - 802 .72 802 49.7 770 189 1,110 1,210 .79 1,210 78.3 - - - 1.73 788 51.0 - - - 904 .75 904 3.90 - - - 1.73 631 <. 02 180 120 233 265 .68 265 29.3 DRN- 1 1,200 344 1,890 2,070 .86 2,070 15.1 - - - 2,710 .93 2,710 1.83 - - - 3,800 .98 3,800 .31 - - - - 1.94 4,080 1.21 - - - 3,740 .98 3,740 1.01 - - - - 1.94 4,060 1.11 Tables 25 Table 2. Instantaneous discharge and properties of water samples collected from water- quality monitoring sites near Manila, Utah - Continued Site identifier ( see table 1) Site type Sample date Sample time Discharge, instanta-neous ( ft3/ s) pH, water, unfiltered, laboratory ( standard units) Specific conductance, water, unfiltered, laboratory ( μS/ cm at 25° C) Specific conductance, water, field, unfiltered ( μS/ cm at 25° C) Temper-ature, water (° C) DRN- 1- Continued 04/ 05/ 05 1610 e. 2 - - 4,140 6.7 04/ 24/ 05 1700 .13 - - 7,880 1.4 06/ 01/ 05 1240 e. 05 - - 3,740 13.9 DRN- 1a drain 08/ 11/ 04 1640 .27 - - 3,100 23.6 09/ 15/ 04 1810 .09 - - 3,630 18.0 10/ 27/ 04 1535 .11 - - 4,340 9.7 11/ 23/ 04 1440 .07 7.9 4,770 4,950 2.6 01/ 19/ 05 1630 .02 - - 4,520 .1 04/ 05/ 05 1545 .02 - - 6,800 10.7 06/ 01/ 05 1220 .2 7.8 4,190 4,350 14.1 DRN- 2 drain 06/ 29/ 04 1740 5.8 8 2,100 2,170 16.9 08/ 11/ 04 1540 1.7 - - 2,710 20.6 09/ 15/ 04 1700 .57 7.8 3,300 3,240 14.5 10/ 27/ 04 1443 .2 - - 5,100 9.2 11/ 23/ 04 1410 .12 - - 5,140 4.8 01/ 19/ 05 1700 .06 - - 5,540 3.7 02/ 25/ 05 1446 .07 - - 5,620 5.4 04/ 06/ 05 1140 .07 - - 5,950 9.3 06/ 01/ 05 1350 1.6 7.9 2,960 3,080 15.1 DRN- 3 drain 06/ 30/ 04 1000 1.9 - - 2,070 14.8 08/ 11/ 04 1025 .1 - - 2,820 14.8 09/ 15/ 04 1120 1.7 - - 1,970 9.5 10/ 27/ 04 1140 .31 - - 2,850 7.3 11/ 23/ 04 1030 .05 - - 3,650 .5 01/ 20/ 05 1220 <. 01 - - 3,690 .1 02/ 24/ 05 1010 e. 01 - - 3,710 5.5 04/ 06/ 05 1010 e. 05 - - 3,730 4.0 06/ 01/ 05 1500 .01 - - 3,960 20.3 DRN- 4 drain 06/ 30/ 04 1100 .33 - - 3,330 18.7 08/ 11/ 04 1220 <. 01 - - 2,960 19.7 09/ 15/ 04 1245 .08 - - 2,460 - 10/ 27/ 04 1240 e. 3 - - 3,040 10.1 11/ 23/ 04 1100 .02 - - 3,220 3.4 01/ 20/ 05 1240 <. 01 - - 3,250 5.4 02/ 24/ 05 1023 <. 01 - - 2,000 3.5 26 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 Table 2. Instantaneous discharge and properties of water samples collected from water- quality monitoring sites near Manila, Utah- Continued Site identifier ( see table 1) Hardness, water ( mg/ L as CaCO 3 ) Alkalinity, water, filtered, incremental titration, lab ( mg/ L) Dissolved-solids concentration, sum of constituents, water, filtered ( mg/ L) Dissolved-solids concentration, ROE, water, filtered ( mg/ L) ROE/ Specific-conductance ratio Dissolved-solids concentration from ROE/ Specific-conductance ratio ( mg/ L) Dissolved-solids load ( tons per day) DRN- 1 - - - - 1.94 3,890 e2.10 - - - - 1.94 7,410 2.60 - - - - 1.94 3,520 e. 47 DRN- 1a - - - 2,820 .91 2,820 2.05 - - - 3,480 .96 3,480 .84 - - - - 1.93 4,040 1.20 2,200 350 4,310 4,680 .95 4,680 .88 - - - - 1.93 4,200 .23 - - - - 1.93 6,320 .34 1,700 347 3,480 3,840 .88 3,840 2.07 DRN- 2 1,000 339 1,660 1,830 .84 1,830 28.6 - - - 2,420 .89 2,420 11.1 1,600 310 2,730 3,080 .95 3,080 4.73 - - - - 1.89 4,540 2.45 - - - 4,780 .93 4,780 1.55 - - - - 1.89 4,930 .80 - - - - 1.89 5,000 .94 - - - - 1.89 5,300 1.00 1,200 292 2,310 2,610 .85 2,610 11.3 DRN- 3 - - - 1,720 .83 1,720 8.81 - - - 2,630 .93 2,630 .71 - - - 1,700 .86 1,700 7.79 - - - - 1.90 2,560 2.14 - - - 3,510 .96 3,510 .47 - - - - 1.90 3,320 <. 09 - - - - 1.90 3,340 e. 09 - - - - 1.90 3,360 e. 45 - - - - 1.90 3,560 <. 10 DRN- 4 - - - 3,050 .92 3,050 2.71 - - - 2,730 .92 2,730 <. 07 - - - - 1.88 2,160 .47 - - - - 1.88 2,680 e2.16 - - - 3,090 .96 3,090 .17 - - - - 1.88 2,860 <. 08 - - - - 1.88 1,760 <. 05 Tables 27 Table 2. Instantaneous discharge and properties of water samples collected from water- quality monitoring sites near Manila, Utah - Continued Site identifier ( see table 1) Site type Sample date Sample time Discharge, instanta-neous ( ft3/ s) pH, water, unfiltered, laboratory ( standard units) Specific conductance, water, unfiltered, laboratory ( μS/ cm at 25° C) Specific conductance, water, field, unfiltered ( μS/ cm at 25° C) Temper-ature, water (° C) DRN- 4- Continued 06/ 01/ 05 1530 .31 7.7 1,190 1,220 22.1 DRN- 5 drain 06/ 30/ 04 1130 e. 01 - - 2,790 - 08/ 11/ 04 1205 <. 01 - - 2,350 - 09/ 15/ 04 1310 <. 01 - - 2,970 17.0 10/ 27/ 04 1230 e. 1 - - 3,240 10.7 11/ 23/ 04 1130 <. 01 - - 3,160 4.4 DRN- 8 drain 06/ 29/ 04 1800 <. 01 - - 5,610 19.1 08/ 11/ 04 1525 .01 - - 4,610 28.1 09/ 15/ 04 1640 .02 - - 4,680 18.0 10/ 27/ 04 1435 .03 - - 4,620 10.4 11/ 23/ 04 1348 .01 - - 4,890 3.2 01/ 19/ 05 1715 <. 01 - - 6,000 1.0 06/ 01/ 05 1310 .02 - - 5,300 22.0 LAT- 1 drain 08/ 11/ 04 1400 .07 - - 1,980 33.0 09/ 15/ 04 1405 .74 - - 1,970 15.3 10/ 27/ 04 1320 e. 1 - - 6,100 7.9 11/ 23/ 04 1315 .01 - - 7,160 3.3 05/ 31/ 05 2000 .14 - - 1,950 15.1 BSD- 1 drain 05/ 27/ 04 1000 e10 - - 1,740 11.4 06/ 16/ 04 0940 6 8 1,830 1,920 12.6 06/ 30/ 04 0810 19 - - 2,270 12.9 08/ 11/ 04 0830 5.4 - - 2,230 13.7 09/ 15/ 04 0900 5.2 - - 2,730 5.0 10/ 27/ 04 0935 13 - - 2,020 5.3 11/ 23/ 04 0850 2.8 - - 5,130 .6 01/ 20/ 05 1415 2.7 - - 6,950 1.2 02/ 24/ 05 1400 1.9 - - 6,900 2.1 04/ 06/ 05 0825 1 - - 5,690 .8 04/ 19/ 05 1420 7.7 - - 1,910 13.7 05/ 31/ 05 1800 16 - - 1,890 20.6 BSD- 2 drain 05/ 27/ 04 1400 e20 - - 1,890 19.0 06/ 30/ 04 0855 22.5 7.9 2,210 2,290 12.6 08/ 11/ 04 1035 8.1 8.1 2,320 2,340 15.4 09/ 15/ 04 1105 9.2 8 2,650 2,640 8.5 10/ 27/ 04 1050 17 - - 2,340 5.9 28 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 Table 2. Instantaneous discharge and properties of water samples collected from water- quality monitoring sites near Manila, Utah- Continued Site identifier ( see table 1) Hardness, water ( mg/ L as CaCO 3 ) Alkalinity, water, filtered, incremental titration, lab ( mg/ L) Dissolved-solids concentration, sum of constituents, water, filtered ( mg/ L) Dissolved-solids concentration, ROE, water, filtered ( mg/ L) ROE/ Specific-conductance ratio Dissolved-solids concentration from ROE/ Specific-conductance ratio ( mg/ L) Dissolved-solids load ( tons per day) DRN- 4 480 172 822 900 .74 900 .75 DRN- 5 - - - - 1.90 2,510 e. 07 - - - - 1.90 2,120 <. 06 - - - - 1.90 2,670 <. 07 - - - - 1.90 2,920 e. 79 - - - - 1.90 2,840 <. 08 DRN- 8 - - - 1.96 5,390 .15 - - - 4,360 .95 4,360 <. 12 - - - 4,500 .96 4,500 .24 - - - - 1.96 4,440 .36 - - - - 1.96 4,690 .13 - - - - 1.96 5,760 <. 16 - - - - 1.96 5,090 .27 LAT- 1 - - - 1,630 .82 1,630 .31 - - - - 1.82 1,620 3.22 - - - - 1.82 5,000 e1.35 - - - - 1.82 5,870 .16 - - - - 1.82 1,600 .60 BSD- 1 - - - - 1.81 1,410 e38.0 700 228 1,340 1,450 .76 1,450 23.5 - - - 1,850 .81 1,850 94.8 - - - 1,830 .82 1,830 26.7 - - - 2,420 .89 2,420 33.9 - - - - 1.88 1,780 62.3 - - - 4,440 .87 4,440 33.5 - - - - 1.81 5,630 41.0 - - - - 1.81 5,590 28.6 - - - - 1.81 4,610 12.4 - - - - 1.81 1,550 32.1 - - - 1,410 .75 1,410 60.8 BSD- 2 - - - - 1.82 1,550 e83.6 940 285 1,700 1,860 .81 1,860 113 890 264 1,750 1,790 .76 1,790 39.1 1,200 284 2,110 2,300 .87 2,300 57.1 - - - - 1.82 1,920 88.0 Tables 29 Table 2. Instantaneous discharge and properties of water samples collected from water- quality monitoring sites near Manila, Utah - Continued Site identifier ( see table 1) Site type Sample date Sample time Discharge, instanta-neous ( ft3/ s) pH, water, unfiltered, laboratory ( standard units) Specific conductance, water, unfiltered, laboratory ( μS/ cm at 25° C) Specific conductance, water, field, unfiltered ( μS/ cm at 25° C) Temper-ature, water (° C) BSD- 2- Continued 11/ 23/ 04 1015 3.5 7.8 5,260 5,430 .7 01/ 20/ 05 1145 2.9 - - 5,900 .5 02/ 24/ 05 1100 3.4 7.9 6,800 6,890 .1 04/ 06/ 05 0950 2.2 - - 6,060 3.2 05/ 31/ 05 1930 24 7.8 2,030 2,120 18.5 SV- 1 drain 05/ 27/ 04 1200 e7 - - 1,310 11.9 06/ 16/ 04 1145 .45 - - 1,300 15.0 06/ 30/ 04 1550 7.9 - - 1,460 19.3 08/ 12/ 04 1100 6.4 - - 822 17.3 09/ 16/ 04 1200 5 - - 1,020 11.0 10/ 28/ 04 1005 9 - - 1,970 5.8 11/ 24/ 04 0905 1.4 - - 1,830 2.1 01/ 20/ 05 0850 1.2 - - 2,260 .7 02/ 24/ 05 0800 1.4 - - 2,870 .1 04/ 06/ 05 1435 .72 - - 1,760 14.4 04/ 19/ 05 1100 .55 - - 1,680 9.7 05/ 31/ 05 1310 .52 - - 1,340 21.2 SV- 2 drain 06/ 30/ 04 1455 9.7 8 1,390 1,420 17.7 08/ 12/ 04 0950 6.5 8 920 935 13.0 09/ 16/ 04 1050 5.1 8.1 1,060 1,080 9.0 10/ 28/ 04 1050 8.3 - - 1,910 6.1 11/ 24/ 04 1010 2.1 7.9 1,970 2,030 .9 01/ 20/ 05 0945 1.1 - - 2,480 .4 04/ 06/ 05 1355 .72 - - 2,070 11.1 05/ 31/ 05 1445 .56 8.1 2,030 2,120 19.8 PC- 2 drain 06/ 16/ 04 1420 e9 - - 1,890 - 06/ 30/ 04 1740 15 7.9 1,900 2,030 18.3 08/ 12/ 04 0845 3.2 7.9 1,900 1,920 14.0 09/ 16/ 04 0930 4.6 7.9 2,100 2,080 9.1 10/ 27/ 04 1641 4 - - 2,070 8.5 11/ 23/ 04 1550 .47 7.6 2,920 3,000 6.5 01/ 20/ 05 1030 .25 - - 3,190 4.2 02/ 24/ 05 0920 .13 - - 3,300 .6 04/ 06/ 05 1255 .08 - - 3,350 14.0 04/ 19/ 05 1255 .15 - - 2,930 14.7 30 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 Table 2. Instantaneous discharge and properties of water samples collected from water- quality monitoring sites near Manila, Utah- Continued Site identifier ( see table 1) Hardness, water ( mg/ L as CaCO 3 ) Alkalinity, water, filtered, incremental titration, lab ( mg/ L) Dissolved-solids concentration, sum of constituents, water, filtered ( mg/ L) Dissolved-solids concentration, ROE, water, filtered ( mg/ L) ROE/ Specific-conductance ratio Dissolved-solids concentration from ROE/ Specific-conductance ratio ( mg/ L) Dissolved-solids load ( tons per day) BSD- 2 2,100 384 4,560 4,850 .89 4,850 45.8 - - - - 1.82 4,840 37.8 2,200 403 5,740 5,940 .86 5,940 54.5 - - - - 1.82 4,970 29.5 700 215 1,450 1,580 .75 1,580 102 SV- 1 - - - 1.69 904 e17.1 - - - 882 .68 882 1.07 - - - 1,040 .71 1,040 22.2 - - - 555 .68 555 9.58 - - - 700 .69 700 9.44 - - - - 1.69 1,360 33.0 - 173 - 1,310 .72 1,310 4.95 - - - - 1.69 1,560 5.05 - - - - 1.69 1,980 7.48 - - - - 1.69 1,210 2.36 - - - - 1.69 1,160 1.72 - - - - 1.69 925 1.30 SV- 2 580 341 999 1,020 .72 1,020 26.7 360 352 592 639 .68 639 11.2 410 296 716 751 .70 751 10.3 - - - - 1.70 1,340 29.9 730 - 1,430 1,460 .72 1,460 8.27 - - - - 1.70 1,740 5.15 - - - - 1.70 1,450 2.81 640 - 1,420 1,490 .70 1,490 2.25 PC- 2 - - - - 1.86 1,630 e39.5 930 257 1,550 1,700 .84 1,700 68.8 880 240 1,470 1,640 .85 1,640 14.2 1,100 254 1,680 1,830 .88 1,830 22.7 - - - - 1.86 1,780 19.2 1,700 303 2,620 2,800 .93 2,800 3.55 - - - - 1.86 2,740 1.85 - - - - 1.86 2,840 1.00 - - - - 1.86 2,880 .62 - - - - 1.86 2,520 1.02 Tables 31 Table 2. Instantaneous discharge and properties of water samples collected from water- quality monitoring sites near Manila, Utah - Continued Site identifier ( see table 1) Site type Sample date Sample time Discharge, instanta-neous ( ft3/ s) pH, water, unfiltered, laboratory ( standard units) Specific conductance, water, unfiltered, laboratory ( μS/ cm at 25° C) Specific conductance, water, field, unfiltered ( μS/ cm at 25° C) Temper-ature, water (° C) PC- 2- Continued 05/ 31/ 05 1540 9.2 7.8 1,590 1,650 17.0 CC- 1 drain 07/ 01/ 04 0955 .87 7.9 3,040 3,300 12.1 08/ 10/ 04 1530 e. 06 - - 3,200 16.1 09/ 15/ 04 1725 .05 - - 3,890 12.9 10/ 26/ 04 1620 .32 - - 4,040 7.8 01/ 19/ 05 1350 .6 - - 4,240 1.5 04/ 05/ 05 1440 .24 - - 4,070 13.3 06/ 01/ 05 1000 .05 - - 3,100 8.8 AW- 1 drain 08/ 10/ 04 1430 4.3 - - 3,640 20.2 09/ 14/ 04 1610 3 7.7 3,900 4,160 15.0 10/ 26/ 04 1300 4.1 - - 4,140 8.6 11/ 22/ 04 1345 3.8 7.7 4,210 4,320 4.4 01/ 19/ 05 1135 2.6 - - 4,150 2.3 02/ 24/ 05 1600 2.3 7.7 3,950 4,030 5.6 04/ 05/ 05 1325 1.6 - - 4,560 9.9 06/ 01/ 05 0930 1.3 7.7 4,240 4,470 8.7 SP- 1 seep 06/ 30/ 04 1210 .01 7.7 3,950 4,140 18.0 08/ 11/ 04 1515 .04 - - 3,910 17.9 09/ 15/ 04 1710 .04 - - 3,930 14.0 10/ 27/ 04 1400 .05 - - 3,970 10.0 11/ 23/ 04 1328 .01 - - 4,190 7.3 SP- 3 seep 06/ 30/ 04 1030 <. 01 - - 3,850 17.9 08/ 11/ 04 1220 <. 01 - - 3,730 24.9 09/ 15/ 04 1230 <. 01 - - 3,960 16.4 10/ 27/ 04 1150 <. 01 - - 3,030 10.3 11/ 23/ 04 1100 <. 01 - - 3,980 2.2 SP- 4 seep 06/ 30/ 04 1230 <. 01 - - 6,470 18.2 09/ 15/ 04 1430 <. 01 - - 5,640 12.1 10/ 27/ 04 1425 .02 - - 5,850 9.5 SPG- 1 spring 11/ 24/ 04 1135 <. 01 - - 796 7.1 06/ 01/ 05 1830 <. 01 7.8 1,000 1,030 7.2 1Ratio is either the average of calculated values for that site, or if there are no calculated values for the site, the average of calculated values for the site type. 32 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 Table 2. Instantaneous discharge and properties of water samples collected from water- quality monitoring sites near Manila, Utah- Continued Site identifier ( see table 1) Hardness, water ( mg/ L as CaCO 3 ) Alkalinity, water, filtered, incremental titration, lab ( mg/ L) Dissolved-solids concentration, sum of constituents, water, filtered ( mg/ L) Dissolved-solids concentration, ROE, water, filtered ( mg/ L) ROE/ Specific-conductance ratio Dissolved-solids concentration from ROE/ Specific-conductance ratio ( mg/ L) Dissolved-solids load ( tons per day) PC- 2 740 191 1,200 1,310 .79 1,310 32.5 CC- 1 1,900 282 2,800 3,120 .95 3,120 7.32 - - - - .96 3,070 e. 50 - - - - 1.96 3,730 .50 - - - - 1.96 3,880 3.35 - - - - 1.96 4,070 6.59 - - - - 1.96 3,910 2.53 - - - - 1.96 2,980 .40 AW- 1 - - - 3,580 .98 3,580 41.5 2,500 286 3,720 4,080 .98 4,080 33.0 - - - - 11.00 4,140 45.8 2,800 - - 4,450 1.03 4,450 45.6 - - - - 11.00 4,150 29.1 2,700 312 3,790 4,080 1.01 4,080 25.3 - - - - 11.00 4,560 19.7 2,700 352 3,960 4,340 .97 4,340 15.2 SP- 1 1,800 357 3,510 3,650 .88 3,650 .10 - - - 3,710 .95 3,710 .40 - - - 3,690 .94 3,690 .40 - - - - 1.92 3,650 .49 - - - - 1.92 3,850 .10 SP- 3 - - - - 1.92 3,540 <. 10 - - - - 1.92 3,430 <. 09 - - - - 1.92 3,640 <. 10 - - - - 1.92 2,790 <. 08 - - - - 1.92 3,660 <. 10 SP- 4 - - - - 1.92 5,950 <. 16 - - - - 1.92 5,190 <. 14 - - - - 1.92 5,380 .29 SPG- 1 - - - 638 .80 638 <. 02 500 314 636 671 .65 671 <. 02 Tables 33 Table 3. Concentration of major ions in water samples collected from water- quality monitoring sites near Manila, Utah [ mg/ L, milligrams per liter; <, less than] Site identifier ( see table 1) Site type Sample date Sample time Calcium, water, filtered ( mg/ L) Magnesium, water, filtered ( mg/ L) Potassium, water, filtered ( mg/ L) HFK- 3 stream 09/ 14/ 04 1840 214 96.7 12.0 SCC- 1 canal 07/ 01/ 04 1225 7.6 1.6 .6 08/ 10/ 04 1125 7.6 1.6 .5 PC- 1 canal 06/ 29/ 04 1400 141 59.4 8.6 09/ 14/ 04 1430 161 90.0 12.3 06/ 01/ 05 0840 46.5 15.8 3.6 DRN- 1 drain 06/ 29/ 04 1635 271 125 13.7 DRN- 1a drain 11/ 23/ 04 1440 504 235 13.0 06/ 01/ 05 1220 320 228 13.8 DRN- 2 drain 06/ 29/ 04 1740 232 106 14.9 09/ 15/ 04 1700 360 162 14.5 06/ 01/ 05 1350 240 143 7.4 DRN- 4 drain 06/ 01/ 05 1530 111 49.1 6.6 BSD- 1 drain 06/ 16/ 04 0940 150 77.8 6.5 BSD- 2 drain 06/ 30/ 04 0855 199 107 9.3 08/ 11/ 04 1035 190 102 9.7 09/ 15/ 04 1105 244 131 11.8 11/ 23/ 04 1015 407 253 16.5 02/ 24/ 05 1100 372 315 19.8 05/ 31/ 05 1930 136 87.6 8.6 SV- 2 drain 06/ 30/ 04 1455 122 67.2 11.2 08/ 12/ 04 0950 69.9 44.6 8.5 09/ 16/ 04 1050 80.9 51.0 5.4 11/ 24/ 04 1010 128 99.9 7.5 05/ 31/ 05 1445 98.4 95.5 9.5 PC- 2 drain 06/ 30/ 04 1740 230 86.9 10.3 08/ 12/ 04 0845 222 79.6 8.5 09/ 16/ 04 0930 268 97.7 10.1 11/ 23/ 04 1550 520 108 10.5 05/ 31/ 05 1540 191 63.2 7.5 CC- 1 drain 07/ 01/ 04 0955 373 233 26.6 AW- 1 drain 09/ 14/ 04 1610 488 322 26.5 11/ 22/ 04 1345 531 350 28.0 02/ 24/ 05 1600 510 337 23.7 06/ 01/ 05 0930 473 372 25.1 SP- 1 seep 06/ 30/ 04 1210 461 164 12.6 SPG- 1 spring 06/ 01/ 05 1830 83.2 70.3 4.2 34 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 Table 3. Concentration of major ions in water samples collected from water- quality monitoring sites near Manila, Utah- Continued Site identifier ( see table 1) Sodium, water, filtered ( mg/ L) Chloride, water, filtered ( mg/ L) Fluoride, water, filtered ( mg/ L) Silica, water, filtered ( mg/ L) Sulfate, water, filtered ( mg/ L) HFK- 3 78.8 22.3 0.8 24.7 767 SCC- 1 1.3 .6 <. 2 3.9 6.6 1.1 .5 <. 2 3.7 6.7 PC- 1 41.0 11.8 .5 22.8 364 60.6 16.6 .6 24.2 635 10.1 3.4 .2 14.7 67 DRN- 1 173 44.2 .7 34.8 1,030 DRN- 1a 568 165 1.1 27.6 2,590 477 140 1.2 22.3 2,070 DRN- 2 163 51.8 .8 36.1 857 288 82.3 1.2 23.0 1,610 280 105 1.0 20.7 1,340 DRN- 4 90.0 28.8 .6 19.9 413 BSD- 1 197 77.6 .5 13.3 686 BSD- 2 224 82.5 .6 18.7 894 210 87.0 .8 18.7 972 235 90.1 .8 20.6 1,200 751 311 1.2 17.9 2,570 1,100 475 1.2 15.7 3,200 232 101 .5 22.6 737 SV- 2 126 27.5 .7 24.2 416 74.7 20.0 .7 21.0 141 92.5 23.1 .7 13.0 272 239 55.4 1.0 19.4 622 256 56.5 1.0 16.1 669 PC- 2 145 46.7 .9 19.4 855 116 38.7 .9 15.6 846 122 37.7 1.0 18.6 974 182 61.0 1.6 18.2 1,540 118 40.7 .7 16.5 645 CC- 1 163 37.5 1.6 31.6 1,770 AW- 1 201 43.1 1.9 29.3 2,440 252 53.8 1.9 33.2 2,640 241 46.0 1.8 27.8 2,410 245 48.7 1.9 30.2 2,550 SP- 1 462 135 1.2 19.0 2,040 SPG- 1 46.0 26.3 .4 12.9 204 Tables 35 36 Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05 S. J. Gerner and others- Characterization of Dissolved Solids in Water Resources of Agricultural Lands near Manila, Utah, 2004- 05- SIR 2006- 5211