WATER-QUALITY INVESTIGATIONS OF 

THE JORDAN RIVER, SALT LAKE COUNTY, 

UTAH, 1980-82 

By Doyle W. Stephens

U.S. GEOLOGICAL SURVEY

Water-Resources Investigations Report 84-4298

Prepared in cooperation with the

SALT LAKE COUNTY DIVISION OF FLOOD CONTROL

AND WATER QUALITY

Salt Lake City, Utah 

1984
UNITED STATES DEPARTMENT OF THE INTERIOR 

WILLIAM P. CLARK, Secretary

GEOLOGICAL SURVEY 

Dallas L. Peck, Director

For additional information 

write to:

District Chief

U.S. Geological Survey

Water Resources Division

Room 1016 Administration Building

1745 West 1700 South

Salt Lake City, Utah 84104

(Telephone: (801) 524-5663)

Copies of this report can 

be purchased from:

Open-File Services Section 

Western Distribution Branch 

U.S. Geological Survey 

Box 25425, Denver Federal Center 

Denver, Colorado 80225 

(Telephone: (303) 234-5888)
CONTENTS

Page

Glossary ......................................................... vi

Abstract ......................................................... 1

Introduction ..................................................... 2

Topography and general hydrology ............................ 3

Precipitation ............................................... 5

Data collection ............................................. 5

Dissolved oxygen ................................................. 5

Trends in dissolved-oxygen concentration and

oxygen demands .............................................. 6

Reaeration rates and time-of-travel ......................... 9

Effects of algal populations ................................ 11

Effects of storm runoff and wastewater-treatment plants ..... 11

Toxic substances ................................................. 16

Identification and distribution of toxic substances ......... 16

Transport of trace elements ................................. 20

Toxic-organic substances in the water ....................... 20

Toxic substances in bottom materials ........................ 21

Priority pollutants in storm runoff ......................... 23

Sanitary quality ................................................. 23

Distribution of bacterial contamination ..................... 24

Sources of bacterial contamination .......................... 29

Wastewater-treatment plant effluents ................... 29

Tributary streams ...................................... 29

Trends in sanitary quality .................................. 32

Effects of storm-water discharges ........................... 32

Turbidity ........................................................ 36

Variation in turbidity ...................................... 36

Variation in the components of turbidity .................... 39

Correlation of turbidity with related parameters and

control of turbidity ....................................... 39

Summary and conclusions .......................................... 42

References cited ................................................. 43
ILLUSTRATIONS

Page

Figure 1. Map showing monitoring sites on and major inflow 

sources to the Jordan River in Salt Lake County, 

Utah ................................................. 4

2-13. Graphs showing:

2. Variation in dissolved-oxygen concentrations with 

river mile during low-flow conditions from 1957 

to 1982 .......................................... 7

3. Variation in dissolved-oxygen concentrations during 

daytime River at 1700 South Street, AprilSeptember 1974-82 ................................

4. Profile of the river channel with selected reference

points, travel times, and reaeration rates ....... 12

5. Total annual loads of oxygen-demanding substances, 

as measured by 5-day biochemical-oxygen demand, 

discharged during 1981 frcm point sources ........ 15

6. Mean concentration and one standard deviation for

total col if orm bacteria at five sampling sites ... 25

7. Mean concentration and one standard deviation for

fecal coliform bacteria at five sampling sites ... 26

8. Mean concentration and one standard deviation for 

fecal streptococcal bacteria at five sampling 

sites ............................................ 27

9. Percentage of samples in which concentrations of 

total and fecal coliform bacteria were greater 

than the sanitary standards at five sampling 

sites ............................................ 28

10. Percentage of samples where ratio between

concentrations of fecal coliform and fecal

streptococcal bacteria was greater than 4.1 and

less than 0.7 .................................... 30

11. Increase in fecal coliform bacterial concentrations 

with time and comparison with the sanitary 

standard at 1700 South Street .................... 34

12. Mean concentrations of fecal coliform bacteria (PC), 

fecal streptococcal bacteria (PS), and total 

coliform bacteria (TC) in conduits ............... 35

13. Variations in turbidity at five sampling sites,

January 1981 to August 1982 ...................... 38
TABLES

Page

Table 1. Frequency of nonccmpliance with water-quality

standards for intended use, 1981-82 ................. 10

2. Estimated total loads for annual-storm runoff from

major tributaries and storm conduits during 10 storms

in 1981 f in pounds of oxygen-dananding substances ... 13

3. Occurrence of constituents that exceeded State 

intended-use standards in the Jordan River and 

three major tributaries ............................. 18

4. Frequency of occurrence of constituents that exceeded

selected concentrations in samples frcm conduits .... 19

5. Mean concentrations of selected trace elements in 

bottom materials in the Jordan River and three 

tributaries ......................................... 22

6. Summary of coliform concentrations discharged by 

wastewater-treatment plants in Salt Lake County, 

September 1980 to October 1982 ...................... 31

7. Comparison of mean bacterial concentrations for 

nonstorm and storm samples collected near the 

mouths of Little Cottonwood and Mill Creeks ......... 33

8. Mean concentrations of indicator bacteria in nonstorm

and storm samples collected at five sampling sites .. 37

9. Variations in the means for turbidity and for 

suspended-sediment, suspended-organic carbon, 

and chlorophyll concentrations ...................... 40

10. Correlation coefficients between turbidity and two

components of suspended sediment .................... 41
GLOSSARY

Chemical-oxygen demand (ODD). The total quantity of oxygen required to 

oxidize the chemical and biological material in a sample. The procedure 

involves refluxing the samples with a strong acid-dichromate solution.

Chlorophyll a and b. The photosynthesizing pigments found in algae and 

other plants which effect the conversion of light energy to chemical energy.

Coefficient of variation (Cv). The standard deviation of a number set 

expressed as a percentage of the mean of that number set.

Correlation coefficient. A measure of the similarity of linear 

relationship between two variables. Values range from minus 1.0 to plus 1.0. 

Values of almost plus 1.0 show a correlation with a positive slope, and values 

of almost minus 1.0 show a correlation with a negative slope.

Dissolved-organic carbon (DOC). The amount of organic carbon passing 

through a 0.45-micrometer silver filter. Determined fcy combustion to carbon 

dioxide with quantification by infrared spectrometry.

Five-day biochemical-oxygen demand (BOD5). The quantity of oxygen used 

to degrade the carbonaceous-organic matter in a sample at 20° Celsius in a 5- 

day period.

Indicator bacteria. Bacterial types that normally are nonpathogenic but 

do indicate the possibility of fecal contamination.

Jackson turbidity unit (JTU). A measure of the ratio of the light 

transmitted through water in a straight line to the intensity of the incident 

light.

K2 . Reaeration coefficient calculated to log e.

Nephelometric turbidity unit (N1U). A measure of the ratio of intensity 

of light scattered at right angles by the suspended matter to the intensity of 

the incident light. Nephelometric turbidity units approximate Jackson 

Turbidity Units.

Priority pollutants. Any of a group of 129 compounds and elements from 

65 pollutant classes which have been identified by the U.S. Environmental 

Protection Agency and currently have recommended quality criteria for 

concentrations in water.

R-square. Coefficient of determination. This is calculated as the 

square of the correlation coefficient and when multiplied by 100 represents 

the percent variation of the dependent variable, which is explained by the 

regression equation. It is a "best-fit" test for the population scatter about 

a curve.
Suspended-organic carbon (SOC). The quantity of organic carbon filtered 

from a sample ty a 0.45-micrometer silver filter. Determined as for DOC

Ultimate biochemical-oxygen demand (BODU). The total quantity of oxygen 

required to degrade the carbonaceous organic matter in a sample at 20° 

Celsius.

CONVERSION FACTORS AND RELATED INFORMATION

Values in this report are given mostly in inch-pound units. Conversion 

factors to metric units are listed below:

Multiply By To obtain

cubic foot per second 0.02832 cubic meter per second

cubic foot per second per mile 0.0176 cubic meter per second per

	kilometer

foot 0.3048 meter

foot per mile 0.1894 meter per kilometer

inch 2.54 centimeter

mile 1.609 kilometer

pound 0.4536 kilogram

square mile 2.59 square kilometer

acre-foot 1,233 cubic meter

Chemical concentration and water temperature are given only in metric 

units. Chemical concentration is given in milligrams per liter (mg/L) or 

micrograms per liter (ug/L). Milligrams per liter is a unit expressing the 

concentration of chemical constituents in solution as weight (milligrams) of 

solute per unit volume (liter of water). One thousand micrograms per liter is 

equivalent to 1 mg/L. For concentrations less than 7,000 mg/L, the numerical 

value is about the same as for concentrations in parts per million.

Water temperature is given in degrees Celsius (°C) , which can be 

converted to degrees Fahrenheit (°Fj by the following equation:

°F= 1.8(PC) + 32

V-U.
WATER-QUALITY INVESTIGATIONS OF THE JORDAN RIVER,

SALT LAKE COUNTY, UTAH, 1980-82

By Doyle W. Stephens

ABSTRACT

Water-quality studies were made on the Jordan River, Salt Lake County, 

Utah, from 1980-82 to investigate specific problems involving dissolved 

oxygen, toxic substances, sanitary quality, and turbidity. The studies were 

coincident with an investigation of the affects of urban runoff on surfacewater quaility in Salt Lake County.

The combination of large organic loads, small discharge, and slight 

reaeration rates resulted in dissolved-oxygen concentrations in the Jordan 

River downstream from 5800 South Street during April-September which 

frequently did not meet State intended use standards. The dissolved oxygen 

typically decreased from about 8 milligrams per liter at the Jordan Narrows to 

less than 5 milligrams per liter at 500 North Street. Accompanying this 

decrease was an increase in chemical-oxygen demand of about 23 percent and in 

biochemical-oxygen demands of 90 percent. An estimated load of 6 million 

pounds of oxygen-demanding substances was discharged to the Jordan River 

annually from point sources north of 9000 South Street. Wastewater-treatment 

plants contributed 77 percent of these substances, nonstorm base flows from 

the major tributaries to the river contributed 22 percent, and storm flows 

contributed less than 1 percent. Most of the organic substances 

were discharged to the reaches characterized fcy the smallest reaeration rates. 

A diversion to the Surplus Canal removed 67 percent of the oxygen-demanding 

substances in the river.

Several toxic substances, primarily trace metals, were detected in the 

Jordan River and its major tributaries. Nearly 78 percent of the water 

samples analyzed for total mercury exceeded the State intended-use standard of 

0.05 microgram per liter. Concentrations of five other toxic substances 

exceeded the standards occasionally: ammonia (18 percent of the samples); 

cadnium (9 percent); copper (9 percent); lead (2 percent); and zinc (6 

percent). The concentrations of trace elements found in bottom sediments 

increased markedly at 5800 South Street and persisted downstream to 500 North 

Street. The pesticides DOT, DDD, DEE, dieldrin, methoxychlor, and 2,4-D were 

detected in bottom materials, but most were at concentrations less than 15 

micrograms per kilogram. Bottom samples from the Jordan Narrows contained KB 

concentrations as great as 320 micrograms per kilogram. Samples were 

collected from three conduits during a storm on October 29, 1981, and analysed 

for priority pollutants as designated fcy the U.S. Environmental Protection 

Agency. Trace metals were identified as common contaminants, but only 2 of 

the 113 organic pollutants (chloroform and phenol) were detected.

The concentrations of bacteria in the Jordan River often exceeded the 

State sanitary standards for total coliform bacteria (5,000 colonies per 100 

milliliters) and for fecal coliforms (2,000 colonies per 100 milliliters). 

Concentrations of three indicator bacteria (total coliform, fecal coliform, 

and fecal streptococcal) generally increased in a downstream direction. 

Contamination from animal waste was indicated in 92 percent of the samples
from the Jordan Narrows, but this decreased to about 50 percent of the samples 

at downstream sites. Contamination from human waste was not found at the 

Jordan Narrows or 9000 South Street, but it increased to 20 percent of the 

samples at 1700 South Street. Storm runoff fran urban areas contributed large 

concentrations of indicator bacteria to the river, with fecal contamination 

frcm animal wastes indicated in about 72 percent of the samples.

The primary sources of turbidity in the Jordan River are Utah Lake and 

discharges frcm the wastewater-treatment plants. Relatively large values of 

turbidity were measured at the Jordan Narrows, with a mean of 88 Nephelcmetric 

turbidity units during June-October and a mean of 43 Nephelometric turbidity 

units during November-May. The means at other sites for same periods were 27 

and 32 Nephelometric turbidity units. Correlation coefficients ranging from 

0.71-0.83 indicated that significant relationships existed between turbidity 

and suspended-organic carbon during June-October at each of five sites. A 

smaller but statistically significant correlation of 0.46 occurred between 

turbidity and suspended-sediment concentration during November-May when data 

for all five sites were combined.

ZNTROXJCTION

The selection of Salt Lake County, Utah, as a study area in the U.S. 

Geological Survey's Nationwide Urban Runoff Program in 1979 provided an 

excellent opportunity to assess the effects of urban runoff on the Jordan 

River as the principal receiving stream in the county. Cooperative agreements 

were established between the Geological Survey and the Salt Lake County 

Division of Flood Control and Water Quality to: (1) Monitor the storm and 

nonstorm urban runoff in the Salt Lake Valley, for the purpose of 

characterizing its quantity and quality, and (2) investigate specific waterquality problems in the Jordan River. Letters were sent to local, State, and 

other Federal agencies requesting their advice about priorities needed for 

water-quality research on the Jordan River. Based on responses to that 

inquiry, the following problems were selected: dissolved oxygen, toxic 

substances, sanitary quality, and turbidity.

Successful planning for river-basin development requires identification 

of specific flow and water-quality problems and quantification of data 

relating to these problems. Previous river-quality assessments by the U.S. 

Geological Survey on the Willamette River, Oregon, the Chattahoochee River, 

Georgia, and the Yampa River, Colorado, identified an intensive, synoptic 

approach as the best procedure for such quantification. By contrast, routine 

monitoring and surveillance sampling by the Geological Survey on the Jordan 

River during 1974-79 provided an indication of general water-quality trends 

but lacked the specific data necessary to define the quantitative nature of 

recognized water-quality problems. Several of the U.S. Environmental 

Protection Agency studies completed under Section 208 of the Clean Water Act 

obtained data frcm problem-oriented sampling, but most of those studies were 

too short to provide meaningful conclusions. Data frcm previous work were 

combined with information gained frcm short, problem-oriented studies 

conducted from 1980 to 1982 to provide the broadest insight to the four stucty 

problems.

The approach to each of these water-quality problems differed slightly, 

and each study is described in one of the following reports: dissolved oxygen
(Stephens, 1984); toxic substances (Thompson, 1984a); sanitary quality 

(Thompson, 1984b); and turbidity (Weigel, 1984). Hydro-logic data collected 

during the overall investigation appear in Pyper and others (1981) and 

McCormack and others (1983), and some historical data were reported by the 

U.S. Geological Survey (1982, and earlier volumes). The interpretive analysis 

of the effects of urban runoff on surface-water quallity in Salt Lake Valley 

appears in Christensen and others (1984).

The objectives of the water-quality investigations of the Jordan River 

were to define the four problems and to quantify the data relating to these 

problems. This report summarizes the results of the four studies.

Topography and General Hydrology

The Jordan River originates as outflow from Utah Lake and flows north 

approximately 55 miles before it is diverted into marshlands south of the 

Great Salt Lake. The lake serves as the terminal receiving body for the 

Jordan Hydro-logic Accounting Unit, a drainage basin of 3,825 square miles in 

the Great Basin Region (U.S. Geological Survey, 1974). Two-thirds of the 

river miles are within Salt Lake County, the area of this study.

The Jordan River enters Salt Lake County at the Jordan Narrows, a gap in 

the Traverse Mountains, 10 miles downstream from Utah Lake (fig. 1). Hie 

altitude decreases from 4,470 feet at the Jordan Narrows to about 4,200 feet 

at Farmington Bay. The mean gradient of the Jordan River through Salt Lake 

County is 6 feet per mile; although the gradient from the Jordan Narrows to 

4200 South Street is 11 feet per mile and from 4200 South Street to the river 

mouth only 1.9 feet per mile. Salt Lake County includes a dense urban area 

commonly known as the Salt Lake Valley, which is bordered by mountains on 

three sides. The Wasatch Range to the east rises to more than 11,000 feet, 

the Oquirrh Mountains on the west rise to more than 9,000 feet, and the 

Traverse Mountains on the south rise to more than 6,000 feet.

The population of Salt Lake County in July 1981 was estimated to be 

641,000 (Marvin Levy, Utah State Health Department, Bureau of Statistical 

Services, oral commun., 1982), which is 42 percent of the total population of 

the State. The Jordan River is the primary receiving water for most of this 

urban area, including seven municipal wastewater-treatment plants in Salt Lake 

County and one in Davis County to the north.

The seven major tributaries to the Jordan River in Salt Lake County 

originate in the Wasatch Range. Little Cottonwood Creek flows into the Jordan 

River at about 4900 South Street, Big Cottonwood Creek enters at about 4200 

South Street, and Mill Creek enters at 3000 South Street. Parleys, 

Emigration, and Red Butte Creeks all are diverted to a storm conduit which 

discharges into the Jordan River near 1300 South Street. City Creek is 

diverted into a storm conduit which discharges into the Jordan River at North 

Temple Street. Streams on the west side of the Jordan River typically are 

intercepted by canals or cease flowing before reaching the river.

During the irrigation season, large quantities of water are diverted from 

the Jordan River at or near the Jordan Narrows and channeled northward through 

seven major canals. The canals east of the river terminate in smaller canals 

and exchange water with streams that drain the Wasatch Range. Return flows
X

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jQs

iCudahy

0

H

0

1

i i

1 2

2

|

3

3

I

4 MILES

4 KILOMETERS

Lane

112°15V

40°45'

112°00>^"

Figure 1 . Monitoring sites on and major inflow 

sources to the Jordan River in Salt Lake 

County, Utah.

-iIll" 50'

EXPLANATION

WASTEWATER-TREATMENT PLANT

1 Sandy

2 Tri-community

3 Murray

4 Cottonwood

5 Salt Lake City Suburban 1

6 Granger-Hunter

7 South Salt Lake

8 South Davis South

MONITORING SITES ON JORDAN RIVER

APPROXIMATE BOUNDARY

OF VALLEY FILL 

RM40 RIVER MILE (Ward and others, 1957)

UTAH
from canals west of the river typically reach the Jordan River less directly 

as nonpoint-source runoff. Ohe only major diversion north of 9000 South 

Street is at 2100 South Street to the Surplus Canal, which is a flood-control 

structure that allows excess water to pass directly to Great Salt Lake.

Large quantities of ground water enter the upstream part of the Jordan 

River. Ward and others (1957, p. 4) reported an average gain of 7.6 cubic 

feet per second per river mile during November 1957 between the Jordan Narrows 

and 6400 South Street. The average gain from 6400 South Street to 3300 South 

Street was 6.7 cubic feet per second per mile. No gain was measured north of 

3300 South Street. Data reported by Hydroscience, Inc. (1976, p. 23) indicate 

a mean summertime gain of 3 cubic feet per second per mile from 9400 South to 

5800 South Streets and 6.3 cubic feet per second per mile from 5800 South to 

2100 South Streets.

Precipitation

The climate ranges from semiarid in parts of Salt Lake Valley to humid in 

areas of the Wasatch Range. Tfte precipitation during 1981 near the Salt Lake 

International Airport was 16.59 inches (National Oceanic and Atmospheric 

Administration, 1981, p. 4). This was 0.69 inch greater than the 93-year mean 

reported for Salt Lake City by Hely and others (1971, p. 16). Precipitation 

in the low areas of the valley generally is slight and infrequent during the 

growing season; thus, most crops are dependent on irrigation.

Data Collection

Five sites were selected on the Jordan River for continuous-streamflow 

recording and water-quality monitoring during 1980-82 (fig. 1). IVo of the 

sites, 1700 South Street (U.S. Geological Survey station no. 10171000) and 

5800 South Street (station 10167300) have been water-quality-monitoring 

stations since 1974, although continuous discharge was measured at 5800 South 

Street only since 1980. Streamflow at 500 North Street (station 10172550) has 

been monitored since 1975, at 9000 South Street (station 10167230) since 1979, 

and at Jordan Narrows (station 10161001) since 1937.

Water samples were collected monthly from December 1980 through August 

1982. Additional samples of the Jordan River and inflowing streams and 

conduits were collected during storms, as part of the Salt Lake County 

project, and during special synoptic-sampling studies.

DISSOLVED OXXGEN

Dissolved-oxygen depletion in the Jordan River has been a recognized 

problem for many years. Small concentrations of oxygen have resulted in 

decreased fish populations and little recreational use of the river, and it 

also has adversely affected the esthetic appeal of the river, which is the 

largest in Salt Lake County. Dissolved-oxygen concentrations in the river 

typically are near saturation as the water enters the Salt Lake Valley at the 

Jordan Narrows. As the water flows north through the valley, it receives 

secondary-treated effluent from eight municipal wastewater-treatment plants, 

storm runoff from urban areas, and numerous nonpoint-source discharges.
 Hie stucty- of the dissolved-oxygen regime in the Jordan River was 

designed to:

(1) Determine historical trends in dissolved-oxygen concentrations and 

concentrations of oxygen-demanding substances;

(2) Measure reaeration rates and time-of-travel during low flow 

through Salt Lake Valley;

(3) Determine the effects of oxygen production and consumption fcy algal 

on the Jordan River north of 5800 South Street; and

(4) Calculate loads of oxygen-demanding substances discharged fcy storm 

runoff and wastewater-treatment plants.

Data collection and analysis were concentrated between 9000 South and 500 

North Streets where most of the dissolved-oxygen problems occur. Data were 

collected from December 1980 through August 1982, with storm-runoff data 

collected through September 1981. High water conditions existed in the river 

during almost the entire period of data collection, with the annual discharge 

at 2100 South Street being 18 to 40 percent greater than the average for the 

preceding 10 years.

Few data are available for dissolved-oxygen concentrations in the Jordan 

River prior to the popularization of the polarographic-oxygen probe in the 

1970's. Gaufin (1958, p. 5-8) measured dissolved-oxygen concentrations of 0 

to 15.3 milligrams per liter at 17 sites, and he concluded that north of 4800 

South Street (river mile 25.2) the river was so polluted that the fish 

population was limited to carp. An intensive survey by the U.S. 

Environmental Protection Agency (1972, p. 18) reported the average dissolvedoxygen concentrations in the river south of 3300 South Street (river mile 

21.5) during August and September equaled or exceeded the State limits of 5.5 

milligrams per liter for a warm-water fishery and 6 milligrams per liter for a 

cold-^ater fishery. North of 2100 South Street, the dissolved-oxygen 

concentrations in the river failed to meet the State standards for either type 

of fishery. Comparison of data collected from 1976-79 with data from 1979-81 

indicated that small dissolved-oxygen concentrations were a problem in the 

Jordan River from the Jordan Narrows to North Temple Street during both 

periods, with no significant changes in dissolved-oxygen concentrations noted 

between data sets (Gunnell and others, 1982, p. 6, 62).

Trends in Dissolved-Qxygen Concentration and Oxygen Demands

Comparison of synoptic measurements of dissolved-oxygen concentrations 

made during the late summer from 1957-82 illustrates the progressive decrease 

in dissolved-oxygen concentrations as the river flows north from the Jordan 

Narrows (fig. 2). The few data available indicate the greatest decrease in 

dissolved-oxygen concentrations during 1972, 1981, and 1982 as compared to 

1957 and 1975. Comparison of a larger data set available for the Jordan River 

at 1700 South Street indicates a general decrease in mean dissolved-oxygen 

concentrations from 1974-82 for samples collected from April to September 

(fig. 3). A similar decrease also was noted for dissolved-oxygen 

concentrations at 5800 South Street from 1974-82, and the percent saturation 

of oxygen decreased correspondingly at both sites during the same time period.
cc 

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DATE OF COLLECTION 

 September 25, 1957 

August 14, 1972 

September 25, 1975

A--A--A August 12, 1981 

H- August 24, 1982

DIRECTION OF FLOW

5 -

4 -

20 25 30 

RIVER MILE, UPSTREAM FROM MOUTH

Figure 2. Variation in dissolved-oxygen concentrations with river mile during low-flow 

conditions from 1957 to 1982. From Stephens (1984).
12

11

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X

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MAXIMUM

MEAN 

-^MINIMUM

/ -L

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1974 1975 1976 1977 1978 1979 1980 1981 1982

Figure 3. Variation in dissolved-oxygen concentrations during daytime 

at 1700 South Street, April-September 1974-82. From Stephens (1984).
Data collected during October-March at 1700 South Street indicated a 16- 

percent decrease in mean dissolved-oxygen concentrations from 1974-77 , a 16- 

percent increase from 1977-80, and a 10-percent decrease during 1981.

The decrease in dissolved-oxygen concentrations downstream of 5800 South 

Street was accompanied by increases in oxygen-demanding substances as measured 

by chemical-oxygen demand (ODD) and biochemical-oxygen demand (BOD). The mean 

ODD increased 23 percent between 5800 South Street and 500 North Street. The 

mean 5-day BOD (6005) increased from 7 milligrams per liter at 5800 South 

Street to 12 milligrams per liter at 1700 South Street then decreased to 7 

milligrams per liter at 500 North Street. The winter mean BODs increased from 

9 to 17 milligrams per liter between 5800 South and 500 North Streets. The 

mean BODs increased 90 percent between the Jordan Narrows and 500 North 

Street.

Dissolved-oxygen concentrations and percent saturation were consistently 

greater at all sites during the winter. That was due to the increased 

solubility of oxygen at lower temperatures and the reduced satisfaction of 

oxygen demands in the river at lower temperatures. Dissolved-organic carbon 

(DOC) and BOD were noticeably greater during in the winter because the oxygen 

demands required to stabilize the organic substances were not exerted in the 

river at low temperatures. The effects of small oxygen concentrations and 

large organic loads on the Jordan River may be summarized lay the frequency of 

noncompliance with State intended-use standards (Utah Department of Social 

Services, Division of Health, 1978, p. 8). About 50 percent of all dissolvedoxygen measurements made during 1981-82 at or downstream of 5800 South Street 

and from 60-90 percent of all BODs measurements failed to comply with the 

standards (table 1).

Multiple-regression analysis was used to identify specific independent 

variables that affected the dissolved-oxygen concentrations at each site. 

Water temperature was a significant variable that was inversely related in 

several equations, reflecting the inverse relationship of solubility and 

temperature. Discharge was positively correlated with dissolved-oxygen 

concentrations which represents association of larger reaeration rates with 

increased discharge and the dilution of oxygen-demanding substances lay 

increased streamflow. The regression analysis indicated that part of the 

summertime BOD at the Jordan Narrows was due to the respiration and decay of 

ptytoplankton transported from Utah Lake.

Reaeration Rates and Time-of Travel

Reaeration is the principal process lay which oxygen is transported into 

the water. The rate of reaeration is dependent on the temperature, depth, and 

turbulence of the water and the concentration of other dissolved substances. 

Measurements of reaeration rates in the Jordan River were made during periods 

of low flow in September and October 1981 and 1982 using the modified tracergas method of Rathbun (1979). Rhodamine-WT dye was used to establish 

dispersion characteristics and to provide information on time-of-travel for 

various reaches of the river. The general trend for the reaeration rate (K2, 

in dimensionless units per day) was to decrease with distance downstream and 

decreasing channel slope. The channel of the Jordan River has a marked change 

in slope near river mile 24, near the confluence with Big Cottonwood Creek
Table 1. Frequency of noncompliance with water-quality standards for 

intended use, 1981-82 (Utah Department of Social Services, 

Division of Health, 1978, p. 8

Dissolved oxygen: Standards are 6 milligrams per liter for the Jordan Narrows 

and 9000 South and 5800 South Streets, and 5.5 milligrams per liter for 

the other sites.

Five-day biochemical-oxygen demans: Standard is 5 mg/L at all sites. 

Nonccmpliance frequency: Percentage of total number of measurements.

Dissolved oxygen 5-day biochemicaloxygen demand

Site

Total number Noncompl iance Total number Noncompl iance 

of measurements frequency of measurements frequency

Jordan Narrows 

9000 South Street 

5800 South Street 

1700 South Street 

500 North Street

29

32

51

61

62

3

0

10

46

52

27

23

26

23

25

44

39

58

87

92

10
(fig. 4). Upstream frcm this point, the reaeration rate averaged 9.5 per day, 

with a travel time of 10.5 hours to flow 11.6 miles from 12300 South Street. 

Discharge in this reach ranged from 84 to 203 cubic feet per second. Between 

4800 South and 1800 North Streets, the reaeration rate averaged only 1.8 per 

day, with a travel time of 15.4 hours to traverse the 16.4-mile reach.

Effects of Algal Populations

Suspended algae (phytoplankton) and attached algae (periphyton) produce 

oxygen as a by-product of photosynthetic activity during daylight. They 

consume oxygen through respiration at all times, but more noticeably at night. 

Phytoplankton populations are quite large in Utah Lake, and much of this algal 

material is present in the Jordan River, particularly at the Jordan Narrows. 

Phytoplankton chlorophyll a, the major photosynthetic pigment, decreased from 

a summer mean concentration of 35 milligrams per liter at the Jordan Narrows 

to about 10 milligrams per liter at 500 North Street. Diel (24-hour) 

production of oxygen was monitored at several sites from 5800 South to 500 

North Streets during July and September 1981 and January 1982 but no net gain 

was detected in dissolved-oxygen concentrations in the river due to algal 

photosynthesis. An oxygen demand ranging from 11 to 22 milligrams per liter 

was measured on July 28, 1981, in this reach. Net gains in dissolved oxygen 

due to photosynthesis south of 9000 South Street are indicated by the data 

assembled by Gauf in (1958), U.S. Environmental Protection Agency (1972, p. 

14), and Hydroscience, Inc. (1976, p. 47). Application of diel-curve analysis 

to data collected by Gauf in (1958, p. 50-54) and the U.S. Environmental 

Protection Agency (1972, p. 62) indicated no net gains of oxygen during a 24- 

hour period at any site where measurements were made north of Fairfield Road, 

which is 5 miles south of the Jordan Narrows.

Effects of Storm Runoff and Wastewater-Treatment Plants

Mean concentrations of BODs, ultimate BOD (BODy) r ODD, and organic carbon 

were slightly greater in storm samples than in nonstorm samples collected from 

the Jordan River. Statistical evaluation of these differences using Student's 

t-test (95-percent confidence level) indicated that only the concentrations of 

dissolved- and suspended-organic carbon (DOC and SOC) were significantly 

greater. When analyzed on a site basis, all sites except 500 North Street 

showed decreases in dissolved-oxygen concentrations during storms; but not all 

differences were statistically significant. Analysis of the data for 500 North 

Street indicated that an increase in dissolved-oxygen concentrations occurs 

during storms due to an increase in oxygenated water that enters the river 

upstream through storm conduits at 1300 South and North Temple Streets.

Considerable quantities of oxygen-demanding substances were discharged to 

the Jordan River annually in storm runoff. The quantities of these substances 

from point sources, based on inflow during 10 major rain-storms during 1981 

are summarized in table 2. More than 80 percent of the BOD entered the river 

downstream from Big Cottonwood Creek (river mile 24) in the reach that has the 

smallest reaeration rate and the least assimilation capacity for oxygendemanding substances.

11
10 15 20 25 30 

RIVER MILE, UPSTREAM FROM MOUTH

Figure 4. Profile of the river channel with selected reference points, travel times, a

rates (l<2 ) Modified from Stephens (1984).
Table 2. Estimated total loads for annual-storm runoff from the major 

tributaries and storm conduits during 10 storms in 1981, in pounds of 

oxygen-demanding substances

5-day biochemical-oxygen demand: Values in parentheses represent that part 

of the load contributed by wastewater-treatment plants discharging to the 

2100 South Conduit and Big Cottonwood Creek.

5-day 

biochemicaloxygen 

Site demand

North Temple

Conduit

800 South

Conduit

1300 South

Conduit

2100 South

Conduit

Mill Creek

Big Cottonwood

Creek

Little

Cottonwood

Creek

9000 South

Conduit

Totals

2,500

1,800

5,500

3,400

(1,700)

8,000

27,200

(23,000)

6,800

2,300

557,500

(24,700)

Ultimate 

biochemical- Chemical Dissolved- Suspendedoxygen oxygen organic organic 

demand demand carbon carbon

4,800

3,600

11,300

7,300

16,500

47,600

15,700

3,600

110,400

22,300 2,200 1,000

13,700 1,100 1,100

44,900 12,200 3,800

15,600 2,600 600

64,000 13,500 3,600

68,200 16,000 5,900

51,000 27,900 2,000

21,100 7,000 19,300

300,800 82,500 37,300

13
Of the seven wastewater-treatment plants in Salt Lake County that 

discharge directly or indirectly to the Jordan River only the South Salt Lake 

plant is not hydraulically overloaded (Gunnell and others, 1982, p. 61). The 

mean daily load of BOD5 discharged from the seven plants in 1981 was 

calculated as nearly 13,000 pounds, with 85 percent of this load entering the 

river downstream of river mile 25, where reaeration rates are decreased. The 

projected annual load of BOD5 from the seven wastewater-treatment plants 

during 1981 was 4.7 million pounds. The stucty was confined to Salt Lake 

County, therefore, loads were not calculated for the South Davis South 

wastewater-treatment plant.

A total annual BOD^ load of 6 million pounds was calculated as the sum of 

the major point sources that discharged to the Jordan River during 1981 (fig. 

5). The wastewater-treatment plants contributed 77 percent of this load, 

nonstorm baseflows from the major tributaries contributed 22 percent, and 

storm runoff contributed less than 1 percent. The storm-runoff load was based 

on 10 major storms and it could be a conservative estimate. Doubling the 

stormflow load however, would make little relative change in the total load 

from point-sources that enters the Jordan River.

The travel time of about 1 day between 9000 South and 500 North Streets 

resulted in only a part of the total-oxygen demand being actually satisfied in 

the river. Not all the oxygen-demanding substances are in the dissolved 

phase, and some particle aggregation and sedimentation produces the dark 

organic silts found in much of the river bottom. The accumulation of these 

oxygen-demanding sediments has long-term effects on the oxygen regime in the 

river.

The diversion to the Surplus Canal at 2100 South Street also decreases 

the total load of oxygen-demanding substances in the river. During the 1981 

water year (October 1, 1980 to September 30, 1981), the total diversion to the 

Surplus Canal was 309,800 acre-feet, which was 72 percent of the flow in the 

Jordan River upstream from the diversion. Ninety percent of the total BODc 

load was discharged to the river from point sources between 9000 South and 

2100 South Streets. Therefore, the Surplus Canal diverted about 4 million 

pounds of BOD5 load from the river during 1981. The load in the Jordan River 

between 2100 South and 500 North Streets, therefore, was reduced to about 2 

million pounds.

The increase in population in Salt Lake County is expected to result in 

the production of even greater loads of oxygen-demanding substances, which 

will further decrease the oxygen concentrations in the Jordan River. Without 

additional wastewater-treatment plants and improvements in the existing 

plants, considerable impairment of the Jordan River oxygen regime likely will 

occur.

14
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13.2 15.1 16.4 18.0 20.3 20.5 20.6 24.0 24.7

RIVER MILE, UPSTREAM FROM MOUTH

25.2 29.0 31.7 31.8

Figure 5.-Total annual loads of oxygen-demanding substances, as measured by 5-day 

biochemical-oxygen demand discharged during 1981 from point sources. From 

Stephens (1984).

15
TOXIC SUBSTANCES

The concern with toxic substances in water steins fron an increased public 

awareness of the carcinogenic, mutagenic, and chronic effects of exposure to 

water-born elements and compounds. The identification of 129 elements and 

compounds as priority pollutants and the 1976 court settlement requiring the 

U.S. Environmental Protection Agency to establish water-quality criteria for 

them (Keith and Telliard, 1979) demonstrated the diverse nature of toxic 

substances that are transported in water.

The stucty of toxic substances in the Jordan River was designed to:

(1) Identify toxic substances that exceed State intended-use standards in 

the Jordan River and major tributaries;

(2) Measure differences between the dissolved phase and the suspended 

phase of selected toxic substances;

(3) Determine selected pesticide concentrations in the Jordan River and 

major tributaries;

(4) Determine concentrations of selected toxic substances in bottom 

materials of the Jordan River and major tributaries;

(5) Identify toxic substances that may be transported to the Jordan River 

as a result of storm runoff frcm urban areas.

The five primary monitoring sites along the Jordan River used in this 

study were: (1) Jordan Narrows; (2) 9000 South Street; (3) 5800 South Street; 

(4) 1700 South Street; and (5) 500 North Street (fig. 1). Sampling also was 

done at three major tributary inflows to the Jordan River: Little Cottonwood, 

Big Cottonwood, and Mill Creeks. Storm runoff frcm urban areas was sampled at 

the following major storm drains to the river: 1300 South, north and south 

conduit; 800 South conduits, north, middle, and south conduit; and North 

Temple conduit.

No comprehensive studies have dealt specifically with toxic substances in 

the Jordan River. Several general studies have reported concentrations of the 

more common toxic substances such as ammonia (Hydr©science, Inc., 1976; Way, 

1977), pesticides (Coburn, 1972; Salt Lake County Soil Conservation District, 

1981), and common trace metals (U.S. Environmental Protection Agency, 1972; 

Salt Lake County Soil Conservation District, 1981).

Identification and Distribution of Toxic Substances

About one-half of the substances for which State intended-use standards 

have been established were not detected in concentrations that exceeded the 

standard during 1981-82. Among these, analyses for arsenic (16 samples), 

boron (27), chronium (131), endrin (27), lindane (6), phenol (25), selenium 

(38), silver (38), and toxaphene (6) indicated that these substances did not 

appear to constitute a hazard in the Jordan River or its three major 

tributaries. State standards have not been established for many other 

substances which are known to be toxic.

16
Reconnaissance during this stucfy identified several toxic substances 

(table 3) which were present in the Jordan River and the three major 

tributaries at concentrations exceeding the State standards.

Ammonia, which is a natural degradation product of nitrogenous-organic 

matter, is toxic to fish and creates an oxygen demand in the water. The State 

standard of 20 micrograms per liter of ammonia (as nitrogen) is based on the 

presence of the un-ionized form, NH3 , which is the most toxic. lonization of 

ammonia in water is dependent on temperature and pH as the temperature or pH 

increases, the degree of ionization decreases. In warm, alkaline waters a 

greater proportion of a given concentration of dissolved ammonia will be 

present in the toxic, un-ionized form than in cooler, less alkaline water. 

Eighteen percent of the samples fron the Jordan River and its major 

tributaries that were analyzed for ammonia had concentrations in excess of the 

State standard. Most of the problem concentrations of ammonia are just 

downstream fran the wastewater-treatment plants.

Cadmium exceeded State standards in 9 percent of the samples fron the 

Jordan River and its principal tributaries. Eighty-six percent of the 

samples that were collected in the storm conduits during storms, however, 

exceeded a concentration that is similar to State standards (table 4). Most 

of the storm conduits discharge to the river downstream of 2100 South Street, 

but most of the samples that exceeded the State cadmium standard were 

collected at 9000 South Street.

Cyanide, and iron typically are present in concentrations that do not 

exceed the State standards in the Jordan River, its major tributaries, and 

conduits that discharge to the river (tables 3 and 4). Copper concentrations 

in excess of the State standard were detected in only 9 percent of the river 

and tributary samples but were common in storm runoff in the conduits. A 

similar relationship was determined for lead, which exceeded State standards 

in only 2 percent of the river and tributary samples but exceeded them in 83 

percent of the storm-runoff samples.

17
Table 3. Occurrence of constituents that exceeded State intended-use 

standards in the Jordan River and three major tributaries

Constituent

Total number 

of samples

Number of samples

in which State

standards were

exceeded

Mean of concentrations 

that exceeded State

standards 

(micrograms per liter)

Ammonia, dissolved

Cadmium, dissolved

Copper, dissolved

Cyanide, dissolved

Iron, dissolved

Lead, dissolved

Mercury, total

Zinc, dissolved

85

228

228

45

213

213

138

220

15

20

20

1

1

4

107

13

NA1

3.1

15.4

-

-

64.5

.17

103

Not applicable. Concentrations of un-ionized ammonia that exceeded 

State standards are determined by calculation using known values for 

temperature, pH, and ammonia concentration.

18
Table 4. Frequency of occurrence of constituents that exceeded selected 

concentrations in samples from conduits

Number of samples. A dash ( ) indicates that no sample exceeded the 

selected concentrations

First line Total number of samples that exceeded selected

concentrations

Second line Number of above samples collected during storm runoff 

Third line Total number of samples

Cadnium, Chronium, Copper, Cyanide, Iron, Lead, Mercury, Zinc, 

dis- dis- dis- total dis- dis- total dissolved solved solved solved solved solved

Selected concentration (micrograms per liter' 1

Conduit

9000 South 2

2100 South

1300 South

South Conduit

1300 South

North Conduit

800 South

South Conduit

800 South

Middle Conduit

800 South

North Conduit

North Temple

12

6

5

27

18

__

19

 

20

__

20

___

19

. .

21

1

1

18

100

10

7

__

8

-~

8

__

6

__

9

1

0

9

9

10

Number

9

6

27

14

9

18

5

5

17

3

2

19

3

3

20

4

3

18

5

5

21

3

2

18

5 1,

of Samples

1

1

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1

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1

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1

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1

1

1

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27

17

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19

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19

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20

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18

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0.05

12

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7

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7

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4

8

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4

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9

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7

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1

1

18

1 Selected concentrations are similar to State standards; however, State 

standards do not apply in these conduits.

2 A concentration of 1.2 micrograms per liter of cadmium was used at the 

9000 South Street conduit to agree with the State 3A standard for the Jordan 

River near 9000 South Street.

19
Concentrations of total mercury exceeded the State standards in 78 

percent of the samples from the Jordan River and its three principal 

tributaries. Eighty-seven percent of the samples collected from storm 

conduits exceeded a total-mercury concentration of 0.05 microgram per liter. 

This represents a conservative estimate of the problem because the analytical 

detection limit for total mercury is 0.1 microgram per liter whereas the 

standard is 0.05 microgram per liter.

Dissolved-zinc concentrations occasionally did not meet the standards in 

the Jordan River and tributary samples, but concentrations in excess of 50 

micrograms per liter were observed in 84 percent of all storm samples from the 

storm drains.

Transport of Trace Elements

Standards for toxic substances may be given in the dissolved, total, or 

total-recover able phase. The U.S. Environmental Protection Agency (1976) 

presents standards for trace elements in either the total or total-recoverable 

phase. Standards established by the State of Utah are primarily for dissolved 

constituents (Utah Department of Social Services, 1978, appendix A). More 

than 90 percent of the arsenic, selenium, and silver, and more than 70 percent 

of the barium and mercury transported in the Jordan River during 1980-81 was 

in the dissolved phase. Ninety-eight percent of the iron was transported in 

the suspended phase.

Mean daily discharges were determined for nonstorm periods and total 

loads of 13 trace elements were calculated at each of the five monitoring 

sites. The mean load for each constituent was then determined as the average 

of the loads at the five sites. Ihe mean load of iron for all sites was 110 

pounds per day, with boron at about 31 pounds per day, zinc at 8 pounds per 

day, and lead at about 5 pounds per day. Loads of other trace elements were 

less than 5 pounds per day.

Toxic-Organic Substances in the Water

Water samples collected during August 1981-82 from the five sites on the 

Jordan River and from Little Cottonwood, Big Cottonwood, and Mill Creeks were 

analyzed for the following 19 pesticides and total poly chlorinated biphenyls 

(KB):

Aldrin Chlordane ODD

DDE DDT Dieldrin

Endosulfan Endrin Heptachlor

Heptachlor epoxide Lindane Mirex

Napthalenes, polychlorinated PCE Silvex

Perthane 2,4-D 2,4-DP

Toxaphene 

2,4,5-T

The only pesticides detected in water from the Jordan River were DDE at a 

concentration of 0.01 microgram per liter at the 1700 South Street site, 2,4-D 

at 0.02 microgram per liter at the Jordan Narrows, and silvex at 0.01 

microgram per liter at the 1700 South and 500 North Street sites. Silvex was

20
detected at 0.02 microgram per liter at Big Cottonwood Creek at the Jordan 

River, and 2,4-D at 0.06 microgram per liter at Little Cottonwood and Big 

Cottonwood Creeks at the Jordan River.

Water samples collected during nonstorm periods during June and August 

1982 were analysed for 27 of the 31 volatile organic conpounds identified by 

the U.S. Environmental Protection Agency as a subcategory of priority 

pollutants (Keith and Telliard, 1979, p. 418). Tetrachloroethylene was 

detected at 500 North Street in concentrations of 5 and 1 micrograms per liter 

during both sampling periods. No other volatile organic conpounds were 

detected.

Toxic Substances in Bottom Materials

The accumulation of 11 trace elements in bottom sediments was 

investigated at five sites on the Jordan River and in the three principal 

tributaries. Mean concentrations of the trace elements were smaller at the 

Jordan Narrows and 9000 South Street than at the three downstream river sites 

or in the tributaries (table 5). Concentrations of arsenic, cadmium, 

chronium, copper, lead, mercury, and zinc increased substantially at 5800 

South Street, and the larger concentrations persisted downstream. Mean 

concentrations of arsenic, cadmium, and chromium in the bottom materials 

generally were twice as large at the three downstream sites as at the Jordan 

Narrows and 9000 South Street. Mean concentrations of copper and zinc were 

six times greater, and lead was eight times greater at the three downstream 

sites. Concentrations of beryllium, selenium, and silver were near detection 

limits and never exceeded 3 micrograms per gram. Analyses for cobalt were 

made only on one sample from each of the five sites, and concentrations ranged 

from less than 5 to 30 micrograms per gram.

Concentrations of most of the trace metals in the sediments in the three 

principal tributaries were similar to concentrations in the sediment of the 

Jordan River at the three downstream sites (table 5). Concentrations of zinc 

were about 50 percent greater, however, and concentrations of copper were 

about 23 percent less in the tributaries.

Analyses were made for 17 pesticides and (PCB) in bottom materials from 

five sites on the Jordan River and from the mouths of the three principal 

tributaries. Only 9 of the possible 18 compounds were detected at least once 

in any of the samples. The compound most frequently detected was PCB, in the 

bottom materials. Sampling on two dates detected concentrations of PCB (320 

and 230 micrograms per kilogram) at the Jordan Narrows. Concentrations of PCB 

in the bottom materials at the downstream sites did not exceed 50 micrograms 

per kilogram.

Chlorinated-hydrocarbon pesticides and their degradation products such as 

DDT, ODD, DDE, dieldrin, and methoxychlor were detected in the bottom 

materials at most sites downstream of the Jordan Narrows. Concentrations of 

these compounds generally did not exceed 15 micrograms per kilogram. A sample 

of bottom material from Big Cottonwood Creek at the Jordan River, however, 

contained a 2,4-D concentration of 320 micrograms per kilogram.

21
Table 5. Mean concentrations of selected trace elements in bottom materials

in the Jordan River and three tributaries

Location

Trace elements (micrograms per gram)

Arsenic Cadmium Chromium Copper Lead Mercury Zinc

Jordan Narrows 6.0 

and 9000 South 

Street

5800 South, 13.0 

1700 South, 

and 500 

North Streets

Little Cottonwood, 15.0 

Big Cottonwood, 

and Mill Creeks

Jordan River 

1.0 2.5 10.0 25.0 0.03 32.5

2.0 5.5 64.5 192.5 .05 186.9

Tributaries 

2.0 7.3 49.7 191.4 .04 282.9

22
Priority Pollutants in Storm Runoff

The possible occurrence of the 129 priority pollutants (except dioxin and 

asbestos) in urban-storm runoff was investigated during a storm on October 29, 

1981. Samples were collected from conduits discharging to the Jordan River at 

1300 South, 800 South, and North Temple Streets. Only 2 of the 113 organic 

pollutants analyzed for were detected in the sampling. Chloroform, at 12 

micrograms per liter, was found in the 800 South Street middle conduit; and 

phenol, at 10 to 30 micrograms per liter, was detected in all conduits except 

the 800 South Street middle conduit. Analyses for cyanide, phenol, and 13 

trace metals, all of which are included in the priority pollutants, showed 

large concentrations of lead and zinc in samples from most of the storm 

conduits. The mean concentrations for the six conduits was 194 micrograms per 

liter for lead and 152 micrograms per liter for zinc. These concentrations 

are 4 and 3 times, respectively, the limits of State standards for the Jordan 

River.

Analyses were made for an additional 13 trace metals, which are not 

classified as priority pollutants. Concentrations of these metals typically 

were less than 150 micrograms per liter. Exceptions were total aluminum, with 

a mean concentration of 4,633 micrograms per liter for the six conduits; total 

iron, 4,420 micrograms per liter; and total strontium, 257 micrograms per 

liter. Ohe large concentrations of these metals probably indicate large 

quantities of soil particles in the storm runoff. Nearly 90 percent of the 

strontium concentrations was present in the dissolved phase.

SANITARY QUALITY 

The stucty of the sanitary quality of the Jordan River was designed to:

1. Determine the extent of sanitary (bacteriological) contamination. 

A. Identify contaminated stream reaches. 

B. Identify probable sources of contamination.

2. Determine trends of sanitary quality in the river.

3. Determine effects of storm runoff from urban areas on the sanitary 

quality of the river.

Data used in this stucty were collected by the U.S. Geological Survey and 

the Salt Lake City-County Health Department. The data collected by the 

Geological Survey were published in P^per and others (1981) and McCormack and 

others (1983). Ohe data collected by the Salt Lake City-County Health 

Department are available primarily as unpublished laboratory analyses.

Due to the difficulty of isolating and identifying pathogenic organisms 

from water, the appearance of common nonpathogens typically is used as an 

indicator of sanitary quality. Historically, the total coliform group has 

been used as an indicator; but recently, fecal coliform and fecal streptococci 

bacteria have been used more generally as they are more specific indicators of 

sources of contamination. Ratios of concentrations of fecal streptococci to 

fecal coliform bacteria are used to distinguish between human and non-human 

sources of contamination.

23
Ml bacterial studies of the Jordan River since the early 1970's have 

concluded that coliform densities increase downstream from the Jordan Narrows 

(U.S. Environmental Protection Agency, 1972; Templeton, Linke, Alsup, and 

Engineering-Science, Inc., 1974; Salt Lake County Water Quality and Water 

Pollution Control, 1978). Concentrations of total coliforms downstream from 

9000 South Street were always greater during the irrigation season (Salt Lake 

County Soil Conservation District, 1981), and agricultural sources were 

believed to be responsible for 1,000 organisms per 100 milliliters of the 

total bacterial concentrations detected (Hydroscience, Inc., 1976). Six of 

the seven wastewater-treatment plants in Salt Lake County are hydraulically 

overloaded (Gunnell and others, 1982, p. 61), which results in decreased 

treatment efficiency and increased bacterial concentrations. The plants were 

estimated to contribute 1,000 to 6,000 total coliforms per 100 milliliters of 

the measured concentrations in the downstream reaches of the Jordan River by 

Hydroscience, Inc., (1976). Nonstorm runoff from the conduits upstream from 

2100 South Street was responsible for as much as 15,000 total coliforms per 

100 milliliters of the total concentrations in the river (Hydroscience, Inc., 

1976).

Distribution of Bacterial Contamination

The 1980-82 stucty of sanitary conditions in the Jordan River found that 

concentrations of indicator bacteria increased markedly as the river flowed 

north through Salt Lake County (figs. 6-8). Great variability typically is 

observed in most biological data, and such variability was a dominant factor 

in all the sanitary data analyzed for this study. The coefficient of 

variation for the bacterial data collected from the Jordan River ranged from 

130 to 350 percent. Mean concentrations of coliform bacteria in the river at 

the Jordan Narrows were fairly large, ranging from 82 colonies per 100 

milliliters for fecal coliforms to 7 f320 for total coliforms. The greatest 

increase in the coliform groups was downstream of 9000 South Street. Fecal 

streptococcal bacteria showed only a gradual increase from a mean of about 

1,500 colonies per 100 milliliters at the Jordan Narrows to about 2,900 

colonies per 100 milliliters at 1700 South Street. Within the 5-mile reach 

from 1700 South to 500 North Streets, the mean increased to more than 11,000 

colonies per 100 milliliters, primarily due to inflow from the conduits at 

1300 South, 800 South, and North Temple Streets.

The Jordan River in Salt Lake County is classified as 2-B (Utah 

Department of Social Services, 1978, p. 45), which establishes standards 

protecting the water for boating, water skiing, and similar uses, excluding 

bathing. Bacterial standards for this class include a maximum 30-day 

geometric mean of 5,000 total coliform colonies per 100 milliliters and a 

maximum of 2,000 fecal coliform colonies per 100 milliliters. Although these 

are geometric means, they are useful as relative indicators of unacceptable 

limits for individual samples. The frequency with which coliform samples 

exceeded the State standard increased downstream of 9000 South Street (fig. 

9). Nearly 75 percent of the samples for total coliform and 45 percent of 

those for fecal coliform samples collected at 500 North Street exceeded the 

State standards. There are no standards for fecal streptococcal bacteria, but 

the ratio of concentrations of fecal coliform to fecal streptococcal bacteria 

can be used as an indicator of sources for the bacteria (American Public 

Health Association and others, 1980, p. 819). Ratios greater than 4.1 are 

typical of pollution derived from human wastes; and ratios less than 0.7 are 

indicators of nonhuman sources, such as domestic animals.

24
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10 15 20 25 30 35

RIVER MILE, UPSTREAM FROM MOUTH

40 45

Figure 7. Mean concentration and one standard deviation for fecal coliform 

bacteria at five sampling sites. From Thompson (1984b).

26
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£ 18,000 f- Io 16,000

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40 45

Figure 8. Mean concentration and one standard deviation for fecal streptococcal 

bacteria at five sampling sites on the Jordan River. From Thompson (1984b).

27
N) 

00

o

Ti o CQ'

o . 3 «

S S'

o <

3 I

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?| ° 5 g ^ CO ^

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PERCENTAGE OF SAMPLES

J5> Ul O5 

O O O

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O^ Q)

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oJordan Narrows
Ninety-two percent of the samples collected at the Jordan Narrows had 

ratios of concentrations of fecal coliform to fecal streptococcal bacteria 

that were less than 0.7 (fig. 10). This decreased to about 50 percent at 5800 

South Street and sites downstream (fig. 10). The percent of samples with 

ratios indicative of human wastes (greater than 4.1) increased frcm 0 at the 

Jordan Narrows and 9000 South Street to 20 percent at 1700 South, then 

decreased to less than 10 percent at 500 North Street. The increase 

corresponds closely with the distribution of seven wastewater-treatment plants 

in the reach from 9000 South and 1700 South Streets. The ratio is useful only 

where the travel time from the source is less than 24 hours. Under low-flow 

conditions in the Jordan River, travel times in this reach are considerably 

less than 1 day; therefore, this ratio should provide a valid indicator of 

contamination.

Sources of Bacterial Contamination

The Jordan River as it enters Salt Lake Valley at the Jordan Narrows, 

contains significant concentrations of total coliform and fecal coliform 

bacteria. The most probable source of this contamination is Utah Lake. A 

report by Environmental Eynamics, Inc., (1975) listed mean total coliform 

concentrations collected at seven sites in Utah Lake during 1968-70. The 

maximum mean, total coliform concentration in 1970 was 6,439 colonies per 100 

milliliters at a site near the northeast shore.

Wastewater-Treatment Plants

ftie seven wastewater-treatment plants that discharge secondary effluent 

to the Jordan River in Salt Lake County were a major source of sanitary 

contamination (table 6). Mean total coliform concentrations ranged from 5,790 

to 125,500 MFN (most probable number) per 100 milliliters and mean fecal 

concentrations ranged from 37 to 62,850 MPN per 100 milliliters. The maximum 

concentrations of both total and fecal coliforms reached 240,000 MHJ per 100 

milliliters. The data showed considerable variability, with the coefficient 

of variation typically greater than 100 percent.

Tributary Streams

Mean concentrations of total coliform bacteria in Little Cottpnwood, Big 

Cottonwood, and Mill Creeks during nonstorm periods were all significantly 

less than the concentrations in the Jordan River near the confluence with 

these creeks. Big Cottonwood Creek had the greatest mean with 8,940 colonies 

per 100 milliliters, which was greater than the State 2-B sanitary standard of 

5,000 colonies per 100 milliliters. Means for Little Cottonwood and Mill 

Creeks were 2,490 and 2,030 colonies per 100 milliliters. TVo of 11 samples 

exceeded the standard for Little Cottonwood Creek, 3 of 11 samples exceeded 

the standard for Big Cottonwood Creek, and none of the samples from Mill 

Creek exceeded the standard.

29
PERCENTAGE OF SAMPLES

CO 

O

(71 

O

0> 

O

500 North Street

1700 South Street

5800 South Street

9000 South Street

Jordan Narrows
Table 6. Summary of ooliform concentrations discharged by waatewater-treatment 

plants in Salt Lake County for the period September 1980 to October 1982

Wastewater- Sandy Tri- Murray Cottonwood Granger- Salt Lake South Salt

treatment Community Hunter City Lake

plant Suburban 1

River mile SiUT 2SLO 24?7 24To 2o7e2oTl 18.0

TOTftL CDLIPORM 

Number of

samples 16 19 18 19 19 19 17

Mean

(colonies 31,040 125,500 5,790 104,430 71,010 64,390 6,230

per 100

millilters)

Coefficient of

variation 263 91 196 114 150 115 139 

(percent)

FECAL OOLIFORM 

Number of

samples 14 19 17 19 18 19 17

Mean

(colonies 200 16,300 37 62,850 22,310 3,310 2,230 

per 100 

milliliters)

Coefficient of

variation 207 334 161 159 256 321 278 

(percent)

31
Mean fecal coliform concentrations were 660 colonies per 100 milliliters 

for Little Oottonwood Creek, 2,670 for Big Cottonwood Creek, and 700 for Mill 

Creek. The frequency of samples that exceeded the fecal coliform standard of 

2,000 colonies was zero for Little Cottonwood Creek, 1 of 6 for Mill Creek, 

and 4 of 8 for Big Cottonwood Creek. The ratio of concentrations of fecal 

coliform to fecal streptococcal bacteria generally was between 0.7 and 4.4 for 

all three creeks, indicating that the bacteria were from mixed human and 

nonhuman sources.

Storm samples collected from Little Cottonwood Creek had significantly 

greater mean concentrations of fecal coliform and fecal streptococcal bacteria 

than nonstorm samples (table 7). Means of the three bacterial types were 

significantly greater in storm samples collected from Mill Creek than in 

nonstorm samples.

rends in Sanitar

Considerable data for bacterial concentrations since 1974 are available 

for sites at 5800 South and 1700 South Streets. Data collected before and 

after July 1980 were grouped as "recent" and "historical" data to determine if 

bacterial concentrations had increased. A group comparison t-test at the 95- 

percent confidence level indicated no significant differences between the two 

periods at 5800 South Street. A possible explanation for the lack of 

differences was the great variability of the data. At 1700 South Street, 

concentrations of fecal coliform and fecal streptococcal bacteria were 

significantly greater in samples collected after July 1980. A siginif icant 

positive correlation was found at this site between concentrations of fecal 

coliform bacteria and time, with a correlation coefficient of 0.5. The 

increase with time and the variability in data are shown in figure 11. The 

mean concentration of fecal streptoccal bacteria at 1700 South Street for 

1974-82 was 1,610 colonies per 100 milliliters and for 1980-82, it was 2,870 

colonies per 100 milliliters.

Effects of Storm-Water Discharges

Runoff discharged to the Jordan River in the conduits contained large 

concentrations of indicator bacteria (fig. 12). Large concentrations of total 

coliform bacteria in storm runoff generally are due to native soil coliform 

bacteria, which are washed off soil particles by overland flow (Mallard, 1980, 

p. 5). Large concentrations of the other indicator bacteria were due to animal 

sources. The median ratios of concentrations of fecal coliform to fecal 

streptococcal bacteria from the tributaries and conduits generally were less 

than 0.7. Additionally, 72 percent of the 130 bacterial samples of storm 

runoff from urban areas had a ratio less than 0.7. This indicates that 

nonhuman fecal waste was the major type of fecal contamination in storm runoff 

from urban areas discharged to the Jordan River. Ratios greater than 4.1, 

which indicate human contamination, were determined only in 11 percent of the 

samples.

32
Table 7. Comparison of mean bacterial concentrations for nonstorm and 

storm samples collected near the mouths of Little Cottonwood and 

Mill Creeks

[concentrations in colonies per 100 milliliters]

Samples Total Fecal Fecal

coliform coliform streptococcal

bacteria bacteria bacteria

Little Cottonwood 

Creek

Nonstorm 7 to 11 2,490 660 620 

Storm 8 to 11 2,670 1,300 11,880

Mill Creek

Nonstorm 6 to 11 2,030 700 820 

Storm 8 to 12 4,620 1,710 8,450

33
4.5

(S)

£ 4.0

o 

o

^ 3.5

QC 

UJ 

Q.

O 

00

co

Sanitary 

standard o

0.5n~ O O

1974 1975 1976 1977 1978 1979 1980 1981 1982

Figure 11. Increase in fecal coliform bacterial concentrations with time and comparison 

with the sanitary standard at 1700 South Street. From Thompson (1984b).

34
MEAN CONCENTRATION, IN COLONIES PER 100 MILLILITE

F

U> 

Ul

U FCS T

13.251 16.4 19.8 31

RIVER MIL,UPSTREAM FROM MOUTH

igure 12. Mean concentrations offecal coliform bacteria (FC), streptococcal (FS), and totalcoliform bacteria (TC) in conduits. FromThompson (1984b).

oooooo

S

o "o 'o o 

o o o o 

JOOOOOO

zz

North Temple Conduit

800 South Conduits

H

1300 South Conduits 

 i 

] 

J Decker Lake Drain 

] 

9000 South Conduit
Large bacterial concentrations in storm runoff resulted in an increase of 

the concentration of some bacterial types in the Jordan River during storms 

(table 8). The mean concentrations of total coliform bacteria varied, but 

they generally were greater during nonstorm periods; whereas, the mean 

concentrations of fecal coliform bacteria were greater at all sites during 

storms. Concentrations of fecal streptococcal bacteria were greater during 

storms at all sites except the Jordan Narrows. Statistical verification of 

the differences between nonstorm and storm data was difficult due to the 

variability within the data sets.

TOEBIDITY

Excessive turbidity in a river is not desirable because it detracts from 

the esthetic appearance, it interferes with sprinkler-irrigation systems, and 

it can adversely affect the fishery potential. The study of turbidity in the 

Jordan River, was designed to:

1. Measure the turbidity and concentrations of suspended sediment in the 

Jordan River from the Jordan Narrows to 500 North Street.

2. Identify the specific components and sources of the turbidity.

3. Describe possible remedial measures to decrease the turbioity.

Few previous studies of water quality of the Jordan River have dealt 

specifically with turbidity, although it was generally recognized as a problem 

(U.S. Environmental Protection Agency, 1972, p. 35; Salt Lake County Water 

Quality and Water Pollution Control, 1978, Sec. II, p. 22; Gunnell and others, 

1982, p. 62). Considerable water-quality data, including turbidity, have been 

collected by the U.S. Geological Survey since 1974 at gaging stations at 5800 

South and 1700 South Streets. More specific data on the causes and 

distribution of turbidity were collected at five sites on the Jordan River 

from January 1981 through August 1982. Samples were collected monthly and 

analyzed for turbidity, suspended sediment, and organic carbon. Ihe samples 

collected during the summer were analyzed for phytoplankton chlorophyll to 

assess the effect of suspended algae on turbidity.

Variation in Turbidity

Relatively large values of turbidity were measured at the Jordan Narrows, 

with a mean of 88 Nephelonetric turbidity units (KOU) during June-October as 

contrasted to and a mean of 43 NTO during November-May. Ihe combined mean for 

all other sites was nearly identical for June to October (27 NTO) and November 

to May (32 NTU). The generally synchronous pattern of variability of 

turbidity at all sites except the Jordan Narrows is indicated in figure 13. 

Ihe latter site also had the greatest variability in turbidity, ranging from 

10 to almost 150 NTU.

36
Table 8. Mean concentrations of indicator bacteria in nonstorm and storm 

samples at five sampling sites

[concentrations in colonies per 100 milliliters]

Site

Jordan Narrows 

Nonstorm 

Storm

Total 

coliform 

bacteria

7,320 

2,090

Fecal 

coliform 

bacteria

82 

140

Fecal 

streptococcal 

bacteria

1,480 

1,120

9000 South State

Nonstorm 9,110 

Storm 8,210

5800 South Street

Nonstorm 19,120 

Storm 7,100

1700 South Street

Nonstorm 32,070 

Storm 40,120

500 North Street

Nonstorm 48,970 

Storm 36,590

970

1,140

2,820

3,080

3,660

8,670

3,030

3,920

1,890

4,010

2,410

9,980

2,870

5,040

11,320

25,500

37
>.- 150

£ 140

9 120

SlOO

{!. 80

60

40

20

0

riii

1700 South Street

J__L

150 

140 -

120 

100 -

80

60

40

20

0

500 North Street

I I

JFMAMJ JASONDJFMAMJJA 

1981 1982

Figure 13. Variations in turbidity at five sampling sites, January 1981 to August 1982.

From Weigel (1984).

38
Variation in the Components of Turbidity

Mean concentrations of suspended sediment did not vary significantly 

among sites or between the November-May and June-October periods, but the 

daily variation among sites occasionally was large. The means for the entire 

stucty period ranged from 169 milligrams per liter at 500 North Street to 193 

milligrams per liter at the Jordan Narrows (table 9). No seasonal trend was 

observed but the mean concentration appeared to decrease from the Jordan 

Narrows to 500 North Street during June to October.

The mean concentration of suspended-organic carbon was larger at all 

sites during June to October. During that period, the concentrations of SOC 

always were largest at the Jordan Narrows, averaging nearly twice the 

concentrations at some downstream sites. The large concentrations of SOC 

coincided with large concentrations of phytopiankton chlorophyll a, which 

averaged 42 micrograms per liter at the Jordan Narrows and decreased 

downstream to 9.2 micrograms per liter at 500 North Street. Phytopiankton 

samples collected during a bloom on August 24, 1982, contained a maximum of 

99,000 cells per milliliter at the Jordan Narrows, with a minimum of 23,000 

cells per milliliter at downstream stations. Blue-green algae constituded 84 

to 98 percent of the total cell count.

Correlation of Turbidity With Related Parameters 

and Control of Turbidity

Correlation analysis was used to identify relationships between turbidity 

and concentrations of suspended sediment and SOC in the Jordan River during 

different periods of the year (table 10). Significant correlations 

(correlation coefficient greater than 0.70) were obtained between turbidity 

and the concentration of suspended sediment during June to October and 

November to May at the Jordan Narrows. SampQ.es collected during June to 

October had significant correlations between turbidity and SOC at all sites. 

Significant correlations were observed between suspended-organic carbon and 

turbidity during November to May only at 1700 South Street. Correlations 

between turbidity and concentrations of suspended sediment were more variable 

at all sites. There were significant correlations during June to October 

between turbidity and the concentration of suspended sediment at the three 

upstream sites: Jordan Narrows and 9000 South and 5800 South Streets. When 

all sites were combined and the overall relationships evaluated, turbidity 

correlated significantly with SOC during June to October.

Concentrations of suspended sediment did not correlate well with 

turbidity at 1700 South Street, but SOC correlated significantly at all times. 

The addition of organic matter to a clay suspension has been shown to result 

in precipitation of an organic-clay complex (van Olphen, 1977, p. 71). This 

mechanism may have operated upstream from 1700 South Street, resulting in a 

decrease in turbidity due to the precipitation of inorganic solids by organic 

material contributed by the wastewater-treatment plants. The decrease in 

turbidity due to removal of inorganic-suspended sediment was accompanied ty an 

increase in turbidity due to suspended-organic sediment. Analysis of a small 

amount of particle-size data indicated a considerable decrease in clay-size 

particles between 5800 South and 1700 South Streets, which tends to support 

this mechanism.

39
Table 9. Variations in the means for turbidity and for suspended-sediment 

and chlorophyll concentrations

susp

[NTU, Nephelometer Turbidity Units; mg/L, milligrams per liter; ug/L, microgra

Turbidity

Location Number of

samples

Mean

(NTU)

Suspendedsediment 

concentration

Suspendedorganic 

carbon (as C)

Concentration

Number of Mean Number of

samples (mg/L)

Entire study period

samples

Mean

(mg/L)

N

s

(January 1981-August 1982)

Jordan Narrows

9000 South Street

5800 South Street

1700 South Street

500 North Street

Jordan Narrows

9000 South Street

5800 South Street

1700 South Street

500 North Street

Jordan Narrows

9000 South Street

5800 South Street

1700 South Street

500 North Street

27

26

25

22

25

11

11

11

10

10

16

15

14

12

15

61

30

30

29

29

88

27

27

27

26

43

32

32

, 31

32

19 193

19 189

21 174

17 181

19 169

June-October

10 228

10 199

11 170

10 191

10 153

November-May

9 154

9 179

10 179

6 166

9 187

24

20

20

20

21

11

10

11

9

10

13

10

9

11

11

2.3

1.4

1.7

2.0

1.9

3.5

1.6

2.0

2.3

2.1

1.2

1.3

1.4

1.8

1.7
Table 10. Correlation coefficients between turbidity and two components of

suspended sediment

Location

Suspended-sediment 

concentration

Suspended-organic 

carbon (as C)

Number of 

samples

Correlation 

coefficient

Number of 

samples

Correlation 

coefficient

Jordan Narrows 

9000 South Street 

5800 South Street 

1700 South Street 

500 North Street 

Combined sites

Jordan Narrows 

9000 South Street 

5800 South Street 

1700 South Street 

500 North Street 

Combined sites

Entire study period 

(January 1981-August 1982)

19 0.86 24

19 l .44 20

21 .61 20

17 .63 20

19 .53 21

95 .54 105

June-October

10 0.92 11

10 .67 10

11 .78 11

10 ! .60 9

10 1 .49 10

51 .59 51

November-May

0.69 

.53 

.57 

.63 

.37 

.60

0.71 

.81 

.81 

.83 

.81 

.75

Jordan Narrows

9000 South Street

5800 South Street

1700 South Street

500 North Street

Combined sites

9

y

10

7

9

44

0

1

1

1

1

.77

.35

.30

.74

.54

.46

13

10

9

11

11

54

1

1

1

1

1

0.06

.45

.42

.74

.27

.23

1 Correlation coefficient less than the 95-percent-confidence level.

41
Particle-size analyses indicated that at least 67 percent of the 

suspended sediment in water samples collected from November to May at the 

Jordan Narrows consisted of clay-size particles. Utah Lake is turbid, and 

precipitated calcite has been suggested as the likely cause (Fuhriman and 

others, 1981, p. 59). Qliis indicates that clay-size particles entering the 

river from Utah Lake, were responsible for much of the turbidity at the Jordan 

Narrows during this time.

Qlie decrease of turbidity in Utah Lake could decrease turbidity in the 

Jordan River upstream from 5800 South Street. Control of algal growth in Utah 

Lake and Jordan River could decrease the turbidity during June through October 

in the river. A decrease in the quantity of organic material discharged from 

the wastewater-treatment plants into the Jordan River could decrease the 

turbidity in the river downstream from 5800 South Street. Further studies 

specifically to identify sources of turbidity in the Jordan River would 

benefit from additional particle-size and phytoplankton analyses. Studies of 

turbidity and suspended sediment in tributary streams and canals possibly 

could identify additional sources of turbidity.

SUMMARY AND CONCLUSIONS

Ihe results of an intensive study of the Jordan River from 1980-82 

indicated that severe water-quality problems exist which may interfere with 

productive use of the river. Concentrations of dissolved oxygen, which were 

less than 5.5 milligrams per liter, were common during April-September 

downstream of 5800 South Street. These small concentrations were due to 

increases in organic materials contributed ty discharges from wastewatertreatment plants, tributary streams, and storm conduits. Most of the oxygendemanding substabces enter the river in the reaches that have the smallest 

reaeration rates and consequently the smallest assimilatory capacity.

Toxic substances were a major pollution problem in the Jordan River. 

Most of the problem substances identified in the river were trace metals. 

Total mercury concentrations exceeded the State's standard of 0.05 microgram 

per liter in about 75 percent of all samples. Large concentrations of 

cadnium, copper, lead, and zinc, were an occasional problem, but less than 10 

percent of all samples exceeded the recommended use standards. Concentrations 

of ammonia that are toxic to fish were present in 18 percent of all samples; 

and these concentrations likely were due to discharges from wastewatertreatment plants. Pesticides and organic compounds identified as priority 

pollutants did not appear to be a serious problem in the Jordan River. 

Concentrations of pesticides such as DDD, DDE, DOT, dieldrin, and 

methoxychlor, which were commonly used in previous years, have been detected 

in bottom sediments. Only DDE, Silvex, and 2,4-D were found dissolved in the 

river water, and they typically were at concentrations less than 0.1 microgram 

per liter. Chloroform and phenol occasionally were detected in water entering 

the river from conduits.

A serious sanitary problem existed in the Jordan River, as indicated ty 

the presence of large numbers of indicator bacteria. Bacterial concentrations 

generally increased as the river flowed northward. Contamination from animals 

appeared in 92 percent of the samples f ran the Jordan Narrows but decreased to 

50 percent downstream. Contamination from humans was rare at the Jordan

42
Narrows but increased to 10-20 percent of the samples downstream. The 

numerous conduits contributed large numbers of indicator bacteria to the river 

and contamination from animal wastes was present in nearly 75 percent of all 

samples obtained from the conduits. Data collected before and after July 1980 

indicate that the bacterial contamination of the river at 1700 South Street 

has increased. With the increasing population in the Salt Lake Valley and its 

effect on already overloaded wastewater-treatment plants, this trend is likely 

to continue.

Turbidity gives the Jordan River a murky appearance, which is 

objectionable to most river users. Turbidity is the most visible pollutant in 

the Jordan River, although it is the least hazardous of the contaminants. 

Much of the turbidity was due to clay-size particles in suspension that enter 

the river at Utah Lake and to suspended-organic materials discharged from 

wastewater-treatment plants. During June to October, turbidity was due 

primarily to suspended-organic matter, whereas, during November to May, 

inorganic-suspended sediment (possibly calcite) was the likely cause.

The establishment of the Jordan River Parkway and the construction of 

numerous foot bridges, jogging paths, and equestrian trails indicate a 

committment to recreational and esthetic enjoyment of the river. Population 

increase in the area will increase the loads of contaminants discharged to the 

river as well as increase the recreational demands on its resources. If 

provisions are not made to minimize the effect of the increased population, 

continued degradation of the river could occur.

REFERENCES CITED

Merican Public Health Association, American Water Works Association, and

Water Pollution Control federation, 1980, Standard methods for the 

examination of water and wastewater (15th ed.): Washington, D.C., 

Merican Public Health Association, 1134 p.

Christensen, R. C., Stephens, D. W., lyper, G. E., McCormack, H. F., and 

Weigel, J. F., 1984, Quality and quantity of runoff and atmospheric 

deposition in urban areas of Salt Lake County, Utah, 1980-81: U.S. 

Geological Survey Water-Resources Investigations Report 84-4011, 223 p.

Coburn, A. A., 1972, Pollution input from the lower Jordan Basin to Antelope 

Island estuary: Salt Lake City, University of Utah, Department Civil 

Engineering, unpublished Master of Science thesis, 122 p.

Environmental E^namics, Inc., 1975, An environmental evaluation of the Utah 

Lake-Jordan River basin: Washington, D.C., National Commission on Water 

Quality, XIII, 15 p.

Fuhriman, D. K., Merritt, L. B., Miller, A. W., and Stock, H. S., 1981, 

Hydrology and water quality of Utah Lake: Provo, Great Basin Naturalist 

Memoirs, v. 5, p. 43-67.

Gaufin, A. R., 1958, Report on limnological and sanitary characteristics of 

Jordan, Price, Provo, and Weber Rivers for 1957-58: Salt Lake City, 

University of Utah, Department of Zoology, 63 p.

43
Gunnell, R. D., Marston, R. R., Oberndorfer, R. Y., 1982, State of Utah 305(b) 

biennial water quality report: Utah Department of Health, Division of 

Environmental Health, Bureau of Water Pollution Control, 177 p.

Hely, A. G., Mower, R. W. and Harr, L. A., 1971, Water resources of Salt Lake 

County, Utah: Utah Department of Natural Resources Technical Publication 

31, 244 p.

Hydroscience, Inc., 1976, The water quality impact of point and nonpoint loads 

to the Jordan River: Salt Lake City, Salt Lake County Council of 

Governments (208 stuc^), 68 p.

Keith, L. H., and Telliard, W. A., 1979, Priority pollutants, a perspective 

view: Environmental Science and Technology, v. 13, no. 4, p. 416-423.

Mallard, G. E., 1980, Microorganisms in storm water A summary of recent 

investigations: U.S. Geological Survey Open-File Report 80-1198, 18 p.

McCormack, H. F., Christensen, R. C., Stephens, D. W., Pyper, G. E., Weigel, 

J. F., Conroy, L. S., 1983, Surface water and climate-logic data, Salt 

Lake County, Utah, water year 1981, with selected data for water years 

1980 and 1982: U.S. Geological Survey Open-File Report 83-694, 586 p.

National Oceanic and Atmospheric Administration, 1981, Climatological data 

annual summary, Utah: Asheville, N. C., Environmental Data and 

Information Service, v. 83, no. 13, 15 p.

typer, G. E., Christensen, R. C., Stephens, D. W., McCormack, H. F., and 

Conroy, L. S., 1981, Surface-water and climate-logical data, Salt Lake 

County, Utah, water year 1980: U.S. Geological Survey Open-File Report 

81-1111, 167 p.

Rathbun, R. E., 1979, Estimating the gas and cfye quantities for modified 

tracer technique measurements of stream reaeration coefficients: U.S. 

Geological Survey Water-Resources Investigations 79-27, 42 p.

Salt Lake County Soil Conservation District, 1981, Jordan River agricultural 

nonpoint water quality assessment for 1979-80: Salt Lake County Division 

of Water Quality and Water Pollution Control, 71 p.

Salt Lake County Water Quality and Water Pollution Control, 1978, Areawide 

water quality management plan: Salt Lake City, 423 p.

Stephens, D. W., 1984, Characterization of the dissolved-oxygen regime of the 

Jordan River, Salt Lake County, Utah: U.S. Geological Survey WaterResources Investigations Report 84-4056, 56 p.

Templeton, Linke, and Alsup, and Engineering-Science, Inc., 1974, Utah LakeJordan River hydrologic basins water quality management planning stucfy: 

Utah State Division of Health, Bureau of Environmental Health, 384 p.

Thompson, K. R., 1984a, Reconnaissance of toxic substances in the Jordon 

River, Salt Lake County, Utah: U.S. Geological Survey Water-Resources 

Investigations Report 84-4155, 31 p.

44
Thompson, K. R. r 1984br Sanitary quality of the Jordan River in Salt Lake

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