APPENDIX T 

Use Attainability Analysis 

Case Studies 

WATER QUALITY STANDARDS HANDBOOK 

SECOND EDITION 
CASE STUDIES 

Introduction 

The Water Body Survey and Assessment Guidance for Conducting Use 

Attainability Analyses provides guidance on the factors that may be 

examined to determine if an aquatic life protection use is attainable 

in a given stream or river system. The guidance proposed that States 

perform physical, chemical and biological evaluations in order to 

determine the existing and potential uses of a water body. The 

analyses suggested within this guidance represent the type of analyses 

EPA believes are sufficient for States to justify changes in uses 

designated in a water quality standard and to show in Advanced 

Treatment Project Justifications that the uses are attainable. States 

are also encouraged to use alternative analyses as long as they are 

scientifically and technically supportable. Furthermore, the guidance 

also encourages the use of existing data to perform the physical, 

chemical and biological evaluations and whenever possible States should 

consider grouping water bodies having similar physical and chemical 

characteristics to treat several water bodies or segments as a single 

unit. 

Using the framework provided by this guidance, studies were 

conducted to (1) test the applicability of the guidance, (2) 

familiarize State and Regional personnel with the procedures and (3) 

identify situations where additional guidance is needed. The results 

of these case studies, which are summarized in this Handbook, pointed 

out the following: 

(1) The Water Body Surveys and Assessment guidance can be applied and 

provides a good framework for conducting use attainability 

analyses; 

(2) The guidance provides sufficient flexibility to the States in 

conducting such analyses; and, 

(3) The case studies show that EPA and States can cooperatively agree 

to the data and analyses needed to evaluate the existing and 

potential uses. 

Upon completion of the case studies, several States requested that 

EPA provide additional technical guidance on the techniques mentioned 

in the guidance document. In order to fulfill these requests, EPA has 

developed a technical support manual on conducting attainability 

analyses and is continuing research to develop new cost effective tools 

for conducting such analyses. EPA is striving to develop a partnership 

with States to improve the scientific and technical bases of the water 

quality standards decision-making process and will continue to provide 

technical assistance. 

The summaries of the case studies provided In this handbook 

illustrate the different methods States used in determining the 

existing and potential uses. As can be seen, the specific analyses 

used were dictated by (1) the characteristics of the site, (2) the 

D-1 
States capabilities and technical expertise using certain methods and 

(3) the availability of data. EPA is providing these summaries to show 

how use attainability analyses can be conducted. States will find 

these case studies informative on the technical aspects of use 

attainability analyses and will provide them with alternate views on 

how such analyses may be conducted. 

D-2 
WATER BO@Y SURVEY AND ASSESSMENT 

Assabet River, Massachusetts 

A. Site Description 

The drainage basin of the Assabet River comprises 175 square miles 

1 ocated in twenty towns in East-Central Massachusetts. The Assabet 

River heqins as the outflow from a small wildlife preservation 

impollndrTent in the Town of Westborough and flows northeast through the 

urban centers of Northborough, Hudson, Maynard and Concord to its 

confluence with the Sudhury River, forming the Concord River. Between 

these arbani7ed centers, the river is bordered by stretches of rural 

and undeveloped land. Similarly, the vast majority of the drainage 

basin is characterized by rural development. Figure 1 presents a 

schematic diaqram of the drainage basin. 

The Assahet River provides the opportunity to study a repeating 

sequence of water quality degradation and recovery. One industrial and 

six dnmestic wastewater treatment plants (WWTP) discharge their 

effluents into this 31-mile long river. All of the treatment plants 

presently provide secondary or advanced secondary treatment, although 

many of them are not performing to their design specifications. Most 

of the treatment plants are scheduTed to be upgraded in the near 

future. 

Interspersed among the WWTP discharges are six low dams, all but 

one of which were huil t at least a half century ago. All are 

"run-of-the-river" structures varying in height from three to eleven 

feet. The last danl built on the river was a flood control structure 

completed in 19HO. 

The headwaters of the Assahet River are formed by the discharge 

fro17 a wildlife preservation impoundment, and are relatively "clean" 

except for low dissolved oxygen (DO) and high biochemical oxygen demand 

(ROD) during winter and summer. Water is discharged from the preserve 

throuqh the foot of the dam that forms the impoundment, and therefore, 

tends to he low in IJO. 90 and ROD problems in the impoundment are 

attributed to winter ice cover and peak algal growth in summer. After 

the discharqe of effluents from the Westborough and Shrewsbury 

mtJfliCipal wastewater treatment plants, the river enters its first 

deyradation/recovery cycle. The cycle is repeated as the river 

receives effluent from the four remaining domestic treatment plants. 

Water quality problems in the river are magnified when the effluents 

are discharcjed into the head of an impoundment. However, the flow of 

water over the dams also serves as a primary means of reaeration in the 

river, and thus, the dams also hecome a major factor in the recovery 

seqmertt of the cyc;e. Water quality surveys performed in 1979 showed 

violation<, of the fecal coliform, phosphorus, and dissolved oxygen 

criteria throt,clholit the river. 

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At present, the entire length of the Assabet River is classified 

R, which is designated for the protection and propagation of fish, 

other aquatic life and wildlife, and for primary and secondary 

recreation. Two different uses have been designated for the Assabet 

River--from river mile 31.8 to 12.4 the designated use is "aquatic 

life" and from river mile 12.4 to the confluence with the Sudbury River 

the designated use is a "warm water fishery". The difference in these 

designated uses is that maintenance of a warm water fishery has a 

maximum temperature criterion of 83 degrees F, and a minimum 00 of 5 

mg/l. There are no temperature or DO criteria associated with the 

aquatic life use. These designations seem contrary to the existing 

data, which document violations of both criteria in the lower reaches 

of the river where warm water fishery is the designated use. 

0. Problem Definition 

The Assabet River was managed as a put and take trout fishery 

prior to the early 1970s when the practice was stopped on advisement of 

the MllWPC because of poor water quality conditions in the river. While 

the majority of the water quality problems are attributable to the 

wastewater treatment plant discharges, the naturally low velocities in 

the river, compounded by its impoundment in several places, led to the 

examination of both factors as contributors to the impairment of 

aquatic life uses. This combination of irreversible physical factors 

and wastewater treatment plant-induced water quality problems led to 

the selection of the Assahet River for this water body survey. 

c 1. Approach to Use Attainability Analysis 

Assessment of the Assabet River is based on the previously 

mentioned site visits and discussions among representatives of the 

Massachusetts Division of Water Pollution Control (MDWPC); the l1.S. 

Environmental Protection Agency (EPA); and the Massachusetts Fish and 

Wildlife Division. This assessment is also based in part upon findings 

reported in the field and laboratory analyses on the Assahet River in 

early June, 1979, and again in early August, 1979. These surveys are 

part of the on-going MDWPC monitoring program, which included similar 

water quality assessments of the Assabet in 1969 and 1974. The water 

quality monitoring includes extensive information on the chemical 

characteristics of the Assahet River. 

Analyses Conducted 

A review of physical, chemical and biological information was 

conducted to determine which aquatic life use designations would be 

appropriate. 

A. Physical Factors 

The low flow condition of the river during the sumer months may 

have an impact on the ability of certain fish species to survive. 

Various percentages of average annual r;ow (AAF) have been used to 

describe stream regimens for critical fisheries flow. As reported in 

o-5 
rl)rt pl 1 /19!?), stlJdies conducted by Tennant indicate that lo",, 30X, 

and 6n? nf &lF describe the range of fisheries flows from absolute 

1'1 j n i 77"~I 'lqw AAF) to optimum (604 of AAF). The average annual flow of 

the ?,5s45Pt >iver, as calculated from 39 years of record at the USGS 

,];11']" 1: r-i /or r:lile 7.7, is 183 cfs. Flow measurements taken at the 

1171;\ ']"'ll]C~ orl four consecutive days in early August, 1979, were 43, 34, 

" 7 , Anti 3? cfs. These flows average about 19 percent of the AAF 

l~dicatil<~ that some impairment of the protection of fish species may 

occ 11 rd11r to low flow in the river. The 7-day lo-year low flow for 

this r,ahch of the river is approximately 18 to 20 cfs. 

The outstanding physical features of the Assabet River are the 

I1 11 I.; s , dhlch have a significant influence on the aquatic life of the 

-i ir'r-. Ml)St fish are incapable of migrating upstream of the dams, thus 

'1. itint; ttlrlir ahility to find suitable (sufficient) habitats when 

; ri+lr,jl dq?tlr quality conditions occur. The low flow conditions 

!f)wv5+ r ‘),j'e ()f the riar~s dlJrinq dry periods also result in high water 

l 4’;ltJ~,jt N,r-tJS, further limitinq fish survival in the river. 

:< . i:~ol,~~;ical Factors 

*s with 

hlh&?' 

data on the physical parameters for the Assabet River, 

data are sparse. The last fish survey of the Assabet River 

d?\ cl)pr! lctP(i bv the Massachusetts Fish and Wildlife Division in 1952. 

'("1')~ :)rrch, hlueqills, pickerel, sunfish, and hass were all observed. 

7 my ."4 5j L+ '1 P t 7iver was sampled by the MDWPC for macroinvertebrates at 

‘,‘,,> ! ~:-3:ions in Ilbnp, 1979, as part of an intensive water quality 

: ,“ii'i - 

Thrl ,!<ita ;qf!re rpvieweri and analvses performed to determine whether 

:ondi tionq precll~fie macroinvertebrate hahitats. The results were 

i I.'-oncl 11si ve. 

r. fhp-1 cd 1 Factors 

Ilf all the chemical constituents measured in the June and August, 

1 II '0 , ddYt>r quality surveys, dissolved oxygen, ammonia nitrogen, and 

t of-II9r 3t I, rfy have the greatest potential to limit the survival of 

d cj~~h+ ic life. Ammonia toxicity was investigated using the criteria 

0 i+l~rj~,j in Water Ouality Criteria 1972. The results of this analysis 

---__ 

1' :'"+e that the concentration of un-ionized ammonia would need to be 

7 "f-,>d<,>A .ii,;Iroxir?ately three times before acute mortality in the 

c, :‘f',- 7 07 >f fish listed would occur. Therefore, ammonia is not a 

:‘,r‘ )hl ,>"T# 

Tc~~.l~er-dtures in the lower reaches of the Assabet frequently exceed 

+ "(1 -‘,? < , ~ll,,V] temperature criteria (83 deqrees F) for maintenance of a 

da“'- writer fishery. However, temperature readings were taken in early 

,311 1 13:~ a'tt-'rnoon and are believed to be surface water measurements. 

'he,; jrrJ short-term localized ohservations and should not preclude the 

r.>~jif !*r~?prtl of a warm water fishery in those reaches. nissolved oxygen 

r> ,- t, r- l r- 3tlclns above Maynard are unsuitable for supporting cold or warm 

fi !*..r c?\n~rips, but are sufficient to support a fishery below this 

: ',1-t. 

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The impoundments may exhibit water quality problems in the form of 

high surface temperatures and low bottom DO. Surface temperatures have 

been found to be similar to those in the remainder of the river. The 

only depth sample was at 13 feet in the wildlife impoundment, where the 

temperature was 63 degrees F, while 83 degrees F at the surface. While 

such bottom temperatures are likely to be sufficient to support a cold 

water fishery, it is likely that the DO at the bottom of the 

impoundments will be near zero due to benthic demands and lack of 

surface aeration, which would preclude the survival of any fish, 

Findings 

The data, observations, and analyses as presented herein lead to 

the conclusion that there are four possible uses for the Assabet: 

aquatic life, warm water fishery, cold water fishery, and seasonal cold 

water fishery. The seasonal fishery would be managed by stocking the 

river during the spring. 

These uses were analyzed under three water quality conditions: 

existing, existing without the wastewater discharges, and inclusion of 

the wastewater effluent discharges with treatment at the levels 

stipulated in the 1981 Suasco Basin Water Ouality Management Plan. The 

no discharge condition is included as a baseline that represents the 

quality under "natural" conditions. 

A. Existing Uses 

A limited number of warm water fish species predominate in the 

Assabet River under existing conditions. The species should not be 

different from those observed during the 1952 survey. The combination 

of numerous low-level dams and wastewater treatment plants with low 

flow conditions in the summer results in dissolved oxygen 

concentrations and temperatures which place severe stress on the 

metabolism of the fish. 

The observed temperatures are most conducive to support the growth 

of coarse fish, including pike, perch, walleye, smallmouth and 

largemouth bass, sauger, bluegill and crappie. 

The minimum observed DO concentrations are unacceptable for the 

protection of any fish. Water Quality Criteria establishes the values 

6.8, 5.6, and 4.2 mg/l of 00 for high, moderate, and low levels of 

protection of fish for rivers with the temperature characteristics of 

the Assabet. The Draft National Criteria for Dissolved Oxygen in 

Freshwater establishes criteria as 3.0 mg/l for survival, 4.0 mg/l for 

moderate production impairment, 5.0 mg/l for slight impairment, and 6.0 

for no production impairment. The upper reaches will not even support 

a warm water fishery at the survival level, except in the uppermost 

reach. On the other hand, the lower reaches can support a warm water 

fishery under existing conditions. 

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B. Potential Uses 

The potential aquatic life uses of the Assabet River would be 

restricted by temperature and low flow, and by physical barriers that 

would exist even if water quality (measured In terms of DO and 

bacteria) Is significantly improved. Despite an overall improvement in 

treated effluent quality, the river would be suitable for aquatic life, 

as it is currently, and would continue to be too warm to support a cold 

water fishery In the sumnertime. The posslbillty of maintaining the 

cold water species in tributaries during the sutmner was investigated, 

but there are no data on which to draw conclusions. Water quality 

observations In the only tributary indicate temperatures similar to 

those in the mainstem. Therefore, the maintenance of a cold water 

fishery in the Assabet is considered unfeasible. 

The attainable uses in the river without discharges or at planned 

levels of treatment are warm water fishery and seasonal cold water 

fishery. These uses are both attainable throughout the basin, but may 

be impaired in Reach 1, as the water naturally entering Reach 1 from 

the wildlife preservation impoundment is low in DO. The seasonal cold 

water fishery is attainable because the discharge limits are 

established to maintain a DO of 5 mg/l under 7010 conditions. If the 

DO is 5 mg/l under summer low flow conditions, it will certainly be 6 

mg/l or greater during the colder, higher flow spring stocking period, 

and a seasonal cold water fishery would be attainable. 

According to the Fish and Wlldlife Division, the impoundments of 

the Assabet River have the potential to be a valuable warm water 

fishery. The reaches of the river that have a non-vegetated gravel 

bottom also have a high potential to support a significant fishery 

because these habltats allow the benthic invertebrates that comprise 

the food supply for the fish to flourish. It was further suggested 

that if the dissolved oxygen concentration could be maintained above 5 

mg/l, the river could again be stocked as a put and take trout fishery 

In the spring. 

Sumnary and Conclusions 

The low flow conditions of the Assabet River have been 

exacerbated by the low dams which span its course. In the summer 

months, the flow in the river is slowed as the river passes through its 

Impoundments and flow below the dams is often reduced to a relative 

trickle. When flow is reduced, temperatures in the shallow river 

(easily walkable In many places) can exceed the maximum temperature 

crlterlon for protection and propagation of a warm water fishery. 

Additionally, the dams limit the mobility of fish. At present, most of 

the river reaches also undergo extensive degradation due to the 

discharge of wastewater treatment plant effluent which is manifest in 

low dlssolved oxygen concentrations. All of these factors impair the 

aquatic life potential of the Assabet River. 

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Three use levels corresponding with three alternative actions 

related to the wastewater discharges are possible in the Assabet. The 

no action alternative would result in very low dissolved oxygen 

concentrations in many reaches which are appropriate only for the use 

designation of aquatic life and warm water fishery. In this scenario, 

fish would only survive in the lowest river reaches, and aquatic life 

would be limited to sludge worms and similar invertebrates in the upper 

reaches. The remaining two alternatives are related to upgrading 

treatment plants in the basin. If the discharges are improved 

sufficiently to raise the' instream DO to 5 mg/l throughout, as 

stipulated in the 1981 Water Quality Management Plan, it will be 

suitable as a warm water or seasonal cold water fishery. Should the 

discharge be eliminted altogether, the same uses would be attainable. 

The treatment plant discharges inhibit the protection and 

propagation of aquatic life. Most of the treatment plants are 

scheduled to be upgraded in the near future, which would relieve the 

existing dissolved oxygen problems. Even if the river is returned to 

relatively pristine conditions, the type of fish that would be able to 

propagate there would not change, due to the existing physical 

conditions. However, the extent of their distribution, their 

abundance, and the health of the biota would be likely to increase. 

The present use designations of the Assabet River are sufficient 

to characterize the aquatic life use it is capable of supporting, while 

physical barriers prevent the year-round attainment of a "higher" 

aquatic life use. The potential aquatic life uses could include 

extension of the warm water and seasonal cold water fishery 

classifications to the entire length of the river, should the planned 

improvements to the wastewater treatment plants be implemented. 

D-9 
WATER BODY SURVEY AND ASSESSMENT 

Blackwater River 

Franklin, Virginia 

I. INTRODUCTION 

A. Site Description 

The area of the Blackwater River which was chosen for this study extends 

from Joyner's Bridge (Southampton County, Route 611) to Cobb's Uharf near 

its confluence with the Nottoway River (Table 1 and Figure 1). ln addition, 

data from the USGS gaging station near Burdette (river mile 24.57) provided 

information on some physical characteristics of the system. 

TABLE 1 

Sampling Locations for Blackwater River Use Attainability Survey 

Station 

No. Location 

River 

Mi le 

: 

3 

Vicinity Joyner's Bridge, Route 611 20.90 

Below Franklin Sewage Treatment Plant Discharge 13.77 

Vicinity Cobb's Wharf, Route 687 2.59 

The mean annual rainfall is 48 inches, much of which occurs in the sutwner 

in the form of thunderstorms. The SCS has concluded that approximately 

41,000 tons of soil are transported to streams in the watershed due to 

rainfall induced erosion. Seventy (70) percent of this originates from 

croplands, causing a potential p llution problem from pesticides and from 

fertilizer based nutrients. In ad 4 ition, 114,000 pounds of animal waste are 

produced annually, constituting the only other major source of non-point 

pollution. 

There are two primary point source discharges on the Rlackwater River. The 

Franklin Sewage Treatment Plant at Station 2 discharges an average of 1.9 

mgd of municipal effluent. The discharge volume exceeds NPDES permit levels 

due to inflow and infiltration problems. The plant has applied for a 

federal grant to upgrade treatment. The second discharge is from Union Camp 

Corporation, an integrated kraft mill that produces bleached paper and 

bleached board products. The primary by-products are crude tall oil and 

crude sulfate turpentine. Union Camp operates at 36.6 mgd but retains its 

treated waste in lagoons until the winter months when it is discharged. The 

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Figure 1. Map of Study Area 

Southampton Co., VA 

Scale 1:5000 

Cobb's Wharf 

Virginia 

-- -- 

North Carolina 

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Union Camp discharge point is downstream from Station 3 just above the 

North Carolina State line at river mile 0.70. 

The topography surrounding the Blackwater River is essentially flat and the 

riparian zone is primarily hardwood wetlands. There is a good surface water 

supply from several swamps. At the USGS gaging station near Burdette, 

Virginia, the discharge for calendar year 1980 averaged 430 cfs. 

The Blackwater River from Joyner's Bridge (Station 1) to Franklin is classified by the State Water Control Board (SWCB) as a Class III free flowing 

stream. This classification requires a minimum dissolved oxygen concentration of 4.0 mg/l and a daily average of 5.0 mg/l. Other applicable standards are maintenance of pH from 6.0 to 8.5 and a maximum temperature of 

32°C. The riparian zone is heavily wooded wetlands with numerous channel 

obstructions. Near Franklin the canopy begins to open and there is an increasing presence of lily pads and other macrophytes. The water is dark, as 

is characteristic of tannic acid water found'in swamplands. 

Below Franklin the Blackwater River is dredged and channelized to permit 

barge traffic to reach Union Camp. The channel is approximately 40m wide 

and from 5m to 8m in depth. This reach of stream is classified by the SWCB 

as a Class II estuarine system requiring the same dissolved oxygen and pH 

limitation as in Class III but without a temperature requirement. 

B. Problem Definition 

The study area on the Blackwater River includes a Class III free-flowing 

stream and a Class II estuarine river. Part of the Class III section is a 

freshwater cypress swamp. The water is turbid, nutrient enriched and 

slightly acidic due to tannins. 

In response to the EPA request for Virginia's involvement in the pilot Use 

Attainability studies, the State Water Control Board chose to examine the 

Blackwater River in the vicinity of Franklin, Virginia. There were several 

reasons for this choice. First, the major stress to the system is low dissolved oxygen (DO) concentrations which occur from May through November. 

Surveys conducted by SWCB staff, and officials from Union Camp in Franklin, 

found that during certain periods "natural" background concentrations of 

dissolved oxygen fell below the water quality standard of 4.0 mg/l. This 

has raised questions as to whether the current standard is appropriate. 

Virginia's water quality standards contain a swamp water designation which 

recognizes that DO and pH may be substantially different in some swamp 

waters and provides for specific standards to be set on a case by case 

basis. However, no site specific standards have been developed in Virginia 

to date. One of the goals of this project was to gather information which 

could lead to possible development of a site specific standard for the 

Blackwater River. Second, the Franklin STP has applied for a federal grant 

to provide for improved BOD removals from its effluent. 

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C. Approach to Use Attainability 

On 20 April, 1982, staff of the SWCB met with several EPA officials and 

their consultant. After visiting the study area on the Blackwater River and 

reviewing the available information, it was determined that further data 

should be collected, primarily a description of the aquatic community. The 

SWCB staff has scheduled four quarterly surveys from June 1982, through 

March 1983, to collect physical, chemical, and biological information. Interim results are reported herein to summarize data from the first collection. Final conclusions will not be drawn until the data has been compiled 

for all four quarters. 

II. ANALYSES CONDUCTED 

A. Physical Analysis 

Data on the physical characteristics of the Blackwater River were derived 

primarily from existing information and from general observations. The entire reach of the Blackwater River from Joyner's Bridge to Cobb's Wharf was 

traveled by boat to observe channel and riparian characteristics. A sediment sample was collected at each station for partical size analysis. 

B. Chemical Analysis 

Water samples were collected at Stations 1-3 for analysis of pH, alkalinity 9 solids, hardness, nutrients, five-day BOO, chemical oxygen demand, 

total organic carbon, phenols, pesticides, and heavy metals. In addition, 

previous data on dissolved oxygen concentrations collected by the SWCB and 

Union Camp were used to examine oxygen profiles in the river. The USGS 

Water Resources Oata for Virginia (1981) provided some chemical data for 

the Blackwater River near Burdette. 

C. Biological Analysis 

Periphyton sampling for chlorophyll-a, biomass, and autotrophic index rietermination was conducted using floating plexiglass samplers anchored by a 

cement weight. The samplers were placed in the field in triplicate and remained in the river for 14 days. They were located in run areas in the 

stream. At the end of this two-week period, the samplers were retrieved and 

the slides removed for biomass determinations and chlorophyll analysis. 

Both a cursory and a quantitative survey of macroinvertebrates were conducted at each station. The purpose of the cursory study was to rapidly 

identify the general water quality of each station by surveying the presence of aquatic insects, molluscs, crustaceans and worms and classifying 

them according to their pollution tolerance. A record was kept of all 

organisms found and these were classified to the family level as dominant, 

abundant, conmon, few or present. The cursory survey was completed with a 

qualitative evaluation of the density and diversity of aquatic organisms. 

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General knowledge of the pollution tolerance of various genera was used to 

classify the water quality at each statlon. The benthic macroinvertebrate 

samples were collected with Hester-Dendy multiplate artiflclal substrates. 

The substrates were attached to metal fence posts and held vertically at 

least 15 cm above the stream bottom. The substrates were left in place for 

six weeks to allow for colonization by macroinvertebrate organisms. In the 

laboratory the organisms were identifled to the generic level whenever possible. Counts were made of the number of taxa identified and the number of 

Individuals within each taxon. 

Fish populations were surveyed at each station by electrofishing. Each station was shocked for 1,000 seconds: BOO seconds at the shoreline and 200 

seconds at midstream. Fish collected were identified to species and the 

total length of each fish was recorded. In addition, general observations 

were made about the health status of the fish by observing lesions, hemorrhaging, and the presence of external parasites. 

Diversity of species was calculated using the Shannon-Weaver index. Additionally, the fish cormnunities were evaluated using an index proposed by 

Karr (1981) which classifies biotic integrity based on 12 parameters of the 

fish community. 

III. FINDINGS 

There are few physical factors which limit aquatic life uses. The habitat 

is characteristic of a hardwood wetland with few alterations. The major 

alteration is dredging and channelizatlon below Franklin which eliminates 

much of the macrophyte communfty and the habitat it provides for other 

organisms. The substrate at each station was composed mostly of sand with a 

high moisture content. This Is characteristic of a swamp but is not ideal 

habitat for colonization by periphyton and macroinvertebrates. 

DO concentrations are typIcally below the Virginia water quality standards 

during the months of May through November. This is true upstream as well as 

downstream from the Franklin STP and appears to occur even wlthout the impact of BOD loadings from Franklin. This phenomenon may be typical of enriched freshwater wetlands. However, during the winter months, DO concentrations may exceed 10 mg/l. Another survey conducted by SWCB showed that 

there were only small changes in DO concentration with depth. 

Representatives from 17 families of macroinvertebrates were observed during 

a cursory investigation. These included mayflies, scuds, midges, operculate 

and non-operculate snails, crayfish, flatworms, and a freshwater sponge. 

The majority of these organisms were facultative at Stations 1 and 2. HOWever, there were a few pollution sensitive forms at Station 1, and Station 

3 was dominated by pollution sensitive varieties. 

Twelve (12) species from seven families of fish were observed during the 

June 1982 study. Several top predators were present including the bowfin, 

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chain pickerel, largemouth bass and longnose gar. Other fish collected were 

the American eel, shiners, pirate perch, yellow perch, and five species of 

sunfish. None of the species are especially pollution sensitive. Results of 

the fish population survey are presented in Table 2. 

TABLE 2 

Results of Fish Population Survey in Blackwater River, 9 June 1982 

Number No. of Diversity Proportion of 

Station Collected Species d Omnivores Carnivores 

:: Joyner's Franklin Bridge STP 19 517 62.305 .r)OOOOO .157098 

3. Cobb's Wharf 44 6 2.35 .ooo .114 

Based on the EPA 304(a) criteria, low seasonal 00 concentrations measured 

in the river should present a significant stress to the biotic community. 

Large fish tend to be less resistant to low DO yet large species such as 

the largemouth bass, American eel and some sunfishes were present in an 

apparently healthy condition. The explanation for this is unclear. The low 

dissolved oxygen concentrations are near the physiological limit for many 

species. Fish may be able to acclimate to low DO to a limited extent if the 

change in oxygen concentration occurs gradually. The fact that fish are 

present in a healthy condition suggests that there is a lack of other significant stressors in the system which might interact with low DO stress. 

It is worth noting that spawning probably occurs in most species before the 

Sumner months when dissolved oxygen concentration become critically low. 

The autotrophic index determinations show the Joyner's Bridge and Franklin 

STP stations as having relatively healthy periphyton communities. In each 

case over 80 percent of the periphytic community was autotrophic in nature. 

Based on the autotrophic index, both of these stations were in better biological health than the most downstream station, Cobb's Wharf. At Cobb's 

Wharf the autotrophic index characterized an autotrophic community which 

was experiencing a slight decline in biological integrity (74 percent autotrophic as compared to greater than 80 percent upstream). 

Chemical analyses conducted on water from the Blackwater River did not 

reveal any alarming concentration of toxicants when compared to EPA Water 

Quality Criteria Documents, although the zinc concentration at Station 1 

was slightly above the 24-hour average recommended by EPA. One sample collected by the USGS had a zinc concentration which was twice this number. 

The source of this zinc is unknown. Any impact which exists from this problem should be sublethal, affecting growth and reproduction of primarily 

D-15 
the most sensitive species. The actual impact of zinc concentrations at 

Joyner's Bridge is unknown. 

Analyses of the periphyton data as well as the water chemistry data indicate that the Blackwater River is nutrient enriched. Some of this nutrient 

load comes from inadequately protected crop lands and from domestic animal 

wastes. The Franklin STP also contributes to higher nutrient concentrations. Additionally, an SWCB report estimated that between river mile 20.0 

and 6.0, 1,600 lb per day of non-point source carbonaceous ROD (ultimate) 

are added to the river. Consequently, these point and non-pant sources 

appear to be contributing to both organic enrichment and lower dissolved 

oxygen concentrations. 

IV. SUMMARY AND CONCLUSIONS 

The Blackwater River from river mile 2.59 to 20.90 has been characterized 

as a nutrient enriched coastal river much of which is bordered by hardwood 

wetlands. Periphytic, macroinvertebrate, and fish cotmnunities are healthy 

with fair to good abundance and diversity. The major limitation to aquatic 

life appears to be low 00 concentrations which are enhanced by point and 

non-point sources of nutrients and BOO. A secondary limitation may be elevated zinc concentrations at Joyner's Bridge. 

The primary difficulty in assessing the attainability of aquatic life uses 

is locating a suitable reference reach to serve as an example of an unaffected aquatic community. Originally, Joyner's Bridge (Station 1) was 

selected for this purpose, but few major differences occur between populations at all three stations. However, the widespread non-point pollution in 

Southeastern Virginia makes the location of an undisturbed reference reach 

impossible, The only alternative, then, is to make the best possible judgment as to what organisms might reasonably be expected to inhabit the 

Blackwater. 

In reference to the Blackwater River, it is probable that most fish species 

are present that should reasonably be expected to inhabit the river, although possibly in lower numbers. (No attempt has yet been made to assess 

this with regard to algal and invertebrate communities.) However, based on 

the 304(a) criteria, the low DO concentrations represent a significant 

stress of the ecosystem and the introduction of additional stressors could 

be destructive. It is also probable that higher oxygen concentrations during winter months play a major role in reducing the impact of this stress. 

Removal of point and non-point source inputs may alleviate some problems. 

However, DO concentrations may still remain low. The increased effect of 

oxygen concentrations should be an increase in fish abundance and increased 

size of individuals. Diversity would probably be unaffected. Nevertheless, 

no attempt has been made to estimate the magnitude of these changes. 

Cairns (1977) has suggested a method for estimating the potential of a body 

of water to recover from pollutional stress. Although this analysis is only 

D-16 
semi-quantitative and subjective, it suggests that the chances of rapid 

recovery following a disturbance in the Blackwater River are poor. 

The absence of an undisturbed reference reach and the dffffcu’lty in quaotifjfing changes in dissolved oxygen, population structure, and population 

abundance make a definite statement regarding attainability of aquatic life 

uses difficult. However, to surmnarize, several points stand out. First, the 

aquatic cotmnunities in the Blackwater River are generally healthy with fair 

to good abundance and distribution. Dissolved oxygen concentrations are low 

for about half of the year which causes a significant stress to aquatic 

organisms. Oxygen concentrations are higher during the reproductive periods 

of many fishes. Because of these stresses and the physical characteristics 

of the river, the system does not have much resiliency or capacity to withstand additional stress. Although a quantitative statement of changes in 

the aquatic cotnnunity with the amelioration of DO stress has not been made, 

it is probable that additional stresses would degrade the present aquatic 

community. 

The occurrence of low dissolved oxygen concentrations throughout much of 

the Blackwater is, in part, a "natural" phenomenon and could argue for a 

reduction in the DO standard. However, if this standard were reduced on a 

year round basis it is probable that the aquatic comnunity would steadily 

degrade. This may result in a contravention of the General Standard of 

Virginia State Law which requires that all waters support the propagation 

and growth of all aquatic life which can reasonably be expected to inhabit 

these waters. Because of the lack of resiliency in the system, a year round 

standards change could irreversibly alter the aquatic community. 

D-17 
WATER BODY SURVEY AND ASSESSMENT 

Cuckels Brook 

Bridgewater Township, New Jersey 

I. INTRODUCTION 

A. Site Description 

Cuckels Brook, a small tributary of the Raritan River, is located entirely 

within Bridgewater Township in Somerset County, New Jersey. It is a perennial stream approximately four miles long, having a watershed area of approximately three square miles. The entire brook is classified as FW-2 Nontrout in current New Jersey Department of Environmental Protection (NJDEP) 

Surface Water Quality Standards. 

Decades ago, the downstream section of Cuckels Brook (below the Raritan 

Valley Line Railroad, Figure 11, was relocated into an artificial channel. 

This channelized section of Cuckels Brook consists of an upstream subsection approximately 2,000 feet in length and a downstream subsection approximately 6,000 feet in length, with the Somerset-Raritan Valley Sewerage 

Authority (SRVSA) municipal discharge being the point of demarcation between the two. The downstream channelized subsection (hereinafter referred 

to as "Lower Cuckels Brook") is used primarily to convey wastewater to the 

Raritan River from SRVSA and the American Cyanamid Company, which discharges approximately 200 feet downstream of SRVSA. At its confluence with 

the Raritan River, flow in Lower Cuckels Brook is conveyed into Calco Dam, 

a dispersion dam which distributes the flow across the Raritan River. Except for railroari and pipeline rights-of-way, all the land along Lower 

Cuckels Brook is owned by the American Cyanamid Company. Land use in the 

Cuckels Brook watershed above the SRVSA discharge is primarily suburban but 

includes major highways. 

B. Problem Definition 

Lower Cuckels Brook receives two of the major discharges in the Raritan 

River Basin. SRVSA is a municipal secondary wastewater treatment plant 

which had an average flow in 1982 of 8.8 mgd (design capacity = 10 mgdl. 

The American Cyanamid wastewater discharge is a mixture of process water 

from organic chemical manufacturing, cooling water, storm water, and sanitary wastes. This mixed waste receives secondary treatment followed by 

activated carbon treatment. In 1982 American Cyanamid's average flow was 

7.0 mgd (design capacity 20 mgd). These two discharges totally dominate the 

character of Lower Cuckels Brook. 

Over 90 percent of the flow in Cuckels Brook is wastewater (except after 

heavy rainfall). The mean depth is estimated to be between 1 and 2 feet, 

and the channel bottom at observed locations is covered with deposits of 

D-18 
FIGURE 1 

CUCKELS BROOK 

STUDY AREA 

wm4 ocTom!R 1982 s*uPLltm LOCATE 

2 

I 0’ 

2 

: 

. 

77 i 

t 

N 

I 

.===== ” 

D-19 
black sludge, apparently derived from solids in the SRVSA and Cyanamid discharges (primarily the SRVSA discharge). In contrast, the channelized subsection of Cuckels Brook above the SRVSA discharge is often only inches 

deep with a bottom of bedrock, rubble, gravel and silt. 

Cuckels Brook (including Lower Cuckels Brook) is classified as FW-2 Nontrout in the NJDEP Surface Water Quality Standards. The FW-2 classification 

provides for the following uses: 

1. Potable water supply after such treatment as shall be required by 

law or regulation; 

2. Maintenance, migration, and propagation of natural and established 

biota (not including trout); 

3. Primary contact recreation; 

4. Industrial and agricultural water supply; and 

5. Any other reasonable uses. 

The attainment of these uses is currently prevented by the strength and 

volume of wastewaters currently riischarged to Cuckels Brook. The size of 

the stream also limits primary contact recreation and other water uses, and 

physical barriers currently prevent the migration of fish between Cuckels 

Brook and the Raritan River. 

C. Approach to Use Attainability 

In response to an inquiry from EPA, Criteria and Standards Division, the 

State of New Jersey offered to participate in a demonstration Water Body 

Survey and Assessment. The water body survey of Cuckels Brook was conducted 

by the New Jersey Department of Environmental Protection, Bureau of Systems 

Analysis and Wasteload Allocation; with assistance from the EPA Region II 

Edison Laboratory. 

The assessment is based primarily on the results of a field sampling program designed and conducted jointly by NJDEP and EPA-Edison in October 

1982. Additional sources of information include self-monitoring reports 

furnished by the dischargers, and earlier studies conducted by the NJDEP on 

Cuckels Brook and the Raritan River. Based on this assessment, NJDEP developed a report entitled "Lower Cuckels 8rook Water Body Survey and Use 

Attainability Analysis, 1983.” 

II. ANALYSES CONOUCTED 

A. Chemical Analysis 

The major impact of the SRVSA discharge is attributed to un-ionized ammonia 

and TRC levels, whose concentrations at Station 4, 100 feet below the discharge point were 0.173 and 1.8 mg/l respectively, which are 3.5 and 600 

D-20 
times higher than the State criteria. The un-ionized ammonia concentration 

of the Cyanamid effluent was low, but stream concentrations at Stations 6 

and 7 were relatively high (though below the State criterion of 0.05 mg/l). 

The Cyanamid discharge contained 0.8 mg/l TRC. Concentrations at both Stations 6 and 7 were 0.3 mg/l TRC, lower than at Station 4 but still 100 

times the State criterion of 0.003 mg/l. The other major impact of the Cyanamid effluent was on instream filterable residue levels. Concentrations 

at Stations 6 and 7 exceeded 1,100 rng/l, over three times the State criterion (133 percent of background). 

The effluents apparently buffered the pH of Lower Cuckels Brook which was 

approximately pH 7 at Stations 4, 6 and 7, and the pti of the upstream 

reference stations was markedly alkaline. Dissolved oxygen concentrations 

decreased in the downstream direction despite low 0005 concentrations both 

in the effluents and instream. This suggests an appreciable sediment oxygen 

demand in Lower Cuckels Brook. Dissolved oxygen levels were greater in the 

two effluents than in the stream at Stations 6 and 7. The dissolved oxygen 

concentration at Station 7 of 4.1 mg/l nearly violated the State criterion 

of 4.0 mg/l; this suggests the potential for unsatisfactory dissolved oxygen conditions during the Sumner. 

The results of the water body survey are generally in good agreement with 

other available data sources. Recent self-monitoring data for both American 

Cyanamid and SRVSA agree well with the data collected in this survey. In 

particular they show consistantly high TRC concentrations in both effluents. High average dissolved solids (filterable residue) concentrations are 

reported for the Cyanamid effluent. Total ammonia levels as high as 33.5 

mg/l NH3 (27.6 mg/l N) were reported for the SRVSA effluent. The pH of the 

Cyanamid and SRVSA effluents is sometimes more alkaline than the water body 

survey values indicating that toxic un-ionized amnonia concentrations may 

sometimes be higher than measured during the water body survey. 

8. Biological Analysis 

Fish and macroinvertebrate surveys were conducted in the channelized subsection of Cuckels Brook above the SRVSA discharge. Only three fish species 

were found: the banded killifish, the creek chub and the blacknose date. 

One hundred and eighty-six (186) out of the total 194 specimens collected 

were banded killifish. Killifish are very hardy and are common in both estuarine and freshwater systems. The largest fish found, a creek chub, was 

146 mm long. 

The results of the macroinvertebrate survey are discussed in detail in a 

separate report (NJDEP, 1982). Four replicate surber samples were collected 

at Stations 1 and 2 above the SRVSA discharge. Diversity indices indicate 

the presence of similar well-balanced communities at both stations. Species 

diversity and equitability were 3.9 and 0.7 respectively at Station 1, and 

4.3 and 0.7 respectively at Station 2. Productivity at Stations 1 and 2 was 

D-21 
low, with mean densities of 59 and 89 individuals per square foot, respectively. The majority of species found at both stations have organic pollution tolerance classifications of tolerant (dominant at Station 1) or facultative (dominant at Station 2). 

Overall, the biological data indicate that the upstream channelized subsection of Cuckels Brook supports a limited fish cotmnunity and a limited macroinvertebrate community of generally tolerant species. The water quality 

data indicates nothing that would limit the conmiunity. One possible limiting factor is that, as a result of channelization, the substrate consists 

of unconsolidated gravel and rubble on bedrock, which might easily be disturbed by high flow conditions. 

Both the chemical data and visual observations at various locations suggest 

that virtually no aquatic life exists along Lower Cuckels Brook: not even 

algae were seen. The discharges have seriously degraded water quality. Unionized ammonia concentrations at Station 4 were close to acute lethal 

levels, while concentrations of TRC were above acute levels at Stations 4, 

6 and 7 (EPA, 1976). The sludge deposits which apparently cover most of the 

bottom of lower Cuckels Brook could exert negative physical (i.e. smothering) and chemical (i.e. possible toxics) effects on any benthic organisms. 

No biological survey of the lower brook was made because of concern about 

potential hazards to sampling personnel. Supplemental sampling of the sediments is planned to ascertain levels of toxics accumulation. 

As part of their self-monitoring requirements, American Cyanamid performs 

weekly 96-hour modified flow-through bioassays with fathead minnows using 

unchlorinated effluent. Of 63 bioassays conducted between 1 May, 1981 and 

31 August, 1982, results from eight bioassays had 96-hour LC50 values at 

concentrations of effluent less than 100 percent (i.e. 26 percent, 58 percent, 77 percent, 83.5 percent, 88 percent, 92 percent, and 95.5 percent). 

These results suggest that the American Cyanamid effluent would not be extremely toxic if it were reasonably diluted by its receiving waters. Within 

Lower Cuckels Brook, however, the effluent receives only approximately 50 

percent dilution and the potential exists for toxic effects on any aquatic 

life that may be present. These effects would be in addition to the toxicity anticipated from the TRC concentrations which result from the chlorination of the effluent. 

III. FINDINGS 

Practically none of the currently designated uses are now being achieved in 

Lower Cuckels Brook. The principal current use of Lower Cuckels Brook is 

the conveyance of treated wastewater and upstream runoff to the Raritan 

River. Judging from the indirect evidence of chemical data and visual observations, virtually no aquatic life is maintained or propagated in Lower 

Cuckels Brook. It has been well documented that fish avoid chlorinated 

waters (Cherry and Cairns, 1982; Fava and Tsai, 1976). Any aquatic life 

that does reside in Lower Cuckels Brook would be sparse and stressed. Migration of aquatic life through Lower Cuckels Brook would probably only occur during periods of high storm water flow when some flow occurs over the 

n-22 
un-named dam (Figure 1) which is designed to direct the flow of Cuckels 

Brook toward Calco Dam. Calco Dam and its associated structures, including 

the un-named dam, normally prevent the migration of fish between Cuckels 

Brook and the Raritan River. 

Lower Cuckels Brook currently does not support any primary or secondary 

contact recreation. No water is currently diverted from Lower Cuckels Brook 

for potable water supply, industrial or agricultural water supply, or any 

other purpose. 

Because Lower Cuckels Brook receives large volumes of wastewater and because there is practically no dilution, water quality in Lower Cuckels 

Brook has been degraded to the quality of wastewater. Moreover, the bottom 

of Lower Cuckels Brook has been covered at observed locations with wastewater solids. As a result, Lower Cuckels Brook is currently unfit for aquatic life, recreation, and most other water uses. The technology-based effluent limits required by the Clean Water Act are not adequate to protect 

the currently designated water uses in Lower Cuckels Brook. SRVSA already 

provides secondary treatment (except for bypassed flows in wet weather), 

and American Cyanamid already provides advanced treatment with activated 

carbon. Because the Raritan River provides far more dilution than does 

Cuckels Brook, effluent limits which may be developed to protect the Raritan River would not be adequate to protect the currently designated water 

uses in Lower Cuckels Brook. The only practical way to restore water quality in Lower Cuckels Brook would be to remove the wastewater discharges. 

However, there are several factors that would limit the achievement of currently designated uses even if the wastewater discharges were completely 

separated from natural flow. 

If it were assumed that the wastewater discharges and sludge were absent, 

and that the seepage of contaminated groundwater from the American Cyanamid 

property was insignificant or absent, then the following statements could 

be made about attainable uses in Lower Cuckels Brook: 

- The restoration of aquatic life in Lower Cuckels Brook 

lmlted to some extent by the small size and lower flow of the 

stream, by channelization, and by contaminants in suburban and highway 

runoff from the upstream watershed. Lower Cuckels Brook could support a 

limited macroinvertebrate community of generally tolerant species, and 

some small fish as were found in the reference channelized subsection 

above the SRVSA discharge (Stations 1 and 2). Unless it were altered or 

removed, the Calco Dam complex would continue to prevent fish migration. 

Wildlife typical of narrow stream corridors could inhabit the generally 

narrow strips of land between Lower Cuckels Brook and nearby railroad 

tracks and waste lagoons. Restoration of aquatic life in Lower Cuckels 

Brook would be expected to have little impact on aquatic life in the 

Raritan River. 

D-23 
Recreation - Lower Cuckels Brook would be too shallow for swlmning 

or boating, and its small fish could not support sport flshlng. 

The industrial surroundings of Lower Cuckels Brook, Includjng 

waste lagoons and active manufacturing facilities and rallroads, 

severely reduces the potentlal for other recreational actlvlties 

such as streamside trails and pfcnlc areas, wading, and nature 

appreciation. As Lower Cuckels Brook is on private Industrial 

property, trespassing along thls brook and 1n the surroundlng area 

is discouraged. 

It would appear unlikely that any of the landowners, or any 

government agency, would develop recreational facilities along 

lower Cuckels Brook or even remove some of the brush which impalrs 

access to most of the Brook. Recreation along Lower Cuckels Brook 

would be limited, occasional, and informal. 

Other Water Uses - Although water quality In Lower Cuckels Brook 

would generally meet FM-2 Nontrout criteria, the volume of natural 

flow in Lower Cuckels Brook would be insufflc1ent for potable 

water supply or for Industrjal or agricultural water use. 

In general, Lower Cuckels Brook would become a small channellzed 

tributary segnent flowing through a heavily industrlallzed area, free 

of gross pollution and capable of supportlng a modest aquatlc community 

and very limited recreatIona use. 

IV. SUMMARY AND CONCLUSIONS 

This use-attainability analysis has discussed the present impalnent of 

the currently designated uses of Lower Cuckels Brook, the role of 

wastewater discharges in such Impairment, and the extent to which 

currently designated water uses might be achieved If the wastewater 

discharges were removed. Further analysis, outside the scope of this 

survey, will be required: to document the costs of removjng SRVSA and 

American Cyanamid effluent from Lower Cuckels Brook, and to evaluate 

the impact of the SRVSA and American Cyanamld discharges on the Raritan 

River. These analyses may lead to the development of site-specific 

water quality standards for Lower Cuckels Brook (designated uses 

llmited to the conveyance of wastewater and the preventlon of 

nuisances), or to the removal of the wastewater discharges from Lower 

Cuckels Brook. In either case, effluent limits would be established tc 

protect water quality In the Raritan River. 

D-24 
WATER BODY SURVEY AND ASSESSMENT 

Deep Creek And Canal Creek 

Scotland Neck, North Carolina 

I. INTRODUCTION 

A. Site Description 

The Town of Scotland Neck is located in Halifax County in the lower coastal 

plain of North Carolina. The Town's wastewater, made up mostly of domestic 

waste with a small amount of textile waste, is treated in an oxidation 

ditch of 0.6 mgd design capacity. The treatment plant is located two-tenths 

of a mile southwest of Scotland Neck off U.S. Highway 258, as seen in Figure 1. The effluent (0.323 mgd average) is discharged to Canal Creek which 

is a tributary to Deep Creek. 

Canal Creek is a channelized stream which passes through an agricultural 

watershed, but also receives some urban runoff from the western sections of 

Scotland Neck. It is a Class C stream with a drainage area of 2.4 square 

miles, an average stream flow of 3.3 cfs, and a 7010 of 0.0 cfs. The Creek 

retains definite banks for about 900 feet below the outfall at which point 

it splits into numerous shifting channels and flows BOO to 1400 feet 

through a cypress swamp before reaching Deep Creek. Curing dry periods the 

braided channels of Canal Creek can be visually traced to Deep Creek. During wet periods Canal Creek overflows into the surrounding wetland and flow 

is no longer restricted to the channels. 

Deep Creek is a typical tannin colored Inner Coastal Plain stream that has 

a heavily wooded paludal flood plain. The main channel is not deeply entrenched. In some sections streamflow passes through braided channels, or 

may be conveyed through the wetland by sheetflow. During dry weather flow 

periods the main channel is fairly distinct and the adjacent wetland is 

saturated, but not inundated. During wet weather periods the main channel 

is less distinct, adjacent areas become flooded and previously dry areas 

become saturated. 

8. Problem Oefinition 

The Town of Scotland Neck is unable to meet its final NPDES Permit limits 

and is operating with a Special Order by Consent which specifies interim 

limits. The Town is requesting a 201 Step III grant to upgrade treatment by 

increasing hydraulic capacity to 0.675 mgd with an additional clarifier, an 

aerobic digestor, tertiary filters, a chlorine contact chamber, post aeration and additional sludge drying beds. The treated effluent from Scotland 

Neck is discharged into Canal Creek. The lower reaches of Canal Creek are 

part of the swamp through which Deep Creek passes. 

D-25 
-- 

\ 

\‘ .- 

m, - 

. f. - ’ ? 

-, 

5 n ’ 

- ‘-. 

-- 

-1 - 

- 

L 11,. ** -.rs. ,. ’ - - 

et <r 

+ -- 

- -,c- .i---““‘~’ \ 

- 

g+y 

,..--.. 

,i: 

‘1m. 

cm -*..$‘,” “\-, . 

----I 

. . 

\. j’ ; 

! 1 

-- 

Figure 1. Study Area, Deep Creek 

and Canal Creek 

D-26 
Deep Creek carries a "C" classification, but due to naturally low dissolved 

oxygen and other conditions imposed by the surrounding swamp, it is felt 

that reclassification to "C-Swamp" should be considered. Deep Creek should 

be classified C-Swamp because its physical characteristics meet the C-Swamp 

classification of the North Carolina Administrative Code for Classifications and Water Quality Standards. The Code states: Swamp waters shall mean 

those waters which are so designated by the Environmental Management Commission and which are topographically located so as to generally have very 

low velocities and certain other characteristics which are different from 

adjacent streams draining steeper topograpy. The C-Swamp classification 

provides for a minimum pH of 4.3 (compared to a range of pH 6.0 to pH 8.5 

for C waters), and allows for low (unspecified) DO values if caused by natural conditions. 00 concentrations in Deep Creek are usually below 4.0 

W/l. 

C. Approach to Use Attainability Analysis 

1. Data Available 

1. Self Monitoring Reports from Scotland Neck. 

2. Plant inspections by the Field Office. 

3. Intensive Water Quality Survey of Canal Creek and Deep Creek at 

Scotland Neck In September, 1979. Study consisted of time-oftravel dye work and water quality sampling. 

2. Additional Routine Data Collected 

Water quality survey of Canal Creek and Deep Creek at Scotland Neck 

in June 1982. Water quality data was collected to support a biological survey of these creeks. The study included grab samples and flow 

measurements. 

Benthic macroinvertebrates were collected from sites on Canal Creek 

and Deep Creek. Qualitative collection methods were used. A twomember team spent one hour per site collecting from as many habitats 

as possible. It is felt that this collection method is more reliable 

than quantitative collection methods (kicks, Surbers, ponars, etc.1 

in this type of habitat. Taxa are recorded as rare, common, and 

abundant. 

II. ANALYSES CONDUCTED 

A. Physical Factors 

Sampling sites were chosen to correspond with sites previously sampled in a 

water quality survey of Canal and Deep Creeks. Three stations were selected 

on Canal Creek. SN-1 is located 40 feet above the Town of Scotland Neck 

Wastewater Treatment Plant outfall. This site serves as a reference station. The width at SN-1 is 7.0 feet and the average discharge (two flows 

were recorded in the September 1979 survey and one flow in the June 1982 

D-27 
survey) is 0.65 cubic feet per second. Canal Creek at SN-1 has been channelized and has a substrate composed of sand and silt. SN-4 is located on 

Canal Creek 900 feet below the discharge point. This section of Canal Creek 

has an average cross-sectional area of 11.8 feet and an average flow of 

1.33 cubic feet per second. The stream in this section is also channelized 

and also has a substrate composed of sand and silt. There is a canopy of 

large cypress at SN-4 below the plant, while the canopy above SN-1 is reduced to a narrow buffer zone. The potential uses of Deep Creek are limited 

by its inaccessability in these areas. 

A third station (SN-5) was selected on one of the lower channels of Canal 

Creek at the confluence with Deep Creek 3200 feet upstream of the U.S. 

Highway 258 bridge. Discharge measurements could not be accomplished at 

this site during this survey because of the swampy nature of the stream 

with many ill-defined, shallow, slow moving courses. Renthic macroinvertebrates were collected from this site. 

Three stations were chosen on Deep Creek. SN-6 is approximately 300 feet 

upstream of SN-5 on Canal Creek at its confluence with Deep Creek and is a 

reference site. SN-7 is located at the U.S. Highway 258 bridge and SN-8 is 

located further downstream at the SR 1100 bridge. SN-7 and SN-8 are below 

Canal Creek. There are some differences in habitat variability among these 

three sites. The substrate at both SN-6 and SN-7 is composed mostly of a 

deep layer of fine particulate matter. Usable and productive benthic habitats in this area are reduced because of the fine particulate layer. It is 

possible that the source of this sediment is from frequent overbank flows 

and from upstream sources. Productive benthic habitats include areas of 

macrophyte growth, snags, and submerged tree trunks. Discharge measurements 

were not taken at any of these three sites during this survey. 

B. Chemical Factors 

Chemical data from two water qualit 

6 

surveys show that the dissolved oxygen 

in Canal Creek is depressed while B 0 

5 

, solids and nutrient levels are elevated. The 1982 study indicates, howe er, that the water quality is better 

than it was during the 1979 survey. Such water quality improvements may be 

due to the addition of chlorination equipment and other physical improvements as well as to the efforts of a new plant operator. 

Both above and below its confluence with Canal Creek, Deep Creek shows poor 

water quality which may be attributed to natural conditions, but not to any 

influence from the waste load carried by Canal Creek. Canal Creek exhibited 

higher DO levels than Deep Creek. 

C. Biological Factors 

The impact of the effluent on the fauna of Canal Creek is clear. A 63 percent reduction in taxa richness from 35 at SN-1 to only 13 at SN-4 indicates severe stress as measured against criteria developed by biologists of 

the Water Quality Section. The overwhelming dominance of Chironomus at SN-4 

O-28 
is indicative of a low 00 level and high concentrations of organic matter. 

To what extent this condition is attributable to the effluent or to natural 

swamp conditions is not clear, No impact to the benthos of Deep Creek was 

discerned which could be attributed to the effluent. 

III. FINDINGS 

Deep Creek is currently designated as a class C warm water fishery but due 

to naturally low dissolved oxygen concentrations may not be able to satisfy 

the class C dissolved oxygen criteria. The 00 criterion for class C waters 

stipulates a minimum value of 4 ppm, yet the DO in Deep Creek, in both the 

1979 and the 1982 studies, was less than 4 ppm. Thus from the standpoint of 

aquatic life uses, Deep Creek may not be able to support the forms of aquatic life which are intended for protection under the class C standards. 

Because of prevailing natural conditions, there are no higher potential 

uses of Deep Creek than now exist; yet because of prevailing natural conditions and in light of the results of this water body assessment, the Cswamp use designation appears to be a more appropriate designation under 

existing North Carolina Water Quality Standards. 

Canal Creek is degraded by the effluent from the Scotland Neck wastewater 

treatment plant. The BOO 

8 

, fecal coliform, solids and nutrient levels are 

elevated while the 00 c ncentration is depressed. The reach immediately 

below the outfall is affected by an accumulation of organic solids, by discoloration and by odors associated with the wastewater. 

IV. SUMMARY AND CONCLUSIONS 

The water body survey of Deep Creek and Canal Creek included a consideration of physical, chemical and biological factors. The focus of interest 

was those factors responsible for water quality in Deep Creek, including 

possible deliterious effects of the Scotland Neck wastewater on this water 

body. The analyses indicate that the effluent does not appear to affect 

Deep Creek. Instead, the water quality of Deep Creek reflects natural conditions imposed by seasonal low flow and high temperature, and reflects the 

nutrient and organic contribution of the surrounding farmland and wetland. 

It is concluded that the C-Swamp designation more correctly reflects the 

uses of Deep Creek than does the C designation. 

In contrast to Deep Creek, Canal Creek is clearly affected by the treated 

effluent. Further examination would be required to determine the extent of 

recovery that might be expected in Canal Creek if the plant were to meet 

current permit requirements or if the proposed changes to the plant were 

incorporated into the treatment process. 

o-29 
WATER RODY SURVEY AND ASSFSSMENT 

Malheur River 

Malheur County, Oregon 

I INTRDDUCTIDh 

A. Site Description 

The Malheur River, in southeastern Oregon, flows eastward to 

the Snake River which separates Dregon from Idaho. Most of 

Malheur County is under some form of agricultural production. 

With an averaqe annual precipitation of less than 111 inches, 

the delivery of irrigation water is essential to maintain the 

hiqh aqricultural productivity of the area. 

The Malheur River system serves as a major source of water for 

the area's irrigation requirements (out of basin transfer of 

water from Owyhee Reservoir augments the Malheur supply). 

Reservoirs, dams, and diversions have heen built on the 

Malheur and its tributaries to supply the irrigation network. 

The first major withdrawal occurs at the Namorf Dam and 

Diversion, at Malheur River Mile 69. Figure 1 presents a 

schematic of the study area. 

Irrigation water is delivered to individual farms by a 

complicated system of canals and laterals. Additional water 

is obtained from drainage canals and groundwater sources. An 

inteqral part of the water distribution system is the use and 

reuse of frriqation return flows five or six times before it 

is finally discharqed to the Snake River. 

R. Problem Definition 

The Malheur River above Flamorf Dam and Diversion is managed 

primarily as a trout fishery, and from Namorf to the mouth as 

a warm-water fishery. The upper portion of the river system 

is appropriately classified. Relow Namorf Dam, however, the 

river is inappropriately classified as supporting a cold-water 

fishery, and therefore was selected for review. This review 

was conducted as part of the U.S. Environmental Protection 

Agency's field test of the draft "Water Body Survey and 

Assessment Guidance" for conducting a use attainability 

analysis. The guidance document supports the proposed rule to 

revise and consolidate the existing regulation governing the 

development, review, and approval of water quality standards 

under Section 303 of the Clean Water Act. 

c ,. Approach to Use Attainability Analysis 

Assessment of the Malheur River is based on a site visit which 

included meetings with representatives of the Malheur County 

Citizen's Water Resources Committee, the USDA-Soil 

Conservation Service, the Dreqon Department of Environmental 

U-30 
MIDDLE FORK OF 

MALHEUR RIVER 

WARM SPRINGS 

RESERVOIR 

SOUTH FORK 

RESERVOIR 

MALHEUR RIVER ALHEUR RIVER -‘vf 

M 

POLE CREEK 

MALHEUR - 

I RIVER 7 

il 

NAMORF 

DIVERSION 

CQTTONWOOO 

CREEK 

LITTLC 

VALLEY VALECANAL Off EGON 

J-H CANAL 

-- I 

GELLERMAN-FROUAN 

CANAL 

NEVADA 

- CANAL 

SNAKE RIVER - 

SIMPLIFIED FLOW SCHEMATIC 

MALHEUR RIVER IRRIGATION SYSTEM 

- FIGURE I - 

D-31 
nualfty (DDEQ), the Oregon Department of Fish and Wildlife 

(CIDFW), and the U.S. Environmental Protection Agency (EPA): 

and upon the findings reported in two studies: 

Final Report, Two Year Sampling Program, Malheur County 

hater Duality Management Plan, Malheur County Planning 

dfffce, Vale, Oregon, 1981. 

Bowers, Hosford and Moore, Stream Surveys of the Lower 

Owyhee and Malheur Rivers, A-Report to the Malheur County 

Qater Resources Committee, Oregon Department of Fish and 

IJlldllfe, January, 1979. 

The first report, prepared under amendments to Section 208 of 

the Clean Water Act, contains extensive information on the 

quantity, quality and disposition of the areas' water 

resources. The second document gives the fish populations 

found in the lower 69 miles of the Malheur River during June 

and July, 1978. Information in the DDFW report is 

incorporated in the 208 report. Additional fisheries 

information supplied by DDFW was also considered. 

A representative of DDEO, Portland, and the Water Duality 

Standards Coordinator, EPA Region X, Seattle, Washington, 

agreed that the data and analyses contained in these two 

reports were sufficient to re-examine existing designated uses 

of the Malheur River. 

II ANALYSES CONDUCTED 

Physical, chemical, and biological data were reviewed to 

determine: (1) whether the attainment of a salmonid fishery was 

feasible in the lower Malheur; and (2) whether some other 

designated use would be more appropriate to this reach. The 

elements of this review follow: 

A. Physical Factors 

Historically, salmonfd fish probably used the lower Malheur 

(lower SO miles) mainly as a migration route, because of the 

warm water and poor habitat. The first barrier to upstream 

fish migration was the Nevada Dam near Vale, constructed in 

mn. Construction of the Warm Springs Dam in 1918, ended the 

anadromous fish runs in the Middle Fork Malheur. The 

construction of Reulah Dam in 1931, befell the remainder of 

anadromous fish runs on the North Fork Malheur. Finally, the 

construction of Brownlee Reservoir in 1958 completely blocked 

salmonfd migrants destined for the upper Snake River System. 

D-32 
With the construction of the major irrigation reservoirs on 

the Malheur River and its tributaries, the natural flow 

characteristics in the lower river have chanqed. Instead of 

high early summer flows, low summer and fall flows and steady 

winter flow, the peak flows may occur in spring, if and when 

the upstream reservoirs spill. Also, a high sustained flow 

exists all summer as water is released from the dams for 

irrigation. A significant change limiting fish production in 

the Malheur River below Namorf is the extreme low flow that 

occurs when the reservoirs store water during the fall and 

winter for the next irrigation season. 

Two other physical conditions affect the maintenance of 

salmonids in the lower Malheur. One is the high suspended 

solids load carried to the river by irrigation return flows. 

High suspended solids also occur during wet weather when high 

flows erode the stream bank and re-suspend bottom sediments. 

The seasonal range of suspended solids content is pronounced, 

with the highest concentrations occurring during irrigation 

season and during periods of wet weather. Observed peaks in 

lower reaches of the river, measured during the two-year 2D8 

Program, reached 13DD mg/l, while hackground levels rarely 

dropped below 50 mg/l. A high suspended solids load in the 

river adversely affects the ability of sight-feeding salmonids 

to forage, and may limit the size of macroinvertebrate 

populations and algae production which are important to the 

salmonid food chain. A second factor is high summer water 

temperature which severely stresses salmonids. The high 

temperatures result from the suspended particles absorbing 

solar radiation. 

B. Riological Factors 

The biological profile of the river is mainly based on 

fisheries information, with some macroinvertebrate samples 

gathered by the Oregon Department of Fish and Wildlife (ODFW) 

in 1978. During the site visit, the participants agreed 

additional information on macroinvertebrates and periphyton 

would not be needed because the aquatic insect numbers and 

diversity were significantly greater in the intensively 

irrigated reach of the river than for the upper river where 

agricultural activity is sparse. 

Although the Malheur River from Namorf to the mouth is managed 

as a warm water fishery, ODFW has expended little time and few 

resources on this stretch of the river because it is not a 

productive fish habitat. Survey results in summer of 1978 

showed a low ratio of game fish to rough fish over the lower 

69 miles of the Malheur River. 

D-33 
In the section between Namorf and the Gellerman-Froman 

Diversion Dam there was little change in water quality 

although water temperatures were elevated. 

fish were 

Only three game 

captured but non-game fish sight-feeders were 

cornnon. Low winter flows over a streambed having few deep 

pools for overwinter survival appears to limit fish production 

in this reach of river. 

In the stretch from the Gellenan-Froman Diversion to the 

mouth, the river flows through a region of intensive 

cultivation. The river carries a high silt load which affects 

sight-feeding fish. Low flows immediately below the 

Gellerman-Froman Dam also limit fish production in this area. 

c s. Chemical Factors 

A considerable amount of chemical data exist on the Malheur 

River. However, since the existing and potential uses of the 

river are dictated largely by physical constraints, dissolved 

oxygen was the only chemical parameter considered in the 

assessment. 

The Dissolved Oxygen Standard established for the Malheur 

River Rasin calls for a minimum of 7S percent of saturation at 

the seasonal low and 95 percent of saturation in spawning 

areas or during spawning, hatching, and fry stages of salmonid 

fishes. One sample collected at Namorf fell below the 

standard to 73 percent of saturation or 8.3 mg/l in Novemher, 

1970. All other samples were ahove this content, reaching as 

high as 170 percent of saturation during the summer due to 

algae. Data collected by the DDE0 from Malheur River near the 

mouth between 1976 and 1979 showed the dissolved oxygen 

content ranged from 78 to 174 percent saturation. The 

dissolved oxygen content in the lower Malheur River is 

adequate to support a warm-water fishery. 

III FIN@INGS 

A. Existing Uses 

The lower Malheur River is currently designated as a salmonid 

fishery, but it is managed as a warm water fishery. Due to a 

number of physical constraints on the lower river, conditions 

are generally unfavorahle for game fish, so rough fish 

predominate. In practice, the lower Malheur River serves as a 

source and a sink for irrigation water. This type of use 

contributes to water quality conditions which are unfavorable 

to salmonids. 

D-34 
8. Potential JJses 

Salmonfd spawning and rearing areas generally require the 

highest criteria of all the established beneficial uses. It 

would be impractical, if not impossible in some areas, to 

improve water quality to the level required by salmonids. 

However, even if this could be accomplished, high summer 

temperatures and seasonal low flows would still prevail. 

While salmonids historically moved through the Malheur River 

to spawn in the headwater areas, year-round resident fish 

populations probably did not exist in some of these areas at 

the time. 

The Malheur River basin can be divided into areas, based upon 

differing ma,ior uses. Suggested divisions are: (1) headwater 

areas above the reservoirs; (2) reservoirs; (3) reaches below 

the reservoirs and above the intensively irrigated areas: (4) 

intensively irrigated areas; and (5) the Snake River. 

In intensively irrigated areas, criteria should reflect the 

primary use of the water. Higher levels of certain parameters 

ife.ee;,;;;;ended :qrlJ$;, nutrfen:;ic;emperature, etc.) should 

ln areas lntenslvely irrigated 

agriculture, even under ideal conditions, will unavoidably 

contribute higher levels of these parameters. Criteria, 

therefore, should be based on the conditions that exist after 

Rest Management Practices have been implemented. 

IV SUMMARY AND CONCLUSIONS 

Malheur River flows have been extensively altered through the 

construction of several dams and diversion structures designed to 

store and distribute water for agricultural uses. These dams, as 

well as others on the Snake River, to which the Malheur is 

tributary, block natural fish migrations in the river and, thus, 

have permanently altered the river's fisheries. In addition, 

water quality below Namorf Dam has been affected, primarily 

through agricultural practices, in a way which severely restricts 

the type of fish that can successfully inhabit the water. One 

important factor which affects fish populations below Namorf is 

the high suspended solids loading which effectively selects 

against sight-feeding species. Other conditions which could 

affect the types and survival of fish species below Namorf include 

low flow during the fall and winter when reservoirs are being 

filled in preparation for the coming irrigation season, as well 

as high suspended solids, and high temperatures during the summer 

irrigation season. 

Realistically, the Malheur River could not be returned to its 

natural state unless a large number of hydraulic structures were 

removed. Removal of these structures would result in the demise 

of agriculture in the region, which is the mainstay of the 

D-35 
county's economy. Furthermore, removal of these structures is out 

of the question due to the legal water rights which have been 

established in the region. These water rights can only be 

satisfied through the system of dams, reservoirs, and diversions 

which have been constructed in the river system. Thus, the 

changes in the Malheur River Basin are irrevocable. 

Physical barriers to fish migration coupled with the effects of 

hiqh sediment loads and the hydraulics of the system have for 

years established the uses of the river. Given the existing 

conditions and uses of the Malheur River below the Namorf 

Diversion, classification of this river each should be changed 

from a salmonid fishery, a use that cannot be achieved, to 

achievable uses which are based on the existing resident fish 

populations and aquatic life to reflect the present and highest 

future uses of the river. Such a change in designated beneficial 

uses would not further jeopardize existing aquatic life in the 

river, nor would it result in any degradation in water quality. 

D-36 
WATER BODY SURVEY AND ASSESSMENT 

Pecan Bayou 

Brownwood, Texas 

I. INTRODUCTION 

A. Site Description 

Segment 1417 of the Colorado River Basin (Pecan Bayou) originates 

below the Lake Brownwood Dam and extends approximately 57.0 miles to 

the Colorado River (Figure 1). The Lake Brownwood Dam was completed in 

1933. Malfunction of the dam's outlet apparatus led to its permanent 

closure in 1934. Since that time, discharges from the reservoir occur 

only infrequently during periods of prolonged high runoff conditions in 

the watershed. Dam seepage provides the base flow to Pecan Bayou 

(Segment 1417). The reservoir is operated for flood control and water 

supply. The Brown County WID transports water from the reservoir via 

aqueduct to Brownwood for industrial distribution, domestic treated 

water distribution to the Cities of Brownwood and Bangs and the 

Brookesmith Water System, and irrigation distribution. Some irrigation 

water is diverted from the aqueduct before reaching Brownwood. 

Pecan Bayou meanders about nine miles from Lake Brownwood to the 

City of Brownwood. Two small dams impound water within this reach, and 

Brown County WID operates an auxilliary pumping station in this area to 

supply their system during periods of high demand. 

Two tributaries normally provide inflow to Pecan Bayou. Adams 

Branch enters Pecan Bayou in Brownwood. The base flow consists of 

leaks and overflow in the Brown County WID storage reservoir and 

distribution system. Willis Creek enters Pecan Bayou below Brownwood. 

The base flow in Willis Creek is usually provided by seepage through a 

soil conservation dam. 

The main Brownwood sewage treatment plant discharges effluent to 

Willis Creek one mile above its confluence with Pecan Bayou. Sulfur 

Draw, which carries brine from an artesian salt water well and 

wastewater from the Atchison, Topeka and Santa Fe Railroad Co., enters 

Willis Creek about 1,700 feet below the Brownwood sewage treatment 

plant. Below the Willis Creek confluence, Pecan Bayou meanders about 

42.6 miles to the Colorado River, and receives no additional inflow 

during dry weather conditions. Agricultural water withdrawals for 

irrigation may significantly reduce the streamflow during the growing 

season. 

The Pecan Bayou drainage basin is composed primarily of range and 

croplands. The stream banks, however, are densely vegetated with 

trees, shrubs and grasses. The bayou is typically lo-65 feet wide, 2-3 

feet deep, and is generally sluggish in nature with soft organic 

sediments. 

D-37 
BROWNWOOO 

-- -- 

--- 

Figure 1 

PECAN BAYOU SEGMENT MAP 

D-37A 
B. Problem Definition 

The designated water uses for Pecan Bayou include noncontact 

recreation, propagation of fish and wildlife, and domestic raw water 

supply. Criteria for dissolved oxygen (minimum of 5.0 mg/l), 

chlorides, sulfates, and total dissolved solids (annual averages not to 

exeed 250, 200, and 1000 mg/l, respectively), pH (range of 6.5 to 9.0) 

fecal coliform (log mean not to exceed lOOO/lOO ml), and temperature 

(maximum of 9D°F) have been established for the segment. 

Historically, Pecan Bayou is in generally poor condition during 

Sumner periods of low flow, when the Brownwood STP contributes a 

sireable portion of the total stream flow. During low flow conditions, 

the stream is in a highly enriched state below the sewage outfall. 

Existing data indicate that instream dissolved oxygen 

concentrations are frequently less than the criterion, and chloride 

and total dissolved solids annual average concentrations occasionally 

exceed the estahlfshed criteria. The carbonaceous and nitrogenous 

oxygen deficencies in Pecan Bayou. The major cause of elevated 

chlorides in Pecan Bayou is the artesian brine discharge in to Sulfur 

Draw. 

Toxic compounds (PCB, DDT, DDD, DDE, Lindane, Heptachlor epoxide, 

Dieldrin, Endrin, Chlordane, Pentachlorophenol, cadmium, lead, silver, 

and mercury) have been observed in water, sediment and fish tissues in 

Pecan Bayou (mainly below the confluence with Willis Creek). It has 

been determined that the major source was the Brownwood STP, but 

attempts to specifiy the points of origin further have been 

unsuccessful. However, recent levels show a declining trend. 

C. Approach to Use Attainability 

Assessment of Pecan Bayou is based on a site visit which included 

meetings with representatives of the State of Texas, EPA (Region VI and 

Headquarters) and Camp Dresser & McKee Inc., and upon information 

contained in a number of reports, memos and other related materials. 

It was agreed by those present during the site visit that the data 

and analyses contained in these documents were sufficient for an 

examination of the existing designated uses of Pecan Bayou. 

II. ANALYSES CONDUCTED 

An extensive amount of physical, chemical, and biological data has 

been collected on Pecan Bayou since 1973. Most of the information was 

gathered to assess the impact of the Brownwood STP on the receiving 

stream. In order to simplify the presentation of these data, Pecan 

Bayou was divided into three zones (Figure 1): Zone 1 is the control 

area and extends from the Lake Brownwood Dam (river mile 57.0) to the 

Willis Creek confluence (river mile 42.6): Zone 2 is the impacted area 

and extends 9.n miles below the Willis Creek confluence. 

D-38 
A. Physical Evaluation 

With the exception of stream discharge, the physical 

characteristics of Pecan Bayou are relatively homogeneous by zone. 

Average width of the stream is about 44-511 feet, and average depth 

ranges from 2.1 to 3.25 feet. The low gradient (2.8 to 3.9 ft/mile) 

causes the bayou to be sluggish (average velocity of about 0.1 ft/sec), 

reaeration rates to be low (K2 of 0.7 per day at 20°C). and pools to 

predominate over riffles (965 to 4Y). Stream temperature averages 

about 18°C and ranges from l-32°C. The substrate is composed primarily 

of mud (sludge deposits dominate in Zone 2), with small amounts of 

bedrock, gravel and sand being exposed in riffle areas. 

Rase flow in Pecan Bayou is provided by dam seepage (Zone 1) and 

the treated sewage discharge from the City of Brownwood (Zones 2 and 

3). Median flow increases in a downstream direction from 2.5 cfs in 

Zone 1 to 17.4 cfs in Zone 3. Significantly higher mean flows (118 cfs 

in Zone 1 and 125 cfs in Zone 3) are'the result of periodic high 

rainfall runoff conditions in the watershed. 

B. Chemical Evaluation 

Existing chemical data of Pecan Bayou characterize the degree of 

water quality degradation in Zone 2. Average dissolved oxygen levels 

are about 2.0 mg/l lower in the impact zone, and approximately 50? of 

the observations have been less than 5.0 mg/l. BOD5, ammonia, 

nitrite, nitrate, and phosphorus levels are much hiqher in the impact 

zone as compared to the control and recovered zones. Iln-ionized 

amonia levels are also higher in Zone 2, but most of the 

concentrations were below the reported chronic levels allowable for 

warm water fishes. None of the levels exceeded the reported acute 

levels allowable for warm water fishes, and less than 4:! of the levels 

were between the acute and chronic levels reported. Total dissolved 

solids, chlorides and sulfates were higher in Zones 3 and 3, mainly as 

a result of the hrine and sewage discharges into Sulfur Draw and Willis 

Creek. 

PCR, DDT, DDD, DDE and Lindane in water, and PCB, DDD, and DDE, 

Heptachlor epoxide, Dfeldrfn, Endrin, Chlordane, and Pentachlorophenol 

in sediment have been detected in Zone 2. PCB, DDT, DDD, and DDE 

concentrations in water have exceeded the criteria to protect 

freshwater aquatic life. The Rrownwood STP was the suspected major 

source of these pesticides. Most of the recent levels, however, show a 

declining trend. PCB was detected also in Zones 1 and 3. 

Heavy metals have not been detected in the water. Heavy metals in 

the sediment have shown the hlghest levels in Zone 2 for arsenic (3.7 

mq/kq), cadmfun (1.1 mg/kg), chromiun (17.4 mg/kg), copper (9.5 mg/kg), 

lead (25.1 mg/kg), silver (1.5 mg/kg), zinc (90 mg/kg), and mercury 

(0.18 mg/kd. 

D-39 
C. Biological Evaluation 

Fish samples collected from Zone 1 are representative of a fairly 

healthy population of game fish, rough fish and forage species. Zone 2 

supported a smaller total number of fish which were composed primarily 

of rough fish and forage species. A relatively healthy balance of game 

fish, rough fish and forage species reappeared in the recovered zone. 

Macrophytes were sparse in Zones 1 and 3. They were most abundant 

in Zone 2 below the Willis Creek confluence and were composed of 

vascular plants (pondweed, coontail, false loosestrife and duckweed) 

and filamentous algae (Clad0 hora and 

abundance below Willis Cree +s most 

of the area from the Brownwood STP. 

Zone 1 is represented by a fairly diverse macrobenthfc community 

characteristic of a clean-water mesotrophic stream. Nutrient and 

organic enrichment in Zone 2 has a distinct adverse effect as 

clean-water organisms are replaced by pollution-tolerant forms. Some 

clean-water organisms reappeared in Zone 3 and pollution-tolerant forms 

were not as prevalent; however, recovery to baseline conditions (Zone 

1) was not complete. 

Net phytoplankton desnities are lowest in Zone 1. Nutrient and 

organic enrichment in Zone 2 promotes a marked increase in abundance. 

Peak abundance was observed in the upper part of Zone 3. The decline 

below this area was probably caused by biotic grazing and/or nutrient 

deficiencies. 

Fish samples for pesticides analyses have revealed detectable 

levels of PCB, DDE and DDD in Zone 1. Fish collected from zone 2 

contained markedly higher amounts of DDE, DDO, DDT, Lfndane and 

Chlordane than Zones 1 or 3. PCB in fish tissue was highest in ZOne 3, 

and measureable concentrations of DDE and DDD have also been observed. 

Concentrations of total DDT in whole fish tissues from Zone 2 have 

exceeded the USFDA Action Level of 5.0 mg/kg for edible fish tissues. 

Species representing the highest concentrations. 

Computer modeling simulation were made to predict the dissolved 

oxygen profile in the impact zone during the fish spawning season. The 

results indicate that about three miles of Pecan Bayou in April and May 

and about 4 l/2 miles in June will be unsuitable for propogatfon, 

considering a minimum requirement of 4.0 mg/l. The model predicts a 

minimum D.O. of 0.8 mg/l in April, 1.2 mg/l in May, and 0 mg/l in 

June. 

D-40 
D. Institutional Evaluation 

Two institutional factors exist which constrain the situation that 

exists in Pecan Bayou. These are the irrigation water rights and the 

Brownwood sewage treatment plant discharge permits. Although the 

sewage treatment plant discharge permits will expire and the problems 

created by the effluent could be eliminated in the future, there is a 

need for the flow provided by the discharge to satisfy the downstream 

water rights used for irrigation. Currently, there are eight water 

users on Pecan Bayou downstream of the Brownwood STP discharge with 

water rights permits totaling 2,957 acre-feet/year. Obviously, the 0.1 

cfs base flow which exists in Pecan Bayou upstream of the STP discharge 

is not sufficient to fulfill these downstream demands. Therefore, it 

appears that the STP flow may be required to supplement the base flow 

in Pecan Bayou to meet the downstream demands for water unless it could 

be arranged that water from Lake Brownwood could be released by the 

Brown Co. WID $1 to meet the actual downstream water needs. 

Modeling studies show that although there would be some 

improvement in water quality as a result of the sewage treatment plant 

going to advanced waste treatment (AWT), there would still be D.O. 

violations in a portion of Pecan Bayou in Zone 2. The studies also 

show that there is minimal additional water quality improvement between 

secondary and advanced waste treatment, although the costs associated 

with AWT were significantly higher than the cost for secondary 

treatment. In this case, the secondary treatment alternative would be 

the recorrmended course of action. 

III. FINDINGS 

A. Existing Uses 

Pecan Bayou is currently being used in the following ways: 

o Domestic Raw Water Supply 

o Propagation of Fish and Wildlife 

' Noncontact Recreation 

0 Irrigation 

O City of Brownwood STP discharge (not an acceptable or approved 

use designation) 

Use as a discharge route for the City of Brownwood's sewage treatment 

plant effluent has contributed to water quality conditions which are 

unfavorable to the propagation of fish and wildlife in a portion of 

Pecan Bayou. 

B. Potential Uses 

The Texas Department of Water Resources has established water uses 

which are deemed desirable for Pecan Bayou. These uses include: 

noncontact recreation, propagation of fish and wildlife, and domestic 

raw water supply. 

n-41 
Of these uses, propagation of fish and wildlife is unattainable in 

a portion of Pecan Rayou due to the effects of low dissolved oxygen 

levels in the bayou primarily during the spawning season. If the 

Brownwood sewage treatment plant effluent could be removed from Pecan 

Bayou, the persistently low dissolved oxygen conditions which exist and 

are unfavorable to fish spawning could be alleviated and the 

propagation of fish and wildlife could be partially restored to Pecan 

Bayou. 

Public hearings held on the proposed expansion of the sewage 

treatment plant indicate a reluctance from the public and the City to 

pay for higher treatment levels, since modeling studies show minimal 

water quality improvement in Pecan Bayou between secondary and advanced 

waste treatment. In addition, an affordability analysis performed by 

the Texas Department of Water Resources (Construction Grants) indicates 

excessive treatment costs per month would result at the AWT level. 

It appears that the elimination of the waste discharge from Pecan 

Bayou is not presently a feasible alternative, since the Brownwood STP 

currently holds a discharge permit and the water rights issue seems to 

be the overriding factor. Therefore, in the future, the uses which are 

most likely to exist are those which exist at present. 

IV. SUMMARY AND CONCLUSIONS 

A summary of the findings from the use attainability analysis are 

listed below: 

O The designated use "propagation of fish and wildlife" is 

impaired in Zone 2 of Pecan Bayou. 

' Advanced Treatment will not attain the designated use in Zone 

2, partially because of low dilution, naturally sluggish 

characteristics (X velocity 0.1 ft/sec) and as a result, low 

assimlitive capacity of the bayou (K2 reaeration rate 0.7 per 

day at 20°C). 

0 Downstream water rights for agricultural irrfgati on are 

significant. 

' Dissolved oxygen levels are frequently less than the criterion 

of 5.0 mg/l in Pecan Bayou. 

' Total DDT in whole fish from Zone 2 exceeded the U.S. Food and 

Drug Administration's action level of 5.0 mg/kg for edible fish 

tissues. 

' Annual average chloride concentrations in Pecan Bayou are 

occasionally not in compliance with the numerical criteria. 

n-42 
Dissolved oxygen levels less than 5.0 mg/l (about 50% of the 

measurements) observed in Zone 2 of Pecan Bayou result from the organic 

and nutrient loading contributed by the Brownwood STP and the 

corresponding low waste assimilative capacity of the bayou. As 

previously mentioned, the major source of toxics found in the water, 

sediment and fish tissues was also determined to be the Brownwood STP. 

PCB and DDT in water have exceeded the criteria to protect freshwater 

aquatic life in Zone 2. Although the toxics appear to be declining in 

the water and sediment, the levels of total DDT found in whole fish 

exceed the U. S. Food and Drug Administration's action level (5.0 mg/k) 

for DDT in edible fish tissue. Investigations are underway by the 

Texas Department of Water Resources to further evaluate the magnitude 

of this potential problem. 

Primarily as a result of the oxygen deficiencies and possibly be 

cause of the presence of toxic substances, the designated use 

"propagation of fish and wildlife" is not currently attained in Zone 2 

of Pecan Bayou. These problems could be eliminated only if the 

Brownwood STP ceased to discharges into Pecan Bayou because even with 

advanced waste treatment the water quality .of the receiving stream is 

not likely to improve sufficiently to support this designated use. 

Other treatment alternatives such as land treatment or overland flow 

are not feasible because of the current discharge is necessary to 

satisfy downstream water rights for agricultural irrigation. If the 

flow required to meet the water rights could be augmented from other 

sources, then the sewage treatment plant discharge could be eliminated 

in the future. 

The annual average chloride level in Pecan Bayou are occasionally 

not in compliance with the established criterion. The primary source 

has been determined to be a privately owned salt water artesian well. 

Since efforts to control this discharge have proved futile, some 

consideration should be given to changing the numerical criterion for 

chlorides in Pecan Bayou. 

In conclusion, it appears that either the Brownwood STP discharge 

into Pecan Bayou should be eliminated (if an alternative water source 

could be found to satfsy the downstream water rights) or the numerical 

criterion for dissolved oxygen and the propogatfon of fish and wildlife 

use designation should be changed to reflect attainable conditions. 

D-43 
WATER BODY SURVEY AND ASSESSMENT 

Salt Creek 

Lincoln, Nebraska 

I. INTRODUCTION 

A. Site Description 

The Salt Creek drainage basin is located in east central Nebraska. 

The mafnstem of Salt Creek originates in southern Lancaster County and 

flows northeast to the Platte River (Figure 1). Ninety percent of the 

1,621 square mile basin is devoted to agricultural production with the 

remaining ten percent primarily urban. The basin is characterized by 

moderately to steeply rolling uplands and nearly level to slightly 

undulating alluvial lands adjacent to major streams, primarily Salt 

Creek. Drainage in the area is usually quite good with the exception 

of minor problems sometimes associated with alluvial lands adjacent to 

the larger tributaries. Sof.ls of the basin are of three general 

categories. Loessfal soils are estimated to make up approximately 60 

percent of the basin, glacial till soils 20 percent, and terrace and 

bottomland soils 20 percent. 

Frequent high intensity rainfalls and increased runoff from land 

used for crop production has, in past years, contributed to flood 

damage in Lincoln and smaller urbanized areas downstream. To help 

alleviate these problems, flood control practices have been installed 

in the watershed. These practices, including several impoundments and 

channel modifications to the mainstream of Salt Creek, were completed 

during the late 1960’s. Channel realignment of the lower two-thirds of 

Salt Creek has decreased the overall length of Salt Creek by nearly 34 

percent (from 66.9 to 44.3 miles) and increased the gradient of the 

stream from 1.7 feet/mile to 2.7 feet/mile. 

Salt Creek is currently divided into three classified segments: 

(upper reach) LP-4, (middle reach) LP-3a, and (lower reach) LP-3b. 

(Figure 1). Segments LP-4 and LP-3b are designated as Warmwater 

Habitats whereas segment LP-3a is designated as a Limited Warmwater 

Habitat. 

B. Problem Definition 

"Warmwater Habitat" and "Limited Warmwater Habitat" are two subcategories of the Fish and Wildlife Protection use designation in the 

Nebraska Water Quality Standards. The only distinction between these 

two use classes is that for Limited Warmwater Habitat waters, 

reproducing populations of fish are "... l.imited by irretrievable maninduced or natural background conditions." Although segment LP-3a 

is classified Limited Warmwater Habitat and segment LP-3b as Warmwater 

Habitat, they share similar physical characteristics. Since the 

existing fisheries of both segments were not thoroughly evaluated when 

the standard was revised, it is possible that the use designation for 

one or other segments is incorrect. This study was initiated to 

determine (1) if the Warmwater Habitat use is attainable for segment 

LP-3a and (2) what, if any, physical habitat or water quality 

constraints preclude the attainment of this use. 

U-44 
/ Y!' I 

..C 

USGS Station 

Fish Sampling 

(Maret, 1978) 

Site 

* Macroinvertebrat: 

Sampling Site 

(Pesek, 1974) 

Figure 1. Monitorir,g sites from which data were used for Salt Creek 

attainability study. -- 

D-45 
C. Approach to Use Attainability Analysis 

The analytical approach used in this study was a comparison of 

physical, chemical and biological parameters between the upper, middle, 

and lower Salt Creek segments with emphasis was on identifying limiting 

factors in the creek. The uppermost segment (LP-4) was used as the 

standard for comparison. 

The data base used for this study included United States 

Geological Survey (USGS) and Nebraska Department of Environmental 

Control (NDEC) water quality data outlined in the US EPA STORET system, 

two Master of Science theses by Tom Pesek and Terry Maret, publications 

from the Nebraska Game and Parks Commission and USGS and personal 

observations by NDEC staff. No new data was collected In the study. 

II. ANALYSES CONDUCTED 

A review of physical, chemical and biological information was 

conducted to determine which aquatic llfe use designations would be 

appropriate. Physical characteristics for each of the three segments 

were evaluated and then compared to the physical habitat requlrements 

of important warm water fish species. Characteristics limiting the 

fishery population were identlfied and the sultability of the physical 

habitat for maintaining a valued fishery was evaluated. General water 

quality comparisons were made between the upper reach of Salt Creek, 

and the lower reaches to establish water quality differences. A water 

quality index developed by the NDEC was used in this analysis to 

compare the relative quality of water in the segments. In addition, 

some critical chemical constituents required to maintain the important 

species were reviewed and compared to actual instream data to determine 

if water quality was stressing or precluding their populations. 

The fish data collected by Maret was used to define the existing 

flshery population and composition of Salt Creek. This data was In 

turn used to determine the quality of the aquatic biota through the use 

of six biotic integrity classes of fish connunities and the Karr Index 

tentative numerical Index for defining class boundaries. 

Macroinvertebrate data based on the study conducted by Pesek was 

also evaluated for density and diversjty. 

III. FINDINGS 

Chemical data evaluated using the Water Quality Index indicated 

good water quality above Lincoln and degraded water quality at and 

below Lincoln. Non-point source contributions were identified as a 

cause of water quality degradation and have been Impljcated in fish 

kills in the stream. Dissolved solids in Salt Creek were found to be 

considerably higher than in other streams in the State. Natural 

background contributions are the major source of dissolved solids load 

to the stream. Water quality criteria violations monitored in Salt 

Creek during lo80 and 1981 were restricted to unionized arrmonia and may 

D-46 
have adversely impacted the existing downstream fishery. Toxics which 

occasionally approach or exceed the EPA criteria are chromium and 

lindane. Since EPA criteria for both parameters are based on some 

highly sensitive organisms which are not representative of indigenous 

populations typically found in Nebraska, the actual impact of these 

toxics is believed to be minimal. 

Channelization was found to be a limiting factor in establlshing a 

fishery in middle and lower Salt Creek. Terry Maret, in his 1977 

study, found that substrate changes from silt and clay in the upper 

non-channelized area to primarily sand in the channelized area causing 

substantial changes in fish comunities. The Habitat Suitability Index 

(HSI) developed by the Western Energy and Land Use Team of the U.S. 

Fish and Wildlife Service was used to evaluate physical habitat impacts 

on one important species (Channel Catfish) of fish in Salt Creek. The 

results indicated that upper Salt Creek had the best habitat for the 

fish investigated and middle Salt Creek had the worst. These results 

support the conclusion that middle Salt Creek lacks the physical 

habitat to sustain a valued warm water fishery. The Karr numerical 

index used to evaluate the fish data revealed that none of the stations 

rated above fair, further indicating the fish community is 

significantly impacted by surrounding rural and urban land uses. 

Analysis of the abundance and diversity of macroinvertebrates 

Indicated that the water quality in Salt Creek became progressively 

more degraded going downstream. Stations in the upper reaches were 

relatively unpolluted as characterized by the highest number of 

taxa, the greatest diversity and the presence of "clean-water" 

organisms. 

IV. SUMMARY AND CONCLUSIONS 

Based on the evaluation of the physical, chemical and biological 

characteristics of Salt Creek, the following conclusions were drawn by 

the State for the potentlal uses of the various segments: 

1) Current classifications adequately define the attainable uses for 

upper and middle Salt Creek. 

2) The Warmwater Habitat designated use may be unattainable for lower 

Salt Creek. 

3) Channelization has limited existing instream habitat for middle Salt 

Creek. Instream habitat improvement in middle Salt Creek could 

increase the fishery but would lessen the effectiveness of flood 

control measures. Since flood control benefits are greater than any 

benefits that could be realized by enhancing the fishery, instream 

physical habitat remalned the limiting factor for the fishery. 

4) Existing water quality does not affect the limited Warmwater Habitat 

classification of middle Salt Creek. 

D-47 
5) Uncontrollable background source impacts on existing water quality 

and the effects of channelization on habitat may preclude attainment 

of the classified use. 

The recommendations of the State drawn from these conclusions are 

as follows: 

1) Keep upper section classification of Warmwater Habitat and middle 

section classification of Limited Warmwater Habitat. 

2) Consider changing the lower section to a Limited Warmwater Habitat 

because of limited physical habitat and existing water quality. 

D-48 
WATER BODY SURVEY AND ASSESSMENT 

South Fork Crow River 

Hutchinson, Minnesota 

I. INTRODUCTION 

A. Site Description 

The South Fork Crow River, located in south-central Minnesota, 

drains a watershed that covers approximately 1250 square miles. This 

river joins with the North Fork Crow to form the mainstem Crow River 

which flows to its confluence with the Mississippi River (Figure 1). 

Within the drainage basin, the predominant land uses are agricultural 

production and pasture land. The major soil types in the watershed are 

comprised of dark-colored, medium-to-fine textured silty loams, most of 

which are medium to well drained in character. 

The physical characteristics of the South Fork Crow River are 

typical of many Minnesota streams flowing through agricultural lands. 

The upper portions of the river have been extensively channelized and 

at Hutchinson a forty foot wide, 12 foot high dam forms a reservoir 

west of the city. Downstream of the dam the river freely meanders 

through areas with light to moderately wooded banks to its confluence 

with the North Fork River Crow River. The average stream gradient for 

this section of the river is approximately two feet per mile and the 

substrate varies from sand, gravel and rubble in areas with steeper 

gradients to a silt-sand mixture in areas of slower velocities. 

The average annual precipitation in the watershed is 27.6 inches. 

The runoff is greatest during the spring and early Sumner, after 

snowmelt, when the soils are generally saturated. Stream flow 

decreases during late Sumner and fall and is lowest in late winter. 

Small tributary streams in the watershed often go dry in the fall and 

wlnter because they have little natural storage and receive little 

ground water contribution. The seven-day ten year low flow condition 

for the South Fork below the dam at Hutchinson is approximately 0.7 

cubic feet per second. 

B. Problem Definition 

The study on the South Fork Crow River was conducted in order to 

evaluate the existing fish community and to determine if the use 

designations are appropriate. At issue is the 28 fisheries and 

recreational use classification at Hutchinson. Is the water use 

classification approprlate for this segment? 

C. Approach to Use Attainability 

The analysis utilized an extensive data base compiled from data 

collected by the Minnesota Pollution Control Agency (MPCA), Minnesota 

Department of Natural Resources (MDNR) and United States Geological 

Survey (USGS). No new data was collected as part of the study. The 

USGS maintains partial or continuous flow record statlons on both forks 

D-49 
STATtON LOCATIONS FOR THE SOUTH FORK 

CROW RIVER USE ATfAlNABlLlTY STUDY 

A 

a 

0 

~I8ctrObhq Slollon 

USGS Contmuour Ruordlng 

GOUQI"O Stotlon 

USGS Pottiol Record Star’& 

\ 

i 

D-50 
and the mainstem Crow River with a data base of physlcal and chemical 

parameters available on STORET. The USGS data was used in the physical 

evaluation of the river. MPCA has a water quality monitoring data base 

on STORET for five stations In the Crow River watershed. The MPCA data 

plus analytical data from a waste load allocation study on the South 

Fork below Hutchinson was used in the chemical evaluation of the river. 

MDNR fisheries and stream survey data, a MDNR report on the analysis of 

the composition of fish populations in Minnesota rivers, and personal 

observations of MDNR personnel was used to evaluate the biological 

characteristics of the river. 

The analytical approach used by the MPCA sought to 1) compare 

instream fish community health of the South Fork to that of the North 

Fork, the mainstem Crow River, and other warm water rivers in the State 

and 2) evaluate physical and chemical factors affecting fisheries and 

recreational uses. The North Fork of the Crow River was used for 

comparison because of sufficient fisheries data, similar land uses and 

morphologies, slmilar non-point source impacts and the lack of any 

significant point source dischargers. 

II. ANALYSES CONDUCTED 

Physical, chemical and biological factors were considered in this 

use attainability analysis to determine the biological health of the 

South Fork and to define the physical and chemical factors which may be 

limiting. A general assessment of the habitat potentials of the South 

Fork Crow River was performed using a habitat evaluation rating system 

developed by the Wisconsin Department of Natural Resources. In 

addition, the Tennant method for determining instream flow requirements 

was also employed in this study. 

Fish species diversity, equitability and composition were used to 

define the biological health of the South Fork relative to that of the 

North Fork, the mainstem Crow and other warmwater rivers in Minnesota. 

Water quality monitoring data from stations above and below the point 

source discharges at Hutchinson were used to compare beneficial use 

impairment values pertaining to the designated fisheries and 

recreational uses of the South Fork Crow River. A computer data 

analysis program developed by EPA Region VIII was used to compute these 

values. 

III. FINDINGS 

The comparison of species diversity values for the North Fork and 

mainstem Crow River to the South Fork showed higher values for the 

North Fork and mainstem Crow. On the other hand, the South Fork had 

higher species equitability values. The percent species composition 

compared favorably to Peterson's (1975) estimates for median species 

diversity for a larger Minnesota river. Recruitment from tributaries, 

marshes, lakes and downstream rivers has given the South Fork a 

relatively balanced cotnnunity which compares well to other warmwater 

rivers in the State. The calculated species diversity and equitability 

indices coupled with the analysis of species composition indicated that 

the South Fork af the Crow River does support a warmwater fishery with 

evidence of some degree of environmental stress. 

D-51 
The MPCA employed the Wisconsin habltat ratlng system and the Tennant 

method designated to quantify minimum Instream flsherles flow 

requirements to identlfy any physical llmitlng factors. Based on the 

Wisconsin habitat evaluation assessment, habitat ratlng score were 

fair. The llmitlng factors Identified via thls assessment were: 1) 

lack of diverse streambed habltat suitable for reproduction, food 

production and cover and 2) instream water fluctuations (low flow may 

be a major controlling factor). 

The State utilized EPA Region VIII’s data analysis program to 

express stream water quality as a function of beneficial use. The 

closest downstream statlon to Hutchinson had the highest warmwater 

aquatic life use impalrment values. Warmwater aquatlc life use 

impairment values declined further downstream indicating that the point 

source dischargers were major contributors to thls use impairment. 

However, primary contact recreatlonal use impairment values were high 

throughout the stream, Thls led the State to believe that the 

impairment of primary contact recreational use Is attrlbutable to 

non-point sources. 

IV. SUMMARY AND CONCLUSION 

The State concluded from the study that: 1) the South Fork of the 

Crow River has a definite fisheries value although the use impairment 

values indicate some stress at Hutchinson on an already limlted 

resource and 2) although the South Fork of the Crow River has a 

dominant rough fish population, game and sport fish present are 

important component species of this rivers' overall cofmnunity 

structure. 

From these conclusions the State recommended that the South Fork 

of the Crow River retain its present 28 flsheries and recreational use 

classification. Furthermore, efforts should continue to mitigate 

controllable factors that contribute to impairment of use. The effort 

should entail a reduction of marsh tilling and drainage, acceptance and 

implementatlon of agricultural BMP's and an upgrade of point source 

dischargers in Hutchfnson. 

D-52 
WATER BODY SURVEY AND ASSESSMENT 

South Platte River 

Denver, Colorado 

I. INTRODUCTION 

A. Site Description 

Segment 14 of the South Platte River originates north of the Chatfield Lake at 

Bowles Avenue in Arapahoe County and extends approximately 16 miles, through 

metro Denver, in a northerly direction to the Burlington ditch diversion near the 

Denver County-Adams County line. A map of the study area Is presented in Figure 

1. Chatfield Lake was originally constructed for the purposes of Flood control 

and recreation. The reservoir is owned by the U.S. Army Corps of Engineers and 

is essentially operated such that outflow equals inflow, up to a maximum of 5,nDD 

cfs. In addition, water is released to satisfy irrigation demands as authorized 

hy the State Engineers Office. There Is also an informal agreement between the 

State Engineers Office and the Platte River Greenway Foundation for timing 

releases of water to increase flows during periods of high recreational use. The 

Greenway Foundation has played an important role in the significant improvement 

of water quality in the South Platte River. 

There are several obstructions throughout Segment 14 including low head dams, 

kayak chutes (at Confluence Park and 13th Avenue), docking platforms, and weir 

diversion structures which alter the flow in the South Platte River. There are 

four major weir diversion structures in this area which divert flows for 

irrigation; one is located adjacent to the Columbine Country Club, a second near 

Union Avenue, a third upstream from Oxford Avenue, and a fourth at the Burlington 

Ditch near Franklin Street. 

Significant dewatering of the South Platte River can occur due to instream 

diversions for irrigation and water supply and pumping from the numerous ground 

water dwells along the river. 

Eight tributaries normally provide inflow to the South Platte River in Segment 

14. These include Big Dry Creek, Little Dry Creek, Bear Creek, Harvard Gulch, 

Sanderson Gulch, Weir Gulch, Lakewood Gulch, and Cherry Creek. 

There are several municipal and industrial facilities which discharge either 

directly to or into tributaries of the South Platte River in this reach. The 

major active discharges into the segment are the Littleton-Englewood wastewater 

treatment plant (WWTP), the Glendale WWTP, the City Ice Company, two Public 

Service company power plants (Zuni and Arapahoe), and Gates Rubber. 

The South Platte River drainage basin in this area (approximately 120,000 acres) 

is composed primarily of extensively developed urban area (residential, 

industrial, commercial, services, roads), parks and recreational areas, gravel 

mining areas, and rural areas south of the urban centers for farming and 

grazing. 

D-53 
\ 

\ 

\ 

\ 

Figure 1 

SOUTH PLA~'E RIVER WDY AREd MAP 
ln the study area, the South Platte River is typically SO-150 feet wide and 1-16 

feet deep (typically l-2 feet) and has an average channel bed slope of 12.67 feet 

per mile, with alternating riffle and pool reaches. The channel banks are 

composed essentially of sandy-gravelly materials that erode easily when exposed 

to high-flow conditions. The stream banks are generally sparsely vegetated with 

trees, shrubs, and grasses (or paving in the urban centers.) 

B. Problem Definition 

The following use classifications have been designated for Segment 14 of the 

South Platte River: 

O Recreatjon - Class 2 - secondary contact 

O Aquatic Life - Class 1 - warm water aquatic life 

O Agriculture 

O Domestic Water Supply 

Following a review of the water quality studies and data available for Segment 14 

of the South Platte River, several observations and trends in the data have been 

noted, including: 

0 Fecal collform values exceeded the recommended limits for recreational 

uses in the lower portlon of Segment 14. 

0 Un-ionized ammonia levels exceeded the water quality criterion for the 

protection of aquatic life in the lower portion of the segment. 

0 Levels of total recoverable metals (lead, zinc, cadmium, total iron, 

total manganese, and total copper) have been measured which exceed the 

water quality crjteria for the protection of aquatic life. 

Although the exact points of origin have not been specified, it is generally felt 

that the source of the ammonia is municipal point sources, and the sources of the 

metals are industrial point sources. 

In addition, the cities of Llttleton and Englewood have challenged the Class I 

warm water aquatic life use on the basis that the flow and habitat are unsuitable 

to warrant the Class I designation, and they have also challenged the 

apporopriateness of the 0.06 mg/l un-ionized ammonia criteria on the basis of new 

toxicity data. The Colorado Water Quality Control Commission in November, 1982 

approved the Class I aquatic life classification and the 0.06 mg/l un-ionized 

ammonia criteria. 

c. Approach to Use Attainability 

Assessment of Segment 14 of the South Platte River was based on a site visit (May 

3-4, 1982) which included meetings with representatives of the Colorado 

Department of Health, EPA (Region VIII and Headquarters) and Camp Dresser & McKee 

Inc., and upon information contained in a number of reports, hearing transcripts 

and the other related materials. Most of the physical, chemical and biological 

data was obtained from the USGS, EPA (STORET), DRURP, and from 

D-55 
studies. It was agreed that there was sufficient chemical, physical and 

biological data to proceed with the assessment, even though physical data on the 

aquatic habitat was limited. 

II. ANALYSES CONDUCTED 

A. Physical Factors 

Streamflow in the South Platte River (Segment 14) is affected by several factors 

including releases from Chatfield Dam, diversions for irrigation and domestic 

water supply, irrigation return flows, wastewater discharges, tributary inflows, 

pumping from ground water wells in the river basin, evaporation from once-through 

cooling at the two power plants in Segment 14, and natural surface water 

evaporation. Since some of these factors (particularly ground water pumping, 

evaporation and irrigation diversions) are variable, flow in the South Platte 

River is used extensively for irrigation and during the irrigation season 

diversions and return flows may cause major changes in streamflow within 

relatively short reaches. During the summer, low-water conditions prevail 

because of increased evaporation, lack of rainfall, and the various uses made of 

the river water (e.g. irrigation diversions). Municipal, industrial, and 

storm-water discharqes also contributes to the streamflow in the South Platte 

River. 

Natural pools in the South Platte River are scarce and the shifting nature of the 

channel bed results in temporary pools, a feature which has a tendency to greatly 

limit the capacity for bottom food production. There are approximately 3-4 pools 

per river mile with the majority being backwater pools upstream of diversion 

structures, bridge crossings, low head dams, docking platforms, drop-off 

structures usually downstream of wastewater treatment plant outfalls, kayak 

chutes, and debris. The hydraulic effect of each obstruction is generally to 

cause a backwater condition immediately upstream from the structure, scouring 

imnediately downstream, and sandhar development below that. These pools act as 

settling basins for silt and debris which no longer get flushed during the high 

springs flows once Chatfield Lake was completed. 

In the plains, channels of the South Platte River and lower reaches of 

tributaries cut through deep alluvial gravel and soil deposits. Sparse 

vegetation does not hold the soils, so stream bank erosion and channel bed 

degredation is common durinq periods of high flow, particularly during the spring 

snowmelt season. The high intensity - low duration rainstorms which occur during 

the summer (May, June, and July) also temporarily muddy the streams. 

An evaluation of the physical streambed characteristics of Segment 14 to 

determine the potential of the Seqment to maintain and attract warm water aquatic 

life was conducted by Keeton Fisheries Consultants, Inc. The study concluded 

that the sediment loads in this reach of the South Platte River could pose a 

severe problem to the aquatic life forms present, however, further study needs to 

be conducted to substantiate this conclusion. Furthermore, some gravel mining 

operations have recently been discontinued thus the sediment problem may have 

been reduced. 

The temperature in the South Platte River is primarily a function of releases 

from the bottom of Chatfield Lake, the degree of warming that takes place in the 

shallow mainstream and isolated pools, and the warming that occurs through the 

mixing of power plant cooling water with the South Platte River. 

D-5tJ 
B. Chemical Factors 

Water quality conditions in the South Platte River are substantially affected by 

municipal and industrial wastewater discharges, irrigation return flows and other 

agricultural activities, and non-point sources of pollution (primarily during 

rainfall-runoff events). Irrigation and water supply diversions also exert a 

major influence on water quality by reducing the stream flow, and thereby 

reducing the dilution assimilative capacity of the river. 

O Dissolved oxygen levels were above the 5.0 mg/l criteria acceptable for 

the maintenance of aquatic life. 

0 Average concentrations of un-ionized ammonia exceeded the State water 

quality criteria of 0.06 mg/l NH3-N only in the lower portion of 

Segment 14 (north of Speer Rlvd.) 

O Average total lead concentrations exceeded the water quality criteria of 

25 ug/l in Rig Dry Creek, Cherry Creek, and the South Platte River 

north of Cherry Creek, ranging from 30-72 ug/l. 

O Average total zinc concentrations exceeded the criteria of 11 ug/l at all 

the DRURP sampling stations, ranging from 19-179 ug/l. 

O Average total cadmium concentrations exceeded the criteria of 1 ug/l in 

Beer Creek, Cherry Creek and several sites in the South Platte, ranging 

from 2.2-3.6 ug/l. 

O Average total iron concentrations exceeded the criteria of 1,000 ug/l in 

Cherry Creek and several locations on the South Platte River, ranging 

from 1129-9820 ug/l. 

0 Average soluble manganese concentrations exceeded the criteria of 50 

ug/l in the South Platte River north of (and including) 19th Street and 

in Cherry Creek, ranqinq from 51-166 ug/l. 

' Average total copper concentrations equalled or exceeded the criteria of 

25 ug/l at all but two of the DRURP samplinq sites, ranging from 25-83 

ug/l l 

c. Biological Factors 

Several electrofishing studies have been conducted on the South Platte River in 

recent years. Most of the sampling took place in the fall with the exception of 

the study in the spring (1979). The data was reviewed by Colorado Department of 

Health personnel and it was generally agreed that the overall health of the 

existing warm water fishery is restricted by temperature extremes (very cold and 

shallow during the winter and low flow and high temperatures during the summer), 

lJ-57 
the lack of sufficient physical habitat (i.e. 

rocks and dams, 

structures for cover including 

and deep pools) and the potentially stressful conditions created 

by the wastewater discharges (i.e. silt and organic and inorganic enrichment). 

Following a review of the physical, chemical, and biological data available on 

the South Platte River, it was concluded that a fair warm water fishery could 

exist with only modest habitat improvements and maintenance of the existing 

ambient water quality and strict regulation prevent overfishing. 

habitat and water quality improvements, 

With large 

brown trout could potentially become a 

part of the fishery in Segment 14 of the South Platte River. 

III. FINDINGS 

A. Existing Uses 

Segment 14 of the South Platte River is currently being used in the following 

ways: 

O Irrigation Diversions and Return Flows 

' Municipal and Industrial Water Supply 

' Ground Water Recharge 

O Once-through Cooling 

' Municipal, Industrial, and Stormater Oischarges 

O Recreation 

' Warm Water Fishery 

The irrigation diversions, water supply, ground water recharge, and cooling uses 

have primarily affected the flow in the South Platte River, resulting in 

significant dewatering at times. Irrigation return flows and wastewater 

dishcharges, on the other hand, exert their effects on the ambient and storm 

water quality in the River. These previous uses ultimately affect the existing 

warm water fishery and how the public perceives the river for recreation 

purposes. 

R. Potential I)ses 

With the exception of a potential for increased recreation and the improvement of 

a limited warm water fishery, it is anticipated that the existing uses are likely 

to exist in the future. The increased recreational use will result from future 

Platte River Greenway Foundation projects. The improvement of a limited warm 

water fishery may come about in the future as the result of habitat improvements 

(Pools, cover) control of toxic materials (un-ionized ammonia, heavy metals, 

cynanide), and the prevention of extensive sedimentation. However, the success 

of the fishery would rely on strict fishery regulations to prevent overfishing. 

D-58 
IV. SUMMARY AND CONCLIISIONS 

A summary of the findinqs from the use 3ttainahilit.y analysis are listed below: 

0 There is evidence to indicate that a warm water aquatic life community 

does exist and the potential for an improved fishery could be attained 

with slight habitat modifications (i.e. cover, pool). 

' Elevated un-ionized ammonia levels were exhibited in the lower portion of 

Segment 14, although this cannot be attributed to the Littleton-Englewood 

WWTP discharge upstream. However, at the present time there is nn basis 

for a change in the existing un-ionized ammonia criterion, particularly 

if EPA's methodology for determining site specific criteria becomes 

widely accepted. 

0 Increased turbidity exists in the South Platte River during a good 

portion of the fish spawning season, which represents a potential for 

problems associated with fish spawning. 

0 Increased sedimentation and siltation in the South Platte River could 

pose a potential threat to the aquatic life present; however, this 

condition might be reduced if Chatfield Lake could be operated to provide 

periodic flushing of the river. 

0 Elevated levels of heavy metals were ohserved in water and sediment 

samples, which could potentially affect the existing aquatic life. 

0 Insufficient data existed to determine the possible effects of chlorine 

and cyanide on the aquatic life present. 

0 Fecal coliform levels were extremely high in the lower portion of the 

South Platte River and Cherry Creek during periods of both low and high 

flow. The source in the South Platte River is apparently Cherry Creek, 

but the origin in Cherry Creek is unknown at this time. 

On the basis of the preceding conclusions and recommendations, the warmwater 

fishery use classification and the un-ionized ammonia criterion (0.06 mg/l) 

recommended for Segment 14 of the South Platte should remain unchanged until 

there is further evidence to support making those changes. 

u-59