‘ ' THE CHARACTERIZATION AND :INELUENRE- ‘ . ’  ' ? f
OF DOMESTIC DRAIN "EFFLUJENTS. ' - .+ .. rr.
- ON THE RED CEDARRRRR‘. - .......

.....

l f Thesis for the Degree of 'M. S.
i;-: MICHIGAN STATE UNIVERSITY
’4; ARTHUR RAY TALSMA
1972

 

   

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ABSTRACT

THE CHARACTERIZATION AND INFLUENCE OF
DOMESTIC DRAIN EFFLUENTS ON THE
RED CEDAR RIVER

BY

Arthur Ray Talsma

A study was undertaken to monitor pollutants \\>
entering the Red Cedar River of central Michigan, and
to determine their effects on the ecosystem. Dissolved
oxygen, conductivity, phosphorus, nitrogen, carbon, sus-
pended solids, chlorides and detergents were among the
chemical parameters considered. Bioassays, live cars,
bottom fauna and coliform analyses were the biological
aspects of interest.

Analyses indicated that pollutants were principally
of domestic origin, coming from storm drains and combined
storm and sanitary drains. Significant differences
were found in water quality and river fauna above
sources of pollution as compared with below sources.

Most parameters showed little or no improvement since

1964.

THE CHARACTERIZATION AND INFLUENCE OF
DOMESTIC DRAIN EFFLUENTS ON THE

RED CEDAR RIVER

BY

Arthur Ray Talsma

A THESIS

Submitted to
Michigan State University
in partial fulfillment of the requirements
for the degree of

MASTER OF SCIENCE

Department of Fisheries and Wildlife

1972

ACKNOWLEDGMENTS

I would like to express my special thanks to
Dr. Niles Kevern for his advice and guidance during this
study. I am also grateful to Dr. Howard Johnson, Dr.
Marvin Stephenson and Dr. Frank Peabody for their help.
Thanks is given to Joseph Ervin, David Jude, Alan
McIntosh and James Seelye, who contributed much to this
study by suggestions and help in the field.

Recognition is given for unpublished data obtained
under project C-2205 of the Office of Water Resources
Research, United States Department of the Interior, as
authorized under the Water Resources Research Act of 1964.

The financial support for this study was provided
by the Environmental Protection Agency, Office of Water

Programs, Training Grant Number 5P3-WP-264.

ii

TABLE OF CONTENTS

Chapter Page
INTRODUCTION 0 O O O O O O O O O I O O 1
DESCRIPTION OF STUDY AREA . . . . . . . . 4
METHODS O O O O O O O O O O O O O O l 3
Sampling Design and Statistics . . . . . . 13
Sampling Procedures. . . . . . . . . . 14
Chemical Methods. . . . . . . . . . . 15
Total Alkalinity, Hardness, and Chlorides . 15
Detergents . . . . . . . . . . . 16
Phosphorus . . . . . . . . 17
Total Kjeldhal Nitrogen . . . . . . . l7
Ammonia-Nitrogen. . . . . . . . . . 18
Dissolved Organic Carbon . . . . . . 18
Dissolved Oxygen. . . . . . . . l9
Chromium . . . . . . . . . . . . 19
Physical Methods. . . . . . . . . . . 19
Temperature, pH, Conductivity . . . . . 19
General Observations . . . . . . . . 20
Fluorescein Dye Survey. . . . . . . . 20
Biological Methods . . . . . . . . . . 21
Bioassays . . . . . . . . . . 21
Bacteriological Methods . . . . . . . 23
Bottom Fauna . . . . . . . . . . . 24
Live Car Methods. . . . . . . . . . 25
RESULTS AND DISCUSSION. . . . . . . . . . 27
Drain Effluent Analyses . . . . . . . 27
River Quality and General Effects of Pol-
IUtion O O O O O O 0 O O O O O O O 4 8

iii

Chapter Page
Dissolved Oxygen and Fish Kills . . . . . 49
Chlorides O O O O O O O O O O O O 56
SuSpended Solids . . . . . . . . . . 60
Phosphorus O O O O O O O O O O O . 62
Nitrogen ‘ O O O O O I O O O O O O 65
Carbon . . . . . . . . . . . 66
Bottom Fauna . . . . . . . . . . . 68
Coliform Bacteria. . . . . . . . . . 83

SUMMARY 0 O O O O O O I O O O O O O O 88

LITERATURE CITED . . . . . . . . . . . . 90

APPENDICES

Appendix

A. Information Concerning Drains . . . . . 96
B. Information Concerning Toxicity Test . . . 109
C. Information Concerning Bottom Fauna . . . 118
D. General Information. . . . . . . . . 121

iv

LI ST OF TABLES

Table Page
1. Statistical Summary of Phosphorous and
Nitrogen Analyses for Major Drain
Effluents . . . . . . . . . . . 28

2. Statistical Summary of Carbon and Chloride
Analyses for Major Drain Effluents. . . 29

3. Summary of Water Parameters for River
Stations 1 and 2. . . . . . . . . 58

4. Summary of Five Water Parameters for River
Stations 1 and 2. . . . . . . . . 63

5. Summary of "Pool" Bottom Fauna Expressed as
Mean Number Per Square Foot . . . . . 74

6. Riffle Bottom Fauna--Organisms and Number
Per Square Foot . . . . . . . . . 76

7. Formulas for Estimating Average Discharge
and Dilution Ratio . . . . . . . . 108

8. Characteristics of Laboratory Dilution

Water . . . . . . . . . . . . 109

9a. Experimental Data for Bioassay IV . . . . 110
9b. Effluent Characteristics for Bioassay IV. . 110
9c. Bioassay IV Procedures. . . . . . . . 110
10a. Experimental Data for Bioassay VI . . . . 113
10b. Effluent Characteristics for Bioassay VI. . 113
10c. Bioassay VI Procedures. . . . . . . . 113
11. Live Car Test on Drain 25 Effluent. . . . 116

Table Page
12. Live Car Test on Drain 6 Effluent . . . . 117
13. Summary of "Pool" Bottom Fauna Expressed as

Number per Square Foot. Sample Date
JUlY 28' 1971. o o o o o o o o o 118

vi

Figure

10.

ll.

12.

l3.

14.

LIST OF FIGURES

Map of Study Area . . . . . . . . .

Monthly Mean Discharge Near Farm Lane for
Years 1970 and 1971 . . . . . . .

Precipitation and Discharge for June, 1971.

River Conductivity Peak Due to Drain
Number 25 . . . . . . . . . .

"Typical" Late Summer Diurnal Oxygen Curve
Compared to One During a Fish Kill . .

Difference in Diurnal Oxygen Curves Between
Stations 1 and 2 . . . . . . . .

Suspended Solids (unpublished data) . . .

Number of Oligochaeta Per Square Foot at
River Sampling Stations . . . . . .

Number of Chironomidae Per Square Foot at
River Sampling Stations . . . . . .

Most Probable Number (MPN) for Coliform
Bacteria Per 100ml of River Water at
Sampling Stations 1-5 . . . . . .

Estimation of 50 Percent Tolerance Limits
by Straight-Line Graphical Interpolation
for Bioassay IV. . . . . . . . .

Estimation of 50 Percent Tolerance Limits
by Straight-Line Graphical Interpolation
for Bioassay VI. . . . . . . . .

Test of Sampling Adequacy Upstream . . .

Test of Sampling Adequacy Downstream. . .

vii

11

38

51

54

61

7O

72

86

112

115

119

119

Figure Page
15. A. Photograph of Drain 66 Discharging
Sewage. B. Photograph of Drain 82
Discharging Sewage. C. Major Fish
Kill of August 11, 1971. D. Photo-
graph of Effluent from Drain 25 . . . 121

16. Map of the Red Cedar River. . . . . . 123

17. Map Showing Sewerage System of Michigan
State University . . . . . . . . 125

viii

INTRODUCTION

Man has always had an influence on the water systems
he uses. In recent years our concern over the pollution
problem has grown because the deterioration of water
quality can be seen in almost every community. A grow-
ing population places increased industrial, recreational,
agricultural and domestic demands on its water supplies.
Consequently we are compelled to correctly manage the
water environment for our own well being.

Defined by the dictionary, pollution is the act of
making foul or unclean. Confusion usually arises because
there are many kinds of pollutants and each may have
various effects on the aquatic system. To the sportsman
stream pollution may mean the degradation of aesthetic
value or a reduction in game species. To the aquatic
biologist stream pollution may involve a change in
species diversity or toxicity to aquatic fauna. The
bacteriologist would be concerned over a possible
increase in bacteria which are harmful to human health.
For the purposes of this study water pollution is con-

sidered as the impairment of the suitability of water

for any of its beneficial uses, actual or potential, by
man-caused changes in water quality (Warren, 1971).

A complete log of information concerning the Red
Cedar River has been collected over the past years.
Aspects of the river climatology, hydrology and biology
are described by Meehan (1958), Vannote (1961) and King
(1962),respectively. The Michigan State University
Institute of water Research has published much of the
information in a series of reports (Brehmer, Ball and
Kevern, 1968), (Grzenda, Ball and Kevern, 1968), (Peters,
Ball and Kevern, 1968), (Kevern and Ball, 1969), (Brehmer,
Ball and Kevern, 1969). A particularly important study
of pollution in the area of Michigan State University
and East Lansing was conducted by Alvin Jensen (1966).
His investigation was concerned with the river water
quality as related to urbanization of the surrounding
area. He found a significant decrease in water quality
as the river flows through the Michigan State University
campus. The change was attributed to polluting drain
effluents on which some specific analyses were made.

Persons from the university and city have generally
surmised that because of a new sewage treatment plant,
improved sewerage and advancements in waste treatment
made in the communities upstream from East Lansing, the
river water quality has improved in recent years. This

study was designed to scientifically test this viewpoint

and extend our knowledge regarding the Red Cedar River.
The investigation began July, 1970, on a 2.63 mile reach
of the river flowing through the Michigan State University
campus and East Lansing community of Michigan. The three
major objectives of the investigation were as follows:
to monitor individual drain effluents for pollutants and
to determine amounts and sources, to evaluate the effects
of the pollutants found on water quality and river life
and to determine changes in the river as a follow-up on
research done in the past, especially that by Alvin
Jensen (1966). CDeterminations were directed toward
domestic sewage and erosional products, including street
runoff. These were the most expected forms of pollution
as both Michigan State University and East Lansing are
highly residential areas with little industry. Most of
the upper drainage basin of the river is in an agricultural
region. '7

The entry of pollutants into a stream sets off a
progressive series of physical, chemical and biological
events which may be recognized as dependable criteria
of stream conditions (Bartsch, 1967). The parameters
selected were those which were felt to best fulfill the

objectives of this investigation.

DESCRIPTION OF STUDY AREA

The Red Cedar River is a warm-water stream in
southcentral Michigan. It originates as an outflow from
Cedar Lake, located in Marion Township, Livingston
County, Michigan. The stream flows past the communities
of Fowlerville, Webberville, Williamston and Okemos
before entering the East Lansing and Michigan State Uni-
versity area. It then connects with the Grand River in
Lansing (Ingham County, Michigan).

With the exception of a bottom fauna sampling
station at Okemos, the study section was within the
boundaries of Michigan State University campus; Hagadorn
Road being at the upstream east boundary and East Kala-
mazoo Street at the downstream west boundary. The study
section is 2.63 miles long and the width varies from 25
to 80 feet (Jensen, 1966). At mid-summer in 1970-and
1971 the stream depth varied from less than one foot to
approximately six feet in the impoundment formed by a
dam located below Farm Lane Bridge (see Figure 1).

Along this reach of river approximately 90 drains (all

of varying size and significance) enter the river. I

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used the same drain numbering system as Jensen (1966)
but encountered difficulties because some former drains
were no longer present or recognizable; also there have
been many new additions. Jensen (1966) had indicated
the presence of 68 drains in the study section. I found
90 drain openings within the same section. Therefore,
of the first 68 drains shown in Figure 1, most are the
same as in 1964 but those with numbers greater than 68
have been newly formed or were undetected by Jensen
(1966).

The river is slow moving from Hagadorn Road to the
dam after which there are riffle pool areas throughout
the remainder of the study section. Above the dam the
bottom is principally sand intermixed with rocks. The
bottom is covered by one to two inches of silt and
detritus. Below the dam the river bed is coarse gravel
and sand covered by an inch or less of silt and detritus.
Sludge beds have formed below some of the drains. The
banks are forested in some areas but much of the river
study section runs along parking lots and lawns of
Michigan State University.

Figures 2 and 3 illustrate the extreme fluctuation
in daily and seasonal flows on the Red Cedar River. As
a result of the fluctuation in flow rate, drainage from
agricultural areas upstream and rapid runoff from

streets and parking lots, the river is often very turbid

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in the lower portions. Because of the turbidity and
scouring effect after rain storms, the plant life
throughout the study section is restricted even though
nutrients are present in excess. Diurnal dissolved
oxygen pulses are common with critically low values
occurring in the study section during summer and early
fall. The aesthetic value of the river and its banks
has been lowered by the_excessive amount of debris and

garbage present.

METHODS

In solving the pollution problem analytical methods
for gathering basic data, monitoring, research and treat-
ment control should be continuously upgraded by systematic
evaluation and standardization (American Chemical Society
Report, 1969). Many authorities including the Federal
Environmental Protection Agency recommend the use of

Standard Methods (APHA, AWWA, WPCF, 1971) for pollution

 

studies. For this reason, whenever possible, analyses
performed for this study were completed using the above
reference. Whenever a question arose concerning the
reliability of an analysis, replicates were run on the
given sample. Standard solutions were used regularly

with all analyses in order to check their accuracy.

SamplingyDesign and Statistics

 

Pollutional evaluation of the river was paramount
in this study, so three scientific restrictions were
placed on sampling. In general, sampling was conducted
when pollutants were thought to be entering the river
and at places where pollutants were more likely to be

found. Also, it was necessary that the drains be

13

 

 

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14

flowing to enable sampling. Following this design,
approximately 45 sampling trips were conducted from

July, 1970, to August, 1971. Sampling during the winter
months was less frequent. Once samples were collected
from the drain effluents, analyses for alkalinity, hard-
ness, chlorides, phosphorus, nitrogen and carbon were
regularly completed. At river stations, dissolved oxygen,
bottom fauna and coliform determinations were performed
in addition to the parameters mentioned above.

The statistics of this study, although principally
descriptive summaries, estimate population parameters
with the aforementioned restrictions. Common statistics
such as means (X), variances (5%), standard errors (Sx)'
test of homogeneity and appropriate tests for significant
differences between means were performed when needed.

Note that in pollutional studies it is often the variance
or range (extraordinary value) that one is concerned about

rather than a mean.

Sampling Procedures

 

Water samples were taken in 1000 ml dichromate-
rinsed, polyethylene, wide-mouth bottles. To sample
the river, bottles were submerged approximately one
foot below the surface at midstream. When sampling
the drains the bottles were held directly under the
effluent except at submerged drains where the samples

were taken nearest the Opening. All significant drains

15

as well as the two river stations were sampled by canoe
or from the bank. The two river sampling stations were
at the beginning, Hagadorn Road, and end of the study
section, below the Michigan State University Limnological
Research Laboratory near East Kalamazoo St. (stations 1
and 2, respectively). These stations were equivalent to
stations 1 and 5 in the study made by Jensen (1966). In
the case of bottom fauna and coliform examinations,
station locations were the same as in Jensen's (1966)
study. Samples were labeled when collected, preserved
appropriately and refrigerated at 4 C until tests were
run. Time, temperature, approximate flow rate, general
observations and sample numbers were recorded while at
the drain sites. When a drain was not flowing during

a sampling trip only the time and flow condition were
recorded. When the flow rate of a drain was considered
insignificant to warrant sampling or enough samples had
previously been taken, only the time, temperature,

approximate volume and general observations were recorded.

Chemical Methods

 

Total Alkalinity, Hardness,
and Chlorides

 

 

Total alkalinity, hardness and chloride determi-
nations were made by the titrimetric methods described

in Standard Methods (APHA, AWWA, WPCF, 1971). The EDTA

 

16

method was used for hardness determinations and the

mercuric nitrate method for chloride analyses.

Detergents

 

Synthetic detergents (containing surfactants) can
cause degradation of water quality by addition of phos-
phorus and by frothing. Due to lack of time I did not
analyze for the presence of detergents in all water
samples. Determinations were made on those effluents
that were foaming or suspected of containing appreciable
amounts of detergents. The methyl green method as
described by Hach (1969) was used. The indicator reacts
with anionic surfactants such as alkyl benzene sulfonate
(ABS) and the more biodegradable linear alkylate sulfonate
(LAS). Color intensity was read on a Klett-Summerson
colorimeter using a number 54 (green) filter. Values for
the samples were read from a standard curve made using
standard alkyl benzene sulfonate. Many of the samples
from the drains were high in phosphates, chlorides and
nitrates, all of which are positive interferences with
this method. For this reason caution was taken while
making the determinations but little interference was
encountered. For example, samples high in phosphorus
but with no detergents present showed zero mg/liter
detergents. Due to a lack of interferences on the water
samples that were analyzed and good reproduction of

standard curve values, the method was considered reliable.

17

Also phosphorus values were complimentary to the detergent
values obtained. Often when detergent concentrations
were high, phosphorus values were above that normally

found in raw sewage.

Phosphorus

 

Total dissolved and suspended acid-hydrolyzable
phosphate determinations were made using the stannous

chloride method as described in Standard Methods (APHA,

 

AWWA, WPCF, 1971). Precautions such as using double
distilled deionized water, acid-washed glassware and
equal timing conditions were employed. The results
include dissolved and suspended orthophosphates and
hydrolyzable phosphates. The hydrolyzable phosphorus,
in turn, includes polyphosphates and some organic phos-
phorus. The analyses were usually performed within two
days after collection, and the results were listed as

mg P/liter.

Total Kjeldahl Nitrogen

 

Total Kjeldahl nitrogen includes free ammonia and
organic nitrogen compounds. The Water Research Laboratory
at Michigan State University made the determinations for
total Kjeldahl nitrogen following the procedure as

described in Methods for Chemical Analysis of Water and

 

Wastes (E.P.A., 1971). After collecting, the samples were

preserved with 40 mg.HgC12/1iter and stored at 4 C until

18

analyzed. For the determination of ammonia after dis-
tillation the Nesslerization method was used. The
ammonia-nitrogen was read from a standard curve, and

the results were expressed as mg N/liter.

Ammonia-Nitrogen

 

The distillation method followed by Nesslerization
was used for ammonia determinations (APHA, AWWA, WPCF,
1971). Only those samples suspected of having high con—
centrations of free ammonia or those found to have high
concentrations of total Kjeldahl nitrogen were analyzed.
Also determinations were made during bioassays when

ammonia concentrations were thought to be influential.

Dissolved Organic Carbon

 

Organic carbon (filterable) determinations were
made by the Water Research Laboratory. The instrumental

method as described in Methods for Chemical Analysis of

 

Water and Wastes (E.P.A., 1971) was used. Samples were

 

preserved and stored at 4 C to prevent oxidation or bac-
terial decomposition of the organic carbon compounds
prior to analysis. Samples were filtered with a 0.45u
Millipore filter, and after acidifying to pH 2.0, the
carbonate and bicarbonate carbon was removed by bubbling
with nitrogen for five minutes. The samples were then
analyzed for organic carbon with a Beckman 915 car-
bonaceous analyzer. Phthalate standard solutions were

used and results recorded as mg C/liter.

19

Dissolved Oxygen

 

Dissolved oxygen was measured by polarographic
probe and by using the azide modification of the Winkler

method as described in Standard Methods (APHA, AWWA,

 

WPCF, 1971). At the Limnological Research Laboratory
water is pumped from the river (station 2) into the
sensor ports of a continuous flow monitor which was
maintained during most of the study period. This
instrument monitored the dissolved oxygen with a mem-

brane electrode. Results were recorded as mg DO/liter.

Chromium

Samples from drain effluents suspected of having
significant chromium concentrations were analyzed by the
Water Research Laboratory. The atomic absorption
SpectrOphotometric method was used, following the pro-

cedure in Methods for Chemical Analysis of Water and

 

Wastes (E.P.A., 1971). Results were recorded as

mg Cr/liter.

Physical Methods

 

Temperature, pH, Conductivity

 

Temperature, pH and conductiVity were monitored by
the continuous flow monitor at the Limnological Research
Laboratory. The accuracy of the monitor was checked
at regular intervals. Because the monitor yielded

information only on river water from station 2,

20

measurements of these parameters from station 1 and
drain effluents were collected by other means. Temper-
ature was measured with a thermometer while at the river
and drain sites. Conductivity and pH measurements were
made immediately upon returning to the laboratory with
an Industrial Instruments Conductivity Bridge model

RC 16B2 and a Beckman Zeromatic II pH meter.

General Observations

 

While at the drain and river sites general obser-
vations were made concerning the severity or intensity of
water quality conditions such as: odor, color, gas films,
oils, foam, dead aquatic fauna, sludge beds and suspended
matter including human feces, sludge and paper. Although
these observations were subjective, they were very helpful
in choosing further tests, often complemented each
other, and were supported by other parameters. For
example, a toxic drain effluent with a yellow-green
color was analyzed and found to have a high chromium

concentration.

Fluorescein Dye Survey

 

Fluorescein dye was used to help determine sources
of pollution. When concerned about an effluent from a
specific drain, possible sources were considered by
using a map of Michigan State University and East Lansing

sewerage system. Speculation as to the contributing

21

source or sources was made by dropping 159 of fluorescein
dye into the sewerage system at points of interest, after
which the drain effluent was checked for dye. In all
cases the dye was easily visible in the drain effluent
and there was no need for fluorometric analysis.

Usually only the building from which the effluent may
have originated was determined. Errors can be made in

a survey procedure of this type and it should be con-
sidered as only one method of many which should be used

to pinpoint a specific source of pollution.

Biological Methods

 

Bioassays

 

Acute toxicity bioassays were used to evaluate
effects of drain effluent wastes on fish. Nine static
bioassays were run on effluents from five different
drains. Bioassay procedures as described by Standard
Methods (APHA, AWWA, WPCF, 1971) were followed as closely
as possible. Because certain procedures and the effluents
tested varied between individual bioassays, some of the
information concerning methods, materials and results
are recorded in Appendix B. The remainder of this
section covers factors that were common to all nine
bioassays.

The static bioassay, with modification by con-

trolled artificial oxygenation was used because effluents

22

tested often contained excessive biochemical oxygen
demands. Dissolved oxygen was maintained by pumping
air into the test containers at a rate capable of
supplying 4-8 mg/liter. Throughout each bioassay the
difference in dissolved oxygen between containers at
any one time was minimal; usually testing started with
approximately 5 mg/liter in each tank and slowly
increased to 7 mg/liter at the end of a 96-hr period.
The test containers were 10 gal.rectangular glass
aquaria with a depth greater than 15 cm. Test con—
tainers were cleaned with detergent and water followed
by acid rinsing and final rinsing with distilled water.

Green sunfish, Lepomis cyanellus, were used as the

 

experimental fish because they were adaptable to labora-
tory conditions and common in the Red Cedar River. Fish
were taken from a common source other than the river
where there was no known prior exposure to unusual con-
ditions. The fish were acclimated to laboratory dilution
water (Appendix B) for two weeks before testing. Incidence
of disease or mortality was less than 5 percent. Fish
were fed daily until two days before testing and not fed
during the bioassay. Fish of a uniform size were used.
The weight of fish in a test container did not exceed

2 g/liter of test solution. The bioassay test period

was 96 hours with the number of dead fish in each test

container being observed and recorded at the end of each

23

24-hr period after introduction of the fish. Fish were
considered dead upon cessation of reSpiratory and other
movements and when there was no reaction to mechanical
proding. Behavior reactions during the test and symptoms
before death were recorded.

The results of the bioassays were expressed in
terms of tolerance limits (TL) as described in Standard
Methods (APHA, AWWA, WPCF, 1971). A 96-hr TL50 of a
toxic substance is that concentration in which 50 percent
of the fish survive for 96 hours. This value was esti-
mated from a plot of the test data on semilogarithmic
coordinate paper with concentrations (percentage by
volume) on the logarithimic axis, and percentage survival
on the arithmetic axis. The straight-line graphical

interpolation was then used to obtain the TL value.

50

Bacteriological Methods

 

Water samples from five river stations (Figure l)
were examined for coliform group bacteria. The coliform
group includes all aerobic and faculatative anaerobic,
gram-negative, rod-shaped, non spore-forming bacteria
which ferment lactose with gas formation within 48 1 3hr
at 35 C : 0.5C. The multiple-tube fermentation technique

for members of the coliform group as described in

Standard Methods (APHA, AWWA, WPCF, 1971) was used.

 

Samples were taken in sterile sodium thiosulfate-treated

glass bottles. Three samples were taken at each station

24

from a bridge by lowering sample bottles through the

surface to obtain representative samples. On both

sampling dates one sample was taken at midstream, and

one approximately equidistant between midstream and

each shore. Little time elapsed between collection and
examination, where the presumptive test with lauryl tryptose
broth was used. The confirmatory test with brilliant green
lactose bile broth was run as a check on the first sampling
date. The results of the examinations were expressed in

terms of the Most Probable Number (MPN).

Bottom Fauna

 

Bottom fauna (benthic macro-invertebrates) samples
were collected with a weighted Petersen dredge. The
dredge samples an area of 1.0 square foot to a depth of
2-4 inches. The Petersen dredge was chosen over that of
a Surber or Eckman sampler because of the depth of
sampling, weak current and coarse bottom. Even with
this rugged dredge there was some difficulty sampling
so the dredge was lowered repeatedly until an adequate
sample was secured. Five "pool" sampling stations were
located at the same sites as described by Jensen (1966)
and are indicated on Figure 1. Two riffle sampling
stations were established, one upstream at Ferguson
Park, Okemos and the other 200 feet below the Limnolog-
ical Research Laboratory. At each station three samples

were taken for each sampling date. One sample was taken

25

at midstream and one approximately equidistant between
midstream and each shore. Samples were returned to the
laboratory in plastic bags and either analyzed immediately
or refrigerated. All samples were screened with a stan-
dard 30-mesh sieve and organisms picked live by hand
with the use of viewer (light and magnifier) and white
pan. At downstream stations numbers of chironomids and
oligochaetes were so prolific in some cases that only
sub-samples were analyzed and appropriate multiplications
made. Complete samples were examined for all other
organisms. Organisms were preserved in 70 percent
ethanol until counted and identified under a binocular
dissecting microscope. Keys by Pennak (1953) and Ward
and Whipple (1959) were used in identification. Infor-
mation theory as proposed by Margalef (1956) was used

to express Species diversity.

Live Car Methods

 

Live cars were placed above and below specific
drains to determine the effects of the effluents upon
fish. Four live cars (boxes or cages) were constructed
with steel frames and wire mesh, each car having a
volume of 2 cubic feet (56.6 liter). They were coated
with asphaltum varnish to prevent corrosion and injury
to the fish. The effluents of four drains were examined
with this technique during separate periods of time.

Three live cars were placed in the river for each drain

 

Ill-[I‘l’ll ll Ill

I ll...‘ l ‘l. i

26

under study and a major control was kept in the river

at the beginning of the study section (Hagadorn Road).
Car 1 was approximately 20 yards above the drain studied,
where there was no influence of the effluent upon the
fish. Car 2 was placed immediately below (3 yards)

the drain where water was 50-100 percent effluent.

Car 3 was approximately 20 yards below the drain in
water which was 0-50 percent effluent. Any difference
in mortality between car 1 and 2 could have been the
result of a toxic effluent from the drain being studied.
A difference between car 2 and 3 would likely be due to
dilution, whereas a difference between the major control
and car 1 could result from the influence of other drains
above the one studied. Ten green sunfish were held in
each live car. Fish were acclimated to the temperature
of the river before the test period started. Many of
the same precautions as followed in the bioassay pro-
cedures were repeated in the live car testing. For
example, fish of similar size were used and their
average weight was recorded for each test. Results

are expressed as cumulative percent mortality for each

live car.

RESULTS AND D ISCUSSION

Drain Effluent Analyses

 

Similar to Jensen's (1966) study, results of
analyses indicated effluents of approximately one-third
of the drains located within the bounds of the study
area contained materials detrimental to the water quality
of the Red Cedar River. One difference is that there are
now 90 drains present, whereas, Jensen (1966) reported 68.
I would consider approximately nine drains to be major
polluters based upon the quantity, frequency of flow and
the type of pollutants found in the effluents. Several
drain effluents contributed high organic loads with a
few containing entirely untreated domestic sewage for
days at a time. High chloride concentrations were fre-
quently found in effluents flowing from several of the
drains, and a few effluents periodically contained lethal
concentrations of chemicals. Gas and oil films were
commonly observed, below certain drains. During rains,
storm drains often contributed heavy silt loads causing
the river to become turbid.

Tables 1 and 2 express measurements of magnitude

and dispersion concerning specific pollutants from the

27

28

 

 

 

 

 

00.0 00.0
00.0 00.0 Imm.0 00.0 00 00.0 00.0 100.0 00.0 00 0
c00umum
00.0 00.0
00.0 00.0 r00.0 00.0 00 00.0 00.0 100.0 00.0 00 00
00.0 00.0
00.0 00.0 t00.m0 00.0 m 00.0 00.0 I00.00 00.0 m 00
00.0 . 00.0
00.0 00.0 r00.0 00.0 00 00.0 00.0 I00.0 00.0 00 00
00.0 00.0
00.0 00.0 r00.0 00.0 00 00.0 00.0 I00.0 00.0 00 0
00.0 00.0
00.0 00.0 I00.0 00.0 00 00.0 00.0 I00.00 00.0 00 00
00.0 00.0
00.00 00.000 I00.000 00.00 00 00.0 00.0 I00.0 00.0 00 00
00.0 00.0
00.0 00.0 I00.00 00.0 00 00.0 00.0 I0m.00 00.0 00 00
00.0 00.0
00.00 00.00 100.000 00.00 00 00.0 00.0 I00.00 00.0 00 00
x x x x
Im m omcmm M 2 Im m mmcmm M z Honfisz
Hou00\mE comouu0z Ho000\0fi manocmmonm G0muo
.muco50mwm
c0000 momma How momm0mcm comouuHG 0cm msouocmmozm mo mumEESm 00000mHumum .0 o0nma

 

 

IL [{l’ l [I II II. ill. {Ill All | I'll]. [I All

29

 

 

 

 

 

0.00 00.0
00.0 0.0 10.00 00.00 00.0 00.0 100.00 00.0 00 0
0000000
0.00 00.0
00.000 000.0 1000.0 000.0 00.0 00.00 100.00 00.00 00 00
0.00 00.0
00.000 0.000 1000.0 00.000 00.00 00.00 100.000 00.00 0 00
0.0 00.0
00.000 0.000 1000.0 00.000 00.0 00.0 00.00 00.0 00 00
0.0 00.0
00.0 0.00 10.00 00.00 00.0 00.0 100.00 00.0 00 0
0.0 00.0
00.0 0.00 10.00 00.00 00.0 00.0 100.00 00.00 00 00
0.00 00.00
00.000 0.000 1000.0 00.000 00.0 00.00 100.00 00.00 00 00
0.0 00.0
00.000 000.0 1000.0 000.0 00.0 00.00 100.00 00.00 00 00
0.00 00.00
00.00 0.000 10.000 00.000 00.0 00.00 100.00 00.00 00 00
x x x x
1m 0 omcmm M 1m 0 mmcmm M nonasz
z c0000
Hou00\mfi mo00000£o 00000\mfi conumu .
.mucos0mmo
c0000 00008 000 mom>0mcm oo0000£o 0cm conumo mo wumEESm 0mo0um0umum .0 o0nme

30

major drains. Values for station 1, representative of
the river above the drains, are included for comparison.
Additional information is given in Appendices A and D.

Certain factors influenced the statistical values
presented and should be considered when studying the
tables. Samples contained observations from different
seasons. For example, chloride concentrations may be
expected to be higher in the winter due to street de—
icing practices. Samples contained extraordinary obser-
vations. For example, high concentration of pollutants
may enter only once a year and are not at all the usual
case for a particular drain. Also, one must consider
the scientific restrictions placed on the sampling.

To reveal similarities, one can compare the results
of certain drain effluent analyses to analyses made on
incoming raw sewage at the East Lansing Waste Water
Treatment Plant. For the month of June, 1971, analyses
made by the plant resulted in the following mean con-
centrations of chemicals: chlorides, 291 mg/liter;
total phosphorus, 6.7 mg/liter; and total Kjeldahl
nitrogen, 11.4 mg/liter. The character and amounts
of raw sewage escaping from combined-sewer overflows,
storm water from separate systems and sewage filth
awaiting the scouring effect of storm—water flow are

discussed by Weibel (1969).

31

Drain 66: Drain 66 is a combined-storm and sanitary
drain which often flowed raw sewage with a high organic
nutrient load. A main sewerage interceptor, comprised of
three pipes passing under the river at this point, became
blocked at times causing the controlling pressure caps
of drain 66 to Open and discharge raw sewage into the
river. There was evidence also that the pressure caps
stayed open at times. This drain was designed to flow
only during rain and melting conditions, but because of
reasons stated above, this was not the case. Fluorescein
dye injected into the main sewerage interceptor below
Michigan Avenue on May 5, 1971, flowed from drain 66
several minutes later. During a storm the effluent of
this drain was diluted with rain water, but when flowing
on a "dry" day long after any rain, the drain effluent
was entirely raw sewage discharged to the river instead
of being treated by the East Lansing Waste Water Treatment
Plant. Values from Tables 1 and 2 show the nutrient load
(phOSphorus, nitrogen and carbon) to be high. Chloride
concentrations were well above those found in the river.
One likely source is domestic waste, particularly urine,
which increases the amount of chloride in sewage about
15 mg/liter above that of carriage water (Sawyer and
McCarty, 1967). Anionic detergent analyses of over
1.5 mg/liter accounted for the foaming seen at times

and the increased phosphorus load. Synthetic detergents

32

having polyphosphates as "builder" have been estimated
to increase the phosphorus concentration of domestic
sewage two to three fold (Sawyer and McCarty, 1967).

On the selected days that I analyzed for ammonia nitro-
gen, results were commonly above 9 mg/liter.

Five bioassays (I-V) were performed using effluents
from this drain. Bioassay IV is presented in detail in
Appendix B, but the others were performed similarly. One
difference being that laboratory dilution water was used
in bioassays I-III, whereaS, river water taken from
station 1 was used for dilution in bioassays IV and V.
The results of the bioassays, expressed as 96hr TL50
values, were as follows: number I = 59.0 percent
effluent, number II = 8.1 percent effluent, number III =
25.7 percent effluent, number IV = 35.0 percent effluent
and number V = 80 percent effluent. A key observation
is that in all five tests some fish died, thus the
effluent from drain 66 had a lethal effect on green
sunfish.

There is evidence that ammonia and detergents were
the toxic agents. The initial ammonia nitrogen concen-
tration for bioassay IV was 15.0 mg/liter. Temperature,
oxygen content and pH all affect the toxicity of ammonia
(Hynes, 1960). Ammonia is very toxic in warm alkaline
water with a low oxygen content. Ellis (1937) states

that under average stream conditions with pH value

33

7.4 and pH 8.5, 2.5 mg/liter NH will be harmful to

3
individuals of the common aquatic species. The initial
detergent concentration for bioassay IV was 1.65 mg/liter.
Many factors influence the toxicity of detergents such

as pH, temperature, type of detergent and dissolved
oxygen. For example, as dissolved oxygen content falls
detergents become more toxic (Herbert 35 11., 1957).
Hokanson (1968) states that in static bioassays, the

mean 24-hour TLm values at 25 C in hard water saturated
with oxygen was 2.54 mg/liter for L.A.S. detergent.
Swisher, O'Rourke and Tomilinson (1964) reported that
L.A.S. is relatively toxic to bluegills with the 96hr.

TLm value of 3 mg/liter for the C 2 homolog and

1
0.6 mg/liter for C14 homolog. According to Pickering
and Thatcher (1970) the acceptable L.A.S. concentration
for fathead minnows is between 0.63 and 1.2 mg/liter
based upon chronic toxicity tests. From the evidence
presented it seems likely that ammonia nitrogen and
detergent concentration of the effluents from drain 66
were responsible in part for the death of green sunfish
in bioassays I through V. Other stressing factors that
likely added to the toxicity were higher than normal
salt content, turbidity, oil film and bacterial popu-
lations.

The effect of river dilution on toxicity can be

estimated. On sample dates the average dilution ratio

34

of drain 66 effluent to the river was 1:85 (Appendix A).
In bioassay number III the effluent was lethal to one-
half the test fish at a ratio of approximately 1:4
(25.7 percent effluent). Therefore, once diluted,
effluent from drain 66 is not likely to be acutely
toxic to fish. Chronic toxicity to fish and other
fauna may, however, result. To have a chronic effect
the drain would have to flow frequently or continuously,
and fish would have to be somewhat limited in movement.
Applying a factor to the acute toxicity level to
estimate a "safe concentration" is difficult and unwise
unless a detailed investigation is made. This is
especially true when working with sewage, which often
contains a mixture of toxic substances. Lloyd (1961)
has found that at times toxicities of mixtures of sub-
stances are equal to the sum of the toxicities of their
components. An excellent discussion of application
factors is given by Warren (1971), who reports that the ‘
Federal Water Pollution Control Administration has
recommended application factors ranging from 0.1 to
0.002 of the acute toxic concentrations depending upon
the substance tested and its characteristics. Concen-
tration of materials that are nonpersistent should not
exceed 0.1 of the 96hr TLm value at any time. The
24-hour average of the concentration of these materials

should not exceed 0.05 of the TLm values after mixing

 

 

......

35

(FWPCA., 1968). By applying a factor of 0.05 to the
96hr TL50 one concludes that the effluent from drain 66
would not chronically effect green sunfish once it has
been completely diluted with the river. Above statements
were based upon averages and approximations and consider
only the effect Of poisonous substances. It may be

wise to note, however, that on a specific date these
statements may be invalid. For example, on June 19,
1971, the dilution ratio Of drain 66 effluent to the
river was estimated to be 1:38. Certainly, this

figure represents a significant difference from the
figure Of 1:85. Therefore, on the above date, the
effluent of drain 66 may well have had a decided effect
upon the aquatic life below its Opening; especially if
one considers additional adverse conditions such as low
oxygen or above average temperatures which are common
with sewage pollution.

Finally, it is important to report that on three
occasions the city sanitation department quickly
responded to my request to have this drain checked and
corrected. It is unfortunate that unless action is 1
taken by a concerned citizen, a drain can pollute for

long periods of time before being corrected.

Drain 25: This drain is a large storm drain which
collects runoff from Michigan State University south

campus. During a storm it discharges a large volume of

36

water into the river. Usually its effluent is very
turbid and dark immediately after a storm but becomes
much clearer with dilution once the initial flushing
effect is over. Gas and Oil films were observed in the
effluent, which likely came from tars and fuel emissions
washed Off the streets. One example of the pollutional
effects Of this drain was Observed during a storm on
August 10, 1971. The muddy effluent, having a distinct
petroleum odor, spilled into the river causing a definite.
color change Of the entire river below its opening. On
this particular date the dilution ratio of drain 25 to
the river was estimated to be approximately 1:5, whereas
the average dilution ratio was estimated to be 1:170.
Although drain 25 was designed to flow during rain and
melting conditions, it Often flowed at a slow rate
(approximately 0.16 cfs) during dry periods. Evidence
from a fluorescein dye survey conducted August 6, 1971,
indicated that this water was coming from beyond a point
where the dye was dropped into the system, north Of
Michigan State University grounds building.

Results of chemical analyses show that this
effluent contains nitrogen, phosphorus and carbon con-
centrations well above that found in the river. Even
though a foam was occasionally Observed below this drain,
analyses for detergents were very low. On one occasion

when a large amount of foam was present (Appendix D),

37

the phosphorus concentration was 19.56 mg/liter, whereas,
the detergent analysis showed only 0.05 mg/liter or less
active detergent. The causative substance evidently was
not methylene green active but was definitely detrimental‘
to the river. Nutrient enrichment and a lowered aesthetic
value certainly can be classified as pollution. Table 2
shows the chloride concentrations from this drain were
high. On four occasions the concentration of chlorides
were above 5,000 mg/liter with resultant conductivities
of 15,000 u mhos cm-l. When this drain discharged high
concentrations Of chlorides the continuous flow monitor,
stationed approximately 200 yards downstream, recorded
conductivity peaks (Figure 4). As can be seen by com-
paring the chloride concentrations Of the drain to the
river, the effluent is quickly diluted. Twelve such
peaks with greater or lesser magnitude were recorded
by the monitor throughout the study period. Hardgrove
(1969) reported similar results and also noted that the
conductivity peaks generally occurred about midday. He
stated that while effects of dilution eliminate a hazard
in the river, intermittent high chloride values imme-
diately below the drain may be harmful to aquatic life. .
A bioassay was conducted on the effluent from
drain 25 on July 22, 1971, the same date as in Figure 2.
None of the fish died even though the chloride con-

centration in container 6 was 5,200 mg/liter (Appendix B).

 

38

 

 

 

 

 

“PM
1 Temp. Cond. pH

6pm‘

4pm:
F: ._RWer
I 2 mi Chlorides
N 9 1300911
(:1 Cond.

P k

R ea

12 1
g noon River
.... it-Chlorides
p— 133mg“

100m-

amo ' 2'0 7 4B ' co 7 so ' 160

Figure 4.

Recorder Units of Monitor

River conductivity peak due to Drain number 25.
[Conductivity expressed as u mhos x 101, -1
temperature in degrees centigrade and pH x 10 .
The conductivity Of drain number 25 during the
peak was 18,932 u mhos cm'”1 and had a chloride
concentration of 7,600 mg/liter.]

39

The fish did, however, exhibit stress symptoms such as
irregularity of respiration and excitability. Clemens
and Jones (1954), using sodium chloride solutions,
reported a 96hr TLm of 5,288 mg/liter Cl- for fathead
minnows. Trama (1954) found the 96hr TLm for bluegills
to be 7,846 mg/liter Cl-. Research indicates that
common salts (NaCl, MgCl2 and CaClz) are not very toxic
to fish compared with other compounds or even other
chlorides like mercuric chloride. The range seems to
be between 5,000 and 10,000 mg/liter c1“ in general.
The major reason appears to be that the osmotic
pressure of fishes is about six atmospheres or approxi-
mately the equivalent of 7,000 mg/liter sodium chloride
(Ellis, 1937). Although 80 percent effluent was not lethal
to fish during the bioassay, information from a live car
test was more revealing. Live cars provide a more
realistic test situation because they are placed into
the stream where interacting systems of great complexity
are present. Warren (1971) concludes that bioassays Often
cannot yield reliable estimates of safe concentrations
of toxic substances and "it is to nature that we must
turn finally for the answers we need."

A live car test showed that after a period of con-
tinuous exposure to the effluent of drain 25, 60 percent
of the test animals died in the live car placed imme-

diately below this drain. Ten percent mortality occurred

40

in a live car placed 20 yards below the drain (Appendix B).
It can be concluded that effluents from this drain had a
lethal effect on green sunfish when held immobile, but
the effect quickly diminished with dilution. One might
hypothesize that in the natural environment fish exhibit
an avoidance reaction to this drain or that certain
invertebrates are limited by its effluent.

High concentrations of chlorides in the effluent
Of drain 25 during the winter likely occurred as a result
of street de-icing practices. Salts used for ice removal
at Michigan State University contain approximately 97 per-
cent NaCl with some CaSO

and M980 _and are 98 percent

4 4
soluble in water. High concentrations in the summer may
have been the result of back-washing water softeners,
laundry effluents or urine contamination. Several other
pollutants also were found in the effluent of drain 25

thus placing it in the category of a major polluting

' .1 r -' '1 .'-‘
drain. . J‘V 5” 0'

Drain 82: Drain 82 is a combined storm and sanitary
drain which often flowed raw sewage having a high nutrient
load (Tables 1 and 2). Its effluent characteristics are
very similar to drain 66 which is part of the same
sewerage system. The effluent was usually dark gray
with particles of feces and paper present. It commonly
smelled like sewage or was even septic. Even though the

drain opening is almost entirely blocked by stones and

41

concrete it can easily be found by the unsightly
appearance that it leaves on the bank of the river.

A sludge bed has developed immediately out from its
Opening. The effluent was warmer than the river and

had an average detergent concentration Of 1.33 mg/liter,
based on five samples. On one occasion the nitrogen
concentration was 392 mg/liter, the highest value
recorded from any of the drains. Because this drain's
opening is dammed by rocks, it was difficult to estimate
its discharge, which was considerable at times. From
the sampling data it appears that near the end of the
study period, this drain was partially corrected because
it flowed less Often, usually only during a rain as
designed. The city of East Lansing had been notified

and supposedly action was taken.

Drain 15: Drain 15 is a storm drain which collects
runoff and service water from the Michigan State Uni-
versity power plant, stadium and bus service areas.
Effluent temperatures averaged 5 C warmer than the
river. Other than high temperature, the effluent was
generally of good quality but at specific times contained
high concentrations of phosphorus, detergents and
chromium. An oily film was characteristic of this 0
drain. A likely source was from the bus service area.
Because detergents were high on occasion, a fluorescein

dye was dropped into a floor drain Of the bus-washing

42

garage, but results were negative. A dye dropped into

a storm drain adjacent to the stadium did give positive
results. High phosphorus concentrations (Table l) were
possibly due to addition Of detergents or sodium phos-
phate, which is at times used in the power plant to
control slatting. On one occasion, when a froth was
observed, the concentration of detergents in the
effluent was 3.5 mg/liter with a phosphorus concen-
tration of 28.53 mg/liter. Analysis of one of four
greenish effluents resulted in a chromium concentration
Of 3.2 mg/liter. Chromium compounds are often added to
cooling water for corrosion control (APHA, AWWA, WPCF, .
1971). Doudoroff and Katz (1953) present data showing
that fishes of the sunfish family can tolerate in hard
water as much as 68 mg/liter Cr for at least 5 days.

The same publication reports that a concentration of

1.4 mg/liter Cr as Cr2(SO4)3 was lethal to sticklebacks
in approximately 96 hours. A bioassay was conducted on
this effluent, which also was 36 C and produced an oily
film. Results were negative in that 80 percent effluent
was not toxic within 96 hours. These results were sup-
ported by a live car test in which none of 10 green sun-
fish died after being held for 13 days immediately below
the effluent. Evidence shows that the effluent was
neither toxic in the bioassay nor after partial dilution

with the river. The average discharge Of this drain

43

was 0.15 cfs with an estimated dilution ratio of 1:827
with complete mixing. Even though this drain's effluent
may not be lethal to fish, information presented indicates
that it is adding to deterioration of water quality in

the Red Cedar River.

Drain 6: Drain 6 is a partially submerged drain,
so sampling its effluent and estimating its flow was
difficult. At times its effluent was sewage-gray in
color, becoming even darker immediately after a storm
and causing a noticeable color change in the river well
below its Opening. Oily films were also observed. The
effluent averaged 2 C warmer than the river throughout
the sampling period. A fluorescein dye survey indicated
that most Of the flow comes down the storm sewer under
Wilson Road with some of the flow coming from the
Michigan State University greenhouse area. From Tables 1
and 2 one sees that this drain's effluent on the average
is quite similar to the river except in phosphorus con-
centration, which is somewhat higher. In my opinion
these values were low estimates of true effluent parame-
ters because of the difficulty in sampling a submerged
drain. It was Obvious while sampling that pure effluents
were not always obtained but only a mixture of river
and drain water.

To determine effects of this drain on fish, a

bioassay was run on its effluent of August 13, 1971,

44

which was gray-green in color and produced a slight Oily
film. The ammonia concentration was 0.24 mg/liter and
detergent concentration, zero. Results of the bioassay
were negative in that no mortality occurred in 80 percent
effluent after 96 hours. Live car test results (Appendix B)
show that this drain's effluent was lethal to 90 percent
of the fish held immediately below its opening from
August 4 to 13. The effluent was lethal to 70 percent .
Of the fish held 20 yards below the drain where there is
approximately a 1:1 or greater dilution. It is important
to note that mortality began at the same time as a major
fish kill occurred further downstream. Toxicity was
probably a result of the combined effect of the drain
effluent and general low oxygen level in the river.

In a second live car test from August 14 to 21, mortality
again occurred in the live car placed immediately below
the effluent. From information presented it appears

that this drain has a detrimental effect on Red Cedar
River water quality and likely effects the behavior Of

some of its aquatic fauna.

Drain 62: Drain 62 is a storm drain receiving
service water from Kellogg Center and storm runoff from
the surrounding area. This drain is included as a
major drain because its effluent, although usually
clear, flowed continuously, averaged approximately 5 C

warmer than the river and often discharged oily products

45

which produced a thin film on the river. Quite fre-
quently its effluent showed the greenish-yellow hue
characteristic of chromium compounds. A dye survey
indicated the principal source was from the Kellogg
Center, probably from the large air—conditioning unit;
this unit would explain the heated effluent and high
chromium concentrations. As stated earlier chromate
compounds are commonly used to control slate build-up
in cooling systems. On one occasion (July 15, 1971)
the chromium concentration was 4.8 mg/liter, whereas, the
concentration of the river was less than 0.03 mg/liter
at station 2. A bioassay was run on the same date; the
96hr TL50 value was 86 percent effluent (Appendix B).
Having an average dilution ratio of 1:451 it was very
unlikely that this drain was directly lethal to aquatic

fauna after complete mixing with the river.

Drain 61: This drain is a 72-inch combined storm
and sanitary drain which is controlled by a large
pressure cap; consequently it flowed only during melt-
ing conditions or a rain. Despite its less frequent
flow the drain's detrimental effect.was great because
of the character and volume of discharge. The effluent
was usually gray—black, contained a large amount Of
suspended material (sewage), smelled septic and noticably
changed the quality of the river for several hundred

yards below its opening. Tables 1 and 2 show that the

46

nutrient level and chlorides were much higher than in

the river. On one occasion results of detergent and
ammonia analySes were 1.05 mg/liter and 10.0 mg/liter,
respectively. The ammonia concentration may be explained
by the fact that when sewage sets in a sewer during low
flow (no rain), pockets Of water may become totally
deoxygenated; anaerobic bacteria reduce nitrates to
ammonia and sulphates to sulphides. Therefore, a mass

of water is formed which is not only deoxygenated but
contains poisons and has a heavy oxygen deficit (Hynes,
1960). Hynes (1960) also states that a further compli-
cation is introduced by the presence Of Oil or detergents
which affect uptake Of oxygen at the waters surface.

On August 10, 1971, the evening before a fish kill the
entire river changed from a muddy-brown color to gray-
black directly out from drains 61, 82 and 105, which ‘
were all flowing. The average dilution ratio of drain 61
to the river was 1:34. Considering information presented,
it seems apparent that this drain contributed to the

deterioration of Red Cedar River water quality.

Drain 36: Drain 36 is a partially submerged storm
drain thus sampling its effluent and estimating its
flow was difficult. By using a dye and entering the
drain through a manhole, I determined that water comes
down a storm sewer under Michigan Avenue. Because the

drain discharges a considerable amount of water even

47

during "dry" periods there must be some source other
than storm runoff. With evidence such as a cloudy-gray
color, higher than normal chlorides and frothing, it
appeared that, at times, this drain's effluent was con-
taminated by sewage. A detergent level of 2.2 mg/liter
was found on April 4, 1971. During a rain its effluent
became very turbid and gray-brown in color. There was
Often a distinct sulphur-like odor and rusty appearance
at the drain opening under dry conditions. In addition
iron-like deposits were noticed in the storm sewer.
Iron and sulfur bacteria can produce precipitates of
ferric hydrate from ferrous compounds (Starkey, 1967).
Tables 1 and 2 indicate that this drain does not sig-
nificantly add to organic-nutrients. Again, Obtaining
representative samples from a submerged drain was diffi-
cult.

A live car test continuing from September 4 through
September 19 proved to be negative, therefore, no data
were collected to suggest toxicity to aquatic fauna. On
occasion a few dead crayfish and amphibians were observed
at the mouth of this drain. More information should be
collected before judging this drain's complete influence
upon the river. It is apparent, however, to a canoeist
that drain 36 is adding to the destruction of the river's

recreational quality.

48

River Quality and General Effects
of Pollution

 

 

Two Objectives are met in this section. First, it
is illustrated that water quality Of the Red Cedar River
changes from Hagadorn Road to East Kalamazoo Street as a
result of an accumulation of pollutants from the many
drains. The effects of pollution on a receiving streamb
Often become confused, because additional sources Of
pollution may enter the environment before the receiving
water has been able to assimilate the entire effects Of
an initial source. When this occurs the effects of sub-
sequent introductions become superimposed on those of
the initial source, and the total effect may confine
large reaches of the stream (FWPCA, 1969). Second, when
possible, a comparison was made of present water quality
parameters with those of the past.

Individual parameters are discussed after which I
have simply listed significant contributing drains based
on individual Observations and the discussion of the
previous section. One or more effects of pollution may
be characteristic of any one effluent. Hynes (1960) has .
divided the effects of pollution into five categories:
addition of poisonous substances, addition of suspended
solids, de-oxygenation, addition of non-toxic salts and
heating. Other less subtle effects should be considered,‘
such as the gradual eutrophication of the river which

may result in changes in fauna or usefulness to mankind.

49

Linton (1967) in a study Of low-level chronic effects ,
Of pollution on rock bass in the river, found that the
annual potential instantaneous rate Of natural increase
for rock bass was negative (pOpulation dying) in the
"polluted zone" from Farm Lane bridge to Okemos Road.

In contrast, values of a "clean zone" were all positive.
He concluded that with respect to environmental obser-

vations, differences in success of the rock bass popu-

1ations can probably be attributed to pollutants.

Dissolved Oxygen and Fish Kills

 

One very destructive kind Of pollution occurs when
relatively large amounts of putrescible organic materials
are introduced into waters causing an oxygen depletion
(Warren, 1971). Evidence indicates that this type Of
destruction has and will continue to occur in the Red
Cedar River unless corrective action is taken.

Water Quality Standards for Michigan Intrastate
Waters (Mich. Water Resources Comm., 1968) state that
for tolerant fish (carp, bullheads) the average daily
D.O. should not be less than 4 mg/liter nor shall any
single value be less than 3 mg/liter. However, Tarzwell
(1957) pointed out that generally under polluted con-
ditions a fish will require more oxygen. One major and
two minor fish kills were observed primarily in the
lower half of the study section. Figure 5 shows the

diurnal oxygen curve of station 2 during the major fish

 

50

 

 

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52

kill of August 11, 1971. During the evening of August 10,
1971, a sudden storm caused several drains to discharge
a large amount of organic matter into the river (see
drain 61 and list below) which, when oxidized by micro-
organisms, caused an oxygen deficit. The action of a
sudden rain also will cause the release of reducing sub-
stances from the disturbed muds (Bamforth, 1962). In
addition oxygen production by primary producers in the
river is reduced by scouring and turbidity. Besides
being affected by low oxygen, fish were likely stressed
by higher than normal ammonia (station 2 = 1.0 mg/liter
NH3) and sulphides which increase during anaerobic
decomposition. Over 1,000 fish of many species, such as
white sucker, spotted sucker, rock bass, green sunfish,
northern pike and various cyprinids died throughout the
river below the Michigan State University dam. TWO
minor kills of approximately 50 fish (mainly white
suckers) also occurred.

Considering Figures 5 and 6, sudden rainstorms
usually result in an oxygen depletion, especially during
low-flow periods. Hardgrove (1969) presented four
illustrations of heavy runoff resulting in an oxygen
drop, although none were as severe as the one presented
in Figure 5. Oxygen concentrations were generally
greater upstream than downstream. Jensen (1966)

reported that oxygen saturation decreased linearly from

 

 

 

 

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55

a mean value of 75 percent at station 1 to a mean value
of 18 percent at station 2 (5). The dissolved oxygen
as shown in Figure 6 was greater at station 1 than 2 in
both the curves taken from Jensen's study (1966) and

in those taken during this study. The location of
station 3, which is between station 1 and 2, is shown
on Figure l. The difference in oxygen content is much
greater than one would expect with normal stream suc-
cession; therefore, given the information from the drain
effluents, it seems apparent that oxygen reduction is
the result of incoming pollution. Jensen (1966) con—
cluded, by correlating increasing phOSphorus, nitrogen
and BOD values with decreasing oxygen concentration,
that sewage entering the river is the factor most
responsible for observed oxygen concentrations. It
appears that there has been some improvement in oxygen
quality near station 2 (5) since 1964. The continuous
monitor and Winkler tests, in this study and as used by
Hardgrove (1969), revealed the normal diurnal oxygen
flux to be similar to the curve presented in Figure 5
(top). A continuum of diurnal oxygen curves taken from
the monitor revealed the average daily value was between
5 and 6 mg/liter with the fluctuation dependent upon
such factors as season, rainfall, cloud cover and plant
growth. Hardgrove (1969) indicated that September

through October and April through May exhibited the

56

greatest degree of development of diurnal oxygen curves.
Data indicates that oxygen levels at station 2 have
increased in recent years; compare the "typical" diurnal
oxygen curve of Figure 5 to the 1964 curve in Figure 6.
At first it may seem invalid to compare just two oxygen
curves taken at different times, during different years
and at slightly different points. But, the curve in
Figure 5 is a representative curve, and Jensen (1966)
also presented other similar curves to the ones shown
in Figure 6; therefore, it appears that the average
daily oxygen concentration near station 2 (5) has
increased from approximately 3 mg/liter in 1964 to
between 5 and 6 mg/liter in 1971. This change in the
lower reach of the river is likely due to the closing
of the East Kalamazoo Street Sewage Treatment Plant.
Data indicate that the following drains have
discharged effluents which were capable of contributing
significantly to oxygen depletion in the river: 61,

82, 25, 66, 33, 36, 6, 47, 58, 103 and 64.

Chlorides

 

Sodium chloride, a universal constituent of sewage,
is reduced in concentration only by dilution. In fact,
before the development of bacteriological tests, chloride‘
determinations served as a basis for detecting contami-
nation of ground-waters by sewage (Sawyer and McCarty,

1967).

57

Table 3 shows that the mean chloride concentration
of the river increased significantly from station 1 to
station 2. Data indicate that drain effluents are
responsible for the increased chloride-concentration
(see discussion of drain 25). Throughout the study
period 12 drains discharged effluents with chloride con-
centrations greater than 1,000 mg/liter, 4 drains greater
than 5,000 mg/liter and 2 drains greater than 20,000
mg/liter. Also, there seems to be little reason for a
significant increase in chlorides due to purely "natural"
stream succession.

Most ecologists are of the opinion that common
salts have little effect on our aquatic systems because,
generally, toxicity to aquatic fauna does not occur at
concentrations under 1,000 mg/liter. The highest level
found in the river at station 2 was 230 mg/liter. How-
ever, freshwater organisms are adapted to living in
waters of low salt content. Thus, an increase in salts
changing the osmotic pressure may directly or indirectly .
affect some stage in the life history of freshwater
animals in ways decreasing their distribution, abun-
dance and value to man (Warren, 1971). Anderson (1950)

found that Daphinia magna were least resistant to

 

chlorides during the molt stage of their life. Because
we are looking at low, non-toxic levels in the river,
concern over the indirect influences of salts might be

more appropriate.

58

 

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59

Chlorides influence the density of water. Judd
(1970) found that salts entering a lake caused an
increase in density of bottom waters and as a result,
there was incomplete spring overturn. The lake received
runoff from adjacent streets and expressways with
chloride concentrations of over 10,000 mg/liter during
periods of deicing. Although in this study we are not
directly concerned with a lake, salts introduced into
the Red Cedar River will eventually flow into Lake
Michigan. Ownbey and Willeke (1965) predicted that
by the year 2020, Lake Michigan would contain 12 mg/liter
Cl- over the present 7 mg/liter because of salt increases
in adjoining rivers. They considered this to have no
overall harmful effect on the lake, but felt as do I,
that much of the salt input could be eliminated.

Other likely influences of an increase in salt
content are the synergistic effects with other toxicants
(Brown, Shurben and Farwell, 1967); the detrimental
effect on plants if used for irrigation water (Peterson,
1968); or the unsuitability of the water for industrial
purposes. Cleary (1967) states that salinities of
50-175 mg/liter are considered "doubtful" by some for
industrial use. This level is below the Federal drink-
ing water standard of 250 mg/liter chlorides.

Drains which contributed effluents having high
chloride concentrations were: 25, l, 2, 80, 67, 66, 82,

36, 62, 22, 64, 61 and 63.

60

Suspended Solids

 

Figure 7 indicates that there was an increase in
suspended solids from Dobie Road, which is above the
communities of East Lansing and Okemos, to station 2.
See Appendix D for the location of Dobie Road relative
to stations 1 and 2.

Suspended solids can effect a lotic environment
in many ways. Jensen (1966) states that turbidity, a
measure of the suspended matter interfering with light
passage, and siltation prevent abundant nitrogen and
phosphorus from supporting large blooms of aquatic
vegetation in the Red Cedar River. Brehmer (1958) con-
cluded that turbid water conditions limited periphyton
production in the river. Suspended solids also can
effect sight feeding fish and destroy spawning habitat;
a probable factor in the population limitation of rock
bass, especially in the lower portion of the study
section.

In stream pollution control work, Sawyer and McCarty
(1967) consider all suspended solids to be potential
settleable solids, as time is not a limiting factor.
Hynes (1960) states that deposits of solids smother
algal growth, kill rooted plants and limit cryptic
animals by altering the nature of the substratum.

As a rule hardness and conductance increase with

an increase in suspended solids (Sawyer and McCarty, 1967).

61

20-

    

Station 2
(downstream)

.-
In
J

 

Dobie Road
(Upflroam)

U.
1

SUSpended Solids (mg/ l)

 

 

5'14 6°18 7-I3 840

Date (1971)

Figure 7. Suspended solids (unpublished data).
[Each value is the average of two determi-
nations.)

62

As can be seen from Table 4 both these parameters
increased from station 1 to 2 and therefore support
the suspended solids data.

Drains which at times appeared to discharge a high
content of suspended solids (silt) were 25, 66, 82, 36,
l, 6, 61 and 8. The three major sources of increased
suspended solids were initial street runoff, sewage

contamination and construction causing soil erosion.

Phosphorus

 

Phosphorus is considered by aquatic ecologists as
an important nutrient because it often limits or con-
trols production of aquatic systems. The role of phos-
phorus in the Red Cedar River has been discussed in some
detail by Brehmer (1958 and 1956), Grzenda (1960) and
Jensen (1966) as well as others.

Table 3 shows the relative magnitude of the phos-
phorus values and the increase from station 1 to 2.

Data from this and past studies show a general range

in phosphorus concentration of 0.1 mg/liter to 0.2
mg/liter. Working with laboratory cultures Chu (1943)
found that optimum growth of all organisms studied in
cultures can be obtained in phosphorus concentrations
from 0.09 to 1.8 mg/liter and phosphorus concentration
from 0.009 mg/liter downward are limiting. Sawyer (1965)
reported that nuisance conditions can be expected when

the concentration of inorganic phosphorus exceeds

63

 

 

 

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64

0.01 mg/liter. As a guide line, the Federal Water
Pollution Control Administration (1968) reported that
the concentration of total phosphorus should not be
increased to levels exceeding 0.10 mg/liter in flowing
streams or 0.05 mg/liter where streams enter lakes or
reservoirs. From information presented one sees that
phosphorus as a plant nutrient is not "limiting" but
is present in excessive amounts in the Red Cedar River.
Increase in mean phosphorus concentration from
station 1 to 2 is principally the result of drains
discharging phosphorus-rich effluents. This is
especially true of effluents containing raw sewage or
detergents. Jensen (1966) working with ortho-phosphorus
reported a similar increase and concluded that large
quantities of phosphorus were being loaded into the
river at the East Lansing Kalamazoo Street Sewage
Treatment Plant which is no longer in operation. Some
enrichment from leaf litter does occur throughout the
study section, but it probably is less than the amount
which enters the river upstream in heavily forested areas.
Above statements are supported by Brehmer (1958) who
reported that physical and chemical characteristics of
the river indicate that municipal drains and sewage
treatment plant outfalls are the most important sources
of phosphorus. Those drains which discharged significant

amounts of phosphorus into the river were: 66, 61, 82,

65

25, 15, 6 and 103; the latter no longer flows. Often
these drains contributed their highest phosphorus con-

centrations during storms.

Nitrogen

As with phosphorus, nitrogen is an important com-
ponent of stream eutrophication. Evidence suggests that
in specific situations nitrogen may be a more important
limiting factor than phosphorus. Sawyer (1965) reported
that nitrogen may be the more critical factor limiting
algal production in natural waters since phosphorus is
stored in algal cells in excess. However, current think-
ing seems to indicate that phosphorus usually is the con-
trolling nutrient. Brehmer (1958) concluded that nit-
rogen, rather than phosphorus, was the nutrient limiting
plant productivity in the river. Results here and
Jensen's (1966) study indicate neither phosphorus nor
nitrogen is limiting, but rather that productivity is
limited by turbidity and siltation. Table 3 shows the
magnitude of the mean nitrogen concentrations and changes
from one station to another. A comparison with past
studies is made more difficult because only total
Kjeldahl nitrogen was measured regularly.

The level of 3.5 mg N/liter at station 2 seems
relatively high when compared with the average total
Kjeldahl nitrogen of raw sewage, which was 11.4 mg/liter

at the East Lansing Waste Water Treatment Plant for

66

June, 1971. Jensen (1966) reported that nitrogen levels
at all stations were above levels commonly found in
unpolluted streams. Mfiller (1953) concluded that exces-
sive growths of plants and algae in polluted waters can
be avoided if the concentration of total nitrogen is not
allowed to rise much above 0.6 mg/liter. The increase
from station 1 to station 2, again can best be explained
by the addition of effluents with high nitrogen con-
centrations.

Although ammonia is generally kept at a low level
because it is almost immediately converted to nitrites
and nitrates or utilized by the aquatic flora, it did on
occasion reach high levels. The ammonia concentration
during a fish kill reached 1.00 mg/liter in the lower
river just after a sudden storm; a concentration con-
sidered as pollutional by Reid (1961). Jensen (1966)
found there was a gradual downstream increase of
ammonia throughout the study section.

Data indicate that as a plant nutrient nitrogen
is present in excess just as with phosphorus. Abundant
growths of algae were observed during the summer and fall
only when the river was not turbid. Primary production

was not measured in this study.

Carbon
Organic substrate concentration was determined by

measuring the actual amount of organic carbon present in

67

a sample. Although BOD and COD determinations have
become accepted standards of measurement in water pol-
lution control work they are essentially ineffective

for several reasons. FWPCA (1969) considers BOD pro-
cedures as inherently nonreproducible, and the unpre-
dictable nature of test results make their interpre-
tation difficult. There are also limitations on COD
analyses such as the degree of oxidation of a compound
tends to depend upon its structure. Stenger and Van Hall
(1968) provide a more complete discussion of the methods
used to estimate organic substrates. With the intro-
duction of the carbonaceous analyzer by Van Hall, Saf-
ranko and Stenger (1963), researchers are tending toward
the more direct analysis. The carbonaceous analyzer
measures the amount of carbon present which can be
reduced to carbon dioxide.

Table 3 shows that the mean carbon concentration
increased from 9.21 mg/liter at station 1 to 11.80
mg/liter at station 2. The increase likely is the
result of drain effluents with high carbon concentrations.
A drain such as 66 which often flowed raw sewage had a
mean carbon concentration of 31.6 mg/liter. For com-
parison, organic carbon can be correlated with B.O.D.
values (Ford, 1968). Jensen (1966) found that B.O.D.
values increased from 3.69 at station 1 to 10.60 at

station 2. He reported that waters having a B.O.D.

68

of 3 are of poor quality, and those with a B.O.D. of
4 are bad quality. Those drains which discharged a
significant amount of dissolved organic carbon into
the river were 25, 66, 82, 103, 8, 64, 61 and, on one
occasion, drain 54 discharged a very dark effluent

with 1,400 mg C/liter for a short period of time.

Bottom Fauna

 

This section deals with the macro-invertebrate
community structure, emphasizing indicator organisms
and community diversity as biological indices of
environmental change. Because of habitat preference
and low motility, bottom organisms are directly affected
by substances that enter the environment (Whilm and
Dorris, 1966). The addition of domestic sewage and
initial storm runoff to a river increases available
energy through added organic matter and also contributes
to turbidity, siltation, toxic materials and low dis-
solved oxygen. These factors generally lead to low
diversity of Species, with only tolerant ones present,
but support large populations because of the energy-
rich ecosystem. Thus we might expect a significant
change in the bottom fauna from station 1 to 2 con-
sidering the data presented in past sections.

As was true of Jensen's (1966) study, bottom
samples indicated productivity was high but diversity.

was extremely low. Figures 8 and 9 show an increase in

69

Figure 8. Number of Oligochaeta per square foot at
river sampling stations. [Open bars are
those of Jensen (1966). Distances on
abscissia are proportional to distances
between stations.]

70

 

 

 

 

 

 

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71

Figure 9. Number of Chironomidae per square foot
at river sampling stations. [Distances
on abscissa are proportional to distances
between stations.]

 

72

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73

Oligochaeta and Chironomidae as one goes downstream from
Hagadorn Road to East Kalamazoo Street. Of the oligo-
chaetes, tubificids are found in concentrated populations
in streams and rivers that are polluted with sewage
(Pennak, 1953). Although Tubificidae were by far the
most common of the Oligochaeta, other families, such as
the enchytraeids, were probably represented in the
samples. In fact, subsamples showed that the majority

of the oligochaetes were the cosmopolitan Tubifex tubifex,

 

which is tolerant of organic pollution. Chironomidae,
which were present in high numbers, are typical of
streams rich in organic matter and can live in rela-
tively low oxygen concentrations. Of course the presence
of oligochaetes and chironomids does not necessarily
mean that the oxygen level in the river is low. Hynes
(1963) has stated that if a river is reasonably well
oxygenated oligochaetes may still be dominant in accumu-
lated organic matter, although accompanied by chironomids
and usually some clean-water animals (Table 5). All

five stations of Figures 8 and 9 were slow moving "pool"
areas with sand and silt bottom for the most part.

In another phase of collecting bottom fauna data,
two riffle sampling stations were established. One at
Ferguson Park, Okemos, above all the drains mentioned
in this study, and the other 200 feet below the Limno-

logical Research Laboratory. A list of organisms

74

Table 5. Summary of "pool" bottom fauna expressed as
mean number per square foot.

 

 

 

Station
Organism

l 2 3 4 5
Oligochaeta 23 58 104 44 398
Chironomidae 29 20 64 59 118
Elmidae 8 6 l 3 l
Pelecypoda 4 7 4 7 ll
Gastropoda l l 3 2 -
Baetidae - l - - -
Rhagionidae - l - - -
Planaria - ~ - - l

Hirudinae - - - - 2

 

75

encountered and numbers of individuals per square foot
is given in Table 6.

Some investigators have classified bottom organisms
according to pollution tolerance, but this is difficult
and there is lack of agreement. One can be reasonably
correct, though, if he is quite general as is Beak (1965)

who lists three groups as follows:

Group 1 Group 2 Group 3
Oligochaeta Chironomidae Odonata
Hirudinea Trichoptera
Pelecypoda Megaloptera
Gastropoda Ephemeroptera
Amphipoda Plecoptera

Group 1 includes the most tolerant. Group 2:
which are facultative with regard to pollution, and
Group 3 are generally sensitive to water pollution.
This classification seems to apply quite well to the
Red Cedar River. Oligochaeta were found with 100 percent
frequency both upstream and down, but it is interesting
to note that the density downstream below the drains is
approximately a lOO-fold increase over that of the -
upstream station.

The occurrence of Hirudinea in downstream samples
is probably related to the increase of available food
(oligochaetes and chironomids). Leeches are commonly
carnivorous and feed on snails, oligochaetes and other

small invertebrates, but others are scavengers which

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79

feed on dead animal matter (Pennak, 1953). Hynes (1963)
notes leeches are found in polluted water, but they persist
even after a river has recovered.

At Okemos the total number of chironomids per
square foot was less than 100, whereas,downstream their
numbers always exceeded 500. Chironomidae, being typical
of streams rich in organic matter, are chiefly herbi-
vorous, feeding on algae, higher aquatic plants and
detritus (Pennak, 1953).

Megaloptera, Trichoptera and Ephemeroptera were
all much more abundant in upstream samples than those
from near the Limnological Research Laboratory. The
caddisfly and mayfly are shown by Odum (1959) to be
part of the community of a clear and fresh stream.
Pennak (1953) lists these orders as typical of fresh-
water habitats wherever there is an adequate supply of
oxygen. The presence of these three orders does not
necessarily indicate that the river at Okemos is a
clear, fresh streamytbecause midges and aquatic worms
were still predominant. It does indicate, though, that
the river is well oxygenated and fairly pollution free ’
(at Okemos) for a warm-water river. It also shows that
there is a "better" balance of organisms (herbivore, -
carnivore, predator, prey) upstream above the drains
mentioned than below. This type of habitat is sup-

portive of game fish also. Neither presence nor

80

absence of a species alone can be taken as reliable
evidence of the existence of the particular range of
conditions man chooses to consider pollutional. The
question of abundance of a particular species needs
consideration, as does abundance of other species with
which it is associated (Warren, 1971).

Margalef as quoted from Wilhm and Dorris (1966)
"proposed analysis of natural communities by methods
derived from information theory. Diversity and infor-
mation may be considered equal for practical purposes
and can be calculated directly from the sample. Unlike
many expressions for describing community structure,
Margalef's index of diversity includes numbers of indi-
viduals representing each species. Maximum diversity
exists if each individual belongs to separate species."
Thus this diversity index which is based on formulas of
Shannon-Wiener accounts for relative abundance of the
different species. Information theory has distinct
advantages because it is not dependent upon constant
sample size and number when making comparisons and only
total number of recognizable species in a unit area is
needed.

The formula

ml
n
I
H M ’5‘
a
zip.
....I
O
m
N

81

is used where

m = number of species,
n. = number of individuals of a particular
species, and

n./N probability of encountering that particular

species in a sample.

Upstream at Okemos, above the drains, H was equal
to 4413. Downstream at station 2, H was equal to 1:32.
The adequacy of six samples is expressed in
Figures 13 and 14 of Appendix C. Wilhm and Dorris
(1968) claim the information value stabilizes by the
fourth sample in a stream environment. They have sum-
marized the question of sampling by stating that because
several species may be super-abundant in a stream receiv-
ing organic wastes, a large probability exists that an
individual observed during sampling belongs to a species
previously recognized. The high redundancy is reflected
in a low index of diversity. Only a few samples would
be necessary to describe this low-information system,
and additional samples would be superfluous. Clean-water
areas are characterized by smaller numbers of individuals
and larger numbers of species. There is less repetition
of information per individual and thus more samples are
needed to describe this system adequately. This may be

true of the upstream station (Okemos), although, new

82

species encountered would likely be rare; H would increase
showing an even greater difference from that downstream.

Two points should be noted concerning the infor-
mation values found. First, the relative difference
between the two values and secondly their comparison to
values of similar studies.

Longitudinal succession is evident in all streams
and rivers (Odum, 1959). In most streams the gradient
decreases, and temperature, organic drift, volume of
flow and general productivity increase as one advances
toward the mouth. River bed sustrate usually changes
too, going from rock and rubble to silt and clay. With
these changes the community structure also changes and
therefore it is natural for the bottom fauna of some
rivers to go from mayfly and caddisfly to bloodworms
and oligochaetes near the mouth. This change may be
quite rapid in nature, but, for the approximately six-
mile reach of river between Okemos and station 2 all
indications show that the change in numbers and species,
as reflected by (H) and the past discussion, is far too
great. The velocity of flow and natural bottom were
approximately the same at both stations, although there
was more intermixed silt at station 2. Supported by
information of previous sections it can be said that the

change in macro-invertebrate community structure is due

83

largely to the great number of drains that enter the
river between the two stations.

Information values found in this study are in agree-
ment with other studies. A complete table is given by
Wilhm and Dorris (1968) where values range from approxi-
mately 3.5 in unpolluted zones to 1.3 near sources of
pollution.

In conclusion, the increase in pollution tolerant
organisms from station 1 to 2, the presence of certain
indicator organisms and the difference in diversity
from Okemos to station 2 all are evidence of a sig-
nificant change in the macro-invertebrate community.

The change within the river section investigated is
greater than "natural succession“ would allow and
therefore coupled with previous data it seems apparent

that the drain effluents have brought about the change.

Coliform Bacteria

 

The coliform bacteria analysis is a unit of
measurement used for determining the human safety of
water. Diseases of intestinal origin, such as typhoid,
dysentery, cholera and infectious hepatitis can be
transmitted by polluted water. Because specific patho-
genic organisms are very difficult to isolate, coliform -
organisms are used as indicators of the disease potential
of water. Of the three main groups of bacteria present

in the intestinal tract of man, coliform organisms are

84

the most closely related to intestinal pathogens. Exper-
ience has established the significance of coliform bac-
teria densities as criteria of the degree of pollution
and thus of the sanitary quality of water (APHA, AWWA,
WPCF, 1971). Coliforms are found in soil as well as in
the intestinal wastes of both man and animals, thus,
surface runoff can add coliform bacteria to streams
(Frobisher, 1957). Usually soil runoff accounts for
densities of less than 1000 organisms/100ml (MPN).

High numbers of coliforms indicate that raw sewage °
has entered the river. It should be realized that the
results reported as MPN are merely an index of the
number of coliform bacteria which, more probably than
any other number, would give the results shown by the
laboratory examination.

Jensen (1966) found that as the river flows through
the Michigan State University campus, MPN of coliforms
increases exponentially on logarithmic graph paper,
indicating several sources of domestic sewage enter the
river throughout the study section. Figure 10, which
includes Jensen's (1966) results, illustrates the same
situation was true during the summer of 1971. In fact
values for August 23, 1971, indicate an even worse sit-
uation. It should be reported, however, that this
analysis took place during a rain which caused several

drains to discharge raw sewage. As might be expected a

85

Figure 10. Most probable number (MPN) for coliform

bacteria per 100ml of river water at
sampling stations 1-5. [Broken lines are
values of 1964 from Jensen (1966).]

 

Most Probable Number x 1030f (.oiiform Bacteria Per IOO ml

201000.
10,000:

5,0004

86

 

 

8-23- 7I
"JO-6'4
I
I
I
I
I 8-2’-64
I
I
’ I
I
I I
I I
I
as I
I ‘ ~ I
I ‘ ‘ I
s ‘ I 6"‘7'
r -----
I
I
I
I A
\
II I \
I \
I, \ 9"5’61
/ \ I
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I \ ’
o- — - - — ..J I
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\ I
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Q\ / I
\ I I
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Contact / \ I
/ \ v
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Michi an's Standard for 'l'otal lad Contact
L4 j '2 V W
I 2 3 5

Sampling Stations

87

sudden summer storm causing a large input of sewage in
proportion to the dilution offered would result in
extremely high coliform densities. Considering Michigan
intrastate water quality standards (Figure 10), portions
of the Red Cedar River are unsafe for total or partial°

body contact; for example, canoeing and fishing.

SUMMARY

1. Analyses indicated effluents of approximately
one-third of the 90 drains located within the bounds of
the study area contained materials detrimental to the

water quality of the Red Cedar River.

2. Untreated domestic sewage, high concentrations
of chlorides, oily products, detergents and heavy silt

loads were discharged into the river by specific drains.

3. Drain 66, 25, 6 and 62 were found to have a
lethal effect on green sunfish either in bioassays or

by live car tests.

4. Data suggest that sudden summer rain storms
were the underlying cause of the major input of pollution

having detrimental effects on river fauna.

5. Low dissolved oxygen resulted in a major fish
kill in the lower portion of the study section during

the summer of 1971.

6. Although on occasion dissolved oxygen revels

became critically low, data indicate that there has been

88

89

some improvement in the average daily dissolved oxygen
near the Limnological Research Laboratory (station 2)

since 1964.

7. Results of this and Jensen's (1966) study
indicate neither phosphorus nor nitrogen is limiting,
but rather that productivity is limited by turbidity

and siltation.

8. An increase in pollution-tolerant organisms
from station 1 to 2, the presence of certain indicator
organisms, and a difference in diversity from Okemos
to station 2 all are evidence of a significant change

in the macro-invertebrate community.

9. Coliform bacteria increase exponentially as
one goes downstream from Hagadorn Road to East Kalamazoo

Street where levels are well above safe standards.

10. When one considers the chemical parameters as

well as coliform numbers and bottom fauna there seems

to be little improvement in the river since 1964.

11. The cumulative effect of several drain
effluents have caused a significant change in the water
quality of the river from Hagadorn Road to East Kalamazoo
Street. The effect is illustrated by an increase in
carbon, nitrogen, phosphorus, chlorides, coliform bac-
teria and pollution-tolerant bottom organisms as one

goes downstream.

LITERATURE CITED

LITERATURE CITED

American Chemical Society Report. 1969. Cleaning our
environment. The chemical basis for action. ACS.
Washington, D.C. 249pp.

Anderson, B. G. 1950. The apparent thresholds of toxicity
to Daphnia magna for chlorides of various metals
when added to Lake Erie water. Trans. Am. Fish.
Soc. 78: 96-113.

 

APHA, AWWA, WPCF. 1971. Standard methods for the exam-
ination of water and wastewater. 13th Ed. APHA,
N.Y., N.Y. 873pp.

Bamforth, S. S. 1962. Diurnal changes in shallow aquatic
habitates. Limnology and Oceanography. 7: 3.

Bartsch, A. F. 1967. Biological aspects of stream pol-
lution. Biology of water pollution. U.S. Dep.
of The Interior. pp. 13-20.

Beak, T. W. 1965. A biotic index of polluted streams
and its relationship to fisheries. Adv. Water
Poll. Res. 1: 191:210.

Brehmer, M. L. 1956. A biological and chemical survey
of the Red Cedar River in the vicinity of Williams-
ton, Michigan. M.S. thesis, Mich. State Univ.
Slpp.

. 1958. A study of nutrient accrual, uptake and
regeneration as related to primary production in a
warm-water stream. Ph.D. thesis, Mich. State Univ.
92pp.

, Ball, R. C., and N. R. Kevern. 1968. The
Biology and chemistry of a warm-water stream.
Mich. State Univ., Institute of Wat. Research.

'Tech. Rep. No. 3.

90

91

Brehmer, M. L. 1969. Nutrients and primary production
in a warm-water stream. Mich. State Univ., Insti—
tute of Wat. Research. Tech. Rep. No. 4.

Brown, V. M., Shurben, D. G., and Fawell, J. K. 1967.
The acute toxicity of phenol to rainbow trout in
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Poll. Abs. 41: no. 1935. (1968).

Chu, S. P. 1943. The influence of the mineral compo-
sition of the medium on the growth of planktonic
algae. II. The influence of the concentration of
inorganic nitrogen and phosphate phosphorus. Jour.
Ecology. 31: 109-148.

Cleary, J. E. 1967. The ORSANCO story. The John
Hopkins Press, Baltimore, Maryland. 335pp.

Clemens, H. P., and WOodrow H. Jones. 1954. Toxicity
of brine water from oil wells. Trans. Amer. Fish.
Soc. 84: 97-109.

Doudoroff, P., and Max Katz. 1953. Critical review of
literature on the toxicity of industrial wastes .
and their components to fish. Sewage and Indus-
trial Wastes. 25: 803-839.

Ellis, M. M. 1937. Detection and measurement of stream
pollution. Bull. U.S. Bur. Fish. 48: 363-431.

E.P.A. 1971. Methods for chemical analysis of water
and wastes. E.P.A. Water Quality Office, Cin-
cinnati, Ohio. 312pp.

Ford, D. L. 1968. Total organic carbon as a wastewater
parameter. Pub. WOrks. 99:89.

Frobisher, M. 1957. Fundamentals of microbiology.
W. B. Saunders Co. Philadelphia, Penn. 6l7pp.

FWPCA. 1968. Water quality criteria. U.S. Dep. of The
Interior. Washington, D.C. p.17.

. 1969. The practice of water pollution biology.
U.S. Dep. of The Interior. Washington, D.C. 281pp.

Grzenda, A. R. 1960. Primary production energetics and
nutrient utilization in a warm-water stream. Ph.D.
thesis, Mich. State Univ. 99pp.

92

Grzenda, A. R., Ball, R. C., and N. R. Kevern. 1968.
Primary production, energetics, and nutrient
utilization in a warm-water stream. Mich. State
Univ., Institute of Wat. Research. Tech. Rep.
No. 2.

Hach. 1969. Water and wastewater analysis procedures.
Hack Chemical Co. Ames, Iowa. 104pp.

Hardgrove, T. W. 1969. Continuous automated monitoring
of chemical and physical characteristics of the
Red Cedar River. M.S. thesis, Mich. State Univ.
124pp.

Herbert, D. W. M., Elkins, G. H. J., Mann, H. T., and
Hemens, J- 1957. Toxicity of synthetic detergents
to rainbow trout. Wat. Waste Treatm. J. Sept. 4pp.

Hokanson, K. E. F. 1968. The effects of synthetic deter-
gents on the early life history of the bluegill,
Lepomis machrochirus (Rafinesque), in the upper
Mississippi riVer. Thesis, Univ. of Minn. 244pp.:
Diss. Abs. 29:B, 1212. (1968).

Hynes, H. B. N. [1960. The biology of polluted waters.
Liverpool Univ. Press. Liverpool, England. 202pp.

. 1963. The biology of polluted waters. Liver-
pool Univ. Press. Liverpool, England. 202pp.

//,Jensen, A. L. 1966. Stream water quality as related to
urbanization of its watershed. M.S. thesis, Mich.
State Univ. 128pp.

Judd, J. H. 1970. Lake stratification caused by runoff
from street deicing. Water Res. 4: 8-20.

Kevern, N. R., and R. C. Ball. 1969. The nutrient
composition, dynamics, and ecological significance
of drift material in the Red Cedar River. Mich.
State Univ., Institute of Wat. Research. Tech. Rep.
No. 6.

King, D. L. 1962. Distribution and biomass studies of
the aquatic invertebrates of a warm-water stream.
M.‘. thesis, Mich. State Univ. 96pp.

Linton, K. J. 1967. The dynamics of five rock bass
pOpulations in a warm-water stream. Ph.D. thesis,
Mich. State Univ. 102pp.

93

Lloyd, R. 1961. The toxicity of mixtures of zinc and
c0pper sulphates to rainbow trout, Salmo gairdnerii .
(Richardson). Annals of Applied Biology 49:
535-538.

Margalef, R. 1956. Information theory in ecology.
Gen. System. 3: 36-71.

Meehan, W. R. 1958. The distribution and growth of fish
in the Red Cedar River drainage in relation to
habital and volume of flow. Ph.D. thesis, Mich.
State Univ. 126pp.

Mich. Water Resources Comm. 1968. Water quality stan-
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of Conservation. Mich. 39pp.

Mfiller, W. 1953. Nitrogen content and pollution of
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Odum, E. P. 1959. Fundamentals of ecology. W. B.
Saunders Co. Philadelphia, Penn. 546pp.

Ownbey, C. R., and G. E. Willeke. 1965. Long term solids
build-up in Lake Mich. Pub. Gt. Lakes Res. Div.
No. 13. 141-152; Wat. Poll. Abs. 40: no. 1223.
(1967).

Pennak, R. W. 1953. Fresh-water invertebrates of the
United States. The Ronald Press Co. N.Y. 769pp.

Perry, J. H. 1950. Chemical engineer's handbook.
McGraw—Hill Book Co. N.Y., Toronto, and London.
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Peters, J. C., Ball, R. C., and N. R. Kevern. 1968.
An evaluation of artificial substrates for measuring
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Peterson, H. B. 1968. Salt build-up from sewage effluent
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Pickering, Q. J., and T. O. Thatcher. 1970. The chronic
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Pimephales promelas, Rafinesque. J. Wat. Poll.
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94

Sawyer, C. N. 1965. Fertilization of lakes by agri-
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Swisher, R. D., O'Rourke, J. T., and H. D. Tomilinson.
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Van Hall, C. B., Safranko, J., and V. A. Stenger. 1963.
Rapid combustion method for the determination of
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35:315.

Vannote, R. L. 1961. Chemical and hydrological investi-
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Ward, H. B., and G. C. Whipple. 1959. Fresh water
biology. John Whiley and Sons, Inc. N.Y. 1,248pp.

Warren, C. E. 1971. Biology and water pollution control.
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95

Wilhm, J. L., and T. C. Dorris. 1966. Species diversity

of benthic macroinvertebrates in a stream receiv-
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Midl. Nat. 76: 427-449.

. 1968. Biological parameters for water quality
criteria. BioScience 18: 477-480.

APPENDICES

APPENDIX A

INFORMATION CONCERNING DRAINS

Drain gggrox-
Number Inches
1 72
2 24
3 12
72 18
96 10

APPENDIX A

Description of Drains

 

August 1971

Drains on South Side of River

 

*
Description

Opening is covered with wire gates.
--Flowed often at low levels and during
rains the effluent was muddy. On one
occasion the chloride concentration was
above 25,000 mg/liter.

Drain with a cement retaining wall
located 100 feet upstream from Bogue
Street.--Effluent generally clear with
low flow. At times the chloride con-
centration was above 5,000 mg/liter.

A concrete drain located 180 yards
downstream from Bogue Street.--Flowed
infrequently and is considered insig-
nificant.

A concrete drain which is usually one-
half submerged and hidden by bushes.--
Flowed infrequently and is considered
insignificant.

Concrete drain with a retaining wall
which is usually 1 foot above the river
level.--No discharge ever recorded even
during extended rains.

 

*

Comments also include information concerning the
effluents based upon general observations and chemical
analyses. Melting conditions gave the same results as

periods of rain.

times.

Each drain was visited at least 20

96

97

Drains on South Side of River-—Continued

 

Drain
Number

11

73

Approx.

Dia.

Inches

18

36

28

12

12

28

Description

This drain has a retaining wall and gen-
erally is one-half submerged.--Flow

was recorded only once during a heavy
rain.

Drain has a small retaining wall.--
Never observed flowing even during a
rain.

A concrete pipe located 75 feet upstream
from Farm Lane. Opening is usually
three-fourths below the water.--Con-
sidered a major drain.

A steel pipe located 20 feet upstream
from Farm Lane.--Drain flowed a small
amount of clear heated effluent. Because
temperatures were commonly above 50 C

the discharge may be the result of a leak
in a hot water line.

This drain has a cement retaining wall
surrounded by broken brick.--This drain
discharges a considerable amount of dark
dirty water during a storm. A froth and
oily film were observed at times.

Flowed during rains and on occasion dur-
ing dry periods, but effluent was gen-
erally clear with low nutrients and salts.

This drain is low on the bank with a
cement retaining wall.--Drain was never
observed flowing and seemed to be par-
tially filled with soil.

The drain is hidden back into the bank
of the river. The drain is partially
filled with gravel and cement blocks.--
Flow was low, clear and considered
insignificant.

98

Drains on South Side of River--Continued

Drain
Number

12

99

100

13

14

101

15

16

17

18

19

Approx.

Dia.

Inches

12

12

12

27

16

36

15

Description

Located across and downstream from the
U.S.G.S. survey station. This drain
has a small cement retaining wall and
is hidden by bushes.--Flowed only
during rains and was considered insig-
nificant.

A tile within a small cement retaining
wall and located 25 yards upstream from
first foot bridge.--Flowed only during
heavy rains and was considered insig-
nificant.

Located 20 feet upstream from first
foot bridge.--Never observed flowing.

Located 20 feet downstream from first
foot bridge.--Never observed flowing.

High on the bank 28 yards downstream
from the dam.--Never observed flowing.

Located 40 yards below dam and has a
cement retaining wall.--Never observed
flowing.

Concrete pipe with large retaining wall
located 20 feet upstream from second
foot bridge.--Considered a major drain.

This drain has a large cement retaining
wa11.--Flowed infrequently and was con-
sidered insignificant.

Located 10 feet downstream from above
drain.--Never observed flowing.

Drain with no retaining wall located
across from M.S.U. botanical gardens.--
Oily films, sewage gray color, and

high turbidity observed infrequently.

Concrete pipe located approximately 75
yards below drain 18. This drain seems
to be different than the one described
by Jensen (1966).--During a rain the
initial effluent was dark and turbid.

99

Drains on South Side of River--Continued

 

Drain
Number

20

79

21

22

23

106

24

25

26

Approx.

Dia.

Inches

6

12

18

24

24

16

12

72

12

Description

Located across from the M.S.U. women's
gym. Consists of a steel pipe low on the
bank.--Never observed flowing.

Tile drain located 20 yards below East
Kalamazoo Street on M.S.U. campus.--
Never observed flowing.

Located 60 yards downstream from third
foot bridge. Outfall slants toward
the river.--Flowed infrequently at a
slow rate and was clear.

Located 200 feet downstream from Jenison
Fieldhouse. This is a cement drain with
no retaining wa11.--Flowed often at a
slow rate and was generally clear.

Froth, oily films and muddy effluents
were observed at times, especially during
a rain.

Located one foot below above drain.--
Drain no longer flows and is filled in.

Cement pipe high on the bank 15 yards
upstream from Harrison Street.--
Flowed only during heavy rains and was
considered insignificant.

Located under Harrison Street Bridge.
This is a metal pipe high on the bank.--
Never observed flowing.

Located 60 yards downstream from Harrison
Street. Drain is oval and blocked by
wire gates. Considered a major drain.

Metal drain one foot from the drain des-
cribed by Jensen (1966) which is now
rusted and does not flow. This drain

is high on the bank and has caused con-
siderable bank errosion.--Appears to be
a storm drain which discharges turbid
water during rains.

100

Drains on South Side of River--Continued

Drain
Number

27

28

70

3O

31

32

33

9O

Approx.

Dia.

Inches

24

12

12

12

72

Description

Metal drain low on the bank across from
Brody parking lot.--Flowed infrequently
and at a slow rate but was a dark sewage
color and smelled as such. High carbon,
nitrogen and phosphorus concentrations
present when sampled.

Concrete pipe located out from the Lim-
nological Research Laboratory.--Flowed
only during heavy rains and was con-
sidered insignificant.

Drains on North Side of River

Steel pipe located high on the embank-
ment of Hagadorn Road.--Storm drain
which discharges runoff from Hagadorn
Road during a heavy rain.

Metal pipe below what appears to be a
water tank.--Flowed infrequently and
was considered insignificant.

Tile drain located 100 yards downstream
Hagadorn Road behind Cedar View Apart-
ments.-Flowed only during a rain and
was considered insignificant.

Located 30 feet downstream from above
drain. Pipe extends below water.
Appears to be a septic drain.--No evi-
dence of flow.

Located 75 yards upstream from River-
side East Apartments. This drain has

a large cement retaining wa11.--Appears
to be a combined storm and sanitary drain
which discharged sewage during a rain.
Analyses showed high phosphorus, nitrogen
and carbon to be present.

Black tile high on the bank behind
Riverside East Apartments.--Never
observed flowing.

101

Drains on North Side of River-~Continued

 

Drain
Number

35

36

91

91

92

38

38

39

4O

Approx.

Dia.

in

Inches

12

72

10

42

Description

Located below parking lot of Riverside
East Apartments. This drain is a cor-
rugated steel pipe protruding from the
bank but hidden by bushes.--Flowed
only during rain and was considered
insignificant.

Located adjacent to west side of River-
side East Apartments. This drain is
one-half submerged and has a large
cement retaining wall.--Considered a
major drain.

Tile drain high on the bank 70 yards
below drain 36.--Flowed only during
heavy rains.

Tile drain high on the bank next to a
wooden fence and 100 yards downstream
from drain 36.-Flowed only during rains
and was considered insignificant.

Steel pipe protruding from bank approxi-
mately five feet.--Flowed only during
rains and was considered insignificant.

Cement drain with no retaining wall low
on the bank behind broken blocks.--
Insignificant.

Steel pipe behind brick and red steel
apartments.--Insignificant.

Located near east end of Baton Rock
Apartments parking lot. Steel pipe
with wire cover located low on the
bank.--Flowed infrequently and was con-
sidered insignificant.

Located 200 yards upstream from Bogue
Street. Combined storm and sanitary
drain with a steel pressure cap.--
Discharged turbid water with high
nutrient loads during heavy storms.

102

Drains on North Side of River--Continued

 

Drain
Number

40

4O

94

95

41

42

71

44

45

46

B

Approx.

Dia.

Inches

72

12

16

16

12

30

10

12

Description

Located within the same retaining wall
as drain 40A. Drain has a large steel
pressure cap which only opened a few
inches during heavy rains.

Steel drain next to 4GB.--Never observed
flowing.

Cement drain located low on the bank
100 yards upstream from Bogue Street.--
Flowed only during rains and seems to
come from a parking ramp.

Cement drain located 75 yards upstream
from Bogue Street.--Same as above drain.

Located 50 feet downstream from Bogue
Street.--Flowed infrequently at a slow
rate.

Concrete pipe behind the M.S.U. Alumni
Chapel. This drain appears as a large
cement retaining wall because Opening
is not visible.--Flowed infrequently
at a slow rate.

Drain is low on the bank with a small
metal retaining wall.--Insignificant.

Located behind Kresge about 10 yards
downstream from drain 71. No retaining
wall and is low on the bank.--Insignifi-
cant.

Drain appears as a large cement retain-
ing wall behind Kresge. Could not find
an opening.--Insignificant because
filled in.

Located 150 yards upstream from Farm
Lane. Drain has a large retaining
wall and is one-half submerged.--
Slight discharge during a rain.

 

ill’llIlL

Drains on North

103

Side of River--Continued

 

Drain
Number

47

48

49

97

98

74

Approx.
Dia. in
Inches

36

24

15

12

26

Description

Located 40 feet upstream from Farm Lane.
Drain is beneath the water and a side-
walk goes up to the retaining wall.--
Seems to be a combined storm and sani-
tary drain which discharges a large
amount of dark oily effluent during a
rain storm. Effluent is nutrient rich.

Located 10 yards downstream from Farm
Lane. Drain is three-fourths below
water and has no retaining wall.--At
times water flows into this drain, but
during rains it discharged some sewage
into the river. When sampled the
effluent was nutrient rich. On one
occasion, 12/4/70, drain 48 flowed raw
sewage for several hours while the city
sanitation department was repairing the
sewerage system.

Concrete pipe with a retaining wall
located a few yards upstream from the
M.S.U. canoe shelter.--Flowed infre-
quently and was usually clear. A
greenish effluent was observed on
occasion during dry periods.

Located behind parking Ramp #2 (M.S.U.).
Appears to be a newly constructed drain
with a retaining wall. Drain is commonly
one-half submerged.--Slight discharge
during rains.

Tile with broken walk surrounding it.
Located just upstream from the U.S.G.S.
survey station.--Insignificant.

Located several yards downstream from
the U.S.G.S. survey station. Drain
has a newly constructed cement retain-
ing wall.--Infrequently discharges a
dark gray effluent at a slow rate.

104

Drains on North Side of River-Continued

Drain
Number

52

53

54

57

58

59

Approx.
Dia. in
Inches

10

12

20

12

60

24

Description

Concrete drain with retaining wall
located behind the Computer Center. The
end section of this drain is broken off.
Flowed infrequently and considered insig-
nificant. '

Located 10 yards upstream from the
first foot bridge. Cement retaining
wall and screen cover. This drain's
description is somewhat different than
that given by Jensen (1966). The drain
was likely reconstructed, since the new
M.S.U. Administration building was
built. Several other former drains

are missing in this area.--Infrequently
discharged a dark turbid effluent at a
slow rate after a rain storm.

Located immediately above dam. Drain
is built into the side walls of the dam.
Drain may be different than in 1964.--
Flowed infrequently. On one occasion
the effluent was rusty, turbid, had a
foul odor and a carbon concentration of
1,400 mg/liter.

Located 20 yards downstream from the
second foot bridge. Drain has a small
retaining wall and generally is three-
fourths submerged.--Insignificant.

A rectangular concrete conduit below

the water. Drain 58 seems to be a
combined storm and sanitary drain of the
East Lansing sewerage system.--Dis-
charged a large volume of sewage gray
effluent into the river during rain
storms. The effluents were nutrient
rich and often smelled septic and

formed oily films.

Located behind M.S.U. WOmen's Gym. This
drain has a large cement retaining wall
surrounded by broken concrete.--Infre-
quently flowed raw sewage and also dis-
charged an effluent with a gray-white
precipitate on occasion.

105

Drains on North Side of River--Continued

 

Drain
Number

60

78

80

103

104

81

82

Approx.
Dia. in
Inches

30

12

36

10

12

4O

24

Description

Located 10 feet upstream from East Kala-
mazoo Street on M.S.U. campus. This
drain is low on the bank and has a
retaining wa11.--Eff1uent was generally
clear with a oily film present.

Located 20 yards below East Kalamazoo
Street on M.S.U. campus. Tile drain
with no retaining wa11.--Insignificant.

Cement drain with the two end segments
broken off. Bank has erroded and a
sludge bed has formed out from the
drain.--Effluent is very dark and turbid
during a rain. On occasion it dis-
charges water with high chloride and
nutrient concentrations.

Steel pipe extending below the water.
Located 10 feet below drain 80.-

Prior to repair in November 1970 this
drain discharged raw sewage into the
river. The effluent had a high nutrient
content due to the feces, paper and

food particles present. Evidently the
city took action after I reported the
situation.

This drain has a cement retaining wall
that is broken off and tilted.--Dis-
charged dark turbid water during storms.

Cement drain with retaining wall located
20 feet below drain 104.--Slight flow
during rains.

Corrugate metal drain located at the
corner of Harrison Street and Michigan
Ave. This drain is part of the East
Lansing combined storm and sanitary
sewerage system.--Considered a major
drain.

106

Drains on North Side of River--Continued

 

Drain Approx. . .
Dia. in Description
Number
Inches

105 36 Located 20 yards below 82 and is covered
with a cement box-like retaining wall.
Also hidden by bushes.--This drain dis-
charged a dark sewage rich effluent
during heavy rain storms. Flow seemed
to subside immediately after a rain.

61 72 Located 10 yards below above drain.
Drain has a large cement retaining wall
and a pressure cap.--Considered a major
drain.

63 20 Located below Kellogg Center parking lot.
Drain has a cement retaining wall.--
Discharged dark turbid water during a
rainstorm.

64 24 Located adjacent to Harrison Street
bridge and has no retaining wall.--
During the winter of 1970-71 this drain
discharged sewage into the river which
formed a sludge bed. During this time
the effluent had very high nutrient and
chloride levels. It appeared that this
drain was corrected at the end of April
1971, after which it no longer dis-
charged sewage.

65 15 Located across from drain 25 and has a
cement retaining wall.-—Flowed infre-
quently and was considered insignifi-
cant.

66 36 Located across from the Limnological
Research Laboratory. This drain has a
cement retaining wall.--Considered a
major drain.

67 12 Located 10 feet downstream from above
drain and has a cement retaining wall.
This drain discharges water for short
periods of time during dry conditions
as well as flowing during rains.--The
effluent was generally clear but pro-
duced an oily film on the river. Nitro-
gen, carbon, chloride and phosphorus
concentrations were considerably higher
than the river on occasion.

107

Drains on North Side of River--Continued

. Approx.
grafgr Dia. in Description
Inches
107 27 Located 80 yards downstream from drain
67. Cement retaining wall present.--
Dark turbid effluent immediately after
a storm began but soon became clear
with dilution.
108 36 Corrugated steel pipe embedded in

loosely poured cement next to M.S.U.
property line fence.--Flowed during
rains and was considered insignificant.

108

Table 7. Formulas for estimating average discharge and
dilution ratio.

 

AS = D2 ' a from the quotient (h/D)

where:
AS = area of segment in square inches.
D = diameter of drain in inches.
a = area corresponding to the quotient (h/D) in
Table 9b of Chemical Engineer's Handbook
(Perry, 1950).
h = average height of segment in inches (depth of

effluent in the drain, measured while sampling).

X = AS K1 K2

where:
X = discharge in cubic feet per second (cfs).
Kl = conversion of inches to feet (144 inZ/ftz).

K = estimated rate of flow (2 ft/sec).

The average dilution ratio of the drain to river can then

be calculated by reducing the fraction X/C.
where:

C = average discharge of the river on sampling

dates (124 cfs).

 

APPENDIX B

INFORMATION CONCERNING TOXICITY TEST

109

Table 8. Characteristics of laboratory dilution water.

 

 

Parameter* 8/19/71 9/13/71
pH 7.82 7.86
Total Alkalinity 320 346
Hardness 322 336
Chlorides 2.50 2.50
D.O. 8.10 8.20

 

*
Values are in mg/liter, except pH.

 

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116

Table 11. Live car test on drain 25 effluent.

 

Cumulative percent mortality of test animals*

 

 

Date Major Control Car 1 Car 2 Car 3
0% 0% 50-100% O-50%
Effluent Effluent Effluent Effluent

7/16/71 0 0 O 0
7/18/71 0 0 0 0
7/19/71 0 0 0 0
7/20/71 0 O 40 0
7/21/71 0 0 4O 0
7/22/71** 0 0 4o 0
7/23/71 0 0 50 10
7/24/71 0 0 60 10
7/25/71 0 O 60 10
7/26/71 0 10 60 10

 

*

Test began 7/14/71 with ten green sunfish accli-
mated to the temperature of the river and/or effluent
(25 C). Average weight = 4.2 gm.

*9:
Two conductivity peaks occurred at station 2 as

recorded by the monitor. Also a bioassay was conducted
of which the 96 hr TL50 was greater than 80 percent
effluent.

117

Table 12. Live car test on drain 6 effluent.

 

Cumulative percent mortality of test animals*

 

Date

 

Major Control Car 1 Car 2 Car 3
0% 0% 50-100% 0-50%
Effluent Effluent Effluent Effluent
Test A
8/4/71 0 0 0 0
8/5/71 0 0 0 0
8/6/71 0 0 0 0
8/8/71 0 0 0 0
8/9/71 0 0 0 0
8/10/71 0 0 0 0
8/11/71** 0 o 30 0
8/12/71 0 0 90 70
8/13/71 0 0 90 70
Test B
8/14/71 0 0 10 0
8/15/71 0 0 10 0
8/16/71 0 0 10 0
8/17/71 0 O 10 0
8/18/71 0 0 10 0
8/20/71 0 0 30 0
8/21/71 0 0 40 0

 

*

Test A began 8/3/71 and test B began 8/13/71 with
10 green sunfish acclimated to the temperature of the
river and/or effluent (22 C). Average weight-~test A =
4.2 gm, test B = 5 gm.

**
A major fish kill occurred downstream--D.O. was low.

APPENDIX C

INFORMATION CONCERNING BOTTOM FAUNA

118

Table 13. Summary of "pool" bottom fauna expressed as
number per square foot. Sample date July 28,

 

 

 

 

1971.
Station North l/4 Midstream South 1/4 Mean
Oligochaeta
1 12 8 48 23
2 76 60 39 58
3 124 96 92 104
4 60 60 12 44
5 552 458 185 398
Chironomidae
l 20 28 40 29
2 20 20 21 20
3 32 88 72 64
4 68 12 98 59
5 282 40 32 118
Elmidae
l 8 j 4 12 8
2 4 10 3 6
3 - 4 - 1
4 - 4 4 3

 

119
40«

u
'9

N
b
1_

'61

Number of Species

a
L

 

 

1
1
a

Sample Number

Figure 13. Test of sampling adequacy upstream.

 

.3 24‘
U 4
G)
O.
U) Ib-
‘+.
O
3
.o 8‘
E .
a
Z

 

Sample Number

Figure 14. Test of sampling adequacy downstream.

APPENDIX D

GENERAL INFORMATION

 

lll’l'l‘lt[(ll“(ll‘ —

Figure 15.

120

Photograph of drain 66 discharging
sewage.

Photograph of drain 82 discharging
sewage.

Major fish kill of August 11, 1971
[shopping cart with dead fish].

Photograph of effluent from drain 25.

 

 

BAA—M 4‘...— fi—‘AAWA‘A‘

121

 

Figure 16.

122

Map of the Red Cedar River.

,__—
._ A_-—-—_ -—'"

E

 

124

Figure 17. Map showing sewerage system of Michigan
State University.* [As of Sept. 1971.]

*

Survey of drains entering the Red Cedar River
within the boundaries of Michigan State University.
Engineering Services Dept., Mich. State Univ., 1965.

 

 

 

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