EXTENT OF CONTAMINATION OF A
COLD-WATER STREAM BY PRIVATE
DOMESTIC WASTE- DISPOSAL SYSTEMS

Thesis for the Degree of M. S.
MICHIGAN STATE UNIVERSITY
DORANCE C. BREGE
1969

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ABSTRACT

EXTENT OF CONTAMINATION OF A COLD-WATER STREAM BY
PRIVATE DOMESTIC WASTE-DISPOSAL SYSTEMS

BY

Dorance C. Brege

This study was an attempt to evaluate the extent of con-
tamination of a cold-water stream by private septic systems.
Fluorescein dye was flushed into nearly all of the 220 septic
systems along a 20 mile stretch of the AuSable River. Visual
inspection of the immediate shore line followed for a 4-5 day
period. Water samples also were taken, stored, and later
examined for fluorescence, and nitrate and chloride concen-
trations.

General surveys of invertebrate bottom fauna, oxygen
fluctuations, vegetation, total phosphorus levels, and stream
velocity were performed to analyze the general health of the
river.

The results of this study indicate few instances of
contamination from private septic systems. In only four cases
was the dye actually observed and in only several instances
does chemical or fluorescence analysis indicate contamination.

Although the chemical load of the stream appears small,

Dorance C. Brege

diurnal oxygen fluctuations, high water temperatures, bottom
fauna, and heavy aquatic vegetation growths indicate deteri-
orating stream conditions.

A discussion of the extent of contamination from private
septic systems and factors affecting the travel of materials
from septic systems to streams is presented. Suggestions on
installation of septic systems to obtain minimal contamina-
tion and suggestions to better evaluate the extent of contam-

ination are given.

EXTENT OF CONTAMINATION OF A COLD-WATER STREAM BY

PRIVATE DOMESTIC WASTE-DISPOSAL SYSTEMS

BY

Dorance C. Brege

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

1969

453353
/&/22 6‘?

ACKNOWLEDGEMENTS

My appreciation is given to my graduate committee,
chairman, Dr. Niles Kevern, and members, Dr. Clarence
McNabb and Dr. Marvin Stephenson.

Thanks is also given to Bernard Fowler and Kenneth
Carlisle for transportation along the river during the
study.

I also thank all of my fellow graduates whose sug-
gestions and assistance improved my study.

This study was financed by an assistantship from
Grayling township and from FWPCA training Grant number

5T1-WP-109.

 

ii

TABLE OF CONTENTS

INTRODUCTION . . C O O O O O O O O O O O O O O O O 0
DESCRIPTION OF STUDY AREA. . . . . . . . . . . . . .

Section I . .
Section II. .
Section III .
Section IV. .

MTHODS O O O O O O O O O O O O O O O O O O O O O O 0

Sampling Methodology. . . . . . . . . . . . .
water Chemistry . . . . . . .
Nitrates . . . . . . . . . . . . .
Chlorides. . .
Fluorescence .

Phosphorus . . . .

Other Parameters. . . .
Oxygen and Temperature . . . . .
Invertebrates. . . . . . . . . . .
Aquatic Plants . . . . . . . . .
Current Velocity . . . . . . . . . . . . .

“SULTS O O O O O O O O O O O O O O O O O O O O O O 0

Results from General River Survey .
Current Velocity . . . . . . .
Vegetation . . . . . . . . . .
Invertebrates. . . . . . . . . . .
Oxygen and Temperature Fluctuations.
Phosphorus . . . . . . . . . . . . .
Results from Individual Septic Systems . .

DISCUSSION 0 O O O O O O O O O O O O O O O O O O O O

Detectability . . . . . . . . . . . . . . . . .
Factors Influencing the Degree of Contamination

iii

Page

TABLE OF CONTENTS--Continued

Suggestions on Improvements of the Stream.
Suggestions for Further Studies. . . . . .

C ONC LUS I CNS 0 O O O O O O O O O O O O O O O O 0

LITERATURE CITED 0 O O O O O O O O O O O O O O O .

APPENDIX 0 o o o o o o o o o o o o o o o o o o 0

iv

Page

70
72

75
75
77

TABLE

1.

LIST OF TABLES

Current velocity measured by Price-Gurley cur-
rent meter at one-half midstream depth on
September 10, 1968. . . . . . . . . . . . . . .

Dry weight of vegetation in grams per square
foot from the AuSable River during the fall of
1968. O O O O O O O O O O O O O O O O O O O O 0

Mean percentage of stream bottom area covered
by vegetation for the main stream of the
AuSable River during the summer of 1968 . . . .

Number of invertebrates per square foot of non-
vegetated bottom area for single samples taken
by Surber sampler on.September 27 and 28, 1968
in the AuSable River. . . . . . . . . . . . . .

Number of invertebrates per square foot of vege-
tated bottom area for single samples taken by
Surber sampler on September 27 and 28, 1968 in
the AuSable River . . . . . . . . . . . . . . .

Total phosphorus concentrations for two series
from the Main Stream, two East Branch samples,
and several selected samples from dwellings . .

Page

51

55

55

59

41

52

LIST OF FIGURES

FIGURE

1.

2.

3.1-
5.4.

AuSable River Basin. From Michigan Water
Resource Commission (1966). . . . . . . . . . .

Study area on the main stream of the AuSable
River, sections as described in the introduc-

tion. 0 C O O O O O O O O O O I .0 O O O C O O 0

Sections I, II, upstream part of 111. down-
stream part of III, and IV, respectively. . . .

Variation in number of families of inverte-
brates represented in bottom samples from vege-
tated and nonvegetated locations, darkened
portions of bars represent families generally
considered to be intolerant . . . . . . . . . .

Diurnal oxygen and temperature fluctuations for
locations and dates as listed . .'. . . . . . .

Distribution of adjusted relative fluorescence
values for control samples and samples from
dwellings . . . . . . . . . . . . . . . . . . .

Distribution of adjusted chloride values (in
milligrams per liter) for control samples and
samples from dwellings. . . . . . . . . . .«. .

Distribution of adjusted nitrate nitrogen
values (in micrograms per liter) for control
samples and samples from dwellings. . . . . . .

Variation in total phosphorus, chloride,

nitrate nitrogen, and fluorescence with loca-
tion as shown by selected control samples . . .

vi

.10

44

48

55

57

59

62

INTRODUCTION

Although reference has been made in surveys by
Hendrickson (1966) and the Michigan Water Resources Commis-
sion (1966) on the AuSable River of the deleterious effects
of effluentfrom the city of Grayling, Michigan, only specu-
lation has occurred as to the magnitude of the effect of
private septic systems. Thus the main objective of this
study was to ascertain the possible input of materials from
private domestic waste-disposal systems into the AuSable.

Due to the fact that the significance of these incoming
materials is their effect in speeding eutrophication of the
river; it is valuable to consider several parameters re-
flecting the river's general condition, due to a combination
of 1) natural causes, 2) effluent from the city of Grayling.
and 5) possible seepage from private septic systems. Factors
considered were benthic invertebrates, diurnal fluctuations
in oxygen concentration, vegetation, stream velocity, and
total phosphorus levels of the stream.

The complexity of quantitatively determining the amount
of contaminants entering the river is due to the large number
of variables involved. Some of these are the probable low

concentrations at which materials are moving, the various

chemical forms involved, variations of quantity due to time
and amount of use of individual septic systems, and distances
involved between septic systems and the river, vertical dis-
tance between tile fields and the water table, and types of
soil through which the materials must flow.

Due to this anticipated difficulty in detecting contami-
nating materials, it was decided that samples for chemical
tests should be taken so as to have optimum probability
regarding time and location for detecting contamination.

Rather than attempt to analyze for all possible forms of
contaminants, indicators, materials that should be easy to
detect and that are indicative of sewage wastes were selected.
Those chosen were nitrate nitrogen and chlorides. Fluorescein
dye also was flushed into nearly all the systems within the
study area. This highly fluorescent dye was believed to be
an obvious indicator of faulty systems. Its presence could
be easily detected by fluorometer or by sight if present in

sufficient concentration.

DESCRIPTION OF STUDY AREA

The AuSable River arises several miles north of the
town of Frederic, Michigan, Section 25, T. 28 N., R. 4 W.,
about 15 miles upstream from the beginning of the study
area, and flows through a relatively homogenous terrain
throughout the study area. The river basin is shown in
Figure 1.

Soils throughout most of the region are very sandy and
can be described as Podzol, rubicon soil. This is a well-
drained soil, with little runoff during rainstorms or spring
melts. The result is a steady stream flow, the main com-
ponent of which is groundwater responsible for the cold-water
characteristics of the river.

Almost the entire land area within the drainage basin
is forested with second growth from the lumbering of the
virgin white pine forest. The watershed is almost entirely
free of agriculture and industry. Except for certain areas,
dwelling density is not high. In most areas dwellings are
not evident, being rather sparsely located in comparison to
cottage density on local lakes.

The study area extended from Pollack Bridge above
Grayling to Townline Road” about 21 miles downstream. For

convenience of discussion the area will be broken into

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several distinct sections based on differences in bottom type,
velocity, depth, vegetation types and density, and other
characteristics. The limits of each section of the study

are given in Figure 2. These study sections are expanded in
Figures 5.1-3.4.

Section I--Section I is the area extending from Pollack
Bridge 8.7 kilometers downstream to the State Street Bridge
within the city of Grayling.

The stream in Section I is composed of intermittent
stream and impoundment areas. The unrestricted stream is
relatively shallow and predominantly sandy with virtually
no gravel areas. Although current velocity is rather slow,
water is cool and well oxygenated. Invertebrate life is
diverse but rather sparse.

Impoundments are an important aspect of Section I, making
up over one-half of the length of the area. The upstream
reservoir, impounded by an old power dam, is over a mile in
length. The bottom is silt filled and shallow, being less
kthan three feet over most of the area, but becoming about 10
feet deep at the dam. BelOW'M-72, the AuSable enters a swampy
impoundment of about one-half mile in length extending into
«£2? cityhof Grayling. The river in this area is greatly
divided, losing nearly all sense of directional flow.. Large

-.qgrowths of waterlilies and emergent tree stumps are the domi-
nant features of the shallow muddy flooding. Toward the
eastern city limits, the width becomes restricted and depth

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Vegetation in the flowing stream is sparse and composed
mainly of several species of potamogetons. Large beds of
potamogetons are present in the impoundments. During most
of the summer, a layer of green algae covered the silty
bottom of the impoundments. Water was generally greenish in
color with a slight fishy smell.

Although the river above M-72 and the old power dam is
cool and well oxygenated, it generally would not be con-
sidered as good trout habitat. Only small pOpulations of
brook, brown, and rainbow trout survive, as do sculpins and
darters. The majority of fish present are cyprinids. Fish
p0pulations within the impoundments are characterized by
suckers, northern pike, and a few trout. Populations of
trout apparently exist throughout Section I during the spring
as witnessed by local fishermen.

Upstream of Business Route 1-75 Bridge, several storm
drainage pipes empty into the river, frequently discharging
colored water. There are a large number of homes surrounding i
the old power dam and extending downstream to the M-72
Bridge.

Section II--Section II begins in Grayling and extends
downstream 9 kilometers to Burton's Landing (Figure 2).
Natural land elevation throughout most of the region is low
as evidenced by Shellenbacker swamp, extending ovef“a large
area of Section II. The river seems to flow along the
northern edge of this swamp. Generally the northern bank is

high and very sandy, while the southern side is lower and wet.

16

Vegetation along the northern bank, where it is high, is
mainly oak and pine while the southern bank is generally
covered with tag-alders or white cedar.

The stream bottom is sandy with little gravel except
for the stretch between Grayling and the 1-75 Bridge.
Significant features of the bottom are logs and tree branches;
as well as rubbish, such as beVerage containers, left from
passing canoes.

Current velocity in this section is relatively slow,
except for the area immediately below Grayling. Natural
slope is low and some dredging has deepened the mainstream
such that current velocity is quite slow in a few places.

Vegetation is represented by about equal quantities
of higher aquatic plants and green algae but is not dense
in comparison with downstream areas. The green algae is main-
ly Cladophora sp- forming long, trailing, wavingmasses which
cling to objects.jutting out from the stream bottom.

The invertebrate lifevpresent is not typical of a cold-
water stream. Most forms are associated with the silty side
areas of the stream or on submerged logs and aquatic vege-
tation, rather than in the shifting sandy bottom.

A sizeable papulation of brown trout appear to survive
year around in the upper one-third of this section immedi-
ately below Grayling. In the remaining two-thirds, few trout
were observed during_summer months. More.characteristic spe-

cies in this area were cyprinids, yellow perch, and suckers.

17

A strong influence within this section is the effluent
from the waste water treatment plant located on the down-
stream edge of Grayling. The plant discharges 0.5 million
gallons per day of primary effluent which comprises roughly
five percent of the average streamflow at Grayling (Michigan
water Resource Commission, 1966). A few hundred yards down-
stream from Grayling the main stream of the AuSable is joined
by the East Branch. The volume of water from the East Branch
is approximately one-half of that from the main stream and is
much cooler and higher in dissolved oxygen during the summer.

There are a significant number of dwellings, mainly
along the northern bank, extending from Grayling downstream
to about one-half mile below the I-75 Bridge. Due to the low
land elevation of the swampy area, many of the cottages and
homes in the area are constructed within several feet of the
water table. Dwellings are also located upon land filled
areas. The proximity of several homes to the water table
makes their septic systems potentially the most likely to
contribute materials to the river.

Section III--Section III is differentiated distinctly
from the end of Section II by-a rather abrupt change in rate
of flow, bottom type, and vegetation. The area extends from
above Burton's Landing to beyond the end of Shaw Road.
Current velocity approximately doubles that found throughout
most of Section II. Bottom type, where not covered with vege-

tation, is almost entirely gravel or rubble with little exposed

18

sand or clay present. Where vegetation has covered the bottom,
deposited sand or silt generally covers the rubble and gravel.

The predominant vegetation form present is Potamogeton
filiformis, but beds of g, crispus and Anacharis Sp. are also
significant. Algae is not noticeable in the main flow but
clumps on the surface are present in quiet areas. Thick beds
of g, filiformis cover extensive sections of the streambed,
while other areas remain either completely free of vegetation
or contain only confined beds of vegetation surrounded by areas
of rubble and gravel. Anacharis sp. is generally confined to
the stream edge, growing in silt deposits in slow water.

Invertebrate p0pulations in this section are more typical
of trout streams, containing a more varied selection of clean-
water organisms than are present in Section II.

This and the succeeding study section can be described
as good trout habitat. Overhanging cedars and other fallen
trees and shrubs, with their water—penetrating sweepers, pro-
vide habitat and cover for most of the larger trout, particu-
larly during the summer. In both of the last two sections.
high sandy banks provide numerous springs, small creeks, and
flowing wells that contribute a significant volume to the
river. The cooling effects of this water undoubtedly plays
a major role in providing the conditions for which the river
is so well-known.

Dwellings on this third section of the river are mainly

cottages. In several subdivided areas, cottages are closely

19

spaced but, normally, they are rather isolated. There are
major stretches containing no cottages at all or only a few
that are well-concealed.

Section IV--The last study section is similar to Section

 

III but differs significantly in surrounding soil types,
depth, and vegetation.

Stream depth is generally deeper in this last section than
the preceding one. Riffle areas are seldom less than two feet
in depth and pools up to six or seven feet deep are common.

The vegetation coverage decreases and at the end of the
study area becomes scarce in the main flow of current com-
pared to upstream areas. In some wide slow areas thick mats
of algae formed over the surface of Anacharis beds growing in
shallow edge water.

Fish populations in this section are similar to the
preceding section, with a high pr0portion of trout and some
suckers, but the deeper pools contain Whitefish which are
present only on the very end of Section III.

A higher prOportion of clay grades into the sandy soil
from Section III and the soil becomes quite heavy toward the
end of Section IV. This probably affects drainage conditions-
in the area; particularly toward the downstream end of the
section; affecting both the Operation of septic tile systems
and the amount of overland flow during the rainy seasons
and spring snow melts. This clay is also evident in the

stream bottom with slippery patches of bare clay being common.

METHODS

SamplinggMethodology

Over two-hundred dwellings within the study area re-
sulted in a large number of samplings. This quantity put a
restriction on the number of samples per individual system
that could be taken. Thus in most cases only two eight-ounce
water samples were collected.

To optimize the probability of detecting contaminants
or injected fluorescein dye, samples were taken at a time
when they would be most likely to contain dye or contaminants.
The movement of nutrients to the stream is largely dependent
upon the following factors: horizontal distance between tile
field and the river, vertical distance between tile fields
and water table, percolation and adsorption prOperties of
soil types, and uptake of nutrients by plant roots. The
amount of use of the system, presence of impermeable soil
layers, presence of springs in the tile fields, and seasonal
differences due to bacterial activity may also affect nutrient
movement.

Although the above factors make obvious a large number
of unknown variables, the following considerations were taken
into account in determining time of sampling. The construc-

tion of a septic system is such that its Operation is basically

20

21

a diSplacement activity. Input of a unit volume causes over—
flow through the effluent conduit of an equal volume of
effluent to the tile system. Depending on the volume of
influent waste water put in at any one time, a variable but
definite time period in the tank is required before discharge.
This condition is necessary if the septic tank is to fulfill
its major objective of solid settling and anaerobic fermenta—
tion. If the septic system is in continuous use, the through-
put rate is high and material flushed into the tank will
reach the tile fields shortly. However, if the septic system
is little used, the throughput rate is low and several days
may be required for material to enter and leave the tank.
In an unused septic system, construction is such that material
within the tank can not leave.

Time is required also for potential contaminants to
travel the distance between the tile field and the river.
The major route of travel here is believed to be filtration
down from the tiles to the water'table and then slow movement
in the water table to the river. Another alternative is
possible if a spring intercepts the tile field and carries
the material to the surface and then rapidly to the river.

Also to be considered is that the longer materials must
travel to reach the river, the more opportunity for absorp-
tion and dilution and the less chance of materials reaching
the river, consequently the less chance for detection.

The final factor considered in the decision of sample

timing is that the material moving through the septic tank

22

does not act as a unit. Influent entering at one particular
time is gradually displaced. Thus, fluorescein placed in
the septic tank would not make a quick "one shot" flow
through the system but would be displaced gradually.

In view of the above considerations, it was decided that
the most appropriate time to sample would be at the latest
possible date during which persons occupied the dwelling.

The reasoning here was to provide the maximum amount of time
for an equilibrium to be set up between the contents of the
septic tank and the tile system and again between the tile
field and possible entrance of a more or less steady front

of material to the river. .In many cases during the summer
vacation period, cottages were occupied continually for
several weeks. Fluorescein dye was put into the system
sometime in the middle 0f the period and samples for analysis
taken 4-5 days later. Sampling timing was the same in cases
where dye was flushed into the system on a weekend or short
periods of stay. However, in the cases where dye was in-
jected into the system while no one was occupying the dwelling,
sampling was delayed until some one did occupy it or until the
end of the study period to sample.

The above problems of timing were not important to homes
having permanent residents. It is believed that if contami-
nants are reaching the river from septic systems having a
rather steady input, there would be an equally constant flow

to the river, an equilibrium having been established.

25

Letters requesting permission to put fluorescein dye
into individual systems were sent to all owners of dwellings
within the study area as listed in the pr0perty records of
Grayling Township. However, due to incomplete records,
changes in addresses, and misunderstandings about the study,
permission to enter buildings was difficult to obtain. Even
after obtaining entrance permission, gaining entrance to the
building was a very irregular, time consuming process,
occurring only after finding the owner at the site of the
dwelling or contacting the person in charge of the dwelling.

After gaining entrance into the building, injection of
the fluorescein dye was a rather simple matter. Two tea-
spoons, about 15 grams, of the dye was placed into all toilets
emptying into known septic tanks. The toilet was then flushed
several times to insure that the dye reached the septic tank.

Visual inspection of the shoreline near the dwelling
for the dye was made at least once a day for a period varying
between 4 and 6 days following the date of dye input. water
samples were then taken for chemical analyses. Visual in-
Spection continued after sampling when the Opportunity
occurred. This amounted to about three times a week through-
out the summer.

Parameters were chosen for water chemistry analysis to
be indicative of either raw sewage or varying degrees of-
purified sewage effluent as it travels through the soil to

the stream. Also affecting the choice was the feasibility of

24

examining the large number of samples. McGauhey (1968) gives
the typical composition of medium strength raw domestic
sewage to contain 100 mg. per liter chlorides but only 0.20
mg. per liter of nitrate nitrogen. Robeck, Cohen, Sayers,
and WOodward (1965) measured qualities of sewage effluent
after filtering through a lysimeter filled with 4 feet of
sand and found the effluent to contain an average of 25 mg.
per liter nitrate nitrogen and 70 mg. per liter chlorides
during 219 days of operation. Thus chloride and nitrate
nitrogen were chosen as indicators.

Fluorescein was the dye chosen to be used in the study
largely because of the ease in obtaining it Upon the short
notice at which the study began. Other fluorescent dyes,
notably rhodamine B, rhodamine WT, and pontacyl brilliant
pink, were alternative choices for this study. These other
dyes may have been more favorable to use from the standpoint
of the high photochemical decay rate of fluorescein. However,
this should not have seriously interfered with detectability
because the dye and sampling areas were not extensively
exposed to sunlight. Fluorescein dye has been used success-
fully to trace movement of ground water for distances up to
2500 feet using several pounds of the dye and up to 5000
yards using about 15 pounds of the dye (Thresh, Bealej‘and
Suckling, 1949). Fluorescein is not significantly adsorbed

by organic or mineral matter.

25

water Chemistry

Nitrates

Nitrate determinations were made by the Brucine method
as modified by Jenkins and Medsker (1964). They state that
this modification is much more sensitive than the method
listed in the 12th edition of Standard Methods for the Exami-
ggtionfigj water_§nggfla§tewater, and gives highly reproducible
results in the range of 0.05 to 0.8 mg per liter nitrate
nitrogen. A Bausch and Lomb Spectronic 20 was used in the
procedures of this method to obtain transmittancy readings.

It should be noted that although Jenkins and Medsker
(1964) give limits for their nitrate nitrogen method to
extend from 0.05 to 0.8 mg per liter, I have extended the
method down to 0.02 mg per liter nitrate concentration.
I believe that a reasonable estimate could be made to this
lower level based on recovery of added nitrate nitrogen to
waters from the study area having a concentration of less

than 0.05 mg per liter nitrate nitrogen.

Chlorides

Chloride determinations were made by the Mohr method.

Fluorescence
Fluorescence of samples was determined by use of a
Turner fluorometer. The recommendations of the 1968 Turner

Manual for fluorometric procedures were followed.

26

The primary filters used were a combination of 2A and 47B,
while the secondary filter used was a 2A—12. The general
purpose lamp #110-850 was used.

Water from an upstream station, sample 52A, was arbitrar-
ily set at a value of 20 to permit anticipated higher and
lower values to be distinguished. If the fluorometer were
set at 0 for this upstream sample, lower values could not be
differentiated. Thus, fluorescence determinations were made

on a relative scale ranging from 0 to 100.

ghOSphorus

In order to establish total phosphorus levels for the
study area, two series of samples, as well as a few other
selected samples from dwellings suspicious of contamination.
were analyzed for total phosphorus concentration by the am-
monium moledate-stannous chloride method. These samples
were analyzed by a Water Quality Laboratory at Michigan
State University. .As samples for phosphorus were stored for
several months, the procedure of acidification of samples to

remove absorbed phosphorus on container walls was necessary.

Other Parameters

 

Oxygen and Temperature
Oxygen.and temperature for diurnal curves were recorded
with a Rustrak recorder, equipped with an oxygen electrode

and thermistor. The oxygen electrode was standardized with

27

a Winkler oxygen test. All oxygen readings were corrected
for temperature changes.

The recorder was set up at various stream locations dur-
ing August and September to determine the extent of the
oxygen sag which was anticipated to be the most severe during
this time period. The sensors were set at midstream so as to
obtain a representative measurement for that portion of the

stream.

Invertebrates

Bottom samples for examination of invertebrates were
taken with a Surber bottom sampler. Bottom material was
thoroughly agitated, hand scrubbing each item from the bottom
and discarding it, until no further invertebrates could be
found. Collected organisms were preserved in 10% formalin
and later sorted.in a white enamel pan and classified into
families. In samples containing vegetation, plants were
pulled out by the roots and pushed into the end of the Surber
net before working over the bottom material. The vegetation
was sorted from the invertebrates and dried as described !
below for vegetation samples.

Bottom samples were taken in gravel riffle areas and in
similar areas covered with vegetation to compare the in-
vertebrate life found within each of these two types of
habitat. Single samples were taken at each particular combi-
nation Of location and type of bottom except at Pollack

Bridge where two samples from gravel riffles were pooled-

28

Samples were taken so environmental conditions of depth,
gravel size, vegetation density, and current velocity were
nearly uniform. All samples were taken during the two day

period of August 27th and 28th.

Aquaticgglants

Vegetation density was defined as the total weight of
vegetation including roots growing within a square foot of
stream bottom. The assessment of vegetation density was
made by sampling selected areas with a Surber sampler.
Evenly spaced points were selected on a map of the study
area and sampling was done as close as possible to the desig-
nated point. Samples were taken.in the most representative
area within a fifty foot section of the river, centered
about the imaginary preselected line.

The Surber sampler was placed on the stream bottom of
the selected area and the resulting mass of flattened vege—
tation was worked until only that actually growing within
the square foot, metal sampler base remained there. The
vegetation was then pulled out and allowed to drift back.
The bottom area was worked over to remove remaining roots.
Samples were then packed in plastic bags and frozen until
they could be oven dried at 105°C to obtain uniform moisture
conditions.

Rough estimates were made also of the total bottom area

covered by Vegetation thick enough so the bottom was not

29

readily visible. Because of this definition, there can be
variability in the quantity of vegetation present at dif—
ferent locations with the same percentage of bottom area
covered.

Several visual estimates were made from canoe of con-
viently mapped sections of the river, each extending about

several hundred feet in length. These estimates, to the

nearest ten percent, were averaged, as were the estimates of

the distance of each section, to produce mean values. These

'values were then used to calculate mean values of percentage

of vegetation coverage for each study section.

Current Velocity

Current velocity was determined with a Price-Gurley

current meter by placing the measuring wheel at about 0.4 of

the depth of the bottom. Standard procedures were employed
for conversion of meter readings to feet per second of

current velocity.

RESULTS

Results from General River Survey

Current yelggity

Current velocities are recorded in Table 1. :As indicated,
stream velocity is relatively slow in Sections I and II except
in the upstream part of Section II where velocity is moderate.
In the last two study sections, velocity is approximately
twice as great as in the preceding sections.

As mentioned in the description of the river, this data
illustrates an inherent physical quality of the river largely
responsible for present conditions of the river. The current
velocity of Section I is sufficient to sustain good water
quality in the clean water above Grayling. However, in the
downstream half of Section III, reaeration is insufficient
to counteract the BOD load from the Grayling sewage treatment
plant effluent. Stream flow is smooth except immediately
downstream from Grayling. No rapids exist in Sections I or
II. By contrast, in Sections III and IV reaeration is suf-
ficient to purify the already partially recovered waters from
upstream. Some increased aeration occurs because of the in-

creased velocity, but rapids and riffles occurring in

50

51

Table 1. Current Velocity measured by Price-Gurley current
meter at one-half midstream depth on September 10,

 

 

 

 

 

 

1968.
Kilometers Velocity
Station below Pollack Bridge (feet per second)
Sectiong;
1 0.0 1.17
2 4.0 1.29
Section II
5 8.7 1.55
4 8.9 2.25
5 9.2 2.08
6 9.5 2.25
7 10.2 2.05
8 10.4 2.69
9 11.0 1.17
10 11.9 1.60
11 12.9 1.19
12 15.6 0.45
15 14.6 1.55
14 15.5 1.47
15 16.7 1.41
16 17.7 1.29
17 18.0 1.47
Section II;
18 18.5 2.65
19 19.6 2.25
20 20.5 2.08
21 21.6 5.42
.22 22.6 1.79
25 25.9 2.28
24 25.0 2.78
25 26.2 2.97
26 27.2 2.65
27 28.9 2.58
28 29.5 2.86
29 51.0 2.78
Segtion IV
50 52.2 2.78
51 55.4 2.97
52 54.7 2.55
55 55.8 2.58

54 56.8 2.84

 

52

Sections III and IV probably have a much larger role in in-
creased aeration. Also, surface turbulence in the downstream
sections is probably greater than can be correlated with the;
current velocities present. Dense, trailing vegetation
growths may not disrupt surface turbulence as much as they
slow current velocity. “Current velocity in Sections III and
IV is also sufficient to prevent accumulations of sand from

occurring in midstream except where vegetation growths occur.

Vegetation

The results of the vegetation survey are listed in Tables
2 and 5, showing density and percent of bottom coverage,
respectively. .As shown in these two tables, the greatest
average density of vegetation in grams of oven dried material
per square foot increases in each succeeding section as one
proceeds downstream. However, the percentage of stream bottom
covered by vegetation is greatest in Section III, about half
as great in Sections II and IV and least in Section I.

It is evident also from the weights of some of the vege—
tation samples and from the method by which these samples
were collected, that in some regions of the river extensive
local coverage by thick, dense vegetation occurs. Compara-
tive published data on quantitative vegetation densities of
coldwater streams seems to be lacking in the literature.
Westlake (1961) found the standing crop of Potamogeton
pectinatus in a sewage effluent drainage channel to average

125 g dry weight/m2 of stream surface. Owens and Edwards

55

Table 2. Dry weight in grams of a square foot of vegetation
from the AuSable River during the fall of 1968.
(To convert to square meters, multiply by 10.75.)

 

 

Kilometers Grams per
Sample below Pollack Bridge square foot

 

Section I

55 4.2 6.5
54 4.5 4.6
55 4.9 15.4
56 5.5 8.6
Average of Section I 8.5

Section II

 

 

1 9.5 0.4
2 9.9 14.6
5 10.6 10.0
4 11.0 6.0
5 11.9 15.0
6 12.8 15.8
7 15.7 0.0
8 14.6 19.7
9 17.1 9.9
10 17.7 15.8
Average of Section II 10.5
Section III

11 18.0 12.1
12 18.2 45.5
15 18.5 18.0
14 18.6 27.6
15 19.1 22.1
16 19.6 21.2
17 19.8 25.7
18 20.0 27.5
19 20.2 28.1
20 20.7 12.5
21 21.4 14.6
22 22.0 16.8
25 22.2 57.5
24 22.6 4.2
25 25.2 16.0
26 25.4 7.2
27 25.7 16.5
28 25.9 20.5

continued

54

Table 2-—continued

 

 

 

Pilometers Grams per
Sample below Pollack Bridge square foot
29 25.0 54.9
50 25.8 51.2
51 26.7 9.8
52 27.0 0.0
55 27.5 12.5
54 27.8 15.2
55 28.2 15.8
56 28.5 47.5
57 28.9 21.5
58 29.4 15.0
59 29.9 18.5
40 50.2 8.5
41 50.5 24.8
42 50.7 15.5
45 51.0 15.4
Average of Section III 19.8
Section IV
44 51.5 56.2
45 51.9 55.5
46 52.5 17.8
47 52.6 17.5
48 52.8 42.6
49 55.1 18.5
50 55.4 15.1
51 55.7 8.1
52 55.9 27.1
Average of Section IV 26.2

 

55

Table 5. Mean percentage of stream bottom area covered by
vegetation for the main stream of the AuSable
River during the summer of 1968.

 

 

 

Sample Percentage
Section I* 20
Section II 26
Section III 47
Section IV 25

 

*-
Includes only that portion extending from the Borcher
Bridge, below the old power dam, to the M-72 Bridge.

56

(1961) measured the dry weight of macrOphytes from 4 fertile
but unpolluted streams in southern England. They found the
average dry weight to range from 55.8 to 585.2 g/m2 of
stream surface. Although these weights are comparable to
those in the present study, they are from streams that are
basically more fertile. Owens and Edwards (1961) list for
the rivers Test and Chess, for example, average values of
5.6 and 5.8 ppm nitrate nitrogen and 0.058 and 0.055 ppm
total phosphorus, .respectively. In comparison with typical
cold water streams, the AuSable River seems to have an ex-
tensive growth of vegetation.

Possible causes of this growth pattern are indefinite.
Certainly a major factor responsible for the quantity of
growth is the enrichment of the river due to the domestic
effluent from the city of Grayling and possible other causes.
Possibly the chemical form of some of the organic compounds
is more suitable for plant use further downstream from K
Grayling than at.Section II clOser to the point of input.
Probably other ecological factors determine suitability of
areas for growth. Current velocity, or some factor corre-
lated with velocity, may be a decisive factor. This is evi—
dent as one proceeds from Section II to Section III. There
is a sharp increase in current velocity, bottom material
changes from sand to gravel, and an immediate increase in
vegetation occurs.

Also notable is that the vast bulk of vegetation present

is a single species, Potamogeton filiformis. Upstream from

57

Grayling a more varied plant community exists, composed of
several species of broadleaved gotamogetong, g, filiformis,
Vallisneria, sp. and Ranunculus sp. However, downstream

from Grayling, g, crispus, and Anacharis sp. are only locally
abundant among the continual coverage of g. filiformis.

This is perhaps the greatest single factor responsible
for the present and future condition of the river. Best
known of the vegetation effects are the diurnal oxygen
pulses produced by oxygen production during sunlight hours
and oxygen consumption during darkness. Although these pulses
did not prove to be drastic in this study, in local, dense
concentrations of vegetation, oxygen concentration probably
was much more reduced than shown by Open water measurements.
This may put an environmental stress on clean-water organisms.z'
either forcing them out of the area or preventing their ,j
development.

Another effect of vegetation is that it slows the veloc-
ity of the water filtering through it. This causes several
results. First, slowing velocity and hindering mixing
prevents the aeration that normally occurs. Second, decreased ‘\
velocity at the base of the plants prevents the development /)
of normally occurring swift water invertebrates. Also, water‘jh
of decreased velocity is incapable of carrying its original
sediment thus, deposits of sand occur in the beds of vege-
tation, gradually building up mounds of sediment.

With an endless enrichment of nutrients from the Grayling

waste water treatment plant effluent, the quantity of

58

vegetation may continue to increase. The decay Of each
annual crop adds more organic matter to the stream, filling }
in pools and allowing additional growth the following year. /
This cycle, while not yet out of control, may eventually

destroy the river as it is known today.

Invertebrates

The results of invertebrate bottom samples taken in non—
vegetated and vegetated areas are given in Tables 4 and 5
respectively. These results are shown graphically in Figure
4, contrasting the number of families having representatives
in each sample with the sample lucations. Tolerance status
of families for Figure 4 are listed in Tables 4 and 5.
Tolerance status is based on species tolerance status listed
by Michigan Water Resources Commission (1966).

Although sampling was not extensive, a pattern for the
study area is evident. At Pollack Bridge, sample 17, in-
vertebrate density is low but representation of intolerant
types is high, especially the Ephemeroptera. Inside the
city of Grayling but above the entrance of the sewage treat-
ment plant effluent, sample 1, a lack of intolerant forms is
already evident. The tolerant invertebrates other than in-
sects are present as well as the tolerant coleOptera, diptera.
and hydropsychid trichOptera. Some intblerant caddis families
are present.

The lack of intolerant forms found in the samples taken

between the entrance of the waste water treatment plant and

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Kilometers Below Pollack Bridqe.

Figure 4

45

Burton's Landing, samples 2 to 7 illustrate the more harsh
conditions of low dissolved oxygen and warm water in this
area. Only a few families of caddis flies and sparse
populations of several families of mayflies are present.
The more tolerant dipterans and coleoptera are well repre-
sented.

The series of samples extending from Burton's Landing
to Sayer's cottage samples 8 to 21, in the middle of Section
IV illustrate the improved water quality of the last two
sections Of the study area. Good representation of nearly
all types of.invertebrates, especially intolerant forms,
occurs within this region. The presence of two families of
stoneflies in the last few samples typifies a degree of
water quality that is not reached anywhere upstream within
the study area.

It is noteworthy that although the number of intolerant
families present varies with location, the number of toler—
ant and faculative families remains quite constant throughout
the study area.

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within the two types of samples shows the vegetated samples
to generally contain larger populations made up of more
limited types than found in nonvegetated samples, both with
respect to total number of families present and numbers of
individual per families. vegetated samples taken in the

same location as nonvegetated samples also contained fewer

46

numbers of intolerant families. POpulations in vegetated
samples were composed mainly of organisms clinging to or
attached to the current swept vegetation. Usually the sub-
strate within these vegetated samples was choked with sand
or silt, preventing the more typical organisms associated
with the gravel bottom from occurring there. Notable large
groups from these samples were the families Ephemerellidae,
Brachycentridae, Chironomidae, and Simulidae. In comparison
with vegetated samples, samples from gravel areas generally
contained moderate populations of many types except for the
caddis family hydrOpsychidae which was abundant in several
samples.

A probable explanation for the observed low numbers of
organisms present is the date of collection. During late
September, many forms would only be present as eggs or very

small larvae which would be difficult to detect.

Oxygen and Temperature Elugtuations

Diurnal curves for oxygen concentration and temperature
are located in Figure 5. Curves are presented to show dis-
solved oxygen concentration, dissolved oxygen saturation
levels, and temperature.

At the upstream end of the study area, a rather typical
natural diurnal curve occurs with high dissolved oxygen dur-
ing the entire cycle. However, below Grayling, Allison's
and Harland's residences, dissolved oxygen is constantly low,

never reaching saturation; while temperature reaches the

Figure 5.

47

Diurnal oxygen and temperature fluctuations for
locations and dates as listed. Dissolved oxygen
concentration is shown as a solid line (-—-),
dissolved oxygen saturation as a dotted line
(...), temperature as a dashed line (---).

Milligrams per liter Oxyqen concentration

Pollack Bridge, August 14 and 15,1968
‘0‘ ._ _

 

18 and 19,1968
l2

 

 

 

48

 

 

 

 

 

 

 

 

 

 

 

 

Allison’s Residence, 11.4 Kilometers below Pollack Bridge, August

 

 

 

 

 

 

 

 

 

 

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z
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.
z
T;
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3

Temperature in Degrees Centigrade

Harland’s Residence,l3.4 Kilometers below Pollack Bridge, August
and 20, 1968

 

 

 

 

Figure 5 continued

Milligrams per liter Oxygen Concentration

 

49

Park's Residence, 19.1 Kilometers below Pollack Bridge, August 30 and
31. 1968 .

  

Ul
hUIOVQO

Stepban’s Residence. 20.3 Kilometers below Pollack Bridge, August 20
and 21, 1968

 

 

 

 

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8
7
6
5
4
3
4
Lmrm ———— -- '12 -———AM '34 PM——J
Fowler’s Residence,26.2 Kilometers below Pollack Bridge, August 23
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1 * ____- ‘23
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l 25,1959

 

  

 

 

 

A A A
v T I

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Figure 5 continued

 

Temperature in Degrees Centigrade

50

upper limits for species normally designated as cold water
types. In reaching Section III, Park's, Stephan's, and
Fowler's residences, oxygen values show a greater fluctua-
tion, becoming supersaturated in late afternoon and dropping
to 6 mg/liter and less before daybreak. In Section.IV, this
variation becomes less distinct, with the low oxygen values
of Section III disappearing.

It is believed that the above oxygen results reflects
the vegetation, pollution level, and water temperature
present within each area of the river. -At Pollack Bridge,
temperature is moderate and vegetation sparse. Thus oxygen
concentration is high. Below Grayling, low vegetation density
and high organic load does not allow oxygen concentrations to
reach saturation. Farther downstream increasing current
velocity and vegetation density react to produce a wide fluc-
tuation in oxygen concentration, with perhaps the stream tur-
bulence preventing' extremely low oxygen concentrations.

In Section IV, current velocity and entering ground water
and tributaries play a dominant role. Although vegetation
is dense, increased amounts of air-water exchange and cool
water prevents the results of Section“III.

The Michigan Water Resource Commission (1966) recorded
similar diurnal oxygen and temperature curves with an im-
'portant exception. They reported large oxygen fluctuations
immediately below Grayling, Allison's and Harland's resi-

dences, with supersaturation during afternoon and low oxygen

51

concentration at night. They also reported large aquatic
plant growths between Grayling and these areas, which were

not observed during this study.

Phosphorus

Total phosphorus concentrations for the Main Stream
for several stations of the East Branch, and for several
sample sites downstream from dwellings suspicious of contami—
nation are listed in Table 6. Figure 9 graphically shows
the series of phosphorus samples.

Upstream from the entrance of effluent from the Grayling
waste water treatment plant, total phosphorus concentration
of the Main Stream is very low, but rises below the sewage
treatment plant. This higher level quickly drops off to a
relatively stable level throughout the study area. The
stream vegetation may be responsible for the apparent rapid

loss of total phOSphorus.

Results fromilggividual Septic Systems

Actual totals of chemical results and fluorescence of
samples, as well as adjusted chemical and fluorescence
results are listed in an Appendix. Adjusted results are
the actual values of the dwelling samples minus the average
of samples taken within that section of the river for that
data. Due to differences of the stream in time and area,
actual results are more difficult to analyze. Samples not

taken directly from the river were considered separately

52

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55

separately within their section and date of collection in
determining adjusted values.

Figures 6, 7, and 8 are graphs showing frequency of
adjusted results occurring within designated ranges. As
evident from these graphs few sample results occur within
a range that could be considered deviate enough from zero
to be indicative of contamination. Belief is that if no
samples are from sites of contamination, that would cause
higher values of parameters, subtraction of the average of
all values, which should be nearly equal for a short dis-
tance and time, would produce adjusted values of zero or
near zero. Samples from sites of contamination would produce
high positive adjusted values. Due to the fact that sampling
was preformed in such a way to include any incoming water
which might include contaminants, these samples would be low
in parameter values relative to control samples and dwelling
samples which included little incoming dilute water.'ASuch
samples would be expected to have negative adjusted values.
Control samples, taken in midstream where contaminants or
pure ground water from the stream edge would have little
effect on parameter magnitude, were clustered about zero.

The small number of samples indicated as being suspi—
cious of contamination in the Appendix, and the graphs in
Figures 6, 7, and 8, do not indicate the dwelling located
along the study area of the river to be a major source of
contamination. Further reasoning behind this statement will

be taken up in the discussion.

54

Figure 6. Distribution of adjusted relative fluorescence
values for control samples and samples from
dwellings.

Frequencey of Occurrence

55

J

 

 

 

 

201 .

1o -

 

.-rl'i

0 . - -
<-15 -15 -10 -5 0 5

 

Adjusted Relative Fluorescence Values

CI: Dwelling Samples
U: Control Samples

Figure 6

 

.. ll.

10 is >I'

56

Figure 7. Distribution of adjusted chloride values
(in milligrams per liter) for control samples
and samples from dwellings.

Frequency of Occurrence

57

gr a

he
9?

 

 

 

 

 

 

 

 

 

 

 

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Adjusted Chloridellalues in Milligrams per liter

0 ‘-'-'- Dwelling Samples
I = Control Samples

Figure 7

58

Figure 8. Distribution of adjusted nitrate nitrogen
values (in micrograms per liter) for control
samples and samples from dwellings.

59

83555

Frequency of Occurrence

l

25-

 

 

 

 

 

 

 

 

 

-400 -95 '50 -25 CI 25 50 75

Adjusted Nitrate Kitroqen Values in Micrograms per liter

0: Dwellinq Samples
I= Control Samples

Figure 8

  

-l]-

100 125 (125

60

No statistical tests were made to distinguish dwelling
samples as being indicative of contamination, nor could any
rightfully be made because of the number of samples taken
per dwelling. Samples considered as being indicative of
contamination were determined by considering the magnitude
and variation of the adjusted values, particularly the con-
trol and upstream values. Those adjusted results being
several times greater than the range of the majority of
results were indicated as being suspicious.

Figure 9 is a plot of total phosphorus, chloride,
nitrate nitrogen, and fluorescence levels of control samples
taken over the range of the study area. These graphs give
the general levels that the various parameters occupied
during the time of the study. Due to the few samples plotted
and differences of parameter levels with time, the graphs
appear erratic. However, general patterns are evident.
Total phosphorus, nitrate nitrogen, and chloride concentra-
tions are low. Total phosphorus and nitrate nitrogen con-
centrations temporarily increase below Grayling. Chlorides
and fluorescence show no strong pattern. Although increases
in parameter levels downstream could possibly be due to
additions of materials from some source such as private
septic systems, this may be due only to small sample size or
sampling in areas where incoming dilution waters caused

samples to be less concentrated.

61

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Figure 9

DISCUSSION

Detectability

A discussion of the factors influencing the detecta-
bility of contaminants is necessary to help evaluate the
results of the study.

The lower limit of a fluorescein solution that was
readily visible was of the magnitude of one part per million
concentration. With a fluorometer, concentrations on the
order of one part per billion could be distinguished.
Considering that the quantity of dye injected was approxi-
mately 15 grams per system, this quantity had a potential
capacity to produce 15,000 liters of visibly fluorescent
water and 15,000,000 liters of fluorescent water detectable
by fluorometer. Assuming that sampling was preformed at a
time so as to intercept the dye, and since not much,dye was
observed or suspected in fluorescence readings, this requires
material from septic systems to be considerably diluted.

Dilution of contaminants is an important factor to con-
sider. The possibility exists that nutrients are reaching
the river in concentrations that are below the sensitivity

of the tests used to detect them. This is particularly true

65

64

in the case of chlorides, which should not be transformed,
readily absorbed, or taken up by plant roots. Chlorides
will eventually reach the stream. Since these were detected
in only several cases, probabilities are that this material
is moving at dilute concentrations.

Samples to be analyzed for nitrate nitrogen had to be
stored for several months before analysis. Although stored
at near freezing temperatures, changes in nitrate concentra-
tions probably did occur. Jenkins (1967) showed that nitrate
concentration for estuarine water of similarly stored samples
increased slightly over about a month period. Personal
observations on samples collected in March of 1969 and fol—
lowed closely showed nitrate concentration to decrease.
However, the relatively low nitrate nitrogen results of this
study are not in disagreement with those from the Michigan
water Resources Commission (1966) or Hendrickson (1966).

Another factor involved here is the matter of timing
the sample collection. Determining the amount of time re-
quired for materials to travel to the stream is very important
in sampling potential contaminants or dye at their maximum
concentrations.

Sources of contamination other than domestic waste may
interfere with the results of the study. Fertilizers from
lawns may result in high nitrate readings. ‘Some synthetic
detergent products are strongly fluorescent and the entrance

of these materials from kitchen sink drains may interfere

65

with fluorometer tests for fluorescein (Turner Fluorometry
Reviews, 1968). .Although these substances are just as
serious pollutants as is domestic waste, they are not the

particular effort of this study and may bias results.

Factors Influencing the Degree of Contamination

I do not believe the private septic system of dwellings
within the study area to be a major contribution of nutrients
to the AuSable River. This conclusion is based upon the re—
sults of the study and the following factors: the number of
systems and amount of use they receive, distance and eleva-
tion from the river, the transformation and absorption of
materials in and near the tile fields, and the uptake of
nutrients by plant roots.

Reference to the Appendix shows that in only four cases
was dye actually observed and in only several other instances
were samples designated as being suspicious. These cases
were probably the result of faulty systems where material
made a relatively direct flow to the river from some point in
the tile field and are not representative of the majority of
septic systems.

According to study records, there are approximately 220
dwellings on the nearly 20 miles of stream bank located
within the study area. These can be subdivided into 68

permanent homes, 25 "half-year" homes, and 127 cottages.

66

Allowing 52 weeks of residence for permanent homes, 26 weeks
for "half-year" homes and 4 weeks for cottages with an
average of 4 persons per dwelling, this amounts to 18,776
weeks spent by people within the study area serviced by
private domestic waste treatment facilities. This is about
15 percent of the amount of time spent by pe0ple in the city
of Grayling as recorded in the Michigan Water Resources
Commission Report (1966). Assuming that the quantity of
domestic waste is roughly pr0portional to the length of time
at the location, then even if the entire amount of waste
from private systems went directly into the river, the effect
would be small relative to the primary effluent from Gray-
ling's municipal waste water treatment plant. However,
there is considerable evidence available to indicate that
septic tank effluent undergoes gross changes in composition
while traveling through the soil.

After materials leave the anaerobic conditions of the
septic tank they enter the aerobic conditions of the tile
field. Here the reduced products of the septic tank become
oxidized. Robeck, Cohen, Sayers, and WOodward (1962) showed
that allowing 5 gal. of domestic sewage to flow daily
through four feet of sand in a lysimeter simulating conditions
below a septic system tile field, substantially lowered the
BOD and total phosphorous levels of the effluent and con-
verted organic and ammonia nitrogen to nitrates. After

several months of using this experimental apparatus. they

67

found populations of microflora associated with organic
breakdown in the lysimeter soil.

Jansson (1958) postulated an internal mineralization—
immobilization nitrogen cycle. He states that heterotrophic
microflora convert organic matter into microbial cells to
the extent that the energy-nitrogen ratio of the organic
additive will allow. The rest of the organic matter is
converted to a surplus inorganic nitrogen pool. In the case
of sewage sludge, which is rich in nitrogen, the nitrogen
supply is sufficient to meet the needs of the microbial demands
for cell synthesis and provide a net mineralization of
nitrate and ammonium compounds available for higher plant
use or denitrification. Jansson (1958) further states that
after mineralization occurs, forming nitrate or ammonium
products, losses of these inorganic nitrogen forms may occur
due to evaporation, leaching, and denitrification.

A small amount of evaporation of ammonia may occur from
the top layer of alkaline soils when organic materials high
in nitrogen are added.

The nitrate pool of soil is quite liable to losses when
the soil is not occupied by;plants. As nitrate ions are
practically not adsorbed by soil colloids, losses occur as
soon as leaching begins.

Denitrification is a typically anaerobic process requir—
ing either alternating aerobic and anaerobic conditions or

continuous semi-aerobic conditions. He states that losses

68

of nitrogen readily occur through denitrification in natural
soils.

Ellis and Erickson (1969) studied phosphorus adsorption
ability of various Michigan soils. They state that the
phosphorus adsorption capacity of calcium phosphate in pounds
per acre for a three foot profile to be 1,699, 1,818, and
2,106 for three soils from the study area, Grayling Sand,
Roseland Sand, and Rubicon Sand respectively. Similar results
were obtained for sodium phosphate. They also state that
soils have the ability to recover their adsorptive capacity
after a period of rest. Three months after saturation, all
but one of the sixteen soils studied had recovered at least
50 percent of its absorptive capacity. They calculate that
a septic tank system serving a permanent residence of four
would require 8,101 cubic feet of soil between the tile
field and water table to prevent phosphorus concentration
leaving the field drainage system from reaching 0.5 ppm after
10 years. This calculation makes the following other assump-
tions. Total phosphorus content of the 200 gal per day dis-
charge is 20 mg/liter. The phosphorus is all soluble
orthophosphate, no phosphorus is removed in the septic tank,
and the soil will recover its adsorptive capacity only once,
and the tile line is placed in the C horizon. The calcula-
tion is made using a Rubicon Sand, with similar phosphorus
adsorption capacity to soils within the study area and thus

the calculation applies fairly well to dwellings within the

69

study area. It should be noted that all figures applying
to the soil and other septic system qualities mentioned are
minimum values, and it is likely that a lesser load is put
on the system and that a greater quantity of phosphorus
can be adsorbed than stated. In a permanent residence it
is likely that absorptive capacity is recovered more than
once. Some phosPhorus is removed in the septic tank. If
the tile lines are placed in the B rather than C horizon,
only 5,144 cubic feet of soil are needed. Also it is evi-
dent that in systems with limited use, phosphorus adsorption
recovery may prevent the soil in the system from ever reach-
ing saturation.

There are several dwellings with septic systems located
near the water table or close to the river; particularly
the group of homes located just below Grayling. However,
most dwellings are situated far back from the river horizon-
tally and elevated rather high vertically. Few dwelling
owners when questioned claimed to have septic systems that
were closer than.100 feet to the river. Many systems were
several hundred feet from the river. Also in the majority
of cases land elevation where dwellings were located were
at least five feet above the stream surface and in some in-
stances elevation is probably greater than twenty feet.
This distance factor allows time for good oxidation and con-
tact volume for adsorption of products from the tile field

to the water table where the primary degradation of septic

7O

tank products occurs. Some degradation may also occur in the
distance material travels from the point of intersection of
the water table to the stream.

Another factor of possible great importance in the move-
ment of nutrients through the soil is the abundance of vege—
tation covering the banks of the stream. Probably of
greatest importance here are trees as opposed to annuals,
which send roots not only to the water table but are known
also to grow roots to the tile field. The United States
Department of Health, Education, and Welfare manual of
septic-tank practice (1967) states that this phenomena has
been used to some degree of success in aiding the disposal
of sewage effluent in tight clay soils where evaporation is
limited. It also states that this factor may be of impor-
tancezhtnorthern resort areas during the summer. Nitrogen
forms from the tile field may be either ammonia or nitrates,
both of which could be utilized by plants. Other oxidized
forms‘of nutrients such as phosphates are probably available
for plant uptake. ,Also if oxidized nutrients are moving at
low concentrations through at least 100 feet of stream bank
covered with vegetation, plant roots will probably absorb

much of the material before it is able to reach the river.

Suggestions on Improvements of the Stream

The Michigan Water Resources Commission Report of 1966

suggests several improvements in the stream. These are to

71

remove the dams causing the large, shallow bodies of water
above Grayling and to remove the effects of the sewage plant
effluent from the city of Grayling. In the long run the
fulfillment of these two suggestions will lower water tempera-
tures and retard eutrophication of the stream. However, the
fact should be stated that fulfillment of these suggestions
will not restore the lower water quality of the downstream
half of Section II to the quality of water fOund in Sections
' III and IV. There are certain inherent qualities of this
area documented in this study that naturally bias the quality
of this water to be low. The shallow, sand bottomed stream
of low velocity simply is not capable of supporting the large
pOpulations of cold-water life found downstream.

Another suggestion is to provide for closer supervision
of installation of private septic systems. The minimum re—
quirements should be those suggested by Hendrickson (1966).
Tile fields should be at least three feet above the water
table and a minimum horizontal distance of 50 feet from the
river or Springs and seepage areas. The large number of
springs located along certain stretches of the river present
a difficult problem in the present location of some septic
systems which may be 50 or 100 feet from the river but dflly
several feet from a small brook or spring running directly
into the river.

An effort should also be made to distribute septic tank

effluent in the tile field such that it spreads over a large

72

area and thus contacts a large volume of unsaturated subsoil.
The size of effective absorption fields of septic systems
located near streams should be based on the ability of sub-
soils to adsorb nutrients rather than solely on the current

standards of permeability of soils.1

Suggestions for Further Studies

In order to examine the extent of contamination in cases
of proPerly installed septic systems more thoroughly, the
following suggestions would be useful in a further study.
Consider only several dwellings, representative of homes and
cottages along the river. These dwellings should be picked
so that complete COOperation is obtained with the owner and
locations of septic tanks and drainage fields are known.

In the case of cottages, where use is seasonal, closely
monitor the fluorescence, nitrate, and chloride levels by
taking several samples per day before and after putting the
fluorescein into the septic system at the beginning of the
period of use. Also, monitor several areas where contami-
nation from private systems is unlikely, to compare with the
results obtained from nearby areas containing tile fields

of permanent homes.

 

1Personal communication with Dr. Boyd Ellis, Associate
Professor of Soil Science at Michigan State University.

CONCLUSIONS

1) As indicated in the description of the river, I would
consider Sections III and IV of the study area to be of rela-
tively good water quality. Sections I and II are of lesser
water quality, with the downstream half of Section II being
notably degraded. The above is most clearly shown by the
invertebrate life present in each section and also by other
aspects discussed. The chemical load of the stream is rela-
tively light, except below Grayling where they temporarily
increase. Vegetation in the stream is a significant factor,
greatly affecting dissolved oxygen, bottom type, and current
velocity. This subsequently affects life forms and eutrophi-
cation of the stream.

2) I am convinced that I was able to detect only cases
of contamination where most of the material was channeled
through a relatively small area, rather directly to the river.
This obviously included defective systems from which sewage
material entered the stream relatively unchanged, but also
may have included cases in which sewage materials filtered
through several feet of soil before reaching the stream.

The results of this study show these cases to be relatively

few.

75

74

5) I also believe that if domestic wastes or products
of waste do reach the river from proPerly installed septic
systems, they must travel in relatively low concentrations
due to the proportionally large volume of ground water they
must encounter in their movement. This would provide
Opportunity for transformation of reduced septic tank
products to oxidized forms, adsorption of some materials,
particularly phosphorous, and absorption of materials by
plant roots.

Due to the position of most dwellings relative to the
river, situated both well elevated and far back from the
river, and due to the small amount of use most of the septic
systems receive, I believe that in most cases, contamination
from these systems is negligible. Only in the case of
permanent homes located close to the water table is contami—

nation suspected but could not be shown.

LITERATURE CITED

LITERATURE CITED

Ellis, B. G. and A. E. Erickson. 1969. Movement and trans-
formation of various phosphorus compounds in soils.
Report from Michigan State University Soil Science Depart—
ment and Michigan Water Resources Commission for period
ending June 50, 1969.

G. K. Turner Associates. 1968. Manual of fluorometric pro-
cedures. Palo Alto, California.

G. K. Turner Fluorometry Reviews. 1968. Fluorometry in
studies of pollution and movement of fluids. G. K. Turner
Associates, Palo Alto, California.

Hendrickson, G. E. 1966. Michigan's AuSable River--today and
tomorrow. Michigan Department of Conservation, Geologi—
cal Survey Bulletin 5, Lansing, 80 p.

Jansson, Sven L. 1958. Tracer Studies on Nitrogen trans-
formations in soil with special attention to mineraliza-
tion-immobilization relationships. .Ann. Roy. Agr. Coll.
Sweden. 24:101-561.

Jenkins, D. 1967. The Differential Analysis and Preservation
of Nitrogen and Phosphorus forms in Natural Waters, pp.
265 to 280. In Robert F. Gould (ed.). 1968. Trace
Inorganics in Water, American Chemical Society,
washington, D. C., 596 p.

Jenkins, David and Lloyd L. Medsker. 1964. Brucine Method
for Determination of Nitrate in Ocean, Estuarine, and
Fresh Waters. Analytical Chemistry 56 (5):610-612.

McGauhey, P. H. 1968. Engineering Management of Water
Quality, McGraw-Hill Book Co., New YOrk, 295 p. From
Babbit, H. E. and Baumann, E. R., 1958, Sewerage and
Sewage Treatment, John Wiley and Conc, Inc., New York.

Michigan water Resources Commission. 1966. water Resource
Conditions and Uses in the AuSable River Basin. State
of Michigan, Water Resource Commission, Department of
Conservation.

75

76

Owens, M. and R. W. Edwards. 1961. The effects of plants
on river conditions, III. CrOp studies and estimates
of net productivity of macrOphytes in four streams in
southern England. J. Ecol. 50:157-162.

Robeck, G. G., J. M. Cohen, W. T. Sayers, and R. L. WOodward.
1965. Degradation of ABS and other organics in unsatur-
ated soils, J. Water Poll. Cont. Fed. 56(10):1225-1256.

Thresh, Beale, and Suckling. 1949. The Examination of water
and Water Supplies, Sixth Edition edited by Windle
Taylor, J. and A. Churchill Ltd., London. 810 p.

United States Department of Health, Education, and welfare,
Public Health Service. 1967. .Manual of Septic-Tank
Practice, Public Health Service Publication No. 526.
U. S. Government Printing Office, Washington, D. C.

Westlake, D. F. .1961. Aquatic macrOphytes and the oxygen
balance of running water. Verh. Int. Ver. Limn.
14:499-505.

APPENDIX

77

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mcwuoano Hmuwa :mmouuwz mumuuwz mocmomwnosHm m>0900mm

 

 

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00000000 00000
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