EPA-R3-73-037
July 1973 Ecological Research Series
Effect of Silt and Silt Removal
In A Prairie Lake
Office of Research and Monitoring
U.S. Environmental Protection Agency
Washington, D.C. 20460
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RESEAECH REPORTING SERIES
Research reports of the Office of Research and
Monitoring, Environmental Protection Agency, have
been grouped into five series. These five broad
categories were established to facilitate further
development and application of environmental
technology. Elimination of traditional grouping
was consciously planned to foster technology
transfer and a maximum interface in related
fields. The five series are:
1. Environmental Health Effects Research
2. Environmental Protection Technology
3. Ecological Research
H. Environmental Monitoring
5. Socioeconomic Environmental Studies
This report has been assigned to the ECOLOGICAL
RESEARCH series. This series describes research
on the effects of pollution on humans, plant and
animal species, and materials. Problems are
assessed for their long- and short-term
influences. Investigations include formation,
transport, and pathway studies to determine the
fate of pollutants and their effects. This work
provides the technical basis for setting standards
to minimize undesirable changes in living
organisms in the aquatic, terrestrial and
atmospheric environments.
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EPA-R3-73-037
July 1973
EFFECT OF SILT AND SILT REMOVAL
IN A PRAIRIE LAKE
By
Clyde K. Brashier
Constance L. Churchill
Gordon Leidahl
Dakota State College
Madison, South Dakota 57042
Project 16010 DZK
Program Element 1B1031
Project Officer
Charles F. Powers
Pacific Northwest Environmental Research Laboratory
National Environmental Research Center
Corvallis, Oregon 97330
Prepared for
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, D.C. 20460
For sale by the Superintendent of Documents, U.S. Government Printing Office, Washington, D.C. 20402 - Price $2.60
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EPA Review Notice
This report has been reviewed by the Environmental
Protection Agency and approved for publication.
Approval does not signify that the contents necessarily
reflect the views and policies of the Environmental
Protection Agency, nor does mention of trade names or
commercial products constitute endorsement or recommenda-
tion for use.
11
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ABSTRACT
A surveillance program has been maintained on two shallow, warm water
prairie lakes and their tributaries. One of these lakes, Lake Madison,
is domestically polluted with the effluent from the sewage treatment
plant of Madison, South Dakota. The other, Lake Herman, is polluted due
to siltation caused by run-off from a large, intensively farmed
watershed. This surveillance program has resulted in comparisons of
chemical nutrients and biota of a heavily silted lake with those of a
relatively unsilted, but domestically polluted lake. The surveillance
program on the Lake Herman tributaries has also led to conclusions
regarding nutrient levels in successive spring run-offs.
During the summers of 1969 and 1970 a total of seventeen gabion-type
silt traps were constructed across the major feeder streams on the Lake
Herman watershed in order to retard lake siltation. The traps were of
several structural types and were constructed in locations with
different types of creekbeds and different water-flow rates in order to
evaluate which combinations of design and location were most effective.
The traps were successful as filters for large debris but had limited
success as silt-retaining devices. However, erosion occurred around or
under many of the traps thus diminishing their effectiveness.
This report was submitted in fulfillment of project 16010 DZK under the
partial sponsorship of the Office of Research and Monitoring of the
Environmental Protection Agency.
111
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CONTENTS
Section
I
II
III
IV
V
VI
VII
VIII
IX
Conclusions
Recommendations
Introduction
Materials and Methods
Experimental
Discussion
Acknowledgments
References
Appendices A-D
1
3
5
11
19
25
131
133
135
v
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FIGURES
1 Map of Lake Madison 6
2 Map of Lake Herman 8
3 Map of Lake Herman Watershed 9
4 A gabion basket. Top view and cross-section of gabion
in stream. 17
5 Variation of pH in Lakes Madison and Herman During 1968 29
6 Variation of pH in Lakes Madison and Herman During 1969 30
7 Variation of pH in Lakes Madison and Herman During 1970 31
8 Variation of pH in Lakes Madison and Herman During 1971 32
9 Variation of Alkalinity in Lakes Madison and Herman
During 1970 34
10 Variation of Dissolved Oxygen in Lakes Madison and
Herman During 1970 35
11 Variation of Silica in Lakes Madison and Herman During
1970 * 37
12 Variation of Silica in Lakes Madison and Herman During
1971 38
13 Variation of Ortho Phosphate in Lakes Madison and
Herman During 1970 39
14 Variation of Total Phosphorus in Lakes Madison and
Herman During 1968 41
11 Variation of Total Phosphorus in Lakes Madison and
Herman During 1969 42
16 Variation of Total Phosphorus in Lakes Madison and
Herman During 1970 43
17 Variation of Total Phosphorus in Lakes Madison and
Herman During 1971 44
vn
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18 Variation of Nitrate in Lakes Madison and Herman
During 1968 45
19 Variation of Nitrate in Lakes Madison and Herman
During 1969 46
20 Variation of Nitrate in Lakes Madison and Herman
During 1970 47
21 Variation of Nitrate in Lakes Madison and Herman
During 1971 48
22 Variation of pH, Dissolved Oxygen, and Temperature in
Lake Herman During 1970 50
23 Variation of Hardness in Lakes Madison and Herman
During 1968 51
24 Variation of Hardness in Lakes Madison and Herman
During 1969 52
25 Variation of Hardness in Lakes Madison and Herman
During 1970 53
26 Variation of Hardness in Lakes Madison and Herman
During 1971 54
27 Variation of Magnesium in Lakes Madison and Herman
During 1970 55
28 Variation of Magnesium in Lakes Madison and Herman
During 1971 56
29 Variation of Magnesium and Ortho Phosphate in Lake
Madison During 1970 58
30 Variation of Iron in Lakes Madison and Herman
During 1970 59
31 Variation of Iron in Lakes Madison and Herman During
1971 60
32 Variation of Manganese in Lakes Madison and Herman
During 1970 61
33 Variation of Manganese in Lakes Madison and Herman
During 1971 ' 62
Vlll
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34 Variation of Potassium in Lakes Madison and Herman
During 1970 64
35 Variations in Population Densities of Planktonic
Blue-Green Algae in Lake Madison During 1968 66
36 Variations in Population Densities of Planktonic
Blue-Green Algae in Lake Madison During 1969 67
37 Variations in Population Densities of Planktonic
Blue-Green Algae in Lake Madison During 1970 68
38 Variations in Population Densities of Planktonic
Blue-Green Algae in Lake Madison During 1971 69
39 Variations in Population Densities of Planktonic
Diatoms in Lake Madison During 1968 70
40 Variations in Population Densities of Planktonic Diatoms
in Lake Madison During 1969 71
41 Variations in Population Densities of Planktonic
Diatoms in Lake Madison During 1970 72
42 Variations in Population Densities of Planktonic
Diatoms in Lake Madison During 1971 73
43 Variations in Population Densities of Total
Phytoplankton in Lake Madison During 1968 74
44 Variations in Population Densities of Total
Phytoplankton in Lake Madison During 1969 75
45 Variations in Population Densities of Total
Phytoplankton in Lake Madison During 1970 76
46 Variations in Population Densities of Total
Phytoplankton in Lake Madison During 1971 77
47 Variations in Population Densities of Planktonic
Blue-Green Algae in Lake Herman 1968 79
48 Variations in Population Densities of Planktonic
Blue-Green Algae in Lake Herman During 1968 80
49 Variations in Population.Densities of Planktonic
Blue-Green Algae in Lake Herman During 1969 81
IX
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Page
50 Variations in Population Densities of Planktonic
Blue-Green Algae in Lake Herman During 1969
51 Variations in Population Densities of Planktonic
Blue-Green Algae in Lake Herman During 1970 84
52 Variations in Population Densities of Planktonic
Blue-Green Algae in Lake Herman During 1970 85
53 Variations in Population Densities of Planktonic
Blue-Green Algae in Lake Herman During 1971 86
54 Variations in Population Densities of Planktonic
Blue-Green Algae in Lake Herman During 1971 87
55 Variations in Population Densities of Planktonic
Diatoms in Lake Herman During 1968 88
56 Variations in Population Densities of Planktonic
Diatoms in Lake Herman During 1968 89
57 Variations in Population Densities of Planktonic
Diatoms in Lake Herman During 1969 90
58 Variations in Population Densities of Planktonic
Diatoms in Lake Herman During 1969 91
59 Variations in Population Densities of Planktonic
Diatoms in Lake Herman During 1970 92
60 Variations in Population Densities of Planktonic
Diatoms in Lake Herman During 1970 93
61 Variations in Population Densities of Planktonic
Diatoms in Lake Herman During 1971 94
62 Variations in Population Densities of Planktonic
Diatoms in Lake Herman During 1971 95
63 Variations in Population Densities of Total
Phytoplankton in Lake Herman During 1968 96
64 Variations in Population Densities of Total
Phytoplankton in Lake Herman During 1968 97
65 Variations in Population Densities of Total
Phytoplankton in Lake Herman During 1969 98
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Page
66 Variations in Population Densities of Total
Phytoplankton in Lake Herman During 1969 99
67 Variations in Population Densities of Total
Phytoplankton in Lake Herman During 1970 100
68 Variations in Population Densities of Total
Phytoplankton in Lake Herman During 1970 101
69 Variations in Population Densities of Total
Phytoplankton in Lake Herman During 1971 102
70 Variations in Population Densities of Total
Phytoplankton in Lake Herman During 1971 103
71 Variations in Population Densities of Copepods in
Lake Madison During 1970 106
72 Variations in Population Densities of Cladocerans
in Lake Madison During 1970 107
73 Variations in Average (Three Sites) Population
Densities of Copepods and Cladocerans in Lake
Madison During 1970 108
74 Variations in Population Densities of Copepods in
Lake Madison During 1971 109
75 Variations in Population Densities of Cladocerans
in Lake Madison During 1971 110
76 Variations in Average (Three Sites) Population
Densities of Copepods and Cladocerans in Lake
Madison During 1971 111
77 Variations in Population Densities of Copepods in
Lake Herman During 1970 113
78 Variations in Population Densities of Copepods in
Lake Herman During 1970 114
79 Variation in Population Densities of Cladocerans
in Lake Herman During 1970 115
80 Variations in Population Densities of Cladocerans
in Lake Herman During 1970 ]_]_£
XI
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81 Variations in Average (Four Sites) Population
Densities of Copepods and Cladocerans in Lake
Herman During 1970 ll
82 Variations in Population Densities of Copepods in
Lake Herman During 1971 118
83 Variations in Population Densities of Copepods in
Lake Herman During 1971 119
84 Variations in Population Densities of Cladocerans
in Lake Herman During 1971 12°
85 Variations in Population Densities of Cladocerans in
Lake Herman During 1971 121
86 Variations in Average (Four Sites) Population
Densities of Copepods and Cladocerans in Lake
Herman During 1971 122
87 Silt Trap No. 1 125
88 Silt Trap No. 13 125
89 Silt Trap No. 4 with debris collected along upstream
face. 126
90 Silt Trap No. 13 with debris collected along
upstream face. 126
91 Silt Trap No. 9 with side erosion (flanking). 127
92 Silt Trap No. 10 with erosion (undercutting). 127
93 Silt Trap No. 16 with upstream and downstream aprons. 128
94 Silt Trap No. 17 with downstream apron. 128
xn
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TABLES
Number Page
I Parameters for Metal Analyses by Means of
Atomic Absorption Spectroscopy 14
II Stock Standards for Metal Analyses 13
III Lake Madison Phosphorus Levels at Different
Locations 26
IV Variation of Nutrients in Lake Herman
Tributaries with Time of Year 28
V Measurements on Water Above and Below 129
Gabion Silt Traps
Xlll
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SECTION I
CONCLUSIONS
1. Spring run-offs from the Lake Herman watershed cause large increases
in iron, phosphorus and nitrogen in Lake Herman. Since these chemicals
are all algae nutrients, they contribute to the summer algal blooms and
thus to ensuing winter fish kills.
2.v The summer nutrient levels in Lake Herman are directly related to
the quantity and quality of the spring run-offs.
3. Successive spring run-offs on the Lake Herman watershed exhibit
decreasing levels of phosphorus, nitrogen and iron but increasing levels
of alkalinity and dissolved silica.
4. Lake Madison, which has a small watershed but which receives the
effluent from a sewage treatment plant, also receives influxes of phos-
phorus and nitrogen in the early spring.
5. Lake Madison exhibits conductivities twice as high and chloride
levels thirty times as high as those in Lake Herman.
6. Gabion silt traps exhibit a limited success as silt retaining
devices.
7- The selection of a proper site for the silt trap is of critical
importance for its effectiveness. Construction of gabion silt traps in
eroded creekbeds and countersinking measures result in erosion around
and under the silt trap.
8. Gabion silt traps are effective as filters for coarse debris.
9. During the three-year project, the phytoplankton densities were con-
sistently higher in Lake Madison (a sewage polluted lake) than in Lake
Herman (a silt polluted lake).
10. Diatom blooms and blue-green blooms were common during the spring,
summer, and fall in both Lake Madison and Lake Herman.
11. The highest densities of the blue-greens and the diatoms were
inversely related in both Lake Madison and Lake Herman.
12. The blue-green alga responsible for the major portion of all blue-
green blooms in Lake Madison was Aphanizomenon flos-aquae. Phormidium
minnesotense was second in abundance of the blue-greens but was sporadic
in occurrence. Species of Cyclotella dominated most of the diatom
blooms in Lake Madison. Species of Nitzschia and Stephanodiscus were of
secondary importance, but dominated some of the lighter blooms.
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13. The blue-green alga primarily responsible for the blue-green blooms
in Lake Herman was Aphanizomenon flos-aquae. Of secondary importance in
the blue-green blooms were species of Anabena and Microcystis. The
diatoms responsible for the diatom blooms in Lake Herman varied con-
siderably from year to year and sometimes from bloom to bloom within a
year. ..Species of Cyclotella, Surirella, Melosira, Nitzschia, and
Stephanodiscus were primarily responsible for the diatom blooms in Lake
Herman-.
14. Euglenoids and green algae were not significantly abundant in either
Lake Madison or Lake Herman during the summer, fall, and winter months.
In Lake Madison, very light blooms of euglenoids and green algae
occurred, each spring. Slight increases in green algae occurred
sporadically in Lake Herman, but these increases were brief and never
contributed significantly to algal blooms. Euglenoids were essentially
nonexistent in Lake Herman.
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SECTION II
RECOMMENDATIONS
Since this study has shown that important algal nutrients are added to
Lake Herman by the spring run-offs and their accompanying silt lp£ds:iji .it
is recommended that (l) conservation methods and proper farming prac- •
tices be employed across the watershed to reduce the levels of phos-
phorus, nitrogen, and silt in the run-off water and (2) further
investigations be conducted to develop silt retaining devices.
In projects dealing with lake siltation, it is important to know the
amount of silt entering the lake. In such projects, it is recommended
that devices, such as weirs and periodic sampling machines, be employed
for determining the amount of silt being carried down a watershed* From
such measurements, an estimate can be made of the amount of soil erosion
occurring in the watershed and the amount of silt entering the lake*
Only in this manner can the effectiveness of remedial measures be
quantitatively evaluated.
Since Lake Madison receives amounts of phosphorus and nitrogen in con-
siderable excess to those required for algal blooms, it is recommended
that the sources of these nutrients into the lake be curtailed.
In areas where extensive soil erosion is occurring, the gabion silt trap
may be used to some benefit as a secondary corrective measure. If the
gabion silt traps are used, it is recommended that (l) they are placed
in regions of a watershed where current velocity is low, (2) they not be
countersunk in the soil in any manner, (3) they be placed.in creekbeds
having a good vegetative cover, (4) aprons be constructed to prevent
soil erosion around the trap, and (5) they be placed in flat-bottomed
creekbeds.
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SECTION III
INTRODUCTION
In 1966 the biology staff of Dakota State College became interested in
studying and comparing two local lakes, one of which was heavily silted
and the other of which was relatively free of silt but received the
effluent from the local sewage treatment plant. In 1967 and again in
1968 government funds for such a project were applied for, first by Dr.
Harold Robinson and then by Dr. Clyde K. Brashier. In the second
instance, the application was successful and the grant was renewed for
two successive years. The project began June 1, 1968, and was completed
May 31, 1971, at a total cost of $64,901, seventy-one percent of which
was provided by the Federal Water Quality Administration. The primary
objectives of the project were (l) to compare chemical nutrients and
biota of a heavily silted lake, Lake Herman, with those of a relatively
unsilted, but domestically polluted lake, Lake Madison; and (2) to con-
struct silt traps in the Lake Herman waterways and determine the
effectiveness of these silt traps. The biology and chemistry depart-
ments of Dakota State College cooperated in this study which was first
directed by Dr. Clyde K. Brashier. In February of 1970, Dr. Brashier
took a leave of absence from the college and since that time Dr.
Constance Churchill, associate professor of chemistry, and Dr. Gordon
Leidahl, assistant professor of biology, have directed the study.
Lake Madison lies about three miles southeast of the city of Madison in
Lake County, South Dakota. The lake is approximately five miles long
and one mile wide and covers about 3200 acres. When full, the lake has
an average depth of twelve feet. A map of the lake is shown in Figure
1. The lake bottom is relatively free of silt. Lake Madison is fed by
tributaries draining a small watershed mostly in pasture, by springs,
and principally by Silver Creek via Bourne's Slough. Silver Creek, in
turn, is fed by Lake Herman during the spring and by the city sewage
lagoon, one mile above the lake during the entire year. The sewage
lagoon receives the effluent from the sewage treatment plant of Madison,
a city of about 6,000. This plant was constructed for a city of
5,000-10,000 population and is of the secondary treatment type involving
settling ponds and bacterial oxidation with a trickling filter system.
Until the summer of 1970, the sewage treatment plant was overloaded by
wastes from a meat packing plant dealing mostly in pork products. Lake
Madison also receives waste materials from year-around and summer
cottages along the lake shore and from nearby feedlots during spring
thaws and after heavy rains. From the middle of November to the middle
of April, the lake has an ice cover and sometimes there are winter fish
kills. For instance, there was a complete fish kill during the 1969-
1970 winter. There are heavy algal blooms and sometimes unpleasant
odors from the lake during the summer months, particularly July and
August.
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Bcnirn-e s
Silver
Creek
Figure 1. Map of Lake Madison
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The landowners around Lake Madison have organized into a group called
the Lake Madison Development Association. In order to reduce algal
blooms and ensuing fish kills, this group has treated the lake with
copper sulfate for the past several summers. They have also tried to
persuade farmers to move feedlots which drain into the lake and the city
of Madison to divert the effluent from the sewage treatment plant. In
order to be more persuasive the group has decided it must clean up its
own contributions to the pollution. Accordingly, they have formed a
sanitation district and are arranging for the construction of a sewage
collection system around Lake Madison.
Lake Herman lies four miles southwest of the city of Madison in Lake
County, South Dakota. It covers approximately 1,350 acres and, when
full, has an average water depth of six and one-half feet. A map of the
lake is shown in Figure 2. Lake Herman drains a watershed of fifty-six
square miles in which most of the land is cultivated fields of corn and
small grains. The watershed has numerous creeks which eventually .drain
into Lake Herman through three major feeder creeks. A map of the Lake
Herman watershed is shown in Figure 3. During the annual spring thaws
and after heavy rains, these creeks are swollen with water carrying a
heavy silt load. At present, the average silt depth in the lake is six
feet. There are very few cabins or homes around the lake, but there is
a popular state park on the east shore. From the middle of November to
the middle of April, there is an ice cover over the lake and there are
frequent winter fish kills. There was a fish kill during the 1968-1969
winter and only an early thaw and coal dusting saved the lake from a
fish kill during the 1970-1971 winter. During the remainder of the year
the lake is often turbid due to wind and wave action stirring up
sediments. Heavy algal blooms occur during the summer.
The college work on Lake Herman and its surrounding watershed, as well
as the importance of the lake and the state park in attracting tourists,
has provoked extensive civic interest. Farmers on the watershed who
employ conservation methods are recognized and civic groups often tour
the watershed to examine conservation methods being used and the silt
traps built by the college. In addition, a city and county group, the
Lake Herman Development Association, began dredging the lake in July of
1970 with the aid of federal, state, county and local funds. The college
is investigating the effects of the dredging with a. grant from the Office
of Water Resources Research.
In order to compare the chemical nutrients and biota of a heavily silted
lake with those of a domestically polluted lake, water samples were.
periodically collected from standard sites on Lake Madison and Lake
Herman. The water samples were analyzed quantitatively for a number of
chemical parameters and qualitatively and quantitatively for planktonic
algae and planktonic crustaceans. In addition, Silver Creek has been
periodically monitored at various points for chemical nutrients being
carried to Lake Madison, and the creeks in the Lake Herman water-shed
have been monitored during the spring thaws and after heavy rains for
chemical nutrients.
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Silver
Creek
Figure 2. Map of Lake Herman
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E
H
r—
Figure 3. Map of
Lake Herman Watershed
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During the summers of 1969 and 1970, seventeen gabion silt traps were
constructed on the Lake Herman creeks. Gabions are individual wire,
box-like structures which are filled with rocks, stacked, and wired
together to form the silt trap. The traps were of several structural
types and were constructed in locations of different creekbeds and water-
flow rates in order to evaluate which combinations of design and location
were most effective in retarding the silt flow. The traps were examined
for effectiveness and possible damage during June of 1970 and 1971. In
addition water samples were collected above, between, and below silt
traps during heavy run-offs for analyses of chemical nutrients and
filtered solids.
10
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SECTION IV
MATERIALS AND METHODS
Generally speaking, for the first year of the study, water samples were
analyzed chemically by Water and Waste Water Analysis Procedures issued
by the Hach Chemical Company and, for the last two years of the study,
by the procedures in FWPCA Methods for Chemical Analysis _of Water and
Wastes, 1967 and 1969. Samples for ammonia, nitrate, nitrite, and
silica analysis were collected in plastic containers and immediately
preserved with 53-55 mg mercury (II) chloride per liter of water sample.
After preservation the samples were refrigerated (0-5° C.) and analyzed
from one to twenty-one days later. Samples for metal analysis were
collected in plastic containers, filtered through Whatman #40 into
200 ml plastic containers, immediately preserved with twelve drops of
35-36% redistilled nitric acid, and analyzed within six months.
Dissolved oxygen samples were collected in glass BOD containers and
preserved immediately as described in Water and Waste Water Analysis
Procedures. The other analyses were on unpreserved samples collected in
plastic containers; the dates of analyses are available. Generally
speaking, pH was determined immediately or within two hours of collec-
tion; alkalinity within two hours; ortho phosphate, conductivity,
turbidity, and dissolved oxygen within six hours; total phosphorus,
hardness, and COD within twenty-four hours; chloride and filtered solids
within seventy-two hours.
All colorimetric analyses were determined with a Bausch and Lomb
Spectronic 20. All metal analyses since January, 1970, were determined
with a Perkin-Elmer Model 303 Atomic Absorption Spectrophotometer used
in conjunction with a Perkin-Elmer recorder readout and Perkin-Elmer 165
Recorder. Conductivities were determined throughout the project with a
Hach Model 2200 Conductivity Meter. Until November of 1969, conductivi-
ties were determined in ppm NaCl using the temperature compensator on
the meter and without salt standards. Since November, 1969, conductivi-
ties have been determined in a constant temperature bath at 25° C. as
described in the 1967 FWPCA manual. Turbidities have been determined
with a Hellige 160 Turbidimeter and a cell with a viewing depth of ten
mm, using the FWPCA recommended procedure. Secchi disk readings were
taken with a disk having a diameter of eight inches and divided into
quarters with alternating black and white markings.
Alkalinity, dissolved oxygen, COD, chloride and hardness have been
determined throughout this project by titrimetric methods. Alkalinity
has been analyzed by titration with approximately 0.02N sulfuric acid to
a pH of 4.5 as detected with a pH meter. Before September 19, 1969, a
50 ml sample was used; since that time a 100 ml sample has been used as
described in the FWPCA method. Dissolved oxygen levels have been deter-
mined throughout the project with a modified Winkler method using
phenylarsine oxide as the titrant and a starch indicator end point. The
procedure is described in the Hach Manual. Chemical oxygen demand (COD)
11
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has been analyzed by dichromate oxidation followed by back titration of
the excess dichromate with ferrous ammonium sulfate as recommended by
FWPCA. Chloride concentrations were determined until August of 1969 by
the Mohr Titration procedure described in the Hach manual. Since that
time chloride has been analyzed by the mercuric nitrate titration recom-
mended by FWPCA. Total hardness has been determined throughout this
project by titration with EDTA using a calmagite indicator as described
in the Hach manual.
Concentrations of nitrate, nitrite, silica, ortho phosphate, total phos-
phorus, ammonia, and potassiums before January, 1970, have been deter-
mined by colorimetric methods. Until the end of August, 1969, combined
nitrate and nitrite concentrations were determined by reduction of
nitrate to nitrite followed by diazotization of sulfanilamide and coup-
ling with an aromatic amine. The procedure used is described in the
Hach manual. Since that time nitrate and nitrite concentrations have .
been determined separately and on samples preserved with mercuric
chloride and filtered through Whatman #40. The concentration of nitrite
has been determined by essentially the same method described above and
recommended by FWPCA. Nitrate levels have been determined through a
color reaction with brucine sulfate as described by FWPCA. Silica
levelshave been determined on samples, preserved with mercuric chloride
and filtered through Whatman #40, by means of reaction with ammonium
molybdate. Ortho phosphate concentrations have been determined on
filtered samples by reaction with ammonium molybdate followed by stan-
nous chloride reduction as described in Standard Methods. Total phos-
phorus concentrations have been determined on unfiltered samples by
boiling 100 ml of sample, or an aliquot diluted to 100 ml, with 1.0 ml
of strong acid solution and 0.80 g of potassium persulfate for ninety
minutes, neutralizing with aqueous sodium hydroxide to a phenolphthalein
end point, and then proceeding as with ortho phosphates. All filtering
associated with phosphate analysis was done through Whatman #40 or #42
and a blank of distilled water, treated in every way like the samples,
was used to adjust the colorimeter to 100% transmittance. Before
January, 1970, potassium concentrations were determined by precipitation
with sodium cobaltinitrite followed by oxidation with dichromate and
colorimetric determination of the excess dichromate.
Since the beginning of this project, ammonia concentrations have been
determined by three different colorimetric methods. Until November,
1969, ammonia levels were determined on un'preserved, filtered samples by
direct Nesslerization as described in the Hach manual. From November,
1969, to April 24, 1970, ammonia levels were determined on samples pre-
served with mercuric chloride, distilled at a pH of 9.5, and Nesslerized
as recommended by FWPCA. Since April 24, 1970, ammonia concentrations
have been determined by a manual modification of the automated FWPCA
method. The solutions were prepared as described for the automated
method. Ten milliliter samples, preserved with mercuric chloride and
filtered through Whatman #40, a blank, and five standards ranging up to
2 mg/1 ammonia-N were simultaneously determined. To each standard,
blank, and sample, 4 ml of sodium hydroxide-EDTA were added, followed in
12
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rapid succession by 3 ml of sodium phenolate, 3 ml of sodium hypochlo-
rite and 4 ml of sodium nitroprusside solution. Each of these reagents
was added in such a manner that the solution was thoroughly mixed. The
blank, standards, and samples were then set in a water bath at 35-37° C.
for approximately twenty minutes and the color intensities determined at
630 millimicrons. Since April, 1971, mercuric chloride in the amount of
53-55 mg/1 has been added to the water used for standards, blanks and
dilutions in ammonia determinations.
General analytical procedures for all metal analyses since January,
1970, were obtained from Analytical Methods for Atomic Absorption
Spectrophotometry. Copper, iron, and manganese determinations have been
made by direct aspiration of filtered, acid-preserved samples using the
operating conditions listed in Table I. Mixed working standards in the
appropriate range were prepared from stock solutions on the day of
analysis. Sodium and potassium determinations required dilution of the
original samples. Eight mixed, working standards in the range of 20-160
mg/1 sodium and 5-40 mg/1 potassium were prepared on the day of
analysis. The standards and samples were then diluted by a factor of
approximately ten with a Model 250 Fisher Diluter. The analyses were
carried out using the parameters listed in Table I. Calcium and magne-
sium samples also required dilution. A blank and eight mixed working
standards in the range of 25-200 mg/1 calcium and 20-160 mg/1 magnesium
were prepared from stock solutions on the day of analysis. The stan-
dards, samples, and blank were diluted with the Fisher Diluter by a
factor of about forty. The diluted samples, standards and blank were
discharged from the diluter into 15 x 125 mm test tubes containing
0.5 ml of LaCl3 solution. The LaCl3 reagent was prepared by slowly
dissolving 29 g of 1,3203 in 250 ml of concentrated hydrochloric acid and
diluting to 500 ml with demineralized distilled water after the hydro-
chloric acid had cooled. Samples were then analyzed using the para-
meters in Table I. Reagents used for metal stock solutions and the
final concentrations of these stock solutions are given in Table II.
Table II Stock Standards For Metal Analyses
Metal
Sodium
Potassium
Calcium
Magnesium
Copper
Iron
Manganese
Reagent Used Concentration
NaCl, Primary Standard
KC1, Primary Standard
CaC03, Primary Standard
MgO, Reagent
Cu Sheet (100.056)
Fe Wire (99.95%)
MnCl2'4H20, Reagent
1000 mg Na+/l
100 mg K+/l
500 gm Ca^l
1000 mg Mgfyl
1000 mg Cutj/1
1000 mg FeWl
1000 mg Mntyl
Planktonic algae samples for quantitative enumeration were collected
with a one-liter Kemmerer water sampler. In deep regions of the lakes,
two liters of lake water were collected from the upper three feet of the
13
-------
Table I Parameters for Metal Analyses by Means of Atomic Absorption Spectroscopy
Na
K
Ca
Mg
Cu
Fe
Mn
Wavelenqth
5890 A
7665 A
4227 A
2852 A
3247 A
2483 A
2795 A
Ranqe
VIS
VIS
VIS
UV
UV
UV
UV
Slit
4
4
4
5
4
3
4
Burner Rotation
90°
0°
00
60°
0°
0°
0°
Scale
Expansion
IX
IX
IX
IX
10X
10X
10X
Chart Speed
20 mm/mi n
20 mm/mi n
20 mm/mi n
20 mm/mi n
5 mm/mi n
5 mm/mi n
5 mm/mi n
Flame
Oxidizing
Oxidizing
Reducing
Reducing
Oxidizing
Oxidizing
Oxidizing
Filter
Out
In
Out
Out
Out
Out
Out
-------
lake, two liters were collected from the middle of the water column, and
two liters were collected immediately above a distance of one foot from
the lake bottom* In shallow water, two liters of lake water were
collected from the upper three feet of the lake and two liters were
collected immediately above a distance of one foot from the lake bottom.
All of the water samples from one site were placed in a pail and brought
into the laboratory. The four or six liters of lake water were gently
stirred with a dipper to mix the sample thoroughly prior to concentrat-
ing it by column sedimentation (concentration by natural settling out in
a cylindrical column). Two one-liter columns (one-liter graduated
cylinders) were filled with lake water from a standard site. One hundred
milliliters of formalin (40% formaldehyde) were added to each column as a
killing and preserving agent. The columns were allowed to stand for two
weeks in a dark room. The upper 750 ml of fluid in each column was then
removed by means of glass tubing, a plastic hose, and a vacuum pump. The
remaining 250 ml in the column was stirred and transferred to a smaller
column (500 ml graduated cylinder) where it was mixed with a second 250 ml
that had been treated in the same manner and had come from the same site.
The column was allowed to stand for two more weeks in a dark room. At
this time, the upper 400 ml was removed by vacuum suction as before. The
remaining 100 ml sample was stirred thoroughly and transferred to a third
sedimentation column (100 ml graduated cylinder) where it was allowed to
stand for a third period of two weeks. The upper 80 ml were removed by
vacuum suction, and the remaining 20 ml were transferred to a vial. The
vial was labeled and sealed with wax until the sample could be counted.
The samples were stored in a dark cabinet at room temperature. The
planktonic algae were later enumerated to genus or species using a
Sedgwick-Rafter counting chamber and a compound microscope with a magni-
fication of 100X. Twenty fields of view were counted at twenty evenly
spaced, predetermined locations on the counting chamber.
Algal samples for qualitative enumeration were collected using a stand-
ard plankton towing with a No. 25 standard silk bolting cloth. They
were preserved in a preservative composed of six parts of water, three
parts of 95% alcohol, and one part of commercial formalin. Five milli-
liters of glycerin was added to each 100 ml of preservative to protect
the samples against loss from preservative evaporation.
Planktonic copepods and cladocerans were collected with a five-liter
Juday plankton trap. The samples were preserved with 70% alcohol and
were later reduced to a volume of twenty milliliters by column
sedimentation. Five milliliters of each concentrated sample were
counted using a five milliliter counting chamber of the Sedgwick-Rafter
type and a compound microscope. Magnifications of 40X and 100X were
used to count the copepods and cladocerans and to identify them to genus
and species.
One objective of this project was to devise relatively simple and
inexpensive silt traps that could be periodically desilted. Because of
low cost, flexibility, durability, and permeability features, gabion
baskets (or simply gabions) manufactured by Maccaferri Gabions of
15
-------
America, Inc. (55 West 42nd Street, New York) were selected as a basic
building material. The gabions are rectangular, wire mesh baskets (see
Figure 4) which are filled with rocks and wired shut. They are manufac-
tured in sizes ranging from approximately six to thirteen feet long and
from approximately one to three feet high, but they can be wired
together in series and used as "building blocks" to form various sizes
and shapes of stream improvement structures. Maccaferri gabions have
been used to construct weirs, groins, groynes, retaining walls, revet-
ments, channel lining and other such structures.
The gabions were shipped as unassembled, one piece units. They were
taken as such to the chosen site, unfolded, flattened, and stretched to
remove all kinks. The creases were arranged in the proper positions for
forming the box, and the side and end panels were folded into a vertical
position. The vertical edges were then joined at six inch intervals
with wire ties. When more than one gabion cell was present in a unit,
the diaphragm panels (partitions which formed the serial gabion cells)
were raised and fixed in the same manner. The heavy-gage selvage wire
at the top corner of each gabion was bent around the top mesh of the
adjoining sides. Thus, a rectangular box with an open lid was formed.
The gabions were then placed in position on a smooth, leveled surface
and adjacent gabions were fastened along each selvage. The gabions were
filled with rocks of five to twelve inches in diameter. For the higher
gabions, connecting wires between the sides and ends were placed across
every 9-12 inches of gabion height in order to maintain a rectangular
shape. For instance, with the eighteen inch high gabions, the basket
was filled to half of its height and two connecting wires running
lengthwise and two running widthwise were tied in, and then the basket
was filled. After all gabions in a trap had been wired together and
filled, the lid of each was folded into place. Each lid was secured
with lacing wire or with ties placed at six inch intervals along all
edges and"diaphragms.
A construction crew of three to five individuals was employed during the
summers of 1969 and 1970 to build the silt traps. Rocks were obtained
from an abandoned gravel pit by means of manual labor and a tractor with
a hydraulic, front-end loader. A dump truck was used to convey the
rocks to construction sites which were seven to ten miles away. At the
construction sites, a second tractor with a hydraulic, front-end loader
was used to unload the rocks. At times the tractor could be used to
deposit the rocks directly into the gabions, but manual labor often had
to be used.
-------
Figure £. Top: A gabion basket, Bottom: Top view and
cross-section of gabion in stream. (Taken from brochure
by Maccaferri Gabions of American, Inc.)
17
-------
SECTION V
EXPERIMENTAL
Lake Madison water samples for chemical analyses were collected from
three standard sites. These sites are referred to as West, Center, and
Southeast and are shown in Figure 1. All reported analyses are from
surface samples; during the winter of 1969-1970 some bottom samples were
collected in Lake Madison, but these showed no significant variation
from the surface samples in nutrient levels. Sampleswere collected
approximately every week during the summer, every two weeks during the
spring and fall (or as the ice break-up or formation permitted), and
once a month during the winter. Lake Madison samples were generally
collected in the late morning or early afternoon; the collection time
for each sample is available. The results of the chemical analyses of
Lake Madison water are listed in Appendix A. Note that there are two
parts of Appendix A, the first listing pH through nitrite values and the
second listing temperature through potassium values. During the three
years of this project water samples were collected irregularly from
Bourne's Slough, the sewage lagoon, various sites along Silver Creek,
and other Madison tributaries after heavy rains. The results of the
chemical analyses of these samples are listed in Appendix B, which is
also in two parts.
Lake Herman water samples for chemical and biological analyses were
collected from one to three standard sites during the first half of this
project and from four standard sites during the last half of this
project. These sites are referred to as North, Center, Dredge, and
Southeast and are shown in Figure 2. All samples were surface samples
and were generally collected in the middle of the afternoon; the time of
each sample collection is available. The results of the chemical
analyses of Lake Herman water are listed in Appendix C, which is in two
parts.
Water samples were also collected at the major Lake Herman inlets and
outlet and randomly across the watershed area during spring thaws and
after heavy rains. Some of the results of chemical analyses of these
Lake Herman tributary samples are listed in Table IV. The locations are
keyed to the Lake Herman watershed map shown in Figure 3. The capital
letters divide the watershed horizontally into one mile sections. The
numerals divide the area vertically into one mile sections. The first
small letter divides a section horizontally into quarter mile parts and
the second small letter divides a section vertically into quarter mile
parts.
Some core samples were collected from the bottom of Lake Herman during
1969 and 1970. These cores were sent to Arnold Gahler of the FWQA
Pacific Northwest Water Laboratory in Corvallis, Oregon. Under his
direction the interstitial water and sediment of these cores were
chemically analyzed. The results of these analyses are available from
19
-------
the authors. South Dakota State University at Brookings, South Dakota
in cooperation with the USDA maintains a research farm two miles no.rth
and one mile east of Lake Herman. The personnel of the research farm
maintain records of area temperatures and precipitation. This informa-
tion for the term of this project is also available from the authors.
The water samples which were collected from Lakes Madison and Herman
were taken at the same times and locations as the samples for. chemical
analysis. Lake Madison samples were collected from three standard sites
throughout the three-year project.. One site was selected at each end of
the lake, and one site was selected near the middle of the lake. These
sites have been designated West, Center, and Southeast and are shown in
Figure 1. The West site is near the major inlet of the lake (Silver
Creek via Bourne's Slough), and the Southeast site is near the only out-
let of the lake. Lake Herman samples were collected from one to three
standard sites 'during the first half of this project and from four
standard sites during the,last half of this project. One site is in the
southeast extension of the lake which is connected to the main portion
of the lake by a narrow but relatively deep channel. A second site is
located near the middle of the lake. A third site is at the north end -
of the lake near the largest inlet of the lake. A fourth site is in the-
east bay of the lake near the only outlet. Dredging was begun in this
bay during the summer of 1970. These seven standard sites were chosen
so that the nature of chemical nutrients entering the lakes and their
subsequent effects upon the biota of the lakes could be determined.
Samples were collected every week during the summer, every second week
during the spring and fall, and approximately every fourth week during
the winter.
Some of the results of the biological analyses of Lakes Madison and
Herman are presented in figures in the discussion section of this
report. Complete tables listing population densities for various species
of green alga, euglenoid alga, diatoms, and blue-green alga are available
from the authors.
Also available from the authors are. tables containing the population
densities of copepods and, cladocerans for Lakes Madison and Herman,
respectively, during 1970 and 1971. The population densities are listed
for the adults of each species of copepod and cladoceran, larval
copepods, total copepods, total cladocerans, and total copepods and
cladocerans. Also the average population density of copepods and the
average population density of cladocerans for the sites of each lake has
been calculated for each collection date.
During the summer of 1969, fourteen gabion silt traps were constructed
on two major creeks of the Lake Herman watershed. The design, location,
nature of the creek, and nature of the surrounding area of each trap is
described in detail in Appendix D. These fourteen traps are designated
as Traps No. 1-14 in this report. Basically, the fourteen traps are
single, vertical walls of rock-filled gabions. Most of them are in
20
-------
eroded creekbeds, and all of them are surrounded by uncultivated land
although several are near cultivated fields. The traps are three-eighths
to two and one-fourth miles from Lake Herman.
Examination of the traps during and after the spring and early summer
run-offs of 1970 revealed that several problems existed in the design of
the traps and in the choice of their location. Erosion of soil around
the silt traps was the major problem. Traps No. 10, 11, and 14 were
damaged by the removal of soil under them (undercutting), and Traps No.
8, 9, 10 and 11 were damaged by the removal of soil at their sides
(flanking). Soil erosion was particularly great in two traps (No. 8 and
11) that were built in creek bends and in one of the larger traps
(No. 14) that was built in an area receiving a large volume of water.
Note below that most soil erosion occurred where part of a trap was
countersunk in a creek bank. Silt Trap No. 8 was damaged by soil erosion
at the end of its main section where it was countersunk about one-half
foot in the creek bank. The hole was three feet wide and two feet and
four inches deep. Silt Trap No. 9 was similarly damaged by soil erosion
at the end of its main section where it was countersunk about one foot
in the creek bank. The hole was three and one-half feet wide and one
foot and eight inches deep. A second hold, which was two feet wide and
nine inches deep, was eroded under the trap where the wing and main sec-
tion meet. The erosion occurred where the main section was countersunk
about one foot in the creek bank. Silt Trap No. 10 was damaged by soil
erosion which caused two holes each of which was approximately two and
one-half feet wide and one and one-half feet deep. A hole was formed at
each end of the main section, where the end was countersunk about one-
half foot in the creek bank, and under the adjacent portion of each wing.
Silt Trap No. 11 was damaged by soil erosion at one end of its main sec-
tion, where it was countersunk about one-half foot in the creek bank, and
under the adjacent portion of the wing. The hole was two and one-half
feet wide and one and one-half feet deep. Silt Trap No. 14 was damaged
by soil erosion under the middle of the trap. The hole was seven feet
wide and two feet deep and was in the middle of the creekbed. The
gabions over the hole dropped about one foot into the hole. Soil erosion
also occurred in the middle of the creekbed immediately upstream from the
trap. The hole was approximately ten feet long, three feet wide, and one
and one-half feet deep.
Difficulty was also encountered in determining how long the silt traps
had to be to prevent water from flowing around their ends. Water was
backed up behind Traps No. 3, 4, 7, 8, 10, 11 and 12 to the extent that
it flowed around the traps. Because the ends of these traps were on
sodded soil, no erosion occurred, but the effectiveness of the traps was
undoubtedly reduced.
The two largest silt traps had yet another problem. Water spilling over
the central portions of Traps No. 13 and 14 caused the removal of soil
where it fell on the downstream side. Probably all of the fourteen traps
are not high enough to prevent water from flowing over portions of them
after heavy rainfall or heavy snow melts. Under such conditions,
21
-------
the effectiveness of the traps is reduced. This was noted especially
to be a problem of Traps No. 2, 11, 12, 13, and 14.
During the summer of 1970, three gabion silt traps (No. 15, 16 and 17)
were constructed, and'some of the damaged traps (No. 10, 11 and 14) were
repaired. The design, location, nature of the creek, and nature of the
surrounding area of each of the new traps is described in detail in
Appendix D. The nature of the creeks, the nature of the surrounding
area, and some of the design features are different than those of the
traps built in 1969. None of the traps are in an eroded creekbed, and
one trap is immediately below a cultivated field. The traps are 375
feet to two and one-half miles from Lake Herman.
Several changes were made in the design of the silt traps. Extensions
(aprons) of the traps' bases were constructed to slow water movement
through the lower portions of the traps and thus prevent or reduce soil
erosion. The aprons of two traps (No. 15 and 16) are two series of
gabions that are each one foot high and three feet and three inches wide.
The aprons extend for six feet and six inches both upstream and down-
stream and extend either the entire length of the trap or across most of
the middle portion. A third trap (No. 17) was built that has no apron
on the upstream side but has two "step-down" aprons on the downstream
side. The first "step-down" apron consists of gabions eighteen inches
high and three feet and three inches wide. Immediately downstream from"
it there is a second apron consisting of gabions one foot high and three
feet and three inches wide. Small rocks about 5 to 6 inches in diameter
were placed in the aprons and in the bases of the vertical walls', of.
these'three silt traps. One half of the bottom of Trap No. 15 was
covered with plastic screen.
To help prevent soil erosion around the silt traps, Traps No. 15, 16 and
17 were built in well-sodded creekbeds which have well-defined ravines
surrounding them. The traps extend entirely across the creeks and far
enough up the surrounding ravines that water will not flow around' the
traps under any circumstances. Only flat-bottomed creekbeds that merge
imperceptibly with the surrounding ravines were chosen as sites for the
silt traps.
Measures that could be taken to repair the damaged silt traps were quite
limited owing to their bulk and weight. Primarily, repair measures con-
sisted of packing rocks into the holes around the traps (Traps No. 10,
11 and -14) and constructing aprons both upstream and downstream (Traps
No. 13 and 14). The aprons were similar to those of Traps No. 15 and 16
except that gabions were not used and the rocks were placed only along
the middle portions of the traps. Approximately one foot of rocks was
piled upstream and downstream for distances of five feet to ten feet
from the vertical walls to form the aprons. Traps No. 10 and 11 had a
layer of rocks about one foot wide and one foot high placed along their
upstream junctions with their creekbeds. No corrective measures were
attempted for traps that had water flowing around their ends. Elaborate
22
-------
reconstruction would have been necessary to solve most of the problems
of this type.
Examination of the traps during June of 1971 revealed that the erosion
of soil around some of the traps was still a problem. Silt Traps No. 10
and 11 had further erosion in the same places as the previous year.
Approximately ten inches of soil had been eroded around the rocks which
had been used to repair the traps. Silt Trap No. 13, which had not been
damaged during the first year following construction, had a single hole
about twelve feet from the middle of the trap. The hole was not in the
creekbed as in the cases of the other traps, but was on well-sodded soil
at the bottom of the ravine and to one side of the creek. The hole was
two feet and two inches wide and one foot and four inches deep. Silt
Trap Nc. 14 was damaged once again by soil erosion under the middle of
the trap. Soil from an area fifteen feet wide and one foot deep was
eroded between July of 1970 and June of 1971. The gabions have dropped
into the hole to nearly fill it.
During the summer of 1971, the silt traps were examined to determine the
amounts of silt deposited behind them. Steel rods, which had been
driven in the ground immediately behind the traps when they were con-
structed, served as markers for determining the amount of silt present.
Silt deposits ranging from one-half inch to three inches in depth were
found behind six of the traps. Silt Traps No. 1, 2, 3, 7, 9 and 12 had
2, ir, 1-g-, 2, 2|-, and 3 inches of silt behind them respectively. No silt
was found behind Traps No. 4, 5, 6, 8, 10, 11, 13, 14, 15, 16 and 17.
However, the upstream side of nearly all of the traps had been densely
covered with roots, grasses, and pieces of wood.
During the spring run-offs of 1970 and 1971 water samples were collected
some distance above, just above, between and below silt traps. The
results and significance of these analyses are discussed in the next
section.
23
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SECTION VI
DISCUSSION
The chemical results listed in Appendices A-C show certain variations as
to location and season of the year. There are also interesting
differences between the two lakes which stem from the fact that one is
polluted from siltation and the other is polluted from domestic wastes.
These results are discussed below as to (l) differences due to location
in Lake Madison, in Lake Madison tributaries, in Lake Herman, and in
Lake Herman tributaries; (2) differences due to time of the year; and
(3) a comparison of each measured chemical parameter between the two
lakes.
The general flow of water in Lake Madison is from the west to the
southeast. An examination of the chemical data on Lake Madison water
with respect to location (see Appendix A) indicates little change in
most nutrient levels from one end of the lake to the other. Such
results would indicate that, either no significant quantity of nutrients
was lost to the atmosphere, sediments, and living organisms with move-
ment of water from the inlet to the outlet, or that other sources
around the lake replenished whatever was lost. Exceptions to this lack
of variation in nutrient level with location are the phosphorus levels,
both ortho and total. There is a consistent gradual decrease in phos-
phorus levels from the west end to the southeast end until the spring of
1970. Some values from Appendix A which illustrate this trend are
listed in Table III. Since March of 1970 the phosphorus levels have
been uniform over the lake or at least have not varied in a systematic
manner. This change to uniform phosphate levels could have been brought
about by either an increase in the supply from around the lake or a
decrease in the loss from inlet to outlet. Since there has been a
gradual decrease of phosphate in Lake Madison during the three years of
this project (see Figures 14-17), it would seem that a decrease in loss
of phosphate from inlet to outlet would be more reasonable. A possible
reason for this decrease in phosphate loss from the lake could be a
change in the level of phosphate entering from Bourne's Slough from a
level high enough to bring about precipitation and settling to a level
relatively stable in lake water. Possibly the slow down of production
during the spring of 1970 and closing in July, 1970, of the local meat
packing plant which overloaded the sewage treatment facility has
influenced the change.
25
-------
Table III Lake Madison Phosphorus Levels at Different Locations
Ortho Phosphate mgPO^/l Total Phosphorus mgPO^/l
Date West Center Southeast West Center Southeast
July 29, 1969 0.40 0.35 0.32
Aug. 26, 1969 0.68 0.43 0.40
Sept. 27, 1969 0.60 0.58 0.50
Oct. 26, 1969 0.11 0.07 0.05 0.81 0.45 0.34
Jan. 14, 1970 0.67 0.43 0.34 0.72 0.48 0.34
Feb. 14, 1970 0.81 0.56 0.52 0.92 0.65 0.57
An examination of the chemical analytical results on Lake Madison trib-
utaries (see Appendix B) indicates a gradual decrease of most nutrient
levels from the treated sewage to the sewage lagoon to Silver Creek at
the lagoon to Silver Creek below the lagoon to Bourne's Slough. This
decrease is not unexpected—undoubtedly many nutrients are lost to the
support of living organisms along the way. It would also be expected
that some phosphorus would be lost to the sediments and some nitrogen to
the atmosphere in the form of nitrogen gas and ammonia. The two para-
meters which do not follow this generally decreasing trend are pH and
dissolved oxygen, both of which tend to increase from treated sewage to
Bourne's Slough. In both cases, this increase is undoubtedly related to
the extensive plant growth, algae, etc., between the two points.
Lake Herman receives nutrients from three main feeder streams entering
the lake at different locations. Furthermore, the lake is often stirred
by wind and wave action. These factors would lead one to expect rather
uniform nutrient levels over the lake. An examination of the chemical
analytical results of Lake Herman water listed in Appendix C does indeed
indicate very little difference and no systematic differences in
nutrient levels with location in Lake Herman during the first two years
of this project. However, since early summer of 1970 the Southeast Bay
of Lake Herman has exhibited chemical nutrient levels inconsistent with
the remainder of the lake. As the map of Lake Herman, shown in Figure 2
indicates, the Southeast Bay is joined to the remainder of the lake by a
rather narrow opening. During the early summer of 1970, plants grew up
from the bottom of the lake at this opening and have served to retard
water flow between the two parts. An examination of the chemical
analytical results on the samples taken from the Lake Herman tributaries
indicates no regular differences in nutrient levels from one place on
the watershed to another. All three of the major feeder streams carry
particularly high levels of phosphorus and nitrogen into the lake.
Both^Lake Madison and Lake Herman follow the same seasonal trends in
nutrient levels. In very general terms, phosphorus, nitrogen and iron
increase at the time of the spring thaw and then rapidly decrease during
the late spring and early summer. Most other nutrients, however,
exhibit an opposite trend—decreasing sharply at the time of the spring
thaw, rising close to normal levels by early summer and then rising very
26
-------
slowly through the fall and winter to the next spring thaw. These
variations are borne out on the basis of the chemical data on the two
lakes and would also be expected after an examination of the chemical
data on the Lake Herman tributaries at the time of the spring thaw. The
latter have much higher levels of phosphorus, nitrogen, and iron than
the lake water but lower levels of most other nutrients.
An examination of the chemical data on the Lake Herman tributaries at
different times of the year indicates some interesting variations.
Table IV lists this data. The sites listed are near the three major
inlets and are keyed to the map shown in Figure 3. From these data it
is apparent that during the late winter and early spring of 1970 and 1971
the levels of ortho phosphate, total phosphorus, ammonia, nitrate, and
nitrite decreased with each successive run-off. On the other hand, the
alkalinity and silica levels increased with each successive run-off. The
increase in alkalinity and silica is probably related to an increase in
surface temperature as the season progressed. Generally, hardness, con-
ductivity and pH also increased with successive-early run-offs. Iron
concerntrations were not determined during the early run-off of 1970 but
showed increases during 1971 successive run-offs. Manganese decreased
during successive run-offs of 1970 but increased in 1971. In later run-
offs occurring during the summer, the above patterns were not followed.
Insufficient Lake Madison tributary samples were collected to allow any
general conclusions regarding seasonal variation in chemical nutrient
levels in these tributaries.
The pH of Lake Madison and Lake Herman has generally ranged from 7.5 to
9.5. Figures 5-8 depict how the pH in both lakes has varied during the
three years of this project. The data depicted is from Appendices A and
C; all Lake Madison values for a particular date are averaged as are
those for Lake Herman except the southeast sample from April of 1970 to
May, 1971. During this period, the southeast Herman pH, being somewhat
different than that of the remainder of the lake, is graphed separately.
It can be seen from these graphs that in both lakes the pH drops to its
lowest annual value during the spring thaw, rises during the summer and
gradually falls off during the autumn. The summer rise is accompanied
by irregular jumps which generally coincide in the two lakes. The
summer rise is undoubtedly related to heavy algal populations. The pH,
on the other hand, by restricting the amount of free carbon dioxide in
the lake water, would influence the species of algae which can thrive.
In both lakes the pH tends to reach a maximum in July or August. It is
interesting that Lake Herman has had a higher pH than Lake Madison
except during the year after the large spring run-off of 1969. There was
a record snow fall during the winter of 1968-1969 and an ensuing
particularly heavy spring run-off. Apparently, Lake Herman, being a
smaller lake and having a much larger watershed, experienced the effects
of the run-off more than Lake Madison.
27
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Table IV Variation of Nutrients in Lake Herman Tributaries with Time of Year
ro
oo
Mar. 3, 1970
G7ca
I7dc
J8ca
Apr. 4, 1970
G7a
I7dc
J8ca
Apr. 23, 1970
G7ca
I7dc
J8ba
Feb. 17, 1971
G7ab
I7dc
J8ca
Mar. 11, 1971
G7ab
J8ca
Mar. 29, 1971
I7dc
J8ca
'c o
• H O
•— 1 CO
CO O
X
r— 1 CT)
< B
49.6
40.7
46.1
68.2
47.6
58.4
117
123
126
62.4
36.5
46.7
50.2
50.8
47.4
61 .-9
i — i
CO O
0 -H
•H CO
rH
•H m
to S
7.78
8.02
7.26
9.7
8.7
9.3
18.6
15.9
10.6
2.3
3.5
3.3
2.6
2.7
10.0
12.2
CD
-p
ro
Q,
in
o
•^
o O
J^ d.
-p
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2.14
1.25
1.46
1.13
0.67
0.50
0.01
0.14
0.13
3.34
1.61
1.15
1.17
0.71
0.56
0.63
D
O
a
0
^-
.-H O
co CL,
-p
O CD
H S
3.97
2.15
3.04
1.48
1.73
1.59
0.11
0.33
0.66
6.29
1.86
2.63
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1.60
i— i
CO 1
•H ro
C PC
O 2
S O")
< S
0.61
0.68
0..64
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0.22
0.00
4.14
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i— i
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-p ro
co O
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^ 6
1.46
1.18
1.44
1.07
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0.125
0.608
0.780
1.225
1.230
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0.645
0.575
i— t
0) |
-P CM
•H O
m 2:
-p
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^ 3.
151.7
111.7
139.8
69.1
104.8
93.8
3.4
8.1
6.4
78.1
44.9
63.4
71.8
68.9
74.0
85.0
-------
9.5-f
9.0-h
8.5 +
ft
8eO-
7.5
.Figure 5. Variation of pH in Lakes Madison and Herman During 1968. -I
co
Hi
1-3
Lake Madison
Lake Herman
fn
cd
I
h
PH
0)
0
0
1-3
I
>»
H
I
bO
0)
-P
o
o
I
>
o
O
-------
9.5--
8*5--
CO
o
7.5-
Figure 6» Variation of pH in Lakes Madison and Herman During 1969.
f
-------
00
10.
p Figure 7. Variation of pH in Lakes Madison and Herman During 1970. ~i
9.5+
9.0+
ft
8.5+
8.0+
7.5
Lake Madison
Lake Herman
Southeast Lake Herman
x
"- N
0
fl c- &
03 O^ >
cd
S
1
(D
O
?l
1-3
1
>>
H
Fl
•-3
1 1
W> ft
?! Q>
o
s
1
o
Q)
Q
-------
CO
ro
P.
_ Figure 8. Variation of pH in Lakes Madison and Herman During 1971. _,
9.5--
9.0-
B.5--
8.0- -
7.:
7.0
!
fi £*- f
l~9 T- ft*
!
h
a
j
0}
I
{>»
H
Lake Madison
Lake Herman
Southeast Lake Herman
I
bO
I
ft
CO
-P
o
o
I
O
-------
The alkalinity of Lake Madison and Lake Herman has generally ranged from
100-250 mg/1 CaC03. Figure 9 shows the seasonal variation of alkalinity
in both lakes during 1970. The data graphed is taken from Appendices A
and C; the values for each lake represent averages. Since the summer of
1970 the alkalinity level in Southeast Lake Herman has been quite
different than that in the remainder of the lake, and it is graphed
separately. Figure 9 represents a rather typical year and, as can be
seen, the alkalinity levels in both lakes reach a minimum at the time of
the spring run-off, rise rapidly during the spring, remain fairly level
or drop slightly during the summer, rise slowly during the autumn and
more rapidly after the ice freeze. Both lakes follow the same general
trend but Lake Herman experiences changes to a greater degree than Lake
Madison. The sharp drop in the alkalinity of Southeast Lake Herman dur-
ing the summer of 1970 is probably related to heavy plant growth.
Dissolved oxygen levels in both Lake Madison and Lake Herman range from
near zero to fifteen parts per million. Figure 10 shows the changes in
dissolved oxygen in the two lakes during 1970. The data graphed repre-
sent averages of the results listed in Appendices A and C. Typically,
dissolved oxygen levels are at a minimum during the winter, rise sharply
during the spring, fluctuate widely during the summer and level off in
the fall. The low dissolved oxygen level in Lake Herman during February
of 1970 corresponds to a fish kill. There was a corresponding low in
Lake Madison during February of 1969, which was also accompanied by a
fish kill. The wide fluctuations in dissolved oxygen levels during the
summer undoubtedly correspond to changes in plant growth. However, the
fact that these fluctuations coincide in the two lakes would suggest
some other more basic factor which the lakes would have in common, per-
haps temperature.
Measurements of chemical oxygen demand (COD) have been made only during
the last year of this project. On the basis of that data, both lakes
seem to follow the same general trend, a slight rise at the time of the
spring run-off, a decrease to an annual minimum during May and early
June, then a rise with fluctuations to a maximum in August, followed by
a decrease during the autumn to a level which is rather constant through
the winter. Thus far, Lake Madison and the Southeast Bay of Lake Herman
reach higher maxima of COD levels than the remainder of Lake Herman, but
for the most part the level in both lakes has remained between 25 and 75
mg/1 COD.
Conductivity levels in both Lake Madison and Lake Herman follow the same
pattern as alkalinity—a sharp decrease during the spring run-off, a
rapid rise during the later spring to a level which remains fairly con-
stant during the summer, and a slowrise during the autumn and winter.
Except for the minimum at the .spring run-off, Lake Herman conductivities
range from 700-1200 jumhos/cm at 25° C. whereas Lake Madison conduc-
tivities range from 1450-1850 jumhos/cm at 25° C. The higher Lake
Madison values would result from the sewage effluent containing city
water. Madison city water is very hard and, in most homes, is put
through a water softener which uses salt. This factor would also
account for chloride differences between the two lakes. Lake Madison
33
-------
CO
250--
200--
o
o
sJ
o
150--
rt
•H
H
a
100--
50--
0 *~
o
fl £>
Figure 9. Variation of Alkalinity
in Lakes Madison and Herman During 1970,
Lake Madison
Lake Herman
Southeast Lake Herman
0>
I
cd
i
^
ft
I
!>>
Ki
-------
Figure 10, Variation of Dissolved Oxygen
in Lakes Madison and Herman During 1970.
20- -
Lake Madison
Lake Herman
co
01
CM
O
bo
C
O
m
m
-------
has chloride levels around 150 mg/1 Cl whereas Lake Herman chloride
levels are around 5 mg/1 Cl. The chloride level in Lake Madison
experiences seasonal variation like those of conductivity and
alkalinity. However, the chloride level in Lake Herman is very close to
constant the year-around, experiencing only a very slight decrease at
the time of the spring run-off and a small increase after the ice
freeze.
Dissolved silica measurements have been determined only since January of
1970. Figures 11 and 12 show the changes in silica levels -in Lake
Madison and Lake Herman during 1970 and 1971. The data used for the
graph represent averages of the results listed in Appendices A and C.
Again, since the Southeast Lake Herman sample has varied.somewhat from
the remainder of the lake during the past year, it is graphed
separately. The seasonal variation in silica follows the same broad
pattern in both lakes but this pattern is quite different than that for
any of the other chemical parameters. An examination-of Figures ,11 and
12 indicates that silica levels drop at the time of the spring run-o'ff
(particularly in Lake Herman) and continue to drop even more rapidly
into early May, then rise sharply and level out until October when there
is another drop. These spring and fall decreases correspond with diatom
blooms.
Ortho Phosphate measurements have been determined since October, 1969.
The normal levels in both/lakes range from 0.1-0.5 mg/1 PO^. Figure 13
shows the seasonal changes of ortho phosphate in Lake Madison and Lake
Herman during 1970. The data used for the graph represent averages of
the results-listed in Appendices A and C. Again, since the Southeast
Lake Herman sample varied somewhat from the remainder of the lake during
the last year of the project, it is graphed separately from June to the
end of the year. As may be noted, there is a sharp rise in ortho phos-
phate levels in both lakes at the time of the spring run-off. This rise
is followed by "a decrease to a near minima in late April and'early May,
summer fluctuations, and a fairly constant level during the fall and
winter months. The summer fluctuations do not always coincide between
the two lakes. 'The rise in 'ortho phosphate in Lake Herman in July of
1970 corresponds to the beginning of1 dredging activity on that lake.
Note the Southeast Bay of Lake Herman also' shows this rise but it is
delayed from that of the remainder of the lake. This delay is reason-
able when the restriction of water flow to this area is considered.
Total-'phosphorus has been determined on both lakes since the beginning
of,s the project. Seasonal variations of total phosphorus in both lakes
during 1968, 1969', 1970 arid "1971 are shown in Figures 14-17 respectively.
The data used for the graphs represent averages of the results listed in
Appendices A and C. Since Southeast Lake Herman was not uniform with
the remainder of the lake the last year of this project, it is graphed
separately during that time. It may be noted that the normal level in
both lakes ranges from 0.3 to 1.5 mg/1 PO^. Both lakes follow the same
seasonal pattern—an increase during the spring run-off, a decrease in
late April and early May to minimal values, summer fluctuations, and a
36
-------
Figure 11. Variation of Silica
co
-J
S
fciO
03
H
•rl
CQ
30.0-
24.0-
1 o . 0"
12.0-
6.0-
0.0
i
<
i-
«. * J, ^ bfc^ V*« 1 1 • • t-fc -^ •*• <-*• v ^. v-.
_in Lakes Madison and Herman During 1 97C
Lake Madison
— — Lake Herman
Southeast Lake Herman
y
* /
'\ /
\ /
' '^ /
i *• /
; x /
x- /
»• / /
; v / /
\ \ f
\ ! \ / /
^ •' * A / "'"
•\ 1 \ ^ / -A
\ ! \ .' 'A A .• '•
\ 1 \ / \v ^.// / :
X i \ / •• .--•"'•• / .- =
\i \ '""" 'i/ \
v \ / /••
* / / '••
V / \
^^-~^ I \!
i iii i i
O »
3C-,£» ^ ^ !>» S H
SOO 03 P* oJP P
a t- p<4 s «>j a 1-3 h»
/
I
bO
P3
<4
!
ft
o>
CO
+>
o
o
!>
o
"J2J
o
ffi
n
-------
oo
03
36,0-4-
30.0+
Oi
o 24.0-
CO
bo
05
H
•H
CO
18.0+
12.0+
6.0
Figure 12e Variation of Silica
in Lakes Madison and Herman During 1971.
a
:/
0)
-—— Lake Madison
Lake Herman
• Southeast Lake Herman
I
{>>
H
P.
-------
2.5 +
Flgure 13. Variation in Ortho Phosphate
in Lakes Madison and Herman During 1970e
CO
vO
2,0+
H
•si
O
1.5-
(D
-P
•Lake Madison
Lake Herman
Southeast Lake Herman
CO
o
O
.Jd
•p
^
o
1.0+
0.5 +
080 L
rt
cd
0)
-------
fairly constant level during the fall and winter months. As with ortho
phosphate, the rise of total phosphorus in Lake Herman in July of 1970
corresponds to a dredging project. This project is being studied with
the aid of a grant from OWRR—a report will be made on that study during
the summer, 1972. The summer fluctuations on the two lakes do not
always correspond. They are probably due primarily to algal bloom
cycles. It is interesting to note that Lake Madison had higher levels
of total phosphorus than Lake Herman until after the heavy spring run-
off of 1969. The 100% increase in total phosphorus levels in Lake
Herman from the summer and fall of 1968 to the corresponding time of
1969 may be attributed to the heavy run-off with its accompanying silt
load in the spring of 1969. From Figure 16, it may be seen that after
the light 1970 spring run-off the level of total phosphorus in Lake
Herman began falling below that of Lake Madison only to increase rapidly
with the commencement of dredging activities. Examining Figures 14-17
with regard to total phosphorus levels in Lake Madison indicates that
this level has undergone an overall decrease during the three years of
this project.
Nitrate levels were determined for the first fifteen months of this pro-
ject as combined nitrate and nitrite and since that time as just
nitrate. The seasonal nitrate levels in both lakes during 1968, 1969,
1970 and 1971 are depicted in Figures 18-21 respectively. The data used
for these graphs represent averages of the results listed in Appendices
A and C; again, since the Southeast Lake Herman sample varied somewhat
from the remainder of the lake the last year of the project, it is
graphed separately during that time. It may be noted from an examin-
ation of Figures 18-21 that seasonal changes in nitrate levels in both
lakes follow the same general pattern as the phosphorus levels. A sharp
increase during spring run-off is followed by a decrease to near minimal
values and summer fluctuations which, in the case of nitrate, continue
into the fall. The summer and fall fluctuations are probably related to
the algal bloom cycles. It is of interest to note the maximum nitrate
levels reached during the spring run-offs. It may be concluded from the
maximum of each year that Lake Herman was affected by run-off to a
higher degree than Lake Madison. It is also apparent that larger run-
offs (1969) caused higher maxima and longer recovery times for the lake.
For instance with the largest run-off in 1969, the Lake Herman maxima
reached 2.75 mg/1 NC>3~N and it was the middle of July before the nitrate
level had fallen to near zero whereas in the lightest run-off year, 1971,
the Lake Herman nitrate level reached a maxima of less than 0.85 mg/1
N03~N and had returned to a near zero level by the middle of April.
The separate nitrite concentrations determined since the fall of 1969
and ammonia levels in the two lakes follow the same general pattern as
the nitrate- levels. The high ammonia levels during the fall of 1968
and 1969 are most likely invalid, arising from the analytical method
used at that time—direct Nesslerization of fall water samples from both
lakes tended to produce turbid suspensions. The simultaneous rise of
ammonia and nitrite during late May and early June of 1970 in Lake
Madison is probably related to a biological change. Both ammonia and
40
-------
o
P-,
2.5 +
Figure 14« Variation of Total Phosphorus
in Lakes Madison and Herman During 1968.
2.0 +
Lake Madison
Lake Herman
a
Dl
pi
ft
ra
o
-P
O
1.5 +
1.0 +
0.5 +
0.0 u
H
oj
1-3
co
I
03
cd
J
1>»
H
ttO
pi
ft
-------
2.5 +
Figure 15. Variatien of Total Phosphorus
in Lakes Madison and Herman During 19&9.
—Lake Madison
Lake Herman
r-J
•si
O
2.0 +
ia
PI
ft
ra
o
H
cd
-P
O
E-l
1.5 +
1.0 +
0.5 +
0.0
a
a)
•-a
i
»
H
ft
0)
CO
4>
O
O
o
525
o
0)
-------
3.754-
Figure 16. Variation of Total Phosphorus
in Lakes Madison and Herman During 1970.
GO
O
AH
bO
CO
o
fi
P-i
-p
O
in
3.004-
2.254-
1.50 +
0.754-
Lake Madison
Lake Herman
Southeast Lake Herman
V
-------
3.75-
3.00-
H
\
O
PH
W)
S 2.25-
to
pi
0
pl
W
01.50-
P-.
r-\
cd
•P
0
>
8.20
/\
/ \
/
/'
/
/
» -*. ^ %*.*• v
in Lakes
\
l\
\ \
•-. \
'•. \
\ \
\\
\ \
•-. \
* '•• \
\ \
\ \
A \ \
A v
/ \ v
/ \ ^
0.75--
0.00 L
Figure 17. Variation of Total Phosphorus
in Lakes Madison and Herman During 1971.
•Lake Madison
Lake Herman
Southeast Lake Herman
I
V™
KJ o a)
I
fn
I
fH
I
r^j
ed
I
0)
rt
I
!>»
H
1
bfl
p(
--. <4
1
P<
0)
CO
1
•p
o
o
1
t>
0
I
o
(D
-------
r Figure 18. Variation of Nitrate in Lakes Madison and Herman During 1968,
2.0+ ^
1.6 +
82!
I
1.2 +
0>
•p
•P
•H
a
0.8 +
0.4- +
0.0 L
to
fl vO
Oj O
-------
figure 19. Variation of Nitrate in Lakes Madison and Herman During 1969.
2« 75 i
\
2.0-
1 .6-J
\
t3
•^ I
1
cT 1.2J
E5
tfl
3
CD I
4J 1
ca 0.84
h
•*
S
0.44
o_n [
p-.,.
^
r\
\
I
1
1
I I
r I '
l i
1
1 i
1 i
1 !
I i
1 i
1 ,'
/ '
" //
/ /'
/ /
/ /
/ /
/ /
- /
//
//
/
jj
- 1
i
Lake Madison
•Lake Herman
Cd ON
CO
o
O
O
O
CD
-------
Figure 20. Variation of Nitrate in Lakes Madison and Herman During 1970.,
1.0-
Lake Madison
Lake Herman
Southeast Lake Herman
-------
00
figure 21. Variation of Nitrate in Lakes Madison and Herman During
1.0--
0.2--
0.6--
-------
nitrite levels tend to be slightly higher in Lake Madison than in Lake
Herman.
The temperature variation in both lakes through this project is what
would be expected from the season of the year and the air temperature.
There are fluctuations during the summer months which coincide very
closely between the two lakes. One difference between the lakes is that
Lake Herman tends to warm up faster in the spring, cool off faster in
the fall, and experiences summer fluctuations to a greater degree than
Lake Madison. This difference is not surprising considering that Lake
Herman has a much smaller total water volume.
Figure 22 shows a plot of the seasonal variation in temperature, dis-
solved oxygen and pH in Lake Herman during 1970. The fact that the sum-
mer fluctuations in these three parameters all coincide is indicative of
at least an indirect relationship between them.
Secchi disk readings and turbidities in the two lakes generally coincide
as would be expected; when secchi disk readings decrease, turbidity,
increases and vice versa. The time of greatest water clarity, greatest
secchi disk readings and lowest turbidity, tends to occur during the
winter and also in early June. The times of lowest water clarity occur
in July and August, at the height of the algal blooms, and in the spring,
during the spring run-offs. Except for the two periods of maximum
clarity, secchi disk readings tend to be in the range of 20-120 cm.
From July, 1969, to May, 1971, secchi disk readings on Lake Madison have
shown an overall increase whereas those on Lake Herman have shown an
overall decrease.
Concentration levels of hardness and calcium follow the same seasonal
pattern in both Lake Madison and Lake Herman. The seasonal changes of
hardness in the two lakes during 1968, 1969, 1970 and 1971 are shown in
Figures 23-26 respectively. The data used for the graphs represent
averages of the results listed in Appendices A and C. Since the South-
east Lake Herman sample varied somewhat from the remainder of the lake
the last year of the project, it is graphed separately during 1970 and
1971. Through most of the year hardness -levels in Lake Madison range
from 540 to 850 mg/1 CaCOs while those in Lake Herman range from 260 to
720 mg/1 CaCO^. Lake Madison also has a correspondingly higher level of
calcium. Both hardness and calcium follow a seasonal pattern like that
of alkalinity—a sharp decrease at the time of the spring run-off,
followed by an increase during April and May to a level which remains
nearly constant through the summer and fall,, and a rise after the ice
freeze. The level of hardness and the time to rise to a'constant
level after the spring run-off is related to the amount' of the spring
run-off. Note the lower hardness levels and the longer recovery time
after the heavy spring run-off of.1969.-(see Figure 24). There seems to
be consistently a slight decrease in the hardness level in both lakes
during the latter part of August.
The concentration of magnesium in Lake Madison and Lake Herman has been
measured since January of 1970. Figures 27 and 28 depict the seasonal
49
-------
01
o
Figure 22. Variation of pH,
Dissolved Oxygen, and
Temperature in Lake Herman
During 1970,
Dissolved Oxygen
Temperature
-.. J
-------
CJl
750-
600-
H
\
c^
O
O
3)
o 450-
HO
a
03
01
S 300-
-a
P
oj
W
150 -
0
c
a
M
La.
— — La:
M
•»
U 1 1
to
3vO rQ ^
i o a>. a]
Figure 23. Variation of Hardness
in Lakes Madison and Herman During 1968,
Lake Madison
Lake Herman
I
0)
H
PI
1
HO
CD
03
I
>
o
o
0)
-------
900 4-
750 4-
o
o
o 600 -J-
en
to
w
w
a 450
h
ed
300
150
rt
ed
CD
i
k
a
a
Figure 24. Variation of Hardness
in Lakes Madison and Herman During 1969,
—— Lake Madison
—-— Lake Herman
^.x
J)
El
pi
I
HO
CO
O
o
o
12;
o
(D
-------
CJl
to
o
o
at
0
ra
a>
a
Tf
fH
0}
750 +
Figure 25. Variation of Hardness
in Lakes Madison and Herman During 1970,
600 +
450+
300+
150+
Lake Madison
Lake Herman
Southeast Lake Herman
td
0)
i
h
o3
I
fn
I
t>.
oj
pi
hs
I
uo
P<
0)
CO
-p
o
o
o
-------
900 --
750 --
o
o
<§ 600 --
en
bO
03
a 450
cd
W
300 --
150
.
\ •-.
\ \
\ \
\ "••
\ \
\ \
Figure 26. Variation of Hardness
in Lakes Madison and Herman During 1971.
Lake Madison
Lake Herman
Southeast Lake Herman
I
fH
OJ
0)
0
2
1-3
I
t>>
H
bO
1
Pi
CD
CO
•P
0
o
t>
o
o
-------
01
en
2004-
1604-
iH
bo
bo 1204-
01
o>
fl
W>
cd
so4-
4-04-
0 L
o
a tr-
ot O^
1-9 t-
Figure 27. Variation of Magnesium
in Lakes Madison and Herman During 1970.
Lake Madison
Lake Herman
Southeast Lake Herman
-------
200+
Figure 28. Variation of Magnesium
in Lakes Madison and Herman During 1971.
160-1-
bo
S
Lake Madison
Lake Herman
"Southeast Lake Herman
(Jl
§
•H
to
-------
changes in magnesium levels in the two lakes during 1970 and 1971. The
data graphed represent averages of the results listed in Appendices A
and C. Southeast Lake Herman is graphed separately during the past year.
The magnesium levels in Lake Madison generally range from 50 to 110
•mg/1 Mg while those in Lake Herman are somewhat lower, 25-75 mg/1 Mg.
The seasonal changes in both lakes follow the same pattern. There is a
sharp decrease at the time of the spring run-off followed by a continued
decrease into late April or early May and a rise in early June. There
are sharp fluctuations during the summer and fall but the level in
November is the same as that in June. With the ice freeze, there is a
steady rise in magnesium levels until the next run-off. The summer and
fall fluctuations generally coincide in the two lakes but occur to a
greater degree in Lake Madison. There is an inverse correlation between
magnesium and ortho phosphate levels in both lakes. Figure 29 shows
this relationship between magnesium and ortho phosphate in Lake Madison
during 1970. Considering the insolubility of magnesium phosphate salts,
this correlation is not surprising.
Copper levels in both lakes normally range from 0-0.01 mg/1 Cu. Between
these levels, the concentration in both lakes seems to fluctuate widely
for no apparent reason. It is interesting that Lake Madison contains no
more copper than Lake Herman in spite of the fact that thousands of
pounds of copper sulfate have been used during the past three years as
an algicide in Lake Madison. It seems likely that the high pH causes
precipitation of this copper and removal to the sediments.
Concentrations of soluble iron in Lake Madison and Lake Herman have been
determined since January of 1970. Figures 30 and 31 show iron concen-
trations in the two lakes through 1970 and 1971 respectively. The data
used for the graphs represent averages of the results listed in
Appendices A and C. Since the Southeast Lake Herman sample varied some-
what from the remainder of the lake the last year of the project, it is
graphed separately during that time. The iron level in both lakes
generally ranges from 0.01-0.06 mg/1 Fe. As may be noted in Figures 30
and 31, Lake Herman experiences a significant increase in iron at the
time of the spring run-off whereas Lake Madison experiences little or no
increase at this time. This difference may reasonably be attributed to
the silt load of the spring run-off waters entering Lake Herman. The
iron levels in both lakes fluctuates through the spring, summer and fall.
The summer and fall changes seem to coincide between the two lakes.
The seasonal changes in manganese levels in Lake Madison and Lake Herman
during 1970 and 1971 are depicted in Figures 32 and 33. The data used
for graphing represents averages of the results listed in Appendices A
and C. Since 'Southeast Lake Herman was not uniform with the remainder
of the lake the last year of this project, it is graphed separately
during that time interval. Soluble manganese levels, like those of
silica, do not really fit into either of the two general patterns
followed by most other chemical parameters. Lake Madison and Lake
Herman have experienced manganese values as low as 0.01 mg/1 Mn and
higher than 1.0 mg/1 Mn. The maximum level seems to occur just prior to
57
-------
CD
bo
a
B
O
O
CM
O
-P
s
2
•H
03
-------
en
Figure 30. Variation of Iron in Lakes Madison and Herman During 1970.
0.25+
0.20 +
H
"5r 0.15+
0.10 +
0.05 +
0.00
»
H
\ vT^-^*
\\ ,- -
': \ /'•
•• v ••
1 * ;
W i
hO ft
Pi CD
-aj CO
-v - /
>[. ^- --^
V'
x ••*
V .-'
N-.-'*'
I 1
•P !>
o o
o s
...-•-•"
1
o
0)
Q
-------
Figure 31 • Variation of Iron in Lakes Madison and Herman During 1971
ON
O
0.25-
0.20-
H
^ 0.15-
fc<
tjf
a
S 0. IO-
1-l
0.05-
0.00
- i
: •.
;.\ \
•r, \
II \\
•t \ \
it \ \
I1 \\
! \\
I ^
/ v .
/ \\
i \'--
a \\
i= A. \:
1* f ^^S. \*-
!/ NV^S'-'X. /'
— —^7 ^^-^^-«*J!i>f^
***^*. /
ill!
r- '
$3 C~- rQ ^ h K>» i
td O^ Q) cd ft nJ i
Lake Madison
Lake Herman
Southeast Lake Herman
H
pf
P.
(D
•p
o
o
J>
o
O
(3)
Q
-------
1.0 +
Figure 32. Variation of Manganese
in Lakes Madison and Herman During 1970.
H
PJ
s
M
a
-------
ro
1 .25--
1 .00--
bO
e
0)
01
0>
0.75--
0.25--
0.00 L
fl i
aJ i
Figure 33. Variation of Manganese
in Lakes Madison and Herman During 1971.
-——Lake Madison
—— Lake Herman
Southeast Lake Herman
ft
(D
CO
-P
O
O
O
0)
-------
or after the spring run-offs. This maximum is followed by a decrease to
a near minimum in early May and wide fluctuations during the summer and
fall. The fluctuations do not coincide between the two lakes and are
generally more pronounced in Lake Madison and Southeast Lake Herman.
Sodium and potassium follow the same pattern of seasonal change in both
Lake Madison and Lake Herman. Figure 34 depicts potassium levels in the
two lakes during 1970. The data graphed represent averages of the
results listed in Appendices A and C. Since Southeast Lake Herman was
not consistent with the remainder of the lake the last year of this
project, it was graphed separately during that time. Sodium levels
generally range from 100-140 mg/1 Na in Lake Madison and 25-50 mg/1 Na
in Lake Herman. Potassium levels, however, are somewhat lower, ranging
from 18-30 mg/1 K in Lake Madison and from 12-25 mg/1 K in Lake Herman.
In both lakes and with both sodium and potassium there is a sharp
decrease at the time of the spring run-off followed by an increase to a
more normal: level in April or May with a very slight rise during the
summer and a greater rise in the fall and winter.
The results of the biological studies will now be discussed with
reference to (l) variations in biota among the standard sampling sites
in each lake, (2) variations in biota at different seasons of the year,
and (3) variations in biota between the two lakes.
Planktonic Algae in Lake Madison and Lake Herman
The Green Algae and Euglenoids. Euglenoids and green algae were not
significantly abundant in either Lake Madison or Lake Herman during the
summer or fall months. In Lake Madison, very light blooms of euglenoids
and green algae occurred from the middle of March to early May during
1970 and 1971. The euglenoids contributed significantly to these light
blooms. Species of Euglena were the most abundant, but Phacus sp. was
occasionally recorded. Among the greens, species of Scenedesmus were
the most abundant in the 1970 bloom, while species of Chlamydomonas
contributed more to the bloom in 1971 than any other group. Other
greens present in Lake Madison during the spring, summer and fall
included species of Pediastrum, Act.inastrum, Ankistrodesmus, Coelastrum
and Sphaerocystis.
Slight increases in green algae occurred sporadically in Lake Herman
during the spring, summer, and fall months, but these increases were
brief and never contributed significantly to the algal blooms. Species
of Ankistrodesmus were the most abundant of the greens and were found
each year, 1968-1971. Other greens that were present, but on a very
sporadic basis, included species of Actinastrum, Cosmarium, Eudorina,
Pediastrum, Scenedesmus, Selenastrum, and Sphaerocystis. Euglenoids
were essentially nonexistent in Lake Herman.
63
-------
30.0-.
25.0--
a
20.0--
•H
to
S 15.0-
10.0--
Figure 34. Variation of Potassium
in Lakes Madison and Herman During 1970.
s
XX.
•Lake Madison
•Lake Herman
Southeast Lake Herman
5.0 L
o
flE-
oj a*
£>
Q>
Pc«
i
h
oj
p,
«»i
t>»
«J
i
I
!>»
H
bO
0
->S
i
O,
o
W
o
0
0
-------
Blue-Green Algae in Lake Madison. In 1968, a blue-green bloom (10-100
organisms/ml) began in late May and early June (Figure 35) and became
extremely dense (100,000 organisms/ml) in early July. Fluctuations in
the blue-greens varied from 1,000 organisms/ml to 100,000 organisms/ml
throughout the summer. The center of the lake had the greatest densi-
ties of blue-greens during the summer. The center and the west end
(near the inlet of the lake) had the greatest fluctuations in popula-
tions of blue-green algae. A decrease in blue-greens throughout the
lake began in early September and by the time an ice cover formed in
November the blue-greens had almost disappeared.
In 1969, the bloom began in late May and June (Figure 36), as it had in
1968, and by July a dense bloom had developed. Although the fluctu-
ations were less than those of 1968 (no densities over 19,000 organisms/
ml occurred), the dense bloom persisted throughout the summer; and,
once again, the center and west end had greater fluctuations in blue-
greens than did the southeast end (near the lake's outlet). The popula-
tion densities of blue-green algae during 1969 differed in one distinct
way from that of 1968. The fall bloom in 1969 was still extremely dense
when an ice cover was formed and persisted into the winter months.
During the ensuing winter a total fish kill occurred in Lake Madison.
The fish kill occurred quite early in the winter; dead fish were seen by
ice fishermen as early as late December.
The blue-green bloom in 1970 (Figure 37) began in May, as it had in
1969, and reached its greatest density in July. However, the bloom was
never as dense as it had been in the previous two years. An unusual
decrease in the blue-green densities occurred in the middle of August.
The decrease was preceded by low levels of phosphates during June and
July (Figure 16), and the phosphates remained unusually low during the
remainder of the summer. The only known change in factors affecting the
chemistry of the lake was a decrease in phosphates from the sewage
effluent of the city of Madison. A meat packing plant in the city of
Madison was permanently closed early in 1970, and we believe there was a
correlation between the closing of the meat packing plant and the
relatively light blue-green bloom in the late summer and fall of 1970.
A -new bloom occurred in October, but rapidly decreased so that it was
almost gone by the time an ice cover was formed in November. A fish
kill did not occur during the ensuing winter.
The species of blue-green that was most abundant in the blooms in Lake
Madison each summer was Aphanizomenon flos-aquae. Another blue-green
Phormidium minnesotens_e was second in abundance in the blooms but was
sporadic in occurrence. Other blue-greens which were present include
species of Anabena, Co'elosphaer'ium, Merismopedia', and Microcys1:is.
Diatoms in Lake Madison. The planktonic diatoms of Lake Madison usually
had three distinct blooms each year (Figures 39 to 42). The first bloom
began in March, reached its peak in late May and early June, and
decreased to very low densities by the middle of July. A second bloom
occurred in August and had declined by late August and early September.
65
-------
Figure 35. Variations in Population Densities of Plankton:
500 000— Lake Madison EXiring 1968
100,000™
Blue-Green Algae in
l/l
s
1/1
c
03
cr>
M
o
10,000 —
l.OOC
IOC —
1C
0
West
Center
•" Southeast
c
ns
0)
O
fH
CO
f-.
O.
>s
,—1
3
O
O
>
o
0)
-------
-j
Figure 36. Variations in Population Densities of Planktonic Blue-Green Algae in
500 OOof- Lake Madison During 1969
ioo,ooop-
f-i
~1
.C
O
fn
CD
West -j
Center*
••• Southeast
O.
0
a>
0
-------
CO
(-1
o
a.
01
OT
• <-•
C
ro
en
o
M
QJ
500,000
100,000
* 10,000
l.OOC
IOC
10
0
Figure 37. Variations in Population Densities of Planktonic Blue-Green Algae in
Lake Madison EXiring 1970
West
Center
••• Southeast
~l
.c
o
c
(O
,Q
(-1
a.
>-
,—I
D
O.
0)
in
o
O
> o
o &
-------
vO
f-l
0)
a.
m
e
in
•<-(
c
ro
0
f-t
m
Figure 38. Variations in Population Densities of Planktonic Blue-Green Algae in
500 000— Lake Madison During 1971
100,000 —
10,000 —
I,DOC—
IOC
1C —
-]
Center
••• Southeast
:rr—--
(O
>->
H)
a,
fn
(O
>.
OJ
c
3
0>
-------
Figure 39. Variations in Population Densities of Planktonic Diatoms in Lake Madison
500,000-
100,000
During 1968
West
Center
"• Southeast
10,000 —
o
(H
0}
CL
Ul
£
c
CO
en
O
o
-
i—i
3
CP
3
Q.
o
-------
500,OOOU
^Figure 40. Variations in Population Densities of Planktonic Diatoms in Lake Madison
During 1969 ~1
01
e
1/5
C
fO
CD
M
o
(-1
4) 10,0001—
1,00(
lod
West
Center
••• Southeast
c
CO
JD
o
,<-!
(T3
(0
a;
c
en
D
<
O.
ffl
CO
o
O
>
O
-------
to
Figure 41. Variations in Population Densities of Planktonic Diatoms in Lake Madison
500,OOO
10,000(—
l-t
&
a.
en
(-1
o
o
>-»
|
i,oocf--
loot—
0
id—
197°
West
Center
••• Southeast
UH
O
M
(O
4)
C
3
a
0
CO
o
o
>
o
o
0)
Q
-------
GO
Figure 42. Variations of Population Densities of Planktonic Diatoms in Lake Madison
500,000- During 1971
100,000 —
Q.
a
c
03
01
O
O
0>
3
0,000 —
l.OOC
100 —
1C
West
Center
••• Southeast
c
ro
1-1
(l)
u-
0
»H
(0
D.
<
>-
<0
cn
a
0)
CO
o
o
>
o
-------
•v]
500,000
100,000
03
D.
e
•(-*
C.
IT!
O
<*-c
O
0)
Figure 43. Variations in Population Densities of Total Phytoplankton in Lake Madison
-~ IXiring 1958 1
West
-— Center
••• Southeast
io,ooq
l.OOC
100
1C
0
c
(0
o>
U-,
o
Q.
>-
i—4
p
0>
<
-fJ
O.
0)
>
o
-------
--J
CJ1
Figure 44. Variations in Population Densities of Total Phytoplankton in Lake Madison
500,OOoC~ During 1969
100,000 —
10,000 —
t-,
OJ
a
01
Cn
O
4-.
O
0)
•i
3
1,000 —
100
1C
0
c
03
0.
O
h
CO
ll
Q.
0)
C
West
— Center
••• Southeast
A
a
o
-------
Figure 45
500,000-
100,000 —
Variations in Population Densities of Total Phytoplankton in Lake Madison
«j 10,000
01
e
1/1
c
05
cn
O)
i
3
1,000
IOC
During 1970
~l
West
--.- Center
"• Southeast
c
to
1-1
0)
tu
(-1
(0
Q.
>.
^-1
?
<
-p
a
a>
CO
o
O
>
o
-------
-J
500,000-
100,000 —
Figure 45. Variations in Population Densities of Total Phytoplankton in Lake Madison
During 1971 I
e
in
•f—\
c
ro
M
OJ
10,000 —
l.OOC
IOC
1C
West
Center
••• Southeast
c
03
I)
UL,
o
M
ft)
In
Q.
0)
c
<
O.
«
UJ
-P
o
O
>
o
o
4)
-------
A third bloom occurred each fall, but varied more in its time of occur-
rence than did the first two blooms. The third bloom in 1968 and 1969
(Figures 39 and 40) occurred in September and had declined by November.
The third bloom in 1970 (Figure 41) occurred mainly in November and
December. There was only one significant difference between collection
sites. In 1969 (Figure 40), three blooms occurred in all parts of the
lake, but the decrease in diatom densities between the blooms was not
nearly as great in the southeast part of the lake as it was throughout
the rest of the lake. This occurred only during 1969.
Species of Cyclotella dominated most of the diatom blooms during this
study. This was especially true during 1970 and 1971 when the diatoms
were the most numerous of the phytoplankton groups. Diatoms which were
of secondary importance, but dominated some of the lighter blooms in
1968 and 1969, were species of Nitzschia and Stephanodiscus. Other
diatoms included species of Cocconeis, Fraqilaris, Gomphonema, Melosira,
Navicula, Pinnularia, Surirella and Synedra.
Comparison of Blue-Greens and Diatoms in Lake Madison
One interesting observation in a comparison of diatoms and blue-greens
is the very high densities of blue-greens in the lake in 1968 and 1969.
They frequently numbered from 2,000 to 65,000 organisms/ml during the
main part of the bloom. The diatoms during these two years seldom
numbered over 1,000 to 1,200 organisms/ml even at their greatest densi-
ties and were usually much less abundant. However, the blue-green
densities in 1970 were very low, reaching a maximum count of only 1,817
organisms/ml during most of the summer. In contrast, the diatom popula-
tion reached a density of 57,663 organisms/ml during the first diatom
bloom in late April and were usually above 10,000 organisms/ml. The
first diatom bloom in 1971 reached a maximum of nearly 29,000-organisms/
ml. In contrast, the blue-green population densities were very low at
the time.
Blue-Green Algae in Lake Herman. The blue-green bloom in Lake Herman
during 1968 (Figures 47 and 48) reached its peak in August when 39,044
organisms/ml were present. The bloom declined rapidly in September and
October and totaled less than 1,000 organisms/ml in early November, just
prior to the formation of an ice cover. Fluctuations in densities
between collection sites do not appear to be significant. Increases in
population densities began first at the north end of the lake (near the
main inlet) and progressed through the lake to the southeast corner.
However, the greatest densities for all parts of the lake were 'approxi-
mately the same in late July and early August. The water depth in the
lake was very low because of drought and during the ensuing winter a
total fish kill occurred.
The greatest densities of blue-greens during 1969 occurred in July
(Figures 49 and 50) when there were 1,036 organisms/ml. There was no
significant blue-green bloom in 1969.
78
-------
\D
Figure 47. Variations of Population-Densities of Planktonic Blue-Green Algae in
500,COOU Lake Herman 1968
100,000 —
10,000 —
x:
o
a
>.
03
O
C
cn
a.
O)
CO
North
Dredge
o
O
>
o
-------
03
O
Figure 43. Variations in Population Densities of Planktonic Blue-Green Algae in
01
a
Ul
in
c
en
O
<+-!
O
^
500,000
100,000
a> 10,000
1,000
IOC
c
to
•
r-l
3
-------
CO
500,000
100,000
« 10,000
«— <
•«H
1—4
r— t
•I-*
« 1,000
in
S
O)
•rH
c
ro
cn
0 IOC
M-i
O
0)
^ 1C
0
Fi_gure 49. Variations in Population Densities of Planktonic Blue-Green Algae in
_ Lake Herman During 1969
~ North
— Dredge
H«^
___
—
—
—
- \ ^ .
"" \ x/ W j^\
I W V v/ \ \
i i * i i i i i i \ i\ i t
-C — 1 •
y k . Yl» *-^ _ Jj _ . *
cja £IT!>-c^-«'a>Tx-tJ><->
D.
-------
CO
in
tr-1
c
03
o
<+H
O
h
03
i
3
500,
ioo,ooop.
Figure 50. Variations in Population Densities of Planktonic Blue-Green Algae in
Lake Herman During 1969
Center
Southeast
10,000}—
i,oocf—
100
0
id-
O
0)
-
i—i
-3
cn
a
0
CO
o
O
>
o
-------
A relatively heavy blue-green bloom occurred in 1970 (Figure 51). It
began in June and reached its greatest density (7,830 organisms/ml) in
the north and central parts of the lake in July. However, the bloom in
the southeast part of the lake reached its greatest density (11,549
organisms/ml) in October (Figure 52), and all parts of the lake had
blooms (5,710 organisms/ml) in November just prior to the formation of'
an ice cover. Although no fish kill is known to have occurred during
the winter, oxygen levels fell below 2 ppm throughout most of the lake,
in February, 1971 (Appendix C). An early thaw prevented a fish kill
from occurring.
Just prior to the termination of this project in June, 1971, the blue-
green bloom had become quite dense for that time of the year. An
increase in blue-greens occurred almost as soon as the ice melted in
March, and by late May there were 3,386 organisms/ml.
The blue-green alga primarily responsible for the blooms in Lake Herman
was Aphanizomenon flos-aquae. Of secondary importance in the blooms
were species of Anabena and Microcystis. Other common blue-green algae
were species of Merismopedia and Phormidium.
Diatoms in Lake Herman. Although diatom counts were not begun until
June of 1968, Figures 55 and 56 show two blooms from June to November.
An additional bloom probably occurred during the spring of 1968. The
population density of the summer bloom reached 28,810 organisms/ml,
and the second bloom reached 12,698 organisms/ml in September.
A relatively small diatom population was present in Lake Herman during
1969 (Figures 57 and 58). The greatest denstiy (830 organisms/ml)
recorded for the year was in the center of the lake in November.
Three diatom blooms occurred in 1970 (Figures 59 and 60). However, the
only part of the lake to develop a population greater than 1,000
organisms/ml was the southeast corner. The population densities there
were 1,097 organisms/ml in April, 2,064 organisms/ml in July and 925
organisms/ml in October. All other diatom populations in the lake
reached maximum densities of considerably less than 1,000 organisms/ml
during these months.
The first diatom bloom in 1971 (Figures 61 and 62) reached a maximum den-
?;.ty of 7,086 organisms/ml in the northern part of the lake, which was a
greater density than during either of the previous two years.
The diatoms responsible for the blooms varied considerably from year to
year and sometimes from bloom to bloom within a year. For example, the
midsummer bloom of 1968 was composed primarily of species of Cyclotella,
while Nitzschia sp. was of secondary importance. However by the end of
that bloom, species of Melosira and Stephanodiscus were becoming more
numerous. Stephanodiscus sp. was the most abundant diatom in the late
fall bloom.
83
-------
Fiaure 51
oo
500,000
ioo,ooop-
S 10,000
0)
a
6
01
•r-H
c
(O
en
O
F-i
o
0
-------
Figure 52. Variations in Population Densities of Planktonic Blue-Green Algae in
500,000-
100,000 —
* 10,000 —
00
CJi
03
Q.
in
6
ui
c
03
f-t
0]
1,000
100
1C
Lake Herman During 1970
~l
—— Center
Southeast
J
c
TO
0)
>.
ffl
0)
c
>-.
1—I
D
Q.
®
03
O
O
>
O
-------
CD
Figure 53. Variations in Population Densities of Planktonic 31ue-Green Algae in
500 COOf— Lake Herrran During 1971 '
100,
10,O
f-t
05
Q.
c
05
cn
M
O
<+-.
O
fH
0)
^
3
1,00
North
Dredge
-------
00
-J
Figure 54, Variations in Population Densities of Planktonic Blue-Green Algae in
500 000— Lake Herman During 1971
100,000 —
•s.
f-i
a.
ifi
to
cn
(-1
o
O
M
10,000 —
1,000
IOC
Center
— Southeast
~1
0
u*
Q.
cn
a
®
cn
0
O
0
0)
"
-------
oo
00
500,000-
100,000
Figure 55. Variations in Population Densities of Planktonic Diatoms in Lake Herman
'During 1968 ~l
« 10,000
o
l/l
c
ro
o
'•4-t
O
0)
3
1,000
IOC —
1C
0
- North
--- Dredge
c
03
>->
u,
-------
CD
\D
Figure 55. Variations in Population Densities of Planktonic Diatoms in Lake Herman
500,000-
100, Oca-
s' 10,000f—
a
t/i
10
1,000
IOC
10 —
c
ro
QJ
LL,
o
f-i
0}
>.
-
I—I
3
Q.
ffl
CO
-P
o
O
>
o
~l
-------
.Figure 57. Variations in Population Densities of Planktonic Diatoms in Lake Herman
»* • * /-\ x- /-i
vD
O
500,000
100,000
o> 10,000
•rH
f-H
• iH
*— <
,-H
•f-*
« 1,000
a.
in
in
•«-t
c
(0
en
o 100
4-i
O
f-l
• i .§ §• i ti s s
* £ £ < s ^ 3 <
-------
\o
500,OOOU
100, ooop-
Jlgure 58. Variations in Population Densities of Planktonic Diatoms in Lake Herman
During 1969 ~1
* 10,000f—
M
0)
a
ul
e
in
c
(0
a>
t-i
O
f-l
0}
1,OOC
100
10
0
xi
x:
O
to
flj
c
- Center
--- Southeast
o>
-------
Figure 59. Variations in Population Densities of Planktonic Diatoms in Lake Herman
•J During 1970
North
Dredge
« 10,OCX
ro
0)
a
in
• r-l
c
ro
Cn
tn
O
o
P
to
lOOt-
!<*-
c
ID
0)
D. at
O
-------
500,
100,
000-
000 —
* 10,000 —
a>
a.
If!
c
CO
o
o
0)
"I
3
1,000 —
IOC —
60. Variations in Population Densities of Planktonic Diatoms in Lake Herman
During 1970 ~1
Center"
— Southeast
0
C
03
it-,
O
M
c
D
>.
r-t
D
a>
O.
0
CO
o
o
>
o
4)
-------
0)
a.
to
c
as
f-t
0)
Figure 61. Variations in Population Densities of Planktonic Diatoms in Lake Herman
' During 1971 ~~I
North
Dredge
0
X!
V
LL.
'\ /
/ x /
\/
_JM
o
S
__J_
^
h
Q.
t ! I
4> >-
>. C •-*
\ 1
• -(->
CT> Q.
3 ffi
«< CO
i I i
0»*
-*-> > u
o o fl>
O ^ Q
|
-------
vD
500,000-
100,000 —
o> 10,000 —
0)
a
c
ro
Cn
O
<±*
O
o
0)
-------
ON
Figure.'_63. Variations in Population Densities of Total °hytoplankton in 'Lake Herman
500,000-
100,000 —
5 10,000 —
->
0)
O.
U)
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_Figure 54. Variations in Population Densities of Total Phytoplankton in Lake Herman
500,000
100,000
J> 10,000
• ^H
•f-t
. — <
1 — 1
s
o3 1 , 000
01
6
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o 100
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100,OCX
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1,000}—
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1C*
0
figure 65. Variations in Population Densities of Total Phytoplankton in Lake Herman
- During 1969 1
1_ _—. North
•— Dredge
O)
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h
(O
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Figure 66.
.500,00dp"
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Variations in Population Densities of Total Phytoplankton -in Lake. Herman
During 1969 "1
• Centerr --•—-" ••<>•
— Southeast
c
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Figure 67. Variations in Population Densities of Total Phytoplankton in Lake Herman
500,000- During 1970 ~1
100,000 —
10,000
1,000 —
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— North
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Figure 63. Variations in Population Densities of Total Rhytoplankton in Lake Herman
During 1970 ~1
• Center T
Southeast
_2 10,000 —
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-Q.
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500,OCK
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en
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10,000
1,000
100
69. Variations in Population Densities of Total Phytoplankton in' Lake Herman
During 1971 ~1
1C —
North
Dredge
c
to
o
^
(0
t-,
0,
O)
c
01
Q-
0
CO
O
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>
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o
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Figure 70. Variations in Population Densities of Total Phytoplankton in Lake Herman
500,000- During 1971
100,000 —
£ io,ooo—
0>
a
c
en
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b
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-------
Species of Surirella were almost entirely responsible for the diatom
populations in 1969. The data for that year indicate very low popula-
tion densities of these species.
Species of Cyclotella and Surirella were equally abundant in the spring
bloom of 1970. The summer bloom was composed primarily of species of
Cyclotella, Melosira, and Nitzschia. The fall bloom included all those
responsible for the earlier two blooms plus Stephanodiscus sp.
Species of Cyclotella composed most of the early bloom in 1971. Although
the species mentioned above were more abundant during years of low dia-
tom densities, during years of high population densities species of
Cyclotella were the most abundant. Other diatoms which were present
include species of Cymatopleura, Fraqilaria, Gomphonema, Navicula,
Pinnularia, and Svnedra.
Comparison of Blue-Greens and Diatoms in Lake Herman
The inverse relationship between diatoms and blue-greens in Lake Madison
was not found in Lake Herman. The greatest densities of diatoms and
blue-greens during this study occurred in 1968. Diatom blooms during
1968 alternated only slightly with blue-green blooms.
Diatom populations and blue-green populations in 1969 were extremely
low as compared with the rest of the project period; thus, the two
groups may not have affected each other at such low densities.
The blue-green densities in 1970 were fairly high, although not nearly
as high as the densities of 1968. Data from-that year indicate rela-
tively low population densities of diatoms.
When the project terminated in June of 1971, data to that point indi-
cated alternating blooms between the diatoms and blue-greens for that
year. The April diatom count was 7,000 organisms/ml while the blue-
greens were about 700 organisms/ml. By late May the blue-greens had
increased to 3,400 organisms/ml and the diatoms had decreased to 700
organisms/ml.
Comparison of Phytoplankton Between Lake Madison and Lake Herman
During the entire three-year project, which began in June, 1968, and
terminated in June, 1971, Lake Madison was more productive in ternis of
total phytoplankton.
The greatest density of phytoplankton in Lake Madison in 1968 was
approximately 40,000 organisms/ml. Although the phytoplankton densities
did not remain that high for any great length of time, they were con-
sistently higher in Lake Madison than in Lake Herman.
104
-------
The phytoplankton densities during 1969 were the lowest of the three-
year project. The greatest density in Lake Herman during 1969 was only
1,200 organisms/ml, and it was usually much lower. Lake Madison was
much lower in total phytoplankton during 1969 than during any other
year. Although the greatest density was only 18,000 organisms/ml, that
was still much higher than the greatest density in Lake Herman. The
phytoplankton density in Lake Madison remained high until an ice cover
formed, while the phytoplankton density in Lake Herman dropped sharply
prior to the formation of an ice cover.
The phytoplankton densities in Lake Madison and Lake Herman were about
the same during 1970. However, the seasonal composition of the phyto-
plankton was quite different. The phytoplankton density in Lake Madison
was the highest in the middle of the summer (57,000 organisms/ml) and
was made up almost entirely of diatoms. The phytoplankton then
decreased rapidly and was quite low (1,000 organisms/ml) by October.
The phytoplankton population in Lake Herman was composed primarily of
blue-greens, which were less abundant than in Lake Madison, and remained
relatively high (6,000 organisms/ml) until an ice cover formed.
An early bloom developed in both lakes during April of 1971. The bloom
in Lake Madison was considerably denser than the bloom in Lake Herman
(27,000 and 8,000 organisms/ml, respectively). The blooms in both lakes
were composed primarily of diatoms. The early bloom of diatoms in Lake
Madison had practically disappeared by late May, and the blue-greens had
not begun to increase at that time; therefore, the phytoplankton density
was a very low 20 organisms/ml. The diatom density in Lake Herman was
quite low by late May but the blue-greens had begun to increase; the
phytoplankton density was about 4,000 organisms/ml. Although no further
densities were recorded for this project, the results from another pro-
ject indicate heavy blue-green blooms in both lakes throughout the sum-
mer and fall of 1971.
Although the greens and euglenoids did not compose a significant portion
of the phytoplankton in Lake Madison, their early blooms undoubtedly
influenced the ensuing phytoplankton. Lake Herman did not have blooms
of green algae or euglenoids.
Copepod and Cladoceran Populations in Lake Madison and Lake Herman
From May, 1970 to June, 1971.
An analysis of copepod and cladoceran populations was begun in May of
1970; thus, they were studied for only a one-year period. The copepod
populations of both lakes were composed of Osphranticum labronectum and
Ectocyclops phaleratus. The cladoceran populations in both lakes were
composed primarily of species of Daphnia, but Bosmina coreqoni was
occasionally collected.
The copepod population in Lake Madison was usually greater than the
cladoceran population (Figures 71 to 76). The cladoceran population in
105
-------
f-l
o
-I-J
T-l
-J
rH
0)
a
u)
c
to
a>
M
o
<4«
o
800
700
600
500
400
300
]
j
200 \
j
100
80
Figure 71. Variations in Population Densities of Copepods in Lake Madison During 1970
—West
Center
...Southeast
60 I
4C-
0
o
(H
ex
<:
O
>
O
-------
Figure 72. Variations in Population Densities of Cladocerans in Lake Madison During 1970
o
-J
Si
Oi
Q.
55
•^
c
0)
JQ
800
700 j-
600 L-
500
400
300
200
100
SO
50
40
20
0
c.
a
.0
<»
u.
o
f-t
West
Center
Southeast
>.
CB
>
o
u
«
Q
-------
Figure 73. Variations in Average (Three Sites) Population Densities of Copepods and
Cladocerans in Lake Madison During 1970
800 -
700 -
600 -
o
00
f-t
M
O
t-i
ffl
-— Copepods
--- Cladocerans
o
(-1
u.
Q.
>.
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w
3
Q.
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-------
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10
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C
(O
M
CD
JQ
800
700
600
500
400
300
200
100
so
60
40
2C
0
Figure 74. Variations in Population Densities of Copepods in Lake Madison During 1971^
West
— Center
••• Southeast
c.
(S
O
-------
ID
-H>
^-<
-J
O)
Q.
ifl
e
10
c
en
O
800
700
Figure 75. Variations in Population Densities of Cladocerans in Lake Madison During 1971
West
—- Center
••• Southeast
600
500
400.
300
200 t-
100
so
60
40
20
0
U.
O
*4
(0
>-
-T5
C71
Q.
CD
>
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-------
33
2
CU
a
tn
e
o
_<4-l
O
Figure 76. Variations in Average (Three Sites) Population Densities of Copepods and,
Cladocerans in Lake Madison During 1971 -\
800 -
700 -
600
500
400
300
200
100
80
60
40
20
0
ID
UH
.C
o
as
f-l
a
0)
c
a
Copepods
Cladocerans
<
a.
>
o
-------
Lake Herman was usually greater than the copepod population except
between early May and mid-July (Figures 77 to 86).
The cladoceran population of Lake Herman peaked much earlier and much
higher in 1970 (Figures 73 and 8l) than did the cladoceran population
of Lake Madison. The greatest density in Lake Herman occurred in late
April and early May and was 250 organisms/1. A second peak (180
cladocerans/l) occurred in early July. By mid-July, however, the
cladoceran population had decreased nearly to zero and it remained very
low during the remainder of the year. The greatest density in Lake
Madison wasn't reached until September, and it was only about 80
organisms/1 (unless a peak had occurred in April prior to the beginning
of the counts). Although there was a sharp decrease in cladocerans
after September, the density remained near 20 organisms/1 (Figure 86).
The cladoceran population in Lake Herman during 1971 did not begin to
increase until mid-May and was above 100/1 by early June (Figure 76).
A peak had not been reached when the project was terminated in early
June.
The copepod populations reached greater densities in Lake Madison (600
organisms/l) than in Lake Herman (250 organisms/l); however, the popu-
lations in Lake Madison decreased much earlier than in Lake Herman.
The copepod populations in Lake Madison decreased to 40 organisms/1
during October and to less than 20 organisms/1 during December. A
population of over 100 organisms/1 was present in Lake Herman throughout
the fall of 1970 and into February of 1971, when it started to decrease.
Early in 1971, the population of copepods was'higher in Lake Herman
than in Lake Madison.
The chemical and biological parameters of Lake Madison (a sewage
polluted lake) and Lake Herman (a silt polluted lake) clearly follow
the same seasonal trends. The sharp rise in some nutrients and fall in
other nutrients at the time of the spring runoff, the summer fluctua-
tions of certain nutrients with biological growth, the seasonal blooms
of diatoms and blue-green alga as well as the inverse relationship
between these two types of blooms all follow the same pattern in both
lakes. It is of particular interest that both lakes have very high
levels of phosphorus. Herein is one instance where agriculture and
silt have released as much phosphorus, if not more, into surface waters
as domestic sewage effluent with its phosphate load from detergents.
Both lakes appeared to have an abundance of phosphorus even at the
height of the algal blooms but the nitrate level in both lakes decreased
to near zero during these blooms.
It is interesting to note that both lakes even responded to a fish kill
in the same manner. Lake Herman experienced a complete fish kill during
the 1968-1969 winter. During the summer of 1969 Lake Herman showed a
marked decrease in the density of phytoplankton growth despite the fact
that there were no significant differences in phosphorus and nitrogen
112
-------
Figure 77. Variations in Population Densities of Copepods in Lake Herman During 1970
<£
-fJ
-H
.-4
O>
Q.
in
UJ
fH
c
(T3
en
0)
"I
P
800 -
700 -
600 -
500
400
300
200
100
80
60
40
20
0
-— North
— Dredge
CD
LU
O
»4
re
O)
C
Q.
ID
>
O
o
5
-------
Figure 78. Variations in Population Densities of Copepods in Lake Herman During 1970
800 -
-— Center
--- Southeast
CD
O.
U>
to
tH
c
to
o>
o
f-4
c
o
JQ
O
IL.
n.
o
-------
f-l
0)
o.
o?
-r-l
C
(8
on
0>
I
800
700
600
500
400
300
200
100
80
60
40
20
0
79. Variation in Population Densities of Cladocerans in Lake Herman During 1970
North
— Dredge
c
13
3
Q.
0>
o
O
>
o
-------
u.
x:
o
f-l
03
ft
a
>-
.-o
a.
o
-------
Figure 81. Variations in Average (Four Sites) Population Densities of Copepods and
Cladocerans in Lake Herman During 1970
0>
Q.
01
in
£
<«-.
O
O
-------
00
f-t
.
•—4
3
o
O
O
.§
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Figure 83. Variations in Population Densities of Copepods in Lake Herman During 1971
\o
£
«3—
-r-i
c
na
a?
ft-
O
0)
XI
3
300
700
600
500 -
400 -
300 -
i
200 [.
I
100
SQ|-
6G |-
40
20
0
c
ro
\
Center
— Southeast
a
Ol
o
2
-------
Figure 84. Variations in Population Densities of Cladocerans in Lake Herman During 1971
0>
-1
Q.
tn
in
C
o
5
-------
Figure 85 . Variations in Population Densities of Cladocerans in Lake Herman During 1971
ro
CD
(n
0)
Q.
in
e
in
i-\
c
(0
o>
M
O
0)
JD
800 -
700 -
600
500
400
300
200
100
80
60
40
2C
0
c
TO
.C
o
O
o
3
-------
10
10
ffl
-l->
-Y-J
~-i
O)
Q.
01
at
••H
c
to
o>
800
700
Figure 86. Variations in Average (Four Sites) Population Densities of Copepods and
Cladocerans in Lake Herman During 1971
Copepods
Cladocerans
600
500
400
300
200
100
80
50
40
20J-
0
"1
x:
O
tt>
u.
(O
Q.
o
O
-------
levels. The lack of biological growth was, however, reflected in lower
pH values and higher alkalinity values during the summer of 1969 as
opposed to other summers. Lake Madison experienced a fish kill during
the 19§9-1970 winter season. During the following summer of 1970, Lake'
Madison had its lowest density blooms which like Lake Herman the pre-
vious summer were accompanied by lower pH levels and higher alkalinity
levels with no significant changes in phosphorus or nitrogen levels.
We cannot explain this relationship between winter fish kill and lower
summer plankton densities.
In terms of the chemical parameters the major differences in the two
lakes occurred in the levels of chloride (Madison about SOX Herman),
conductivity (Madison about 2X Herman) and sodium (Madison about 3X
Herman). The explanation for these differences undoubtedly lies in the
source water for the two lakes. Lake Madison, receiving the effluent
from the sewage lagoon thus receives the city water which has been
chlorinated and most of which has been softened with sodium chloride
softeners. Lake Herman waters are, however, usually slightly more
turbid than Lake Madison waters. This difference would arise from the
shallowness of Lake Herman—the wind and wave action would be expected
to stir up the sediments to a greater degree.
In terms of biological parameters, Lake Madison (sewage polluted lake)
had a higher density of phytoplankton than Lake Herman (silt polluted
lake), except during the summer of 1970 following the winter fish kill
in Lake Madison. This higher density growth in Lake Madison cannot be
explained in terms of the usual phosphorus and nitrogen levels because
both lakes had an abundance of these nutrients. The extra growth
probably results from sewage components not determined by analysis.
Along this line, it is of interest to note that frequently the phyto-
plankton counts decrease in number in going from the west sampling site
to the southeast sampling site in Lake Madison—paralleling the inlet
of the sewage effluent and the lake outlet. As mentioned earlier phos-
phorus and nitrogen levels at the various sampling sites on Lake
Madison also followed this same trend before the summer of 1970. At
that time a meat packing plant which overloaded the city sewage treat-
ment facility was closed.
Another point which should be mentioned is that the variety of species
of both diatoms and blue-green algae present in significant quantity was
much more restricted in the sewage polluted lake. For instance, the
only diatom species occurring in any quantity in Lake Madison were
Cyclotella, Nitzschia and Stephanodiscus. Lake Herman diatoms occurring
in significant quantities included these three species in addition to
Surirella and Melosira. In Lake Madison the only blue-green alga in
abundance was Aphanizomenon flos-aquae with Phormidium minnesotense
occurring sporadically. Lake Herman also contained high densities of
Aphanizomenon flos-aqua, but Anabena and Microcystis were also
important. These differences may result in part from the summer copper
sulfate treatment of Lake Madison.
123
-------
In order to retard soil erosion on the Lake Herman watershed a number of
silt traps were constructed on the feeder streams. A gabion type of
silt trap was selected because it is relatively inexpensive, can be con-
structed with a minimal amount of engineering advice, and does not
permanently retain water. Basically, the resulting trap is a wire
basket packed with rocks and placed in a creekbed. Figures 87 and 88
give a general idea of the appearance of gabion silt traps. These traps
are described with regard to size, location and creekbed type in
Appendix D.
The silt traps were found to be effective as coarse filtering devices.
Figures 89 and 90 show two of the traps; note the debris collected
against the upstream side of these traps. Analyses of water samples,
collected just above and below the traps, for filtered solids and
turbidity indicate that the traps had little if any effect as a silt
filter,, Some of these analytical results are listed in Table V.
However, it was found that water far enough above the gabion to still
be flowing rapidly showed a higher level of filtered solids and tur-
bidity than the water samples collected just above or below the gabion
(see Table V). Thus, it may be concluded that the gabions were effec-
tive in the sense that they retarded the flow of water, causing some of
the silt load to be dropped. Since a high quantity of filtered solids
is associated with high values of total phosphorus; the gabion
silt traps are also decreasing the level of phosphorus reaching the lake.
After the two rather light run-off years since most of the traps were
constructed, there is only a deposit of one-half to three inches of silt
behind six of the traps; but this amount could increase substantially
after heavy run-offs like that occurring in the spring of 1969.
Whatever success was achieved by the silt traps was diminished by
damages. Six of the traps had soil erosion around them; two of these
are shown in Figures 91 and 92. These traps were all in creekbeds which
lacked vegetative cover, and most of them were partially countersunk in
the creekbed. The traps had been placed intentionally in eroded creek-
beds with the hope that they would stop further erosion and allow silt
to fill the eroded areas. Apparently, pressure from water backed-up
behind a silt trap caused the water to break through at any weak point.
Once a small hole was formed under or at the side of a trap, it was
soon enlarged by increased water movement through this area. The place-
ment of gabion silt traps in eroded creekbeds and countersinking
measures should be avoided.
The three traps built in 1970 were constructed with aprons to protect
the creek bottom against erosion (see Figures 93 and 94) and were con-
structed in well-sodded creekbeds. These traps have not been damaged by
soil erosion. However, it is felt that the amount of run-off since
their construction has not been sufficient to test adequately these
features. It should be noted that no silt has been deposited behind
these traps, which is probably best explained at this time by small
amounts of run-off during the past year.
124
-------
Figure 87. Silt Trap No. 1.
' aKW*MT* - ' • ' '
^fSPf , •
,
-•^"
>•
,
Figure 88. Silt Trap No. 13.
125
-------
Figure 89. Silt Trap No. 4 with debris collected along upstream face.
... ••*••
,;:• A " •' *
tZs^m^mm
!5®8^-*'*^ ;
• • • •/J"ais»*CT* i.jt!1^-
"Swwc- ", •• ^ . •
:«<
Figure 90. Silt Trap No. 13 with debris collected along upstream face.
126
-------
.
-• '":-" !
\m
m
¥>!"* *• •'* *•% ••:
«bl • •
*S*iCW;
-------
Ffsfc., .>— '. . -- ' -.
•.,.:,>&.. -"'- -
Figure 93. Silt Trap No. 16 with upstream and downstream aprons.
HHT
-V
Figure 94, Silt Trap Mo. 17 with downstream apron.
128
-------
Table V Measurements on Water Above and Below
Gabion Silt Tra'ps
Date and Filtered Solids , Turbidity
Location .brams/iiter jacksbn Units
April 4, 1970
Water Running
off field above
Gabion 4 2.525 391
Water about 15
Yards above
Gabion 4 0;085 231
Water just
Above
Gabion 4 0.066 223
March 11, 1970
Just above
Gabion 15 0.0446 36.5
Between Gabions ,
15 and 16 0.0475 38i6
Just below
Gabion 16 0.0403 39.1
All in all, a relatively low level of success seems to have been
obtained by the gabion-type of silt traps* It seems likely that those
which are not rendered ineffective by erosion will retain some silt over
a period of years. However, more effective types of silt traps and per-
haps other changes are needed if -most of the soil e'rosibn on the Lake
Herman watershed is to be halted.
129
-------
SECTION VII
ACKNOWLEDGMENTS
The support of Dakota State College is acknowledged with sincere thanks.
The encouragement and aid of Dr. Harry P. Bowes, President of Dakota
State College, and Dr. Clyde K. Brashier, Chairman of the Division of
Science and Mathematics, have made this project possible.
Dr. Robert Anderson, Professor of Biology at the University of Missouri
at Kansas City, has served as a consultant on algal identification and
was generous in his advice on several aspects of this project. Robert
Buckman and Robert Herting served as directors of the silt trap con-
struction team during the summer of 1969 and 1970 respectively. Karla
Wickre has typed this report.
The directors extend a very special thanks to their research assistants
who have carried out the bulk of this work—Charles Rohrer, Robert
Williams, Jerome Jensen, and Andreas Nielson. Charles Rohrer has
developed many of the chemical analytical methods- described and pre^
pared parts of this report.
The support of the project by the Environmental Protection Agency and the
help provided by Mr. Arnold Gahler, Grant Project Officer, is also
acknowledged with sincere thanks.
131
-------
SECTION VIII
REFERENCES
1. Anderson, J. B., editor, Newsletter—Analytical Quality Control
Laboratory. (No. 6-9, Cincinnati, Ohio, Environmental Protection
Agency Water Quality Office, July, 1970-April, 1971).
2. FWPCA, Analytical Techniques _for the National Eutroghicatj-on
Research Program, (Cincinnati, Ohio, LI. S. Department of the
Interior, October, 1967).
3. FWPCA, FWPCA Methods for Chemical, Ajn,a_ly_si_s of_ .Water and Wastes,
(Cincinnati, Ohio, U. S. Department of the Interior, November,
1969).
4. Hach, Water and Wastewa_t.er Ajnal_y_sis, Procedures, Catalog #9 (2nd
Revised Edition, Ames, Iowa. Hach Chemical Company, 1968).
5. Palmer, C. Mervin, Al_gjL§_ jLri Water Supplies, (Publication Mo, 657,
Public Health Service, U. S, Department of Health, Education and
Welfare, Washington, D. C., 1962).
6. Perkin-Elmer, Analytical Methodj; fojr Atomic Absorption
Spectrophotometry, (Norwalk, Connecticut, Perkin-Elmer, September,
1968).
7. Prescott, G. W., Algae o_f the Western Great Lajcejs Area, (Revised
Edition, Dubuque, Iowa, William C. Brown Company, 1962).
8. Prescott, G. W., How to Know the Freshwater Al^ae, (2nd Edition,
Dubuque, Iowa, William C. Brown Company, 1970),
9;. Sawyer, C. N. and McCarty,, P. L,, Chem,ij.try_ _fcr_ ,San_it^£X Engineers,
(2nd Edition, New York; N. Y., McGraw-Hill Book Company, 1967).
10. Smith, Gilbert M., The Freshwater Algag of the United State_s, (2nd
Edition, New York, N. Y., McGraw-Hill Book Company, 1950).
11. Standard Methods for the Examination of_ Water and Wastewaters, (12th
Edition, New York, N. Y., American Public Health Association, Inc.,
1965).
12. Stewart, K. M. and Rohlich, G. A., Ejjtrophication—A Review,
(Publication No. 34, State of California, The Resources Agency,
State Water Quality Control Board, 1967).
13. Ward, Henry Baldwin and Whipple, George Chandler, Freshwater
Biology, (2nd Edition, New York, N. Y., John Wiley and Sons, Inc.,
1959).
133
-------
14. Weber, Cornelius I, A Gu_ide t£ .the Conmon Diatoms at Water Pollution
Surveillance S^s_tem S^atj.£n_s, (Cincinnati, Ohio, Analytical Quality
Control Laboratory, U, S, Environmental Protection Agency, 1971).
15. Whitford, L. A, and Schumacher, G. J., A Manual of the Freshwater
Algae _in North GaroHna, (Tech. Bulletin No. 188, Raleigh, North
Carolina, North Carolina Agricultural Experiment Station, 1969).
134
-------
SECTION IX
APPENDICES
Page No.
A. Results of Chemical Analyses of Lake Madison ... 136
B. Results of Chemical Analyses of Lake Madison Tributaries . . 158
C. Results of Chemical Analyses of Lake Herman ........ 169
D. Description of Silt Traps and Silt Trap Sites ....... 193
135
-------
Appendix A Results of Chemical Analyses of Lake Madison
C U)
Date
June, 1968
July
August
September
October
December
Jan., 1969
February
March
June 13
West
24
"cL
8.2
8.6
8.1
7.4
7.6
7.45
8.7
8.3
7.8
7.8
^~* — 1
^
CO
-HO
.— i fT3
fO C_)
~ii
« — $ O^
-H
0 CM
tO O f-l
S g1 §1?
11.12
12.01
8.4
9.4
6.7
6.6
2,4
1.3
7.9
10.45
>.
•r-t
•H ,— 1 O T3 r-l
U (D -H ~V^
^J ^ rH « — 1
T3 0 O
C £ r-H
O Q- jC O>
o cu o e
174.3
167,7
133
187
175,5
176.5
710 118.5
725 116
+1 M
CO O
jC JC
Q. Q.
in o)
-HO O
>£X v"\
^t
O -rH O O p-t O
•rH cn _c ex, ro a.
r-( -P +3
CO £ OS H S
0.49
1.38
0.95
0.80
0.77
0.68
0.58
0.625
1.05
0.56
r-l
z
•rH CO
C 3C
O 2
J i1
3
3.4
0.93
1.14
2.53
2.81
1.5
1.50
0.30
0.58
, — |
2
(U 1
-4-> CO
COO
f_l ^^
,{_}
zi1
0.0*
0.0
1.12
2
1.05
0.338
1.93
2.05
0.125
0.09
r — 1
Z
a> i
+J CM
•rH O
f . *^
H-J
2 3^
*A11 nitrate values from June, 1968, through August 20, 1969, are actually nitrate plus nitrite
determined according to Page 41 of the Hach Manual.
-------
Appendix A Results of Chemical Analyses of Lake Madison
co
-si
Date
July 1
Southeast
8
Southeast
15
West
Center
Southeast
22
West
Center
Southeast
29
West
Center
Southeast
Aug. 5
West
Center
Southeast
a:
Q.
7.7
8.8
8.50
8.73
8.65
8.35
8.9
8.5
8.55
8.7
8.9
8.95
9.0
8.7
5>
CO
•HO
r— 1 tO
mo
x
<%
139
129
138
131
126
138
134
135
130
139
128
130
129
129
c
0)
en
X
O
•o
0)
> r-i
p—l'^s.
0 OJ
tfi O «-i
to
a.
U)
r-l O
0) \. X>H
T3 r-l CN Q>s.
to r-( O -H OO
O O -H CO .CO.
i — i i — i +)
cS i1 5> i1 5S1
115.5
119
119.9
116,4
120.8
118.1
118.9
122.7
121.0
120.8
122
121
119
en
p
o
Q.
o en
H S
0.49
0.35
0.48
0.48
0.39
0.64
0.67
0.50
0.40
0.35
0.32
0.46
0.40
0.39
r— 1
m i
t-i ro
ca:
oz
Is1
0.18
0.51
0.40
0.23
0.50
0.60
0.46
0.45
0.36
0.32
0.28
0.25
0.40
0.20
z z
-------
Appendix A Results of Chemical Analyses of Lake Madison
Date
Aug. 14, 1969
West
Center
Southeast
20
West
Center
Southeast
26
West
Center
Southeast
Sept. 12
West
Center
Southeast
27
West
Center
Southeast
Q.
8.8
8.9
9.1
8.75
8.78
8.74
9.4
9.0
8.45
8.5
8.6
8.7
8.6
8.7
8.6
"co
,-1 ro
S^
<§•
135
132
130
140
136
143
136
139
134
147
140
140
151
147
150
c
0>
X
o
T3
0)
O CM
UXD •— I
(/> f~y"^
"-< CP O cn
Q6 OS
10.2
9.4
12.5
10.4
9.7
9.9
12.8
11.2
8.40
6.9
8.75
9.0
8.8
11.3
10.0
ductivity
, NaCl
C H
0 Q.
0 0.
750
740
720
845
885
855
770
750
730
795
780
745
775
760
760
0)
•v-t
oo
. — (
gg1
122
119
118
122
120
119
122
120
119
125
123
134
129.2
125.4
127.3
-t O O
\ x: ^t & '-i
CM D.\ D."\
fO O ^ •'T
O -r-i O O •-* O
•rH CO ,C £X <0 CU
r-l -P -P
•^i CO M CD 0
CO £ OS f-
0
0
.0
0
0
0
0
0
0
0
0
0
0
0
0
i1
.64
.54
.35
.64
.56
.46
.68
.43
.40
.72
.57
.40
.60
.58
.50
as i
•*-> oo
C <£
C
1 6
0.32
0.37
0.33
1.97
2.72
1.91
2.65
2.67
2.07
0.70
0.81
0.66
0.77
0.77
0.84
r
V
-------
Appendix A Results of Chemical Analyses of Lake Madison
GO
\o
Date
x
Q.
•H co
CO
«— < CO
COO
0)
x >.
O -P
•o >
0) T-lr-l
><-< -KJ
«-«\. o ^4 cyi
3
O
Q.
(0
0
s: •-<
^ o c
to a. o
-P g
*— 1 r— 4
2^ >
1 0) 1
ro -i-> co
X CM
£i
••-( CT>
Oct. 14, 1969
West
Center
Southeast
26
West
Center
Southeast
Nov. 9
West
Center
Southeast
Dec. 14
West
Center
Southeast
8.7
8.72
8.75
8.76
8.71
8.72
8.7
8.7
8.7
8.6
8.5
8.45
155
154
154
154
155
157
143
156
156
154
165
165
13.5
13.0
12.0
13.7
13.95
11.1
15.2
13.4
10.8
15.7
7.7
9.4
780
790
790
750
745
740
1610*
1610
1600
1750
1720
1730
126.3
127.3
125.4
190
203
212
124
122
122
143
133
134
0.11
0.07
0.05
0.05
0.06
0.05
0.10
0.20
0.21
0.55
0.48
0.41
0.81
0.45
0.34
0.37
0.25
0.24
0.46
0.25
0.19
0.046
0.025
0.030
0.16
0.162
0.025
0.022
0.052
0.072
0.05
0.038
22.7
23.0
28.2
17.6
9.66
8.82
9.24
16.0
16.8-
2.90
5.22
4.35
*Starting with this sample, all further conductivities were determined according to the procedure in
the FWPCA Manual and are expressed in >jmhos/cm at 25° C.
-------
Appendix A Results of Chemical Analyses of Lake Madison
Date .
Jan. 4, 1970
West
14
West
Center
Southeast
27
West
Center
Southeast
Feb. 14
West
Center
Southeast
Marchl4
West
Center
Southeast
o.
8.4
7.89
7.90
7.86
7.83
7.87
7.87
7.70
7.75
7.68
8.20
7.00
7.32
>••• — i
'.H n
CO
.— 1 fO
too
Se
173
177
175
172
186
179
175
186
182
180
71
90
122
c
0)
CD
X
o
73
CD
o o)
in O
£g
7.4
3.25
2.2
1.8
0.25
0.9
1.1
3.1
2.9
1.3
-p -P
•rH fO
-P 0
a in u
^H T> O
Q ^\ C .c o
O CT1 OSiD
OS 0 ^ CM
1830
1870
1770
1740
1911
1807
1776
1911
1859
1818
624
788
1239
i
ro O
f-t Z
•1-1 en
Z B
0.62
0.05
0.02
0.05
0.010
0.082
0.030
0.00
0.040
0.022
0.695
0.760
0.065
z
-P CM
•HO
(H 2
-P
•H cn
z a.
9.1
5.17
6.12
6.64
7.18
6.11
7.29
10.6
16.3
7.9
107.1
371.8
25.5
-------
Appendix A Results of Chemical Analyses of Lake Madison
Date
April 24
West
Center
Southeast
May 8, 1970
West
Center
Southeast
28
West
Center
June 5
West
Center
Southeast
11
West
Center
Southeast
cu
8.88
8.93
8.93
8.80
8.82
8.87
7.97
7.97
7.67
7.68
7.67
7.80
7.80
7.73
-HOO
58
.-tnj
.X
£e
150
150
131
147
148
148
176
170
180
175
175
180
174
172
c
ffi
O>
X
O
-o
0 Cs)
ino
01
•H CD
Q e
15.6
14.5
13.5
8.8
9.0
8.6
6.9
7.1
4.05
4.5
6.1
4.9
5.5
5.1
r— f
sir
44.5
52.4
36.2
36.8
29.7
32.5
31.0
28.2
33.3
27.1
Conductivity
ymhps/cm at
25° C.
1470
1480
1470
1540
1530
1540
1520
1500
0)
TJ.-I
OCJ
i— (
109
121
123
117
121
126
120
123
118
119
115
122
122
115
.— t
(0 O
0 -rH
•rH cn
.— 1
fH CT»
cn s
0.85
0.77
0.45
1.28
0.34
0.49
6.5
7.1
8.5
9.5
9.5
10.8
11.3
12.2
a.
-p
0.78
1.43
0.93
0.42
0.48
0.43
0.72
0.71
0.78
0.73
0.75
0.43
0.63
0.44
z
(0 I
•f-< co
c. X
o z:
0.29
0.24
0.28
0.26
0.22
0.23
1.14
1.00
1.38
1.21
1.03
1.32
1.18
1.37
z
9) 1
-P CO
to O
(-1 Z
-p
z, e
0.168
0.100
0.125
0.059
0.045
0.045
0.20
0.28
0.466
0.128
0.198
0.104
0.115
0.110
.—i
0) 1
-P OJ
-p
•H CJ)
Z 3.
11.3
9.4
7.6
3.4
3.1
4.6
37.0
50.2
41.9
44.0
53.7
59.5
69.0
55.8
-------
Appendix A
c
en
X
O
>- •— i
-P \ T5
• H 00 O
CO > •*-<
Date
June 18, 1970
West
Center
Southeast
July 1
West
Center
Southeast
7
West
Center
Southeast
14
West
Center
Southeast
21
West
Center
Southeast
•-T-
"3.
7.70
7.69
7.68
8,20
8.10
8.00
8.30
8.23
8.11
8.56
8.45
8.25
8.20
8.12
8.02
.,-! O
?— 1 f-H
•H 6 ID \
•P O TJ rH OJ
O^x^ •
3 1
-P CM
•r-O
uz.
-H 01
•z.-^.
69.4
54.8
51.5
3.04
3.49
10.14
1.63
1.09
2.17
2.78
1.77
3.33
3.2
2.6
2.0
-------
Appendix A Results of Chemical Analyses of Lake Madison
CO
Date
:r
a.
*co
i — ) (O
roO
Dissolved Oxygen
mg 02/1
•— i
§1f
••-tea
-PO
T3O
cxo
06 in
O3.0J
oo
r— 1
r— 1
10 O
0 -r-t
•H C/>
r-H
•* cn
to
a.
o»
0
m
3
0
JC
ex
aj
r-t O
m a.
o g>
f- S
to i
"c :r
•— i
•z.
+> ro
to O
S g
0 1
4-> CM
•HO
July 28, 1970
West
Center
Southeast
Aug. 4
West
Center
Southeast
11
West
Center
Southeast
18
West
Center
Southeast
Sept. 3
West
Center
Southeast
8.52
8.30
8.19
8.16
7.87
7.75
8.74
8.33
8.09
7.99
7.98
7.80
8.13
7.90
7.62
161
162
163
179
173
172
166
168
170
166
167
168
170
170
171
10.9
8.4
9.65
5.2
4.35
3.75
14.7
9.9
6.9
6.0
5.5
6.0
12.6
8.5
14.2
^•ss.o
45.0
>55.0
139
126
50.6
55.5
56.9
40.4
54.2
38.9
35.5
1617
1607
1607
1669
1648
1638
1597
1617
1628
1653
1663
1653
1695
1685
1675
141
141
136
140
138
138
149
144
141
123
125
123
139
133
133
26.0
27.7
27.8
30.7
31.2
31.7
25.8
30.5
28.4
31.5
20.0
33.3
29.4
30.3
28.7
0.32
0.33
0.34
0.63
0.58
0.61
0.09
0.26
0.37
0.33
0.29
0.40
0.43
0.43
0.54
0.38
0.33
0.35
0.79
0.58
0.61
0.18
0.31
0.37
0.72
0.48
0.52
0.68
0.43
0.54
0.06
0,10
0.14
1.46
1.92
1.70
0.51
0.48
0.93
0.16
0.20
0.44
0.52
0.48
0.65
0,00
0.02
0.03
0.02
0.00
0.00
0.03
0.07
0.002
0.003
0.013
0.099
0.020
0.014
1.46
1.68
1.46
9.02
4.47
5.64
5.68
8.48
11.7
3.16
4.09
6.54
5.83
4.95
4.74
-------
Appendix A Results of Chemical Analysis of Lake Madison
Date
CL
>-— i
58
^-1 OJ
—i
"o CM
o> O
in
.—i
Conductivity
pmhos/cm at
25° C.
TO -H
i-l ^
ou
1 — 1
5?
,— i
co O
O -iH
•H CO
i—l
co e
o>
CO
o.
o
f; •— «
0 O
.C CX
O E
(O
fH
0
ex
at
o
jz -H
co a.
o a>
HI e
2
CO 1
Iff
0) i
-p co
CO O
•—1
-P CM
•rH O
2 3.
Sept. 22, 1970
West
Center
Southeast
Oct. 6
West
Center
Southeast
21
West
Center
Southeast
Nov. 3
West
Center
Southeast
Dec. 19
West
Center
Southeast
8.23
8.23
8.31
8.31
8.40
8.38
8.31
8.22
8.40
8.22
8.32
8.35
8.12
8.10
8.20
169
170
170
175
174
174
164
167
169
168
167
167
183
177
157
6.0
7.1
6.9
8.1
8.5
8.9
9.9
10.0
10.6
11.8
11.9
12.8
12.2
12.8
42.2
31.9
32.6
36.3
39.0
34.2
32.6
32.1
31.3
33.0
36.3
33.0
35.0
32.0
28.3
1701
1661
1651
1787
1766
1755
1787
1828
1797
1776
1766
1736 .
1813
1823
1603
141
138
152
145
147
147
142
152
142
207
186
199
160
156
134
29.2
30.5
31.1
28.3
27.0
30.1
16.0
15.6
25.4
14.3
21.3
19.5
19.5
23.0
15.3
0.12
0.20
0.21
0.095
0.13
0.19
0.093
0.091
0.16
0.13
0.16
0.15
0.12
0.17
0.09
0.26
0.27
0.26
0.20
0.20
0.19
0.20
0.21
0.30
0.26
0.34
0.34
0.16
0.17
0.11
0.16
0.17
0.16
0.09
0.08
0.07
0.07
0.08
0.06
0.32
0.35
0.18
1.00
0.14
0.21
0.047
0.082
0.088
0.030
0.028
0.028
0.06
0.084
0.11
0.134
0.089
0.086
0.213
0.148
0.225
2.12
1.87
2.02
1.97
1.21
1.21
4.44
3.55
8.92
3.33
3.10
2.22
1.11
1.99
1.66
-------
Appendix A Results of Chemical Analyses of Lake Madison
c
(D
0)
U)
Date
Jan." 19, 1971
West
Center
Southeast
Feb. 12
West
Center
Southeast
March 5
West
Center
Southeast
April 12
West
Center
Southeast
30
West
Center
Southeast
a
7.94
7.85
7.72
7.66
7.63
7.51
7.41
7.51
7.62
8.60
8.38
8.32
8.10
8.09
8.13
in n
c o
•^ o
.-( (0
re o
194
192
189
210
202
202
190
193
201
148
149
148
148
148
149
X
O
73
0)
> ^
O
0 -^
•r-t CO
.—1
30.1
44.1
32.4
32.4
30.1
28.9
25.3
28.0
29.1
14.4
18.0
18.0
15.5
17.8
18.5
CO
0.
U)
O
.C r-t
o O
s: ex
M en
o 6
0.18
0.17
0.18
0.19
0.20
0.20
2.64
0.40
0.21
0.00
0.001
0.001
0.097
0.050
0.043
o
.c
o.
n»O
-P
0.23
0.16
0.13
0.228
0.183
0.207
0.390
0.387
0.128
0.028
0.140
0.010
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12
10
10
35.0
12.0
12.0
-------
Appendix A Results of Chemical Analyses of Lake Madison
C CO
o> o> D
Date
May 12, 1971
West
Center
Southeast
27
West
Center
Southeast
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8.12
8.18
8.24
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-------
Appendix A Results of Chemical Analyses of Lake Madison
Date
June, 1968
July
August
September
October
December
Jan., 1969
February
March
June 13
West
24
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864
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530
546
537
-------
Appendix A Results of Chemical Analyses of Lake Madison
oo
Date
July 8, 1969
Southeast
15
West
Center
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22
West
Center
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29
West
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18.3
-------
Appendix A Results of Chemical Analyses of Lake Madison
\D
Date
Aug. 14, 1969
West
Center
Southeast
20
West
Center
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26
West
Center
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Sept. 12
West
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-------
Appendix A Results of Chemical Analyses of Lake Madison
I
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Date
Oct. 14,
West
Center
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26
West
Center
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Nov. 9
West
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Dec. 14
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-------
Appendix A Results of Chemical Analyses of Lake Madison
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Jan. 14, 1970
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-------
Appendix A Results of Chemical Analyses of Lake Madison
en
K>
Date
May 8, 1970
West
Center
Southeast
28
West
Center
June 5
West
Center
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11
West
Center
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18
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22.2
22.6
22.4
-------
Appendix A Results of Chemical Analyses of Lake Madison
en
GO
Date
July 1, 1970
West
Center
Southeast
7
West
Center
Southeast
14
West
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21
West
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28
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23.2
23.6
23.8
23.2
-------
Appendix A Results of Chemical Analyses of Lake Madison
01
Date
Temperature ° C
M
a. C
^H 0 >-
T3 U) 4->
!Q o-o
[— ' —
Hardness
mg CaC03/l
£-•
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Potassium
mg K/1
Aug. 4, 1970
West
Center
Southeast
11
West
Center
Southeast
18
West
Center
Southeast
Sept. 3
West
Center
Southeast
22
West
Center
Southeast
24
24
23
25.5
25
24.5
24
24
23
17
17
16
10
13
14
9
13
13
9
13
13
10
10
13
10
12
13
50
75
80
30
70
80
50
50
89
114
120
125
36.7
29.9
27.8
18.7
17.1
15.2
24.4
24.4
17.3
13.1
12.5
11.9
15.3
15.3
18.3
651
625
632
658
655
638
641
636
627
656
646
641
671
666
696
114
113
110
122
116
117
118
118
120
121
120
119
127
124
125
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0.01
0.01
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0.01
0.01
0.01
0.01
0.01
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0.00
0.00
0.00
0.00
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0.02
0.02
0.04
0.04
0.03
0.04
0.04
0.04
0.03
0.03
0.02
0.04
0.04
0.02
0.04
56.3
56.3
57.0
74.0
73.4
74.5
77.5
76.3
75.1
47.4
47.4
47.4
50.6
51.2
49.0
0.12
0.12
0.11
0.02
0.02
0.05
0.05
0.05
0.05
0.12
0.04
0.05
0.02
0.01
0.02
109
112
108
107
109
107
110
111
93
115
116
112
119
120
117
23.0
24.0
23.6
22.9
23.5
23.0
23.5
23.9
23.1
23.2
23.4
23.1
23.6
24.2
23.8
-------
Appendix A Results of Chemical Analyses of Lake Madison
01
en
Date
Oct. 6, 1970
West
Center
Southeast
21
West
Center
Southeast
Nov. 3
West
Center
Southeast
Dec. 19
West
Center
Southeast
Jan. 19, 1971
West
Center
Southeast
o
o
Temperature
15
15
15
10
9.5
9.5
4
4
4
0.0
0.0
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0.0
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13
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12
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91
108
183
153
143
202
176
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14.1
10.8
18.8
17.3
14.1
14.2
14.2
14.2
17.9
18.9
18.9
21.9
18.3
18.5
Hardness ,
mg CaC03/l
686
681
691
696
686
671
691
678
691
682
776
632
854
829
799
•r* tO
oo
r— 1
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130
129
126
131
131
160
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128
128
144
144
124
162
156
148
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80.5
80.5
78.6
79.2
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108.7
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121
122
123
121
121
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121
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128.6
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134.5
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Potassium
mg K/1
24.2
23.7
24.2
24.2
22.9
24.2
23.4
22.8
22.9
27.4
27.7
23.9
30.1
29.7
27. 6-
-------
Appendix A Results of Chemical Analyses of Lake Madison
(Ji
Date
Feb. 12, 1971
West
Center
Southeast
March 5
West
Center
Southeast
April 12
West
Center
Southeast
April 30
West
Center
Southeast
May 12
West
Center
Southeast
o
Temperature
0
0
0
0
0
0
7
6
6.5
11.5
11
11
15
15
15
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77
82
102
150
310
320
260
261
283
1 Ul
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Turbidity
(Jackson Tui
bidity Uni1
22.0
20.5
21,8
25.9
21.8
20.6
23.1
21.2
21.2
20.6
18.3
18.7
20.5
21.2
20.0
Hardness
mg CaC03/l
868
819
829
737
771
796
617
627
622
622
623
665
632
635
650
e -i
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<-) O
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to cn
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166
153
150
148.8
147.0
152.0
116.6
117.8
117.8
118.2
118.6
118.6
96.1
111.6
100.8
cn 6
151.4
138.8
134.8
147.2
130.3
139.5
106.6
110.9
109.6
106.2
110.3
110.3
88.2
102.6
97.8
Potassium
mg K/1
28.2
28.1
27.1
24.3
28.0
26.8
22.2
21.6
22.0
21.6
22.0
21.6
18.8
20.4
18.6
-------
Appendix A Results of Chemical Analyses of Lake Madison
rH X—-
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(0
Date
May 27, 1971
West
Center
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M
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V
-------
Appendix B Results of Chemical Analyses of Lake Madison Tributaries
01
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*— * fO O CM
(CO ui O
s^ o> O
Date Q. < e s o
July 23, 1968
Bourne's Slough 13.7
24
Silver Creek at
Bourne's Slough 4.2
Bourne's Slough 9.65
29
Silver Creek at
Lagoon 165
Bourne's Slough 144
December
Treated Sewage
Lagoon
April 9, 1969
Silver Creek above
Lagoon 7.8 54.6
Silver Creek at
Laqoon 7.4 72.7
0) -3
4-* £H
(C O
^" f f~"t
-!-> Q. Q.
T-4 O1 01
> •-* O O
IH ^-i <» \_ .c r-i x;r-i
O (0 "-<^^ "BO ^ ^"
D "Z. fH ^-1 OiH O O ^O
^i TD o o 1-1 co x: D, mix
"^^^ C S i-~< •— * -4-* 4-*
S OQ.OS CO£ O£ H«6
6.40
0.68
36.2
28.6
1.2
2.0
«-H (—1 »— J
"V-^ ^^X. '^^X*.
^Z S 21
mi o> i o i
^n CO -M CM -P CM
co: coo -^* o
§2^ ^ «^ fn 21
4_> -+J
-------
Appendix B Results of Chemical Analyses of Lake Madison Tributaries
Date
August 27, 1969
Treated Sewage
Silver Creek above
Lagoon
Silver Creek at
Lagoon
Bourne's Slough
September 27
Silver Creek at
Bourne's Slough
Bourne's Slough
February 13, 14, 1970
Treated Sewage
Lagoon
Silver Creek at
Lagoon
Silver Creek Between
Lagoon and Slough
Bourne's Slough
Q.
7.1
8.0
8.2
9.0
9.05
9.35
7.10
6.89
6.95
6.93
7,16
CO
X
o
-P"\ -O
-rt CO 0>
CO > «-!
—) (0 0 CM
TO O */) O < — '
^ tfl Q\^
r— { CTi *H O> (^ CJ1
< £ Q £ OS
210
234
188
172 9.13
160 6.3
157 11.0
204 \ . 9
25C
245
552 0.0
263
•p
•H
•H r-4
-P O
O to
Z3 2-
T>
C S
O Q.
u a
1800
1200
1700
1800
1500
o
Q) ^"^^ jG •—*
"O *•— ' C^ CU ^^-^
•^ \ to O ^
fH r-l 0 -H 0 O
o o -H to x: a.
r-H r-l -(->
XI CT* 'H CT> rH CP
O6 tn E O6
518
123
504
172
191
156
8888**873 24.6 19.8
7145
7145
10491
3485
738 29.1 22.2
739 27.51 21.9
950 78.5 28,8
214 11.1 1,14
osphoru
jC • — i
cx*"****-*.
^"
rHO
too.
_f_]
tSg1
0.16
5.4
1.95
0.82
0.54
18.6
28.8
30.6
44.1
3.78
•— i •— i
\ \.
z z
to I 0)1
iH CO -P CO
c re mo
Q-Z f-tZ
£ +j
< i1 SS1
0.75
0.070
0.310
1.05 0.19*
1.13 0.64
16.82
17.95
15.23
15.75
2.47
r-t
\
•z.
Q) 1
-P CM
•HO
(H 2
4-)
•H C7>
«&-, «^
56.4
15.5
261
58.9
68.1
10.8
9.6
*Beginning with this sample nitrates were determined according to the FWPCA Manual method.
•^Starting with this sample, all further conductivities were determined according to the procedure in
the FWPCA Manual and are expressed in umhos/cm at 25° C.
-------
Appendix B Results of Chemical Analyses of Lake Madison Tributaries
C ta
Date
•H C>
CO
^0
r-4 (O
SOU
.i£
a: --* y;
a. < £
en
X
o
•o
0)
>
o
U)
cfl
Q
.—i
CM
o
o^
O* O t
-sHflS
>
*pH S
-5-2 O
~Kf)X5
-4 TJO
v. C«^CO
2> 06 10
T3.-I
OO
fiff
ID
O
-.H
.—1
CO
(9
.c
Q.
CO
,-t O
\^ JC ^s
oj a. ~\
o ^~
co jz. a,
O> M Oi
f-1
0
CU
(O
o
.C ^i
^-iO
CO CU
-4-*
o a>
^i
•z,
iO !
••H OO
ex
0^.
Is1
r-H
a> i
-t-» CO
O3 O
fa ^2*
4->
•i-l Q>
Z
Q$ 6
-(J CM
.^o
+J
s i
March 21, 1970
Treated Sewage
Silver Creek above
Lagoon
Silver Creek at
Lagoon
6.91 202 2.38
7.48 231 15.35
7,18 226 0.42
April 4
Silver Creek at
Memorial Creek
Silver Creek below
City Dump
Silver Creek at
Lagoon
Silver Creek Between
Lagoon and Slough
Silver Creek at
Bourne's Slough
Bourne's Slough
Tributary East of
Lake Madison Resort 7.40 63.8 10.6
Tributary North of
Johnson's Point 7.13 56,^ 9.8
Tributary West of
Wentworth Park 7.38 60.9 10.1
7.53 70.2 11.6
7.49 86e9 11.2
7.20 165 5.9
7.77 91.8 12.0
7.54 98.2 12.25
7.20 95.7 7.85
2687 827
2100 172
4120 481
50.5
56.9
58.3
55.9
106
52.1
73.6
41.4
306
20.2
40.9
77.5
5.1
7.4
4.1
19.92 14.26 15.19 14,30 0.770 299.9
9.30 Ool4 0.29 0.97 0.239 24.3
16.46 12.09 12.65 19.24 0.020 62.4
7.39 0.92 1.49 0.55 1.17 74.8
8.26 0.84 1.20 0.79 0.78 77.2
14.5 10.44 13 0.23 47.2
8.02 0.98 1.53 0.98 1.87 68.2
9.0 1.37 1.87 1.64 0.49 54.9
8.8 1.62 1.74 1.96 0.58 52.8
9.51 0.62 2.36 0.67 2 92.6
7.69 0.74 1.32 0.75 0.95 105.4
9.1 0.83 2.07 0.45 0.99 111.6
-------
Appendix B Results of Chemical Analyses of Lake Madison Tributaries
Date
April 4, 1970
Tributary North of
Fischer's Point
23
Bourne ' s SI ough
Madison Outlet Creek
June 5
Bourne's Slough
11
Silver Creek at
Bourne ' s Slough
July 14
Silver Creek above
Lagoon
Lagoon
Silver Creek below
Lagoon
Bourne's Slough
o.
7.72
7.91
8.90
7.38
8.10
7.70
8.53
8.45
7.56
c
0)
X
-P\ TJ
•*-> rt o>
CO > — I
1-1 O -<\
^ CO O CM
to O o) O
Ji OJ
f—t C71 iH CT>
< S 0 6
53.0 10.85
156 12.85
150 15.7
199 2.5
239
256
152
173
188
-P-P
•fH <0
•*H f^
-P 0
Z3 0> O
r-1 T5 O
Q\ CjC O
8 CD OS If)
E O ^CN
28.6 1760
40.7 2290
1719
2617
2430
1495
0)
T3 .-1
00
i— t
cSi
3.8
56.8
123
155
311
140
529
419
225
•— i
to O
o -^
-H CO
r— 1
•rH C7»
CO E
9.0
9.97
0.70
14.4
22.1
21.6
24.0
22.3
27.2
hosphate
1
O £
0.98
0.96
0.24
0.88
3.28
0.34
3.49
2.75
2.26
hosphorus
1
°^
^ o
nj (X
-p
3.90
1.17
1.04
1.18
5.37
0.43
6.11
4.65
2.74
i— t
z
CO 1
-rl CO
ccn
§z
en
< e
0.34
0.96
0.26
0.46
3.85
3.13
2.81
_,
0) 1
-P CO
mO
f-iZ
Si"
0.62
0.67
0.07
0.82
0.118
0.408
0.408
0.009
z^
-------
Appendix B Results of Chemical Analyses of Lake Madison Tributaries
Date
July 28, 1970
Silver Creek below
Lagoon
Silver Creek at
Bourne's Slough
Bourne's Slough
August 26
Treated Sewage
Silver Creek at
Lagoon
Silver Creek between
Lagoon and Slough
Silver Creek at
Bourne's Slough
Bourne's Slough
o.
9.90
7.90
8.51
6,55
7.43
7.88
7.32
8.23
CO
-HO
n a
mo
129
157
168
171
188
179
221
174
c
0)
en
X
0
•a
03
OCX)
O E lO J^ CJ>
E O a.
-------
co
Appendix B Results of Chemical Analyses of Lake Madison Tributaries
c
Date
February 17,
Silver Creek
1971
at
Memorial Creek
Silver Creek
City Dump
Silver Creek
Lagoon
March 5
Bourne's Sloi
below
below
agh
>^H
f-l {^)
.58
.-lOJ
toC_5
O. <£ c
7.57 58.9
7.07 54.8
7.38 49.7
7.13 81.2
X
0
•a
0)
O CM
w o
as*
11.6
11.4
11.6
7.6
•—i
§>
89.9
76.7
43.0
42.7
-P-P
•H m
^_| £~
-P 0
D to o
TD 0
C-SO
o e in
o a. CM
192
535
383
465
Q)
•o -H
o o
6%
23.8
106
23.2
38.7
03
Q.
at
•-* o
^H O
(0 CU
O C7)
M E
3.33
2.87
2.89
1.52
_,
2
ro 1
•.H CO
c n:
0 Z
0.80
0.49
0.51
0.80
1—1
2
0) 1
-P CO
to o
(-1 2
-p
•r-t CT>
2 e
0.830
1.120
0.885
0.425
.—i
z
CM
-HO
M ?^
-p
2 a.
63.8
72.3
39.9
59.0
-------
Appendix fi Results of Chemical Analyses of Lake Madison Tributaries
ON
at
•o
o
CD
j^
D
CO
t-t
CD
a
s
a>
Date ^
July 30, 1968
Silver Creek at
Lagoon
Bourne's Slough
April 9, 1969
Silver Creek above
Lagoon
Silver Creek at
Lagoon
August 27
Treated Sewage
Silver Creek above
Lagoon
Silver Creek at
Lagoon
Bourne's Slough
September 27
Silver Creek at
Bourne's Slough
Bourne's Slough
CD -H 1 0>
CO O D -H
S CO f-1 C r*
4-( "O +^ C t/) ^} D O)
O CD *H O >•» W) O S« — 1 • — ' " — I •«•< < — 1 QJ' — ' • — 1
s~ ^ ^t T3 u5 -p o> o 3*^^ ^-*^N^ **^^ w \^ c*\^ a^^^
jC -p CD, — ^ «rH x *f~i c co •»""* QJ oj ^3 CD d) o> ro c 3 co
4-> 0) -(-"^i ja 0 TS Ti O OCJ QO C tL, c S CTIS -H2:
Q. CD •— 1~\ f-i (0--I t-t •-> CX O W C T3
CD 4-^ -rHCT> ^^-Qcocr* coo> o o> t-t fj> co o* co CP o o>
Q — a,-— H. — a: a os os us sa se toe
-
976
741
114
122
978
1386
942
626
8 632 2.2
3.5 593 1.0
a
D
-H
10 -H
CO^>N^
CO ^^
4^
Si1
15.5
20.0
19.8
21.7
22.2
-------
Appendix B Results of Chemical Analyses of Lake Madison Tributaries
. u)
u
ON
en
o
0>
(H
D
fO
(-C
0)
Q.
£
CD
Date H
February 13, 14, 1970
Treated Sewage
Lagoon
Silver Creek at
Lagoon
Silver Creek between
Lagoon and Slough
Bourne's Slough
March 21
Treated Sewage
Silver Creek above
Lagoon
Silver Creek at
Lagoon
April 4
Silver Creek at
Memorial Creek 6
Silver Creek below
City Dump
Silver Creek at
Lagoon
Silver Creek between
Lagoon and Slough
0) -^ | o)
-P •-' f-i-M
m 0 P.H
S W £c r-i
4-t "O +•> C to C*)
0 0) ^H o >- U>O
-— » h T3 U)4-> 0) U
_C-M -— -HJri-H C TO
-t->(U -P .-! J3 OT) T3 O
QjO) '-'^v. M cn
CIS.
cn
to cn
S 6
264
249
257
394
227
26.4
39.2
45.0
107
0)
to
a) C D ffl
ens >^z
C TJ
nJ cn O cn
S S co 6
0.41 522
0.67 498
0.45 449
14.5 566
1.60 146
0.11
0.29
0.46
0.28
e
tffSs^
fO ^
^_)
O CT*
d. S
29.8
34.2
31.8
40.2
28.0
-------
Appendix B Results of Chemical Analyses of Lake Madison Tributaries
>ft
* "°
o
©
3
-H
rtj
Q.
g
Date fS
April 4, 1970
Silver Creek at
Bourne's Slough
Bourne's Slough
Tributary East of
Lake Madison Resort
Tributary North of
Johnson's Point
Tributary West of
Wentworth Park
Tributary North of
Fischer's Point
23
Bourne's Slough
Madison Outlet Creek
«$
M-5
0
-p <&
0.<£
6
4
3
1
2
2
4
1.5
OJ
-O
•— 1^-~_
I
0
0
0
0
0
2
i-l CJi
.024
.008
.539
.080
.285
.266
M4-1
^*C
>- rs
-!-» C
^t O >-
T5 (/5 4-*
-Q O "O
M ^5 erH
2^2-'Q
-g-
196
186
391
280
268
415
21
19
u> n •— i
in O fi\^
CO O 3 (0
cm -HO
-o o o
f-i ' •-« 2>
CO Dl fO 8
JP s C?
261 64.0
259 71.9
139
87.4
104.3
98.6
438 97.2
561 91.9
*—i -™i
0) p" 0>
Q.CJ CU<
O, O
O
o
0.
0.
0.
0.
0.
0.
-
0.
0.
O"1 ^ O"i
S n S
00 0.16
01 0.23.
01
00
00
00
00 0.05
00 0.04
3 «o
D °5
•— « r— 1 ® .— 5 __ J— i
-------
Appendix B Results of Chemical Analyses of Lake Madison Tributaries
C
0
0)
h
D
•+->
<0
to
0)
0)
Date H
July,14, 1970
Silver Creek above
Lagoon 27
Lagoon 28
Silver Creek below
Lagoon 28
Bourne's Slough 27
28
Silver Creek below
Lagoon 27
Silver Creek at
Bourne's Slough
Bourne's Slough
August 26
Treated Sewage
Silver Creek at
Lagoon
Silver Creek between
Lagoon and Slough 27
Silver Creek at
Bourne's Slough
Bourne's Slough
0) ^H 10)
+> r-1 f-t -P
<0 o 3 "-*
M-i -o -PC
O Q) •<-< O >-
-— . (-, T3 tn -P
-p Q) .p,-, Ja o -a
O. <1> •— f\ In <0 -H
Q) *4n , j «T» T H™) O
>.r "• ' ^^* i1-* ' "^
f ^ x^_x LJLiv— ^ r"^ ** *'
1
^
2
2
6
5
1.5
1
6
3
17.
22.
21.
16.
1
7
4
5
104
28.
29.
11.
11.
19.
17.
10.
0
8
4
4
7
7
4
Hardness
mg CaCO /I
1112
1145
888
724
770
921
651
987
908
947
947
651
•H tO
00
OJ CT>
0 6
283
179
201
153
174
184
117
193
204
221
201
181
.—i
0) D
£°
cSS1
0.01
0.01
0.01
0.00
0.01
0.01
0.01
0.01
0.01
0.01
0.01
0.01
r— 1
-------
Appendix B Results of Chemical Analyses of Lake Madison Tributaries
oo
O)
O (i -O
Date
October 6, 1970
Bourne's Slough
January 19, 1971
Silver Creek at
Lagoon
February 17
Silver Creek at
Memorial Creek
Silver Creek below
City Dump
o
r-i
Q. _ ^
3
1 0.194
1 0.130
1 U)
M-P
£~C
>• O
-PC
•MO >-
T310-P
•r-l^^ *r-{
J3 OT3
M 00 "H
£2-°
24.9
30.9
81
86
•— i
0) CO
u>O S^n
(DO S^^
C
c S
(0 en
86.9
116.7
5.4
8.7
o>
U)
0)r-l ^1
C"^N> S>1\^
fO C D <0
cnS -H "Z.
C "O
S S CO S
0.32 156
10.2
0.19 12.3
0.33 57.4
e
*r*i
ta ^H
in ^\
ra V
-p
o en
a. S
24.4
17.1
11.2
10.5
Silver Creek below
Lagoon 0 1 0.018 34.7 168 40.5 0.01 0.12 13.2 0.23 13.1 11.7
March 5
Bourne's Slough 25.0 164 42.8 0.33 16.5 0.43 23.7 9.9
-------
Appendix C Results of Chemical Analyses of Lake Herman
Date
Juper«68
July
September
October
November
December
January, 1969
February
March
May 6
Center
June 26
Center
Q.
8.49
8.62
8.2
7.85
8.2
8.3
8
9.7
7.8
7.15
8.0
TK co
c R
•H U
^i CO
-
O -P
•H
•o >
0) .H .-1
> .-( -P O
<— 1 ^\ O (0
0 CM . P Z
in O -—IT)
in Q\ C 6
•H en o cn o Q.
Q a OS O CL
8.1
8.9
9.2
10.8
8.2
6.0
1.7
1.0
3.9
8.86 395
8.9 395
O)
-p
m
£.,
CL.
in
^-( O
(P \, -C •— i
•rH^v^ (DO ^J"
M r-l O -rH O O
o o -M co _c a.
r- < r— 4 -P
x: cn ->H cn JH cn
u e co s o H
6.75
6.7
21.5
13.1
12.8
15.0
15.5
18.35
4.95
7
3.2
Phosphorus
/I
"t
r-l O
(0 (X
£ i1
0.55
0.36
0.37
0.39
0.27
0.34
0,29
0.33
2.0
2.0
r-t
•z.
m \
CDC
cn
-P CM
O> O -rH O
f-t"Z M Z
-P -P
•H cn •*-' cn
2 g 23.
0.5*
0.06
0.08
0.47
0.27
0.065
0.495
1.25
2.75
0.75
0.44
Nitrates from June, 1968, through August 22, 1969, are actually nitrate plus nitrite and are
determined according to the procedure on page 41 of the Hach Manual.
-------
Appendix C Results of Chemical Analyses of J-ake Herman
Date
July 3, 1969
Center
10
Dredge
Center
17
Dredge
Center
24
Dredge
Center
Southeast
31
Dredge
Center
Southeast
Aug. 7
Dredge
Center
Southeast
o.
8.15
8.3
8.45
7.1
7.25
8.6
8.4
8.25
8.1
8.15
8.4
•rH CO
CO
-^ o
r-< (0
a) O
s^
•—I m
155
161
159
163
161
163
163
164
173
173
187
175
172
182
0)
• — ^v*
0 CM
O)O 1-1
o) C^ ^*^
•rH en o en
Q 6 O £
9.6
9.9
9.8
7.3
7.8
7.2
7.1
8.55
8.25
8.1
8.9
7.8
8.1
8.3
•«-*
-*-i • — i
-MO
O (O
3 Z
•a
c e
o a
o a.
410
420
425
380
375
380
385
380
400
385
400
420
415
425
a)
-»->
6 i1 « ? 5 i4
6.00
4.80
4.25
2.5
2.5
5.21
6.09
4.38
8.04
5.84
5.36
5.06
5.30
5.06
Phosphorus
/I
•sr
-H 0
(O CLr
-P
H i"
0.75
0.70
0.71
0.73
0.78
1.08
1.06
1.11
1.22
1.07
1.24
1.36
1.19
1.21
•— i
•z.
(0 1
•rH CO
C X
O 2
P
< i1
0.11
0.18
0.15
0.25
0.17
0.17
0.14
0.16
0.28
6.25
0.28
0.30
0.47
0.29
•—< •— i
0) 1 C*> •+-> CM
(0 O v-i O
PH ?^ £H -S
-fj -p
•r-i en *r-i en
Z S 23.
0.35
0.22
0.20
0.05
0.09
0.015
0.01
0.005
0.01
0.01
0.00
0.115
0.075
0.11
-------
Appendix C Results of Chemical Analyses of Lake Herman
Date
Aug. 15, 1969
Dredge
Center
Southeast
22
Dredge
Center
Southeast
28
Dredge
Center
Southeast
Sept. 4
Dredge
Center
Southeast
17
Dredge
Center
Southeast
a
8.4
8.4
8.25
7.75
8.3
8,25
8.25
8.50
8.2
8.25
8.4
8.15
8.0
8.4
c o
•^ o
«— 1 to
03 CJ
J^
< i1
171
170
180
172
172
178
174
174
178
179
176
180
180
181
187
c
0)
a*
X
O
T5
i — i ^^
O CM
«>O .-i
co (^ """"^^
•>H QJ O O>
OB OS
8.4
7.9
10.0
7.40
7.95
9. .50
8.1
8.0
9.2
7.6
7.8
8.1
8.5
8.1
10.3
-p
•rl
£ U
O (D
3 Z
•a
c e
o a.
U 0.
380
395
400
375
325
360
440
400
405
400
400
402
300
350
in
0) 2
-P ^i
CO O
.C £.
a a.
U) CO
•-( O O
(B \ XI r-l .C r~(
•o .-i CM >
0)1 0) 1
-P CO -P CM
-H CT>
2 S 2 i.
0.075
0.10
0.053
0.032
0.020
0.068
0.050*
0.00
0.00
trace
trace
0.00
0.13
0.13
0.00
*Beginning with this sample all nitrates were determined according to the FWPCA Manual method.
-------
ro
Date
Oct. 4, 1969
Dredge
Center
Southeast
19
Dredge
Center
Southeast
Nov. 3
Dredge
Center
Southeast
North
Dec. 21
Dredge
Center
Jan. 4, 1970
North
Southeast
"a.
8.3
8.3
8.6
8.4
8.4
8.5
8.35
8.35
8.35
8.35
8.1
8.12
8.15
8.15
Appendix C Results of Chemical
c
en
X >,
O -P
4->~\ T3 >
-rH CO 0) -rH <-4 rH -t->0 -Or-,
•rH O I— <~\ O CO "-l^\
•—1(0 OCM -3~Z. f-i^->
(OO 05 O •— i "O OO
_X 01 Q\ C £ -H
• — i CT> e*~f CT* O CJ* O O- f| en
<:£ Qe o £ o Q. o £
183
182
189
179
179
189
177
176
178
178
187
188
199
215
8.3
8.2
7.9
11.95
11.6
12.6
13.0
13.5
13.3
13.6
11.6
11.8
10.8
8.8
389
400
450
867*
423
430
887*
900
900
900
990
1000
1030
1090
4.82
4.58
5.06
3.86
3.86
3.62
3.80
3.62
3.38
3.38
4.17
4.41
5.3
4.3
Analyses of Lake Herman
in
o> 3
(0 O
.C £
a a.
lf> tfl r-t
•— 1 O O \.
\ .c -« .c -< -z.
Ol CL'^'N CU "^\ fO I
CO O ^T ^" •*-* 00
O-H oo <— i O ex
•r-i(/) ^CL, roCL, OS
•<-( C? M C7* O CT> S Cn
we oe f-s CO
to O
h -z.
SS1
0.000
0.023
0.16
0.012
0.024
0.015
0.04
0.12
0.10
0.04
0.070
0.035
0.00
0.11
> — i
0) 1
-P CN
•^ o
-P
Z ^
4.84
6.67
6.00
5.82
5.84
4.22
6.2
4.6
7.1
7.6
3.21
1.09
5.9
9.9
*Starting with these samples, all further conductivities were determined according to the procedure
in the FWPCA Manual and are expressed in ^imhos/cm at 25° C.
-------
Appendix C Results of Chemical Analyses of Lake Herman
w
Date
fc
Alkalinity
mg CaC03/l
0)
Ol
>~
X
o
T3
0)
>rH
rH\
O CM
0) O
05
•rH TO
Q S
>-
-p -P
•rH CO
SB
-P 0
o\ •
p in O
rH TJ 0
Q \ c .co
8cp o S in
5 o a, CM
0)
TlrH
rHrH
00
rH
6W
i—>
to O
O TH
TH in
i-H
•r-* CJ1
CO S
o
.C -H
a, \
rHO*
nj a.
2 g1
r— (
z
•a i
i-» CO
c or
0 Z
Ji1
r-H
0) 1
-P CO
to O
rH Z
-P
•H C?
Z 6
rH
0) 1
-P CM
•H 0
rH Z
-P
•H CT>
2: ^
Jan. 23, 1970
North
Dredge
Center
Southeast
Feb. 6, 7
North
Dredge
Center
Southeast
March 14
North
Dredge
Center
Southeast
April 24
North
Dredge
Center
Southeast
7.60
7.52
7.54
7.60
7.53
7.40
7.50
7.30
7.00
6.90
8.87
8.50
8.17
8.18
8.22
8.14
235
202
202
220
230
214
217
234
54.0
38.3
41.2
51.0
147
146
145
138
5.15
4.2
7.0
2.7
6.5
2.3
6.3
5.2
10.6
13.5
11.8
11.8
12.1
11.1
1220
1080
1080
1140
1160
1120
1110
1180
210
150
160
35.8
28.3
33.2
30.6
7.2
7.0
6.7
6.5
7.7
7.2
7.7
7.2
6.4
5.5
3.8
5.3
4.8
5.3
5.8
5.8
11.5
7.2
7.2
7.8
23.7
23.4
23.0
21.3
7.98
7.32
4.93
6.03
12.4
12.9
12.8
12.5
0.52
0.48
0.46
0.59
0.52
0.48
0.52
0.39
1.35
0.93
0.62
1.07
0.26
0.26
0.23
0.20
0.74
0.55
0.57
0.68
0.72
0.59
0.63
0.52
1.99
1.33
1.52
1.91
0.63
0.59
0.56
0.56
1.36
1.05
0.77
0.88
0.26
0.43
0.43
0.33
0.27
0.32
0.21
0.33
0.00
0.10
0.10
0.02
0.07
0.05
0.00
0.03
1
1
0.74
0.9
0.15
0.08
0.21
0.29
4.72
9.10
4.40
3.33
10.6
9.71
8.94
11.2
97.4
92.2
69.4
60.8
9.4
7.0
5.8
9,4
-------
Appendix C Results of Chemical Analyses of Lake Herman
Date
Way 8, 1970
North
Dredge
Center
Southeast
27
North
Dredge
Center
Southeast
June 4
North
Dredge
Center
Southeast
11
North
Dredge
Center
Southeast
Q.
8.10
8.11
8.08
8.26
8.30
8.27
8.35
8.34
8.27
8.22
8.27
8.33
8.20
8.31
8.24
8.74
Alkalinity
mg CaC03/l
149
149
148
148
147
155
155
156
153
156
157
158
160
163
161
165
c
0)
en
X
0
-o
o>
> ^H
O CN
in O
in
Si1
7.8
8.2
9.45
8.35
8.9
9.5
7.8
7.4
9.2
r-l
24.9
22.6
27.2
24.0
17.9
17.9
19.4
19.6
15.9
18.1
17.6
25.0
Conductivity
jumhos/cm at
250 c.
785
785
779
785
733
712
795
806
800
800
800
800
Chloride
mg Cl/1
6.5
5.5
5.1
5.1
4.8
5.5
5.5
5.5
5.5
4.3
4.8
5.1
4.8
5.1
4.8
4.3
r—t
CM
OJ O
O -r-l
•r-l CO
, — 1
£ g
10.4
11.0
10.6
9.5
10.9
10.9
10.9
10.4
10.9
10.5
10.7
9.5
11.6
11.5
11.3
8.5
o>
-»->
fO
x:
ex
in
o
x: r-\
-3-
o o
+->
0.23
0.22
0.23
0.21
0.33
0.31
0.31
0.32
0.32
0.34
0.33
0.35
0.31
0.35
0.30
0.42
01
D
(n
O
Q.
U)
O
.C — I
cx\
•=t
r~< O
a) CX
O CD
H &
0.26
0.32
0.33
0.30
0.46
0.50
0.52
0.56
0.47
0.48
0.45
0.49
0.48
0.49
0.47
0.92
(0 1
••H CO
c pa
O "Z.
0.29
0.29
0.35
0.27
0.37
0.26
0.37
0.27
0.15
0.17
0.18
0.30
0.37
0.55
0.49
0.40
r— {
co
m o
+>
•H cn
2; 6
0.09
0.08
0.09
0.06
0.14
0.22
0.15
0.17
0.11
0.14
0.15
0.12
0.07
0.03
0.05
0.06
. — i
4-> CN
•HO
+J
•H CJ1
^ 3s
4.6
4.6
4.6
5.2
0.0
0.0
1.26
0.5
1.6
3.2
1.6
1.6
3.4
3.2
4.5
1.6
-------
Appendix C Results of Chemical Analyses of Lake Herman
-j
en
Date
o.
Alkalinity
rng CaCOg/l
Dissolved Oxygen
( ™9 ^2/1
i
COD
mg/1
i
Conductivity
umhos/cm at
^5° C.
1
Chloride
img Cl/1
. — t
nj O
o VH
•* CO
1 — 1
5?
0)
CO
jc
o.
en
0
JT -H
0 O
.c a.
rH CJ1
O e
U1
a
rH
0
"5.
in
o
-C rH
-H O
03 a-
. — i
z
CO 1
-rH CO
§ Cn
< 6
rH
0) 1
4->
-------
Appendix C Results of Chemical Analyses of Lake Herman
Date
July 21, 1970
North
Dredge
Center
Southeast
28
North
Dredge
Center
Southeast
Aug. 4
North
Dredge
Center
Southeast
11
North
Dredge
Center
Southeast
X
Q.
8.89
8.85
8.57
9.58
9.10
9.07
8.92
10.11
8.89
8.87
8.94
9.47
9.33
9.12
9.17
10.17
~CO
.-i eo
(BO
Si1
150
150
148
107
152
170
152
114
162
161
160
132
158
159
156
136
0>
X
0
•o
O
U)
Si*
8.9
8.7
6.8
11.0
11.5
12.1
8.9
14.8
5.8
6.2
6.9
7.4
19.0
15.0
15.2
15,8
•r-i (0
+-> 0
.-i T3 0
Q\ c.co
o cr o EIO
784
784
794
712
768
778
778
747
51.6 778
^55.0 788
?55.0 778
54.5 747
71.7 758
62.6 768
53.2 768
86.4 758
O) r-t
Tl o
o
( — 1 «
5.77
5.05
5.53
5.33
5.53
5.29
6.25
5.77
5.53
5.77
5.29
5.29
5.53
5.77
5.29
5.53
*— i
to O
O -^1
•^ CO
•—t
u> W
17.7
15.2
18.2
8.3
18.5
19.4
18.0
8.4
20.7
19.8
19.4
13.5
19.5
19.9
23.9
12.4
(D
<0
a.
U)
0
.C — i
0 O
.c a.
(-1 Cp
0.72
0.67
0.71
0.50
0.83
0.88
0.88
0.10
1.07
1.11
0.97
0.75
0.93
1.14
1.09
0.18
o
a
10
o
JC •-<
-i O
a.
o en
1.25
1.29
1.06
1.04
1.19
1.16
1.10
0.50
1.56
1.66
1.48
1.29
1.71
1.45
1.46
1.45
, — i
ID I
1-1 co
C DC
0 Z
0.28
0.19
0.21
0.19
0.11
0.27
0.15
0.34
0.25
0.20
0.36
0.26
0.26
0.18
0.29
0.25
. — i
•z.
en
n) O
fa ^"
-f-* O^
0.001
0.005
0.066
0.003
0.01
0.02
0.01
0.00
0.00
0.02
0.00
0.03
0.000
0.058
0.010
0.000
2
1
O
£_t
-»J CT»
2.5
3.2
2.6
3.6
1.36
1.23
2.36
1.00
3.34
2,22
2.78
3.34
3.05
4.09
2.84
6.75
-------
Appendix C Results of Chemical Analyses of Lake Herman
Date
Aug. 18, 1970
North
Dredge
Center
Southeast
Sept. 3
North
Dredge
Center
Southeast
22
North
Dredge
Center
Southeast
Oct. 6
North
Dredge
Center
Southeast
13
Dredge
a
9.04
9.19
8.97
9.63
9.23
9.32
9.23
9.99
9.16
9.16
9.15
9.14
9.03
9.07
9.07
8.80
8.93
>— -i
"co
•rHO
r-l (0
COO
,X
r— 1 CT»
163
163
163
135
173
176
176
138
177
179
176
168
186
187
186
189
185
c
01
X
0
TJ
01
> r-l
r— 1 ^\
0 CM
tn o
(O
•rH CTI
a e
9.2
9.0
9.1
11.4
9.8
10.9
10.2
10.0
9.6
9.5
9.5
9.4
10.4
r— 1
f^*V^
O en
O E
62.0
56.9
55.5
61.3
54.9
59.8
54.6
71.3
46.7
54.5
50.2
58.1
48.0
46.7
42.7
61.3
51.5
-p -P
••H CD
-P 0
3 in o
T> 0
C JZ 0
0 E IT)
o a»cM
788
778
788
730
771
797
787
747
806
800
800
786
873
873
873
883
874
TD r-l
fH —1
oo
r— 1
.C CTI
U 6
4.8
4.8
4.8
5.8
5.4
6.7
5.7
5.4
5.94
8.78
6.20
7.23
5.68
6.20
5.68
6.72
6.72
* — i
as O
0 -rH
.rH tO
• (
tH CT>
27.8
27.0
26.3
14.3
26.2
26.3
26.5
20.7
21.9
23.9
23.9
22.5
23.3
24.5
24.5
27.6
24.8
a>
CO
a.
U)
o
0 O
x: a.
•p
f-t 'CT
o e
1.28
1.16
1.13
0.61
1.44
1.48
1.61
0.53
1.50
1.52
1.56
1.26
1.74
1.66
1.71
1.48
1.61
3
0
a.
to
0
.C r-H
r-«O
O Dl
1.98
1.89
1.92
1.51
2.13
1.96
1.91
1.39
2.11
2.15
2.68
2.36
2.81
2.80
2.34
3.03 -
3.01
r— 1
(0 1
'ex
oz
§ a>
< e
0.10
0.07
0.07
0.10
0.07
0.06
0.09
0.10
0.01
0.04
0.06
0.03
0.03
0.24
0.01
0.04
0.15
i — i
4.30
3.16
3.26
4.20
1.56
4.19
2.09
3.13
1.25
2.18
2.07
1.61
1.46
2.02
1.40
1.00
1.50
-------
Appendix C Results of Chemical Analyses of Lake Herman
oo
Date
Oct. 21, 1970
North
Dredge
Center
Southeast
Nov. 3
North
Dredge
Center
Southeast
Dec. 19
North
Dredge
Center
Southeast
Jan. 19, 1971
North
Dredge
Center
Southeast
"ex
8.97
8.97
8.98
8.66
8.91
8.85
8.85
8.55
8.18
8.14
8.11
8.23
7.93
7.84
7.78
7.77
>, ^-H
-H 00
c O
-^ CJ
r— t O3
<0 CJ
5 i1
188
188
187
186
190
190
190
185
212
225
219
223
240
239
240
265
c.
a>
CT>
X
0
-o
O CM
ul O
U)
S i1
10.6
10.8
11.0
9.8
12.5
12.3
13.0
12.2
10.8
I0»0
11.2
6.1
5.0
4.1
4.5
• — i
O Cn
O B.
38.4
38.4
36.1
47.7
36.0
39.7
39.5
43.0
30.4
36.8
31.8
36.0
31.4
32.8
29.4
31.9
•rt CO
-MO
D u> O
-o o
C.CO
o e in
o a,cM
893
873
904
883
873
873
873
893
992
1022
1022
1052
1082
1092
1092
1208
0)
•a -<
FH ' — '
0 O
. — i
6%
6.20
6.20
6.72
6.72
6.20
6.20
6.20
5.68
6.20
7.23
7.75
7.23
6.97
6.97
6.46
4.91
raO
O ••— (
-.-(CO
, — 1
18.0
16.8
18.8
18.0
20.0
14.6
16.3
15.5
20.8
18.6
21.3
18.0
31.3
28.7
28.9
24.4
Phosphate
4/1
0 O
-C CX
o s
1.70
1.72
1.70
1.07
1.66
1.72
1.67
1.08
1.70
1.58"
1.61
0.98
1.99
2.02
1.84
1.52
Phosphorus
4/1
^ o
ro ex
-p
o cn
H- £
4.33
2.02
3.57
1.66
3.23
2.46
2.31
1.92
2.14
1.95
2.02
1.48
2.07
2.09
1.74
1.56
CO 1
c :r
0 Z
0.03
0.12
0.18
0.05
0.02
0.02
0.02
0.03
0.05
0.39
0.89
0.11
0.45
0.12
0.21
0.41
• — i
z
CD 1
+-> ro
ro O
M Z
£g
0.127
0.025
0.055
0.082
0.057
0.051
0.000
0.078
0.100
0.123
0.102
0.029
0.19
0.22
0.21
0.11
• — i
-P CM
•H O
f-t Z
•H cn
4.44
4.64
2.62
10.8
1.44
1.11
3.23
1.31
3.55
2.87
3.33
2.22
5.24
5.52
4.84
4.12
-------
Appendix C Results of Chemical Analyses of Lake Herman
-j
\D
Date
Q.
CO
^HO
•— « (8
too
«~~i O^
< e
c
Q)
on
X
0
•o
0 Cv)
tn O
3 3
^
Conductivity
>imhos/cm at
25° C.
.—1
•z.
as i
••H CO
c a:
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.^ O
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•i-t rj>
2 a.
Feb. 12, 1971
North
Dredge
Center
Southeast
March 5
North
Dredge
Center
Southeast
April 12
North
Dredge
Center
Southeast
30
North
Dredge
Center
Southeast
7.71
7.52
7.82
7.66
7.54
7.37
7.48
7.47
8.56
8.40
8.37
8.42
8.54
8.49
8.46
8.29
262
261
277
290
154
132
194
198
163
163
163
139
164
162
162
154
2.9
1.3
2.9
3.8
5.1
5.0
3.1
3.0
13.3
12.5
11.8
12.8
10.7
11.0
10.7
10.3
37.0
30.9
36.4
37.2
39.7
49.9
47.6
39.2
25.6
25.6
23.9
25.7
35.7
28.4
32.3
28.1
1267
1257
1309
1330
720
633
891
900
731
731
731
632
726
726
726
706
6.20
6.20
5.68
5.94
5.4
6.2
6.5
6.2
5.3
4.9
4.8
4.8
5.3
5.1
5.9
4.9
37.4
38.1
40.1
41.4
20.3
19.1
27.7
26.6
17.2
18.5
15.5
17.2
26.9
21.3
20.5
21.0
1.69
1.72
1.82
1.93
1.52
2.08
2,03
1.86
1.03
1.03
1.01
0.71
0.80
0.83
0.80
0.49
1.79
1.88
4.77
8.20
1.90
2.78
2.50
2.22
1.50
1.47
1.49
1.23
0.80
0.83
0.80
0.88
0.28
0.52
0.30
0.37
0.38
0.76
0.67
0.69
0.08
0.02
0.03
0.05
0.00
0.00
0.00
0.06
0.237
0.181
0.205
0.121
0.585
1.315
0.635
0.495
0.009
0.025
0.030
0.027
0.03
0.02
0.02
0.03
3.01
2.16
3.01
2.38
31.3
32.5
25.7
29.8
20
20
13
20
12.0
19.8
21.0
19.8
-------
Appendix C Results of Chemical Analyses of Lake Herman
Date
"a.
Alkalinity
mg CaC03/l
[
!
Dissolved Oxygen
mg C>2/1
§1?
-P-P
•5 6
-PO
DCOO*
•oo
OS Lf)
1
Chloride
mg Cl/1
i — i
i
-P CM
•HO
-p"
•H CT»
May 12, 1971
North
Dredge
Center
Southeast
27
North
Dredge
Center
Southeast
8.36
8.39
8.35
8.28
8.62
8.59
8.63
8.51
166
167
166
164
170
170
170
171
9.85
9.9
10.2
9.9
21.4
11.9
12.5
11.7
29.6
19.9
20.8
20.1
36.3
35.8
37.3
34.7
736
736
736
746
730
710
710
730
5.2
5.4
4.6
4.6
4.9
4.7
5.0
4.6
11.5
16.2
8.7
9.0
19.2
19.1
19.1
21.3
0.68
0.69
0.69
0.48
0.60
0.59
0.59
0.40
0.68
0.75
0.70
0.56
0.76
0.78
0.85
0.65
0.00
0.04
0.03
0.05
0.02
0.02
0.02
0.00
0.01
0.02
0.02
0.005
0.008
0.012
0.006
0.005
0.0
0.0
0,0
0.0
4
1
4
4
-------
Appendix C Results of Chemical Analyses of Lake Herman
CO
Date
June, 1968
July
August
September
October
November
December
Jan. s 1969
February
March
May 6
Center
o
S-l
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501
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517
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704
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246
248
-------
Appendix C Results of Chemical Analyses of Lake Herman
00
i-O
Date
June 26, 1969
Center
July 3
Center
10
Dredge
Center
17
Dredge
Center
24
Dredge
Center
Southeast
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Center
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383
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380
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0.0
6.6
2.2
-------
Appendix C Results of Chemical Analyses of Lake Herman
CO
co
Date
Aug. 7, 1969
Dredge
Center
Southeast
15
Dredge
Center
Southeast
22
Dredge
Center
Southeast
28
Dredge
Center
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Sept. 4
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-------
Appendix C Results of Chemical Analyses of Lake Herman
•
o
^
O O>
Date
Sept. 17,
Dredge
Center
Southeast
Oct. 4
Dredge
Center
Southeast
19
Dredge
Center
Southeast
Nov. 3
Dredge
Center
Southeast
North
Dec. 21
Dredge
Center
fO
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1969
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15.0
15.9
13.8
13.2
16.4
13.3
16,7
12.3
18.0
15.0
13.0
-------
Appendix C Results of Chemical Analyses of Lake Hernan
oo
CJl
Date
Janr 4, 1970
North
Southeast
23
North
Dredge
Center
Southeast
Feb. 6, 7
North
Dredge
Center
Southeast
March 14
North
Dredge
Center
Southeast
o
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HC r->
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t-t ni -<-t M
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489
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28 93.4
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-------
Appendix C Results of Chemical Analyses of Lake Herman
oo
0s-
Date
April 24,
North
Dredge
Center
Southeast
May 8
North
Dredge
Center
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27
North
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mg K/1
15.1
15.3
15.1
14.5
16.0
16.2
16.2
16.0
18.0
17.8
18.0
18.1
-------
Appendix C Results of Chemical Analyses of Lake Herman
CO
-J
Date
June 11, 1970
North
Dredge
Center
Southeast
18
North
Dredge
Center
Southeast
July 1
North
Dredge
Center
Southeast
7
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45.7
45.7
46.3
46.3
CD
-------
Appendix C Results of Chemical Analyses of Lake Herman
Date
July 14, 1970
North
Dredge
Center
Southeast
21
North
Dredge
Center
Southeast
28
North
Dredge
Center
Southeast
Aug. 4
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28.7
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31.8
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17.0
16.6
17.4
17.3
17.2
17.2
18.1
17.9
17.9
18.2
-------
Appendix C Results of Chemical Analyses of Lake Herman
00
vD
Date
Aug. 11, 1970
North
Dredge
Center
Southeast
18
North
Dredge
Center
Southeast
Sept. 3
North
Dredge
Center
Southeast
22
North
Dredge
Center
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17.5
17.2
17.4
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17.6
17.7
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17.9
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18.1
18.2
17.6
18.1
17.6
18.6
-------
Appendix C Results of Chemical Analyses of Lake Herman
rH
CO
\D
O
Date
Oct. 6, 1970
North
Dredge
Center
Southeast
13
Dredge
21
North
Dredge
Center
Southeast
Nov. 3
North
Dredge
Center
Southeast
Dec. 19
North
Dredge
Center
Southeast
Temperatun
15.5
16
15.5
16
7
10
10
10
11
3
3
3
3
0.5
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0.0
0.3
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37
41
48
28
56
50
54
34
63
50
41
43
Turbidity
(Jackson Ti
bidity Uni'
20.5
20.5
18.4
25.9
26.3
23.5
21.0
21.0
31.4
19.6
21.3
25.8
23.1
21.1
23.2
21.1
21.1
in
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C CO
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400
405
400
400
395
395
400
400
402
421
408
401
414
454
480
480
507
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83.5
85.9
84.0
83.5
81.7
86.8
83.5
83.5
80.2
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83.5
95.8
105
118
113
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Magnesium
mg Mg/1
43.0
44.1
43.0
44.1
42.4
48.1
47.8
48.7
49.0
42.5
46.5
47.1
46.5
52.9
53.8
51.2
56.4
co C
c
0.03
0.03
0.03
0.13
0.04
0.04
0.02
0.03
0.02
0.02
0.04
0.02
0.02
0.05
0.07
0.09
0.03
i — i
3 CO
40
39
39
40
38
39
38
38
39
39
39
39
39
41.1
40.8
40.8
41.3
Potassium
mg K/1
18.3
18,9
18.4
19.0
18.2
18.4
18.2
18.2
18.4
18.6
18.1
18.0
18.1
20.7
20.6
21.0
21.0
-------
Appendix C Results of Chemical Analyses of Lake Herman
Date
Jan. 19, 1971
North
Dredge
Center
Southeast
Feb. 12
North
Dredge
Center
Southeast
March 5
North
Dredge
Center
Southeast
April 12
North
Dredge
Center
'Southeast
iperature C
£
f-
0.0
0,0
0,0
0.0
0
0
0
0
0
0
0
0
8.5
8,5
8
8
3 w
^ Q
0
x: ^P x:
Q. QJ 0 1=
3J *4-i - C \
-P C O (0 t*)
•HO O)O
•O U) >- 0>(J
••-i .v -P cm
X> 0 -^ T3U
f-i «S TD
D •-) -H
25.1
22.4
21.9
30.9
22.3
22.5
22.5
27.0
24.2
27,9
26o7
24.2
28.2
28.9
28,2
29.4
M
5?
612
523
523
592
572
553
562
622
340
268
402
405
323
322
321
276
e -<
•H (B
0 O
r— <
(0 cn
0 6
99.4
106
110
126
116
119
118
123
65.8
53.9
84,6
85.6
69.4
68.4
69.4
57.2
• — i
0) D
0.0
Q.
o cn
0 6
0.01
0.00
0.01
0.01
0.01
0.01
0.01
0.01
0.01
.— 1
0)
C 0,
o
0.03
0.02
0.02
0.02
0.04
0.01
0.02
0.01
0.14
0.15
0.11
0.15
0.04
0.04
0.03
0.04
oj cn
c -s.
cn
^ s*
71.8
61.3
62.3
69.4
71.1
69.0
82.3
71,1
35.9
28.9
47.2
47.2
38.9
38.3
38.3
32.1
0)
-------
Appendix C Results of Chemical Analyses of Lake Herman
vQ
IV)
Date
April 30,
North
Dredge
Center
Southeast
May 12
North
Dredge
Center
Southeast
May 27
North
Dredge
Center
Southeast
o
iperature C
e
0)
1971
11.5
11.5
11.5
11.5
15
15
15
15
17
16.5
16
15
*•<
s
o
Q. ®
Q) <4-<
Q —
9
9
9
7
8
8
9
6
8
12
8
6
3
••-I
.c
o 3
X C
-p c r>
-r4 O
"O U) >.
J3 0 -rH
f-4 fO "O
£^3j3
26.3
26.3
26.3
32.0
30.1
28.2
30.4
30.1
25.9
28,2
30.1
30.1
at o
U5O
(MO
C fS
•oo
(0 cp
376
373
349
321
345
341
349
341
340
346
340
340
*rH (O
o o
<— }
fo en
0 6
69.0
67.4
69.4
65.6
50.0
62.7
49.7
51.5
70.3
71.3
69.0
72.6
•— 1
01 3
0,0
0.
0.01
0.01
0.01
0.01
0.01
0.01
0.00
r-4
o>
0
0.02
0.01
0.02
0.03
0.02
0.02
0.03
0.02
0.05
0.02
0.05
0.05
€
•|— 1 r—4
o> en
CS
en
eo en
S S
39.2
38.6
38.9
36.5
28.0
36.5
29.4
29.5
41.6
41.3
41.0
41.0
-------
Appendix D Description of Silt Traps and Silt Trap Sites
.§ilt Trap No. 1
Silt Trap No. 1 is sixty-one feet and nine inches long, three feet and
three inches wide, and three feet and three inches high. All of its
parts are similar.
The trap is approximately two and one-fourth miles from Lake Herman and
is in Section 1-6 (see Figure 3). It is the farthest upstream of the
eight silt traps in its series and is one-fourth of one mile above Trap
No. 2.
Trap No. 1 is in a slough-like expansion of the creek. The creekbed and
creek banks are densely covered with vegetation which consists primarily
of grasses and sedges. The area surrounding the trap is slough-like and
is neither pastured nor cultivated. Approximately seventy feet from the
creek is a cultivated field which extends along the creek for 650 feet.
Above this point, the creek flows across cultivated fields for one-half
mile.
Silt Trap No. 2
Silt Trap No. 2 is twenty-six feet long, three feet and three inches
wide, and one foot high. All of its parts are similar.
The trap is approximately one and one-half miles from Lake Herman and is
in Section J-6 (see Figure 3). It is one-fourth mile below Trap No. 1
and is sixty feet above Trap No. 3. Trap No. 2 is the second trap in a
series of eight traps.
Trap No. 2 is in a slough-like expansion of the creek. The creekbed and
creek banks are densely covered with vegetation which consists primarily
of grasses and sedges.
The area surrounding the trap is slough-like and is neither pastured nor
cultivated. Approximately fifty feet from the creek is a cultivated
field which extends for approximately 150 feet along one side of the
creek. Two hundred feet upstream from the trap the creek' flows across a
cultivated field for one-fourth mile. Much of the creekbed in this
field is under cultivation.
Salt Trap No. 3
Silt Trap No. 3 is sixteen feet and three inches long and three feet and
three inches wide. It has three parts which differ in their heights.
The main section of the trap is nine feet and nine inches long and
eighteen inches..high. On each side of the main section is a wing which
is three feet aricT'.three inches long and-one foot high. The main section
of the trap lies" in the creekbed and the wings are on the creek banks.
193
-------
Portions of the trap were countersunk in the creekbed and creek banks so
that they would lie level.
Trap No. 3 is approximately one and one-half miles from Lake Herman and
is in Section J-6 (see Figure 3). It is sixty feet below Trap No. 2 and
195 feet above Trap No. 4. Trap No. 3 is the third trap in a series of
eight traps, and it is in the same pasture as Traps No. 2-8.
Trap No. 3 is in a creekbed which is approximately ten feet wide and two
feet deep. The creek bottom is moderately well covered with vegetation
which consists primarily of sedges, grasses, and invader species. The
creek banks are nearly vertical and lack vegetation.
Silt Trap No. 4
Silt Trap No. 4 is forty-two feet and three inches long and three feet
and three inches wide.. It has three parts which differ in their heights.
The main section of the trap is nineteen feet and six inches long and
three feet and three inches high. On each side of the main section is a
wing. One wing is thirteen feet long and one foot high, and the other
wing is nine feet and nine inches long and one foot high. The main sec-
tion of the trap lies in the creekbed and the wings are on the banks of
the creek.
Trap No. 4 is approximately one and one-half miles from Lake Herman and
is in section J-6 (see Figure 3). It is 195 feet below Trap No. 3 and
375 feet above Trap No. 5. Trap No. 4 is the fourth trap in a series of
eight traps, and it is in the same pasture as Traps No. 2-8.
Silt Trap No. 5
Silt Trap No. 5 is twenty-nine feet and three inches long and three feet
and three inches wide. It has three major parts which differ in their
heights. The main section of the trap is nine feet and nine inches long
and three feet and three inches high. On each side of the main section
is a wing which is nine feet and nine inches long. Each wing has two
parts. The bagion ,at the end of each wing is one foot high. The next
two gabions (nearest the main section) in each wing are eighteen inches
high. The main section of the trap is countersunk to varying degrees
which range from none in the middle to sixteen inches near the creek
bank.
Trap No. 5 is approximately one and one-half miles from Lake Herman and
is in Section J-6 (see Figure 3). It is 375 feet below Trap No. 4 and
275 feet above Trap No. 6. Trap No. 5 is the fifth trap in a series of
eight traps, and it is in the same pasture as Traps No. 2-8.
Trap No. 5 is in an eroded creekbed which has very little vegetation
during the spring months. In early summer, various invader species give
moderate cover to the creekbed. The creek is approximately ten feet
wide and two feet deep.
194
-------
Silt Trap No. 6
Silt Trap No. 6 is nineteen feet and six inches long and three feet and
three inches wide. It has three parts which differ in their heights.
The main section of the trap is six feet and six inches long and three
feet and three inches high. On each side of the main section is a wing
which is three feet and three inches long and one foot high. The main
section lies in the creekbed and the wings lie partially in the creekbed
and partially on the creek banks.
Trap No. 6 is approximately one and one-half miles from Lake Herman and
is in section J-6 (see Figure 3). It is 275 feet below Trap No. 5 and
510 feet above Trap No. 7. Trap No. 6 is the sixth trap in a series of
eight traps, and it is in the same pasture as Traps No. 2-8.
Trap No. 6 is in a creekbed which is approximately twelve feet wide and
two feet deep. The creek banks are not well defined and grade impercep-
tibly with the surrounding area. The creek bottom is covered for the
most part with vegetation which consists mainly of grasses.
Silt Trap No. 7
Silt Trap No. 7 is twenty-six feet long and three feet and three inches
wide. It has three parts which differ in their heights. The main sec-
tion of the trap is sixteen feet and three inches long and eighteen
inches high. On each side of the main section is a wing. One wing is
six feet and six inches long and one foot high. The other wing is
three feet and three inches long and one foot high. The main section
lies in the creekbed, and the wings are on the gently sloping creek
banks.
Trap No. 7 is approximately one and one-fourth miles from Lake Herman
and is in section J-6 (see Figure 3). It is 510 feet below Trap No. 6
and 1,470 feet above Trap No. 8. Trap No. 7 is the seventh trap in a
series of eight traps, and it is in the same pasture as Traps No. 2-8.
Trap No. 7 is in a creekbed which is approximately fifteen feet wide and
two feet deep. The creek banks are not well defined and grade impercep-
tibly with the surrounding area. The creek bottom is lacking in vegeta-
tive cover after this time.
Silt Trap No. 8
Silt Trap No. 8 is forty-two feet and three inches long and three feet
and three inches wide. It has two parts which differ in their heights.
The main section of the trap is thirteen feet long and three feet and
and three inches high. Only one wing is present. It is twenty-nine
feet and three inches long and one foot high. The main section lies in
the creekbed and has one end countersunk in the high, vertical bank.
The wing lies on the gently sloping bank on the other side of the creek.
195
-------
Trap No. 8 is approximately one mile from Lake Herman and is in section
J-6 (see Figure 3). It is 1,470 feet below Trap No. 7. Trap No. 8 is
the eighth trap in a series of eight traps on this branch of the creek,
and it is in the same pasture as Traps No. 2-8=
Trap No. 8 is in the bend of a deeply eroded creekbed. The bank at the
outside of the bend is vertical and lacking in vegetation. The other
bank is ill-defined and grades imperceptibly with the surrounding area.
The creek bottom is lacking in vegetative1 cover during the spring months.
Sparse vegetative cover of invader species occurs during the summer
months.
Silt Trap No. 9
Silt Trap No. 9 is twenty-nine feet and three inches long and three feet
and three inches wide. It has two parts which differ in their heights.
The main section of the trap is thirteen feet long and three feet and
three inches high. Only one wing is present. It is nineteen feet and
six inches long and one foot high. The main section of the trap lies in
the creekbed, and the wing lies on the creek bank.
The trap is approximately two miles from Lake Herman and is in section
J-6 (see Figure 3). It is the farthest upstream of the four traps on
this branch of the creek. Trap No. 9 is one-half mile above Trap No,.,. 10
and is in a pasture. Cultivated fields lie approximately eighty to one
hundred feet from each side of the creek as it flows through the •
pasture. The creek passes through a cultivated field one-eighth'mile
upstream from the trap.
Trap No. 9 is in a creekbed which is approximately seven feet wide and
two feet deep. The creek banks are vertical and lack vegetative cover.
Very little vegetation is found in the creekbed.
Silt Trap No. 10
Silt Trap No. 10 is nineteen feet and six Inches long and three feet and
three inches wide. It has three parts which differ;in their heights.
The main section of the trap is six feet and six inches long and three
feet and three inches high. On one side of the main section is a wing.
Each wing is six feet and six inches long and one foot high. The main
section of the trap lies in the creekbed, the wings are on the creek
banks.
Trap No. 10 is approximately one and one-fourth miles from Lake Herman
and is in Section J-7 (see Figure 3). It is approximately one-half mile
below Trap No. 9 and is 525 feet above Trap No. 11. Trap No. 10 is the
second trap in a series of four traps. It is in a pasture and is
approximately 600 feet downstream from where the creek flows through a
cultivated field.
196
-------
Trap No. 10 is in a creekbed which is seven feet wide and two feet deep.
The creek banks are vertical and lack vegetative cover- Very little
vegetative cover is found in the creekbed.
Silt Trap No. 11
Silt Trap No. 11 is thirty-nine feet long and three feet and three
inches wide. It has three parts which differ in their heights. The
main section of the trap is nine feet and nine inches long and three
feet and three inches high. On each side of the main section is a
wing. One wing is nineteen feet and six inches long and one foot high.
The other wing is nine feet and nine inches long and one foot high.
Trap No. 11 is approximately one and one-fourth miles from Lake Herman
and is in Section J-7 (see Figure 3). It is 525 feet below Trap No. 10
and one-third mile above Trap No. 12. Trap No. 11 is the third trap in
a series of four traps and is in the same pasture as Trap No. 10.
Trap No. 11 is in a winding portion of the creek which is ten feet wide
and two feet deep. The creek banks are nearly vertical and are sparsely
covered with vegetation. The creek bottom is lacking in vegetation
during spring months, but it later has sparse vegetative cover.
Silt Trap No. 12
Silt Trap No. 12 is thirty-five feet and nine inches long and three feet
and three inches wide. It has two parts which differ in their heights.
The main section of the trap is nineteen feet and six inches long and
three feet and three inches high. On one side of the main section is a
wing which is sixteen feet and three inches long and one foot high.
Trap No. 12 is approximately three-fourths miles from Lake Herman and is
in Section J-7 (see Figure 3). It is one-third mile below Trap No. 11.
Trap No. 12 is the fourth trap in a series of four traps.
Trap No. 12 is in a slough-like expansion of the creek which is about
thirty feet wide. The creekbed and creek banks are densely covered with
tall vegetation which form a well-developed sod. About one-fourth of
the vegetative cover is Reed Canarygrass (Phalaris arundinaceae). Giant
ragweed, nettles, dogbane, grasses, and sedges are also present. The
creek banks are not well defined and grade imperceptibly with the
surrounding area.
Trap No. 12 is in a grassland area which is not pastured. A cultivated
field lies several hundred feet to one side of the creek, but no culti-
vated fields lie directly between this trap and Traps No. 10 and 11.
Silt Trap No. 13
Silt Trap No. 13 is seventy-eight feet long, three feet and three inches
wide, and three feet and three inches high. All of its parts are similar.
197
-------
Trap No. 13 is approximately one-half mile from Lake Herman and is in
Section J-8 (see Figure 3). It is the farther upstream of the two traps
in its series. Trap No. 13 is one-eighth mile above Trap No. 14 and is
in a pasture which has cultivated, fields adjacent to it.
Trap No. 13 is in a ravine that is twenty to twenty-five feet deep. The
trap extends across the bottom of the ravine and part way up its sides.
Because of this construction, water does not flow around the ends of the
trap under any conditions. The bottom of the ravine is partially
covered with rocks and gravel. The rest of the ravine is covered with
vegetation that forms a good sod.
Silt Trap No. 14
Silt Trap No. 14 is eighty-seven feet and nine inches long, three feet
and three inches wide, and three feet and three inches high. All of its
parts are similar.
Trap No. 14 is approximately three-eighths mile from Lake Herman and is
in Section J-8 (see Figure 3)» It is one-eighth mile below Trap No. 13
and is the second trap of the two in its series. Trap No. 14 is in the
same pasture as Trap No. 13 and is not near cultivated fields.
Trap No. 14 is near the base of a hill and in a small ravine chat is-
approximately ten feet deep. The trap extends across the small creek in
the ravine and part way up the sides of the ravine. The creek is
>;fifteen feet wide and two feet deep. The ravine and the creekbed above
the trap are densely covered with vegetation which consist primarily of
grasses, sedges, and several invader species.
Silt Trap No. 15
Silt Trap No« 15 consists of a vertical wall, such as found in Traps No.
1-14^ but, in addition, it has lower gabions on its downstream and
upstream sides, which are herein termed aprons. The central, vertical
wall is eighty-one feet and three inches long, three feet and three
inches wide, and three feet and three inches high. The apron on the
downstream side of the vertical wall consists of two series of gabions
which are immediately adjacent to each other and to the vertical wall.
The first series of gabions (adjacent to the vertical wall) is eighty-
one feet and three inches long, three feet and three inches wide, and
one foot high. Thus, it extends completely across the front of the
central, vertical wall. The second series of gabions in the downstream
apron is fifty-eight feet and six inches long, three feet and three
inches wide, and one foot high. It extends along the middle portion of
the trap. The apron on the upstream side of the vertical wall also'con-
sists of two series of gabions which are immediately adjacent to each
other and to the vertical wall. The first series of gabions (adjacent,r
to the vertical wall) is eighty-one feet and three inches long, three
feet and three inches wide, and one foot high. Thus it extends com-
pletely across the back of the central, vertical wall. The second
198
-------
series of gabions in the upstream apron is sixty-five feet long, three
feet and three inches wide, and one foot high. It extends along the
middle portion of the trap. Immediately in front of the upstream apron
is a layer of loose rocks which is about one foot wide. Beneath one-
half of the length of the trap is a layer of plastic screen (plain Poly-
Filter X, Carthage Mills Incorporated, Cincinnati, Ohio). A well-
developed sod is present under the entire trap.
Trap No. 15 is 625 feet from Lake Herman and is in Section H-7 (see
Figure 3). It is the farther upstream of the two traps in its series
and is 250 feet above Trap No. 16. Trap No. 15 is in a pasture and is
approximately one-fourth mile below a cultivated field.
Trap No. 15 is in a ravine which is about forty feet deep and has steep
sides. The ravine is well covered with vegetation which consists pri-
marily of grasses. The trap extends far enough up the sides of the
ravine that water does not flow around it under any conditions.
Silt Trap No. 16
Silt Trap No. 16 is constructed in the same manner as Trap No. 15. It
has a central, vertical wall and aprons on the upstream and downstream
sides. The central, vertical wall is fifty-eight feet and six inches
long, three feet and three inches wide, and three feet and three inches
high. The apron on the downstream side of the vertical wall consists of
two series of gabions which are immediately adjacent to each other and
to the vertical wall. The first series of gabions (adjacent to the
vertical wall) is thirty-nine feet long, three feet and three inches
wide, and one foot high. It extends along the middle portion of the
trap. The second series of gabions in the downstream apron is con-
structed in the same manner as the first series of gabions and also
extends along the middle portion of the trap. The apron on the upstream
side of the vertical wall consists of two series of gabions which are
immediately adjacent to each other and to the vertical wall. The first
series of gabions (adjacent to the vertical wall) is fifty-eight feet
and six inches long, three feet and three inches wide, and one foot
high. Thus, it extends completely across the back of the central,
vertical wall. The second series of gabions in the upstream apron is
thirty-nine feet long, three feet and three inches wide, and one foot
high. It extends along the middle portion of the trap. Immediately in
front of the upstream apron is a layer of loose rocks which is about
one foot wide.
Trap No. 16 is 375 feet from Lake Herman and is in Section H-7 (see
Figure 3). It is 250 feet below Trap No. 15 and is the second trap in
this series of two traps. The trap is in a pasture and is approximately
one-fourth mile below a cultivated field.
The nature of the ravine and the surrounding area is the same as for
Trap No. 15 (see above). The trap extends far enough up the sides of
199
-------
the ravine that water does not flow around the trap under any
conditions.
Silt Trap No. 17
Silt Trap No. 17 consists of a vertical wall and two "step-down" aprons
on the downstream side. The vertical wall is fifty-eight feet and six
inches long, three feet and three inches wide, and three feet and three
inches high. Adjacent to it and on its downstream side is a second
series of gabions which are thirty-five feet and nine inches long, three
feet and three inches wide, and eighteen inches high. Immediately
adjacent to this "step-down" apron is a series of gabions which form a
second "step-down" apron. This apron is twenty-six feet long, three
feet and three inches wide, and one foot high. Smaller rocks (five to
six inches in diameter) than were usually used were placed in the aprons
and in the base of the main, vertical wall.
Trap No. 17 is approximately two and one-half miles from Lake Herman and
is in Section E-7 (see Figure 3). It is the only trap built on the
north creek.
Trap No. 17 is in a small ravine at the edge of a cultivated field. The
ravine is about twelve feet deep and is well covered with vegetation.
The creek which passes through this ravine is not well defined and
grades imperceptibly with the ravine. The field has been planted in
alfalfa for the past two years. The creek and strips approximately
twenty feet wide on each side of it are not cultivated at any time. The
trap extends far enough up the sides of the ravine that water does not
flow around it under any conditions.
200
-------
1 Accexxion Number
w
Q 1 Subject Field & Group
05C
SELECTED WATER RESOURCES ABSTRACTS
INPUT TRANSACTION FORM
5 Organization _. , _ . , _
Chemistry and Biology Departments
Dakota State College
Madison, South Dakota 57042
Title
Effect of Silt and Silt Removal In A Prairie Lake
10
Author(s)
Churchill, Constance L.
Brashier, Clyde K.
Leidahl, Gordon
16
Project Designation
EPA Project Number 16010 DZK
21
Note
22
Citation
Environmental Protection Agency report number,
EPA-R3-73-037, July 1973.
23
Descriptors (Starred First)
*water pollution sources, *sediments, *nutrients, *eutrophication,
aquatic soils, mineralogical water properties
25
Identifiers (Starred First)
*Gabion silt traps, *Lake Herman, Madison, South Dakota
27 Abstract
A surveillance program has been maintained on two shallow, warm water prairie lakes
and their tributaries. One of these lakes, Lake Madison, is domestically polluted
with the effluent from the sewage treatment plant of Madison, South Dakota. The
other, Lake Herman, is polluted due to siltation caused by run-off from a large,
intensively farmed watershed. This surveillance program has resulted in compari-
sons of chemical nutrients and biota of a heavily silted lake with those of a
relatively unsilted, but domestically polluted lake. The surveillance program on
the Lake Herman tributaries has also led to conclusions regarding nutrient
levels in successive spring run-offs.
During the summers of 1969 and 1970 a total of seventeen gabion-type silt traps
were constructed across the major feeder streams on the Lake Herman watershed in
order to retard lake siltation. The traps were of several structural types and
were constructed in locations with different types of creekbeds and different
water-flow rates in order to evaluate which combinations of design and location
were most effective. The traps were successful as filters for large debris but
had limited success as silt-retaining devices. However, erosion occurred around
or under many of the traps thus diminishing their effectiveness.
(Churchill—Dakota State College)
Abstractor
tonstance L. Churchill
Intstituli.
'"Dakota State College, Madison, South Dakota 57042
WRiIOZ (REV. JULY 1969)
WRS1 C
SEND, WITH COPY OF DOCUMENT, TO: WATER RESOURCES SCIENTIFIC INFORMATION CENTER
U.S, DEPARTMENT OF THE INTERIOR
WASHINGTON, D, C „ 20240
*U.S. GOVERNMENT PRINTING OFFICE:1973 546-308/27 1-3
-------
|