United States
Environmental Protection
Agency
Great Lakes National
Programs Office
Room 932, 536 S. Clark St.
Chica.j, Illinois 60605
EPA-905/9-79-006-A
Applicability of
Land Treatment of
Wastewater in the
Great Lakes Area
Basin
Impact of Wastewater
Diversion, Spray Irrigation
on Water Quality in the
Muskegon County,
Michigan Lakes
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Preface
The U. S. Environmental Protection Agency was created because of in-
creasing public and governmental concern about the dangers of pollu-
tion to the health and welfare of the American people. Noxious air,
foul water, and spoiled land are tragic testimony to the deterioration
of our natural environment.
The Great Lakes National Program Office (GLNPO) of the U.S. EPA was
established in Region V, Chicago, to provide specific focus on the
water quality concerns of the Great Lakes. The Section 108(a)
Demonstration Grant Program of the Clean Water Act (PL92-500) is
specific to the Great Lakes drainage basin and thus is administered
by the Great Lakes National Program Office.
Land disposal of wastewater in the Great Lakes area is one alternative
for treatment that can provide tertiary quality effluent when properly
managed. This report evaluates the impact of wastewater diversion
and spray irrigation on water quality in the Muskegon County, Michigan
lakes.
We hope the information and data contained herein will help planners
and managers of pollution control agencies to make better decisions
in carrying forward their pollution control responsibilities.
Edith J. Tebo, Ph.D.
Director
Great Lakes National Program Office
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EPA-905/9r-79-006-A
May 1979
APPLICABILITY OF LAND TREATS OF WASTEWATER
IN THE GREAT LAKES AREA BASIN:
IMPACT OF WASTEWATER DIVERSION, SPRAY IRRIGATION
ON WATER QUALITY IN THE MUSKEGON COUNTY, MICHIGAN, LAKES
by
P. L. Freedman, R. P. Canale, and M. T. Auer
Department of Civil Engineering
The University of Michigan
Ann Arbor, Michigan 48105
for
Michigan Water Resources Commission
Department of Natural Resources
Lansing, Michigan 48926
EPA Grant No. G005104
Project Officers
J. M. Walker and S. Poloncsik
Office of Research and Development
SECTION 108 (a) PROGRAM
GREAT LAKES NATIONAL PROGRAM OFFICE
U.S. ENVIRONMENTAL PROTECTION AGENCY, REGION V
CHICAGO, ILLINOIS 60605
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FOREWORD
The Great Lakes are the world's largest fresh water resource. It Is
shared by the United States and Canada. In the U.S., this lake system
serves important water needs of people and industries in eight states,
six of which comprise the area served by EPA Region V. The usefulness
of the lakes, for many purposes, has been impaired by past misuses of
the lakes themselves and of land resources in contributing drainage
basins. Management of the Great Lakes Area Basin to halt or reverse the
degradation of vital water resources is of great importance to both
countries. Lake Michigan presents special concerns because of its
headwater relationship to the lower Great Lakes and because of the
intensity and variety of human activity that impacts upon it. Responsi-
bilities for developing and enforcing ameliorative management in the
Lake Michigan basin rest with the U.S. and the four states that share
the shoreline of the lake.
Land application of wastewater is one of the management options for
upgrading water after use. From historical precedent and for many
theoretical reasons, land application has the potential for effecting
full renovation of wastewater before release into the environment.
Whether this potential is realized will depend on many factors of soil,
climate and management which must be understood for each situation.
Performance must be assessed ultimately in terms of impact on contiguous
aquatic systems. The acquisition of background and early operational
data for a large land application system in Muskegon County, Michigan,
has been the objective of an intensive three-year study conducted for
EPA Region V by the Michigan Water Resources Commission, with sub-
contracts to Michigan State University and the University of Michigan.
The three reports covering this work carry the general title, "Applicability
of Land Treatment of Wastewater in the Great Lakes Area Basin," with
respective subtitles:
The Muskegon County System—An Overview, Monitoring Considerations
and Impacts on Receiving Waters.
Effectiveness of Sandy Soils at Muskegon County, Michigan, for
Renovating Wastewater.
Impact of Wastewater Diversion, Spray Irrigation on Water Quality
in Muskegon County, Michigan, Lakes.
In these volumes, data collected from 1972 through 1975 are evaluated in
relation to the applicability of land treatment for renovating municipal
and industrial wastewaters in Muskegon County. Short-term and long-term
projections are made regarding management practices that can influence
the renovative effectiveness of soils and crops. Observed and projected
effects of wastewater diversion and treatment on water quality and
ecosystem responses in lakes and streams that drain into Lake Michigan
are described.
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EPA REVIEW NOTICE
This report has been reviewed by the Office of Research and Development
and the Great Lakes National Program Office of Region V, U.S. EPA,
Chicago, 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 recommendation for use.
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ACKNOWLEDGMENTS
This project was carried out under the auspices of The University of
Michigan's Great Lakes Resource Management Program (GLRMP). Dr. John
Armstrong is Director of GLRMP and was largely responsible for the con-
ception and initial design of the project. He provided many important
ideas concerning the formulation and implementation of the overall
research plan.
Dr. Peter Meier and Thomas Kelly assisted with the design and implemen-
tation of the field monitoring program. The authors appreciate the help
of Bruce Bartley, Michael Gould, and Paul Silfven for their efforts with
sample collection and field water quality analysis. The majority of
the nutrient analysis was conducted by Mary Lee Sharp under the direc-
tion of Dr. K. H. Mancy.
Dr. John Walker (US Environmental Protection Agency Project Coordinator)
provided several valuable suggestions concerning the presentation of the
results and compiled the data presented in Table 1 and Appendix E.
Warren Slocum (State of Michigan Environmental Protection Bureau) helped
summarize the industrial discharge data and inventory presented in
Appendix F.
Various sections and drafts of the manuscript were typed by Lee Hallmark,
Diane Rumps, and Aleda Thomas. Mrs. Thomas was also responsible for the
final editing of the report and without her diligence and perseverance
the report could not have been produced.
Xll
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TABLE OF CONTENTS
Page
FOREWORD ............................... i
EPA REVIEW NOTICE ........................... ii
ACKNOWLEDGMENTS ....................... ..... ±i±
LIST OF TABLES ............................ viii
LIST OF ILLUSTRATIONS ......................... x
SECTIONS
I. SUMMARY AND CONCLUSIONS .................... 1
WHITE LAKE ......................... 2
MUSKEGON LAKE ........................ 3
MONA LAKE .......................... 4
II. RECOMMENDATIONS ........................ 8
FUTURE WATER QUALITY STUDIES ................ 8
MANAGEMENT RECOMMENDATIONS ................. 9
III. INTRODUCTION ......................... 1:L
IV. DESCRIPTION OF STUDY AREA AND SOCIO-ECONOMIC HISTORY ..... 13
V. HISTORY AND OPERATION OF THE MUSKEGON DIVERSION SPRAY-
IRRIGATION SYSTEM ..................... 17
VI. METHODS AND MATERIALS ..................... 21
GENERAL .......................... 21
Sampling Methods .................... 28
PHYSICAL AND CHEMICAL METHODS OF ANALYSIS ......... 29
Alkalinity ....................... 29
Biochemical Oxygen Demand ................ 29
Chemical Oxygen Demand ................. 32
Chloride ........................ 32
Dissolved Oxygen .................... 32
Hydrogen Ion Activity .................. 32
Iron .......................... 33
Ammonia Nitrogen .................... 33
Nitrate, Nitrite Nitrogen ................ 33
Phosphorus ....................... 33
Relative Irradiance ................... 3^
iv
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SECTIONS Page
Solar Radiation 34
Silicon 34
Specific Conductance 34
Total Organic Carbon 34
Temperature 35
Transparency 35
BIOLOGICAL METHODS OF ANALYSIS 35
Chlorophyll a 35
Primary Productivity 35
VII. GENERAL LIMNOLOGICAL OBSERVATIONS 37
INFORMATION 37
PHYSICAL AND CHEMICAL PARAMETERS 37
pH and Alkalinity 37
Conductivity and Chlorides 40
Oxygen and Oxygen Demanding Substance 40
Nitrogen 41
Phosphorus 42
Silicon 42
Iron 43
BIOLOGICAL PARAMETERS
Chlorophyll a 43
Primary Productivity 43
Secchi Disc 44
Phytoplankton, Zooplankton, and Benthos 44
SUMMARY 44
VIII. WHITE LAKE 45
INTRODUCTION 45
TRIBUTARY-RELATED CONSIDERATIONS 46
Hydrology 46
Concentration of Chemical Species in Tributaries 50
Nutrient Loads 64
Summary 81
LAKE-RELATED CONSIDERATIONS 81
Spatial and Seasonal Distributions 81
Long-Term Changes 100
Summary 103
v
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SECTIONS PaSe
SPECIALTY STUDIES .................... 107
Algal Growth Nutrient Bioassays ........... 107
Macrophytes ..................... HO
Sediment-Nutrient Relationships ........... 114
Modeling ....................... 117
IX. MUSKEGON LAKE ....................... 124
INTRODUCTION ...................... 124
TRIBUTARY-RELATED CONSIDERATIONS ............ 124
Hydrology ......................
Concentrations of Chemical Species in Tributaries . . 126
Nutrient Loads .................... 1"
Summary ....................... 152
LAKE-RELATED CONSIDERATIONS ............... 152
Spatial and Seasonal Distributions .......... 152
Long-Term Changes .................. I69
Summary ....................... I'l
X. MONA LAKE ......................... 175
INTRODUCTION ...................... i75
TRIBUTARY-RELATED CONSIDERATIONS ............ 175
Hydrology ......................
Concentrations of Chemical Species in Tributaries . . 177
Nutrient Loads. .... ............... I88
Summary .......................
LAKE-RELATED CONSIDERATIONS ............... 201
Spatial and Seasonal Distributions .......... 201
Long-Term Changes .................. 215
Summary ....................... 22^
LITERATURE CITED .......................... 222
APPENDICES
A - MUSKEGON ALGAL NUTRIENT BIOASSAY STUDY,
WHITE LAKE PROJECT ................... 227
B - SUBMERGED AQUATIC MACROPHYTES IN
WHITE LAKE, MICHIGAN ... ............... 229
VI
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APPENDICES Page
C - NUTRIENT RELEASE FROM ANAEROBIC SEDIMENTS
IN WHITE LAKE, MICHIGAN 231
D - MODEL PROJECTIONS OF PHOSPHORUS CONCENTRATIONS 233
E - WATER QUALITY AND LOADING RATE DATA FOR THE MUSKEGON
COUNTY TREATMENT SYSTEM 236
F - INDUSTRIAL AND MUNICIPAL DISCHARGE INVENTORY 248
G - AVAILABILITY OF DATA FROM U.S. EPA STORAGE AND
RETRIEVAL COMPUTER SYSTEM "STORET" 258
vii
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LIST OF TABLES
Table Page
1. Chronology of some important events relevant to the
Muskegon County Wastewater Treatment Project 19
2. Sampling cruse schedule 22
3. Location of tributary sampling stations 23
4. Summary of methods of analysis 30
5. USEPA interlaboratory comparison study 31
6. Water quality characteristics—averages of all data 38
7. White Lake drainage basin areas 47
8. White Lake tributary flow data, July 11 and 12, 1967 (MWRC, 1967) . 48
9. Average concentrations of selected chemical species in
tributaries to White Lake, 1972-1975 51
10. Estimated municipal and industrial loads to White Lake
prior to diversion in kilograms per day 66
11. Annual average White Lake tributary loads in kilograms per day. . . 68
12. Estimated total yearly nutrient loads to White Lake,
1972-1975 in thousand kilograms per year 73
13. Normalized yearly average White River loads in kilograms per day. . 75
14. Flow weighted average concentrations of total phosphorus
and dissolved inorganic nitrogen in tributaries to White Lake . . 78
15. Key to symbols used in Figure 25 (after Vollenweider, 1975) .... 80
16. Yearly average flux of nutrients leaving and entering White
Lake in kilograms per day 82
17. Average annual values for selected water quality parameters
in White Lake, 1972-1975 102
18. Muskegon Lake drainage basin characteristics 125
19. Average concentrations of selected chemical species in
tributaries to Muskegon Lake, 1972-1975 128
20. Estimated municipal and industrial loads to Muskegon Lake
prior to diversion in kilograms per day 140
viii
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Table Page
21. Average Muskegon Lake tributary loads in kilograms per day. . . 141
22. Estimated total yearly nutrient loads to Muskegon Lake,
1972-1975 in thousand kilograms per year 146
23. Normalized yearly average Muskegon River loads in kilograms
per day 148
24. Flow weighted average concentrations of total phosphorus
and dissolved inorganic nitrogen in tributaries to
Muskegon Lake 151
25. A summary of the yearly average flux of nutrients leaving and
entering Muskegon Lake in kilograms per day 153
26. Average annual values for selected water quality parameters
in Muskegon Lake, 1972-1975 170
27. Mona Lake drainage basin characteristics (projected long-
term average) 176
28. Average concentrations of selected chemical species in
tributaries to Mona Lake, 1972-1975 178
29. Average Mona Lake tributary loads in kilograms per day 190
30. Estimated municipal and industrial loads to Mona Lake prior
to diversion in kilograms per day 196
31. Estimated total yearly nutrient loads to Mona Lake,
1972-1975 in thousand kilograms per year 199
32. Flow weighted average concentrations of total phosphorus
and dissolved inorganic nitrogen in tributaries to Mona Lake. 200
33. A summary of the yearly average flux of nutrients leaving and
entering Mona Lake in kilograms per day 202
34. Algicide application to Mona Lake (Michigan DNR, 1976) 218
35. Average annual values for selected water quality parameters
in Mona Lake, 1972-1975 219
ix
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LIST OF ILLUSTRATIONS
Figure Page
1. Annual average nutrient loadings to the Muskegon Lakes 6
2. Annual average surface water concentrations of selected
water quality variables in the Muskegon Lakes 7
3. The Muskegon Lakes study area 14
4. White Lake sampling stations 24
5. Muskegon Lake sampling stations 25
6. Mona Lake sampling stations 26
7. Tributary and lake sampling stations 27
8. White River average annual flow at Whitehall, Michigan
(USGS Station // 04122200) 49
9. Mean monthly flow of the White River at Whitehall,
Michigan (USGS Station # 04122200) 49
10. Dissolved inorganic nitrogen concentrations at Station 201
in White River, 1972-1975 53
11. Dissolved inorganic nitrogen concentrations at Station 202
in White River, 1972-1975 54
12. Dissolved inorganic nitrogen concentrations at Station 227
in White River, 1973-1975 55
13. Phosphorus concentrations at Station 201 in White River,
1972-1975 56
14. Phosphorus concentrations at Station 202 in White River,
1972-1975 57
15. Phosphorus concentrations at Station 227 in White River,
1973-1975 58
16. Silicon concentrations at Station 201 in White River, 1972-1975 ... 59
17. Silicon concentrations at Station 202 in White River, 1972-1975 ... 60
18. Chloride concentrations at Station 201 in White River, 1972-1975. . . 61
19. Chloride concentrations at Station 202 in White River, 1972-1975. . . 62
x
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Figure Page
20. Location and diversion status of point sources and
municipalities in the White Lake basin 65
21. Silicon load of the White River, 1973-1975 69
22. Cloride load of the White River, 1973-1975 70
23. Dissolved inorganic nitrogen load of the White River,
1973-1975 71
24. Total phosphorus load of the White River, 1973-1975 72
25. Vollenweider Model relating phosphorus loading per unit
of surface to hydraulic load (mean depth divided by lake
retention time) for Muskegon Lakes (Vollenweider, 1975) .... 79
26. Dissolved inorganic nitrogen concentrations at Stations 203
and 204 in White Lake, 1972-1975 83
27. Total dissolved phosphorus concentrations at Stations 203
and 204 in White Lake, 1972-1975 84
28. Nitrate concentrations in White Lake, 1972-1975 86
29. Ammonia concentrations in White Lake, 1972-1975 87
30. Dissolved oxygen in the bottom waters of White Lake,
1972-1975 89
31. Soluble reactive phosphorus concentrations in White Lake,
1972-1975 91
32. Total dissolved phosphorus concentrations in White Lake,
1972-1975 92
33. Total phosphorus concentrations in White Lake, 1972-1975 93
34. Dissolved iron concentrations in White Lake, 1972-1975 95
35. Dissolved silicon concentrations in White Lake, 1972-1975 .... 96
36. Chlorophyll a concentrations in White Lake, 1972-1975 98
37. Primary productivity rates in White Lake, 1972-1975 . . 99
38. Correlation between chlorophyll a and Secchi disc (after
Dillon and Rigler, 1975) 104
39. Correlation between phosphorus and summer chlorophyll a
(after Dillon and Rigler, 1974) 105
40. Pre- and post-diversion status of selected two-meter, yearly
average water quality parameters in White Lake 106
xx
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Figure
41. Chlorophyll a concentrations - 2 November 1973 bioassay 108
42. Chlorophyll a concentrations - 27 April 1974 bioassay 109
43. Distribution of macrophytes in White Lake 112
44. Macrophyte and phytoplankton concent in White Lake 113
45. Concentrations of nutrients in White Lake sediment
interstitial waters 115
46. Nutrient release from White Lake sediments-laboratory studies. . . 116
47. Nutrient release from White Lake sediments—-in AJJu studies. . . . 118
48. White Lake phosphorus model 120
49. Comparison of model calculations and observed data (1974)
for dissolved and particulate phosphorus in White \Lake 121
50. Comparison of rehabilitation schemes for White Lake 122
51. Muskegon River average annual flow at Newaygo, Michigan
(USGS Station # 04122000) 127
52. Muskegon River mean monthly flow at Newaygo, Michigan
(USGS Station # 04122000) 127
53. Dissolved inorganic nitrogen concentrations in the
Muskegon River, 1973-1975 130
54. Dissolved inorganic nitrogen concentrations in the
Muskegon River, 1972-1975 131
55. Phosphorus concentrations in the Muskegon River, 1973-1975 .... 132
56. Phosphorus concentrations in the Muskegon River, 1972-1975 .... 133
57. Silicon concentrations in the Muskegon River, 1972-1975 134
58. Chloride concentrations in the Muskegon River, 1972-1975 135
59. Location and diversion status of point sources and
municipalities in the Muskegon Lake basin 138
60. Silicon load of the Muskegon River, 1973-1975 142
61. Chloride load of the Muskegon River, 1973-1975 143
62. Dissolved inorganic nitrogen load of the Muskegon River,
1973-1975
xii
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Figure Page
63. Total phosphorus load of the Muskegon River, 1973-1975 145
64. Total dissolved phosphorus concentrations at Stations
103 and 106 in Muskegon Lake, 1972-1975 154
65. Dissolved inorganic nitrogen concentrations at Stations
103 and 106 in Muskegon Lake, 1972-1975 155
66. Nitrate concentrations in Muskegon Lake, 1972-1975 157
67. Ammonia concentrations in Muskegon Lake, 1972-1975 158
68. Dissolved oxygen in the bottom waters of Muskegon Lake,
1972-1975 160
69. Soluble reactive phosphorus concentrations in Muskegon
Lake, 1972-1975 161
70. Total dissolved phosphorus concentrations in Muskegon
Lake, 1972-1975 162
71. Total phosphorus concentrations in Muskegon Lake, 1972-1975 . . . 164
72. Dissolved iron concentrations in Muskegon Lake, 1972-1975 .... 165
73. Dissolved silicon concentrations in Muskegon Lake, 1972-1975. . . 166
74. Chlorophyll a. concentrations in Muskegon Lake, 1972-1975 167
75. Primary productivity rates in Muskegon Lake, 1972-1975 168
76. Correlation between chlorophyll a and Secchi disc (after
Dillon and Rigler, 1975) 172
77. Correlation between phosphorus and summer chlorophyll 0.
(after Dillon and Rigler, 1974) 173
78. Pre- and post-diversion status of selected two-meter, yearly
average water quality parameters in Muskegon Lake 174
79. Dissolved inorganic nitrogen concentrations in Black
Creek, 1973-1975 179
80. Phosphorus concentrations in Black Creek, 1973-1975 180
81. Phosphorus concentrations in Black Creek, 1972-1975 181
82. Dissolved inorganic nitrogen concentrations in Black
Creek, 1972-1975 182
83. Dissolved silicon concentrations in Black Creek, 1972-1975. . . . 183
xiii
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Figure Page
84. Chloride concentrations in Black Creek, 1972-1975 184
85. Dissolved inorganic nitrogen concentrations in Little
Black Creek, 1973-1975 186
86. Total phosphorus concentrations in Little Black Creek,
1973-1975 187
87. Location and diversion status of point sources and
municipalities in the Mona Lake basin 189
88. Dissolved inorganic nitrogen load of Black Creek, 1973-1975 191
89. Total phosphorus load of Black Creek, 1973-1975 192
90. Dissolved inorganic nitrogen load of Little Black Creek,
1973-1975 193
91. Total phosphorus load of Little Black Creek, 1973-1975 194
92. Dissolved inorganic nitrogen concentrations at Stations 3
and 4 in Mona Lake, 1972-1975 203
93. Total dissolved phosphorus concentrations at Stations 3
and 4 in Mona Lake, 1972-1975 204
94. Nitrate concentrations in Mona Lake, 1972-1975 206
95. Ammonia concentrations in Mona Lake, 1972-1975 207
96. Dissolved oxygen in the bottom waters of Mona Lake, 1972-1975. . . . 208
97. Soluble reactive phosphorus concentrations in Mona Lake,
1972-1975 210
98. Total dissolved phosphorus concentrations in Mona Lake,
1972-1975 211
99. Total phosphorus concentrations in Mona Lake, 1972-1975 212
100 Dissolved iron concentrations in Mona Lake, 1973-1975 213
101. Dissolved silicon concentrations in Mona Lake, 1972-1975 214
102. Chlorophyll a concentrations in Mona Lake, 1972-1975 216
103. Primary productivity rates in Mona Lake, 1972-1975 217
104. Pre- and post-diversion status of selected two-meter, yearly
average water quality parameters in Mona Lake 221
xiv
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SECTION I
SUMMARY AND CONCLUSIONS
A regional program of wastewater management went into full operation in
Muskegon County, Michigan in 1974. The program consists of wastewater
collection, treatment, and spray-irrigation on farmland. This system has
replaced outdated inefficient treatment plants which had discharged
poorly treated wastes directly to Muskegon County surface waters. The
major overall goals of the project were to stimulate economic growth in
the region by providing efficient waste treatment facilities at a reason-
able cost, to restore water quality in three lakes important for recrea-
tion, and to meet State of Michigan water quality standards for waste-
water discharges.
The research described in this report was designed to evaluate the impact
of the wastewater management system on the quality of the surface waters
of Muskegon County. Within this study particular emphasis was placed on
an analysis of the effects of the diversion project on the trophic status
and nutrient budgets of White, Muskegon, and Mona Lakes. No studies were
conducted to define levels of organics, trace metals, suspended solids,
pesticides, or other pollutional contaminants which may have been altered
as a result of the diversion project. In this report the term water
quality shall have limited scope relating primarily to parameters concerned
with eutrophication and nutrient budgets.
The program of approximately biweekly lake and stream monitoring was imple-
mented in the late spring of 1972 (the only year of the study period prior
to all diversions). Diversion began in 1973 and was essentially fully
implemented by 1974. White, Muskegon, and Mona Lakes were monitored at
several stations and depths for phytoplankton growth nutrients, chlorophyll a,
primary productivity, and various other physical and chemical parameters.
Major tributaries to each lake were also monitored at multiple locations.
These locations included the White River and Mill Pond Creek in the White
Lake Basin; the Muskegon River and Bear Lake Creek in the Muskegon Lake
Basin; and Little Black and Black Creeks in the Mona Lake Basin. Stations
were selected to evaluate the effects of the diversion and spray-irriga-
tion project. The results from these studies provided baseline data on
limnological and stream conditions. By combining the tributary data with
information on municipal and industrial nutrient loads it was possible to
evaluate the potential and actual effectiveness of the diversion spray-
irrigation project to reduce nutrient loads to each of the three lakes.
The detailed lake monitoring program provided a suitable data base to
assess changes in lake water quality in actual response of the diversion
project. A lake-by-lake summary of the analysis follows.
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WHITE LAKE
Baseline limnological investigations of White Lake show that prior to the
diversion, the lake was highly productive and could be considered eutrophic.
The lake was plagued by excessive growths of algae and nearly 20% of the
lake bottom was heavily covered with macrophytes. Maximum summer chloro-
phyll a measurements were approximately 50 yg/£ and maximum primary produc-
tivity values ranged between 100 and 200 Ug C/£/hr. Macrophyte densities
were as high as 150 grams dry wt/m2. Secchi disc visibility was low, aver-
aging less then 2 meters. Average surface total phosphorus concentrations
were approximately 40 ygP/fc and bottom water concentrations often reached
100 to 200ygP/«, during the summer. Winter dissolved inorganic nitrogen
concentrations were observed to exceed 1 mgN/A. Bottom waters were deple-
ted of oxygen during the summer for two to three months.
The White River was found to be the major nutrient source to White Lake
before diversion, with significant nutrient contributions also originating
from the Whitehall Wastewater Treatment Plant and the Whitehall Leather
Company. These discharges were diverted in 1973 and 1974 respectively.
The calculated average pre-diversion point source nutrient loads contri-
buted 23% of the annual total phosphorus and 31% of the annual dissolved
inorganic nitrogen load to White Lake. This would be the maximum reduction
in nutrient loads expected to result from the diversion project. Such a
reduction would not be expected to result in a dramatic change in the trophic
status of the lake.
No significant reductions in phosphorus or nitrogen river concentrations
or loads were actually observed for White Lake despite the diversion. The
potential reduction was believed to be obscured by relatively large fluc-
tuations in unknown upstream loads. On the other hand, water quality in
the White River was not degraded by the spray-irrigation drainage.
Detailed limnological studies were designed to examine the dynamics of
spatial and temporal variation in certain water quality characteristics.
Seasonal nutrient dynamics were closely tied to algal uptake, thermal
stratification, hypolimnetic anoxia, bacterial decomposition, ammonifica-
tion, nitrification, and allochthonous loads. Seasonal nutrient depletion
due to algal and macrophytic uptake were observed for phosphorus and nitro-
gen. Summer hypolimnetic concentrations of nutrients were extremely high as
a result of active decomposition and sediment release. Bioassay and nutri-
ent ratio analyses characterize the spring and summer surface waters as
nitrogen limited. This is confirmed by the dominance of nitrogen-fixing
blue-green algae. These organisms proliferate in nitrogen poor environments
while other algae which require dissolved inorganic nitrogen (ammonia, nitrite
or nitrate) fail to grow. Phosphorus was determined to be the potential
limiting nutrient in the fall. Detailed limnological and nutrient cycle
modeling is required for the proper and detailed assessment of algal growth
limitation.
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Studies were conducted in White Lake to evaluate the significance of macro-
phytes to the total lake nutrient budget and to determine the importance
of nutrient exchange between sediments and the water column to lake
nutrient dynamics. These factors were considered to be important to lake
chemistry and ecology and to have the potential to negate some of the
beneficial effects of the nutrient diversion program.
An evaluation was made of limnological data collected over four years
(1972-1975) on White Lake to determine if any improvements in water quality
would be observed to result from the diversion project. Average surface
concentrations of dissolved inorganic nitrogen and phosphorus were essen-
tially unchanged between 1972 and 1975, although ammonia levels dropped
slightly in the surface waters and markedly in the bottom waters while
nitrate in surface waters increased. Average chlorophyll a. levels were
reduced from 12.4 vg/£ in 1972 to 8.6 in 1974 and 1975. These improve-
ments were not reflected in increased water clarity. Analysis of summer
hypolimnetic dissolved oxygen suggests slightly improved conditions.
Bottom waters still experienced anoxia, but the rate of depletion was
slower and the vertical extent somewhat less. This could be a result of
decreased BOD loadings and possibly a reduction in autochthonous loads.
Less severe hypolimnetic anoxia would result in reduced nutrient release
from the sediments and improved conditions for benthic fauna.
Analysis of White Lake using simple models (Vollenweider, 1975; Dillon and
Rigler, 1974, 1975) and a complex productivity model suggest that under
1975 loading conditions White Lake will remain eutrophic. The diversion
has, however, had the effect of shifting the condition of the lake to a
state whereby further reductions in nutrient loads can result in signifi-
cant improvements in chlorophyll «• levels and water transparency. Various
additional management alternatives are briefly evaluated using the produc-
tivity model.
MUSKEGON LAKE
The baseline limnological conditions in Muskegon Lake were similar to White
Lake. The lake was characterized by high nutrient and algal concentrations
and could also be classified eutrophic. Macrophytes were present but not
severely troublesome. Average chlorophyll a levels in 1972 were approxi-
mately 25 yg/Jl; however, the peak level was over 50 yg/£. Peak summer pri-
mary productivity was high averaging about 60 to 75 pg/&. Secchi disc visi-
bility averaged about 1.5 meters. Surface water concentrations of total
phosphorus averaged 67yg P/£; in 1972 however; values were measured in
excess of lOOyg P/£. Winter dissolved inorganic nitrogen concentrations
approached 400 pgN/£. The bottom waters of Muskegon Lake were, like White
Lake, characterized by high phosphorus and ammonia concentrations. Summer
bottom water anoxia was observed; however, this condition was less stable
than in White Lake. Nitrate was observed at times in summer bottom waters;
suggesting the occurrence of nitrification and thus the presence of oxygen.
Unstable anoxic conditions are believed to be related to storm, circulation,
and ship traffic induced disruptions of the thermocline and Lake Michigan
water intrusion.
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The Muskegon River was found to be the major nutrient source to Muskegon
Lake. Two municipal treatment plants, the S.D. Warren Paper Company, and the
Storey (Ott) Chemical Company contributed significant nutrients to the lake
prior to diversion. The pre-diversion point sources of nutrients accounted
for 38% of the annual total phosphorus load and 50% of the annual dissolved
inorganic nitrogen load. Storm water loads were estimated to contribute
less than 10% of the total phosphorus load. The remaining load originates
from Muskegon River upstream non-point loads.
A reduction of approximately 20 to 25% in nutrient loads (total phosphorus
and inorganic nitrogen) to Muskegon Lake was actually observed subsequent
to the diversion. The observed reduction was somewhat less than the
anticipated reduction because of variable upstream loads. The spray-irriga-
tion drainage did not have any consistent undesirable effects on Muskegon
River water quality. The spray site load to Musekgon Lake was at most 1.5% of
the total phosphorus load and 11% of the dissolved inorganic nitrogen load.
Specific observations during periods of lagoon discharge and spray site fer-
tilization are not available.
The seasonal dynamics of plankton and nutrient cycles in Muskegon Lake were
similar to those observed in White Lake. Spring and summer surface nutrient
depletion was caused by phytoplankton blooms. Summer hypolimnetic anoxia and
bottom water nutrient accumulation were also observed. All processes were
closely tied to the algal uptake, death, and decomposition cycles and thermal
stratification. In Muskegon Lake nutrient ratio analyses suggest phosphorus
limitation in the spring and fall. Summer waters are nitrogen limited, and
as a consequence nitrogen fixing blue-green algae proliferate.
Significant changes in nutrient conditions in Muskegon Lake were observed
between 1972 and 1975 following nutrient diversion. Phosphorus levels
were decreased by approximately 50%. Although dissolved inorganic nitro-
gen was not observed to decrease, the nitrate to ammonia ratio increased
favoring the more oxidized form. Average chlorophyll a concentrations
were reduced by 62% to 9.5 yg/£ in 1975. These reductions did not
result in increasing water clarity. Hypolimnetic dissolved oxygen levels
were slightly improved. Analysis of Muskegon Lake data using the Vollenweider
model show that at present loading conditions the lake will remain eutrophic.
The system condition has however been shifted to a state where additional
reduction in nutrients may result in observable changes in water clarity.
MONA LAKE
Mona Lake was the most highly productive of the three lakes. Nutrient
concentrations were extremely high. Total phosphorus concentrations reached
maximum values of 535 yg P/Jl in surface waters and 2,400 yg P/£ in hypo-
limnetic waters in the summer. Dissolved inorganic nitrogen levels of
2 mg/£ were measured in the bottom waters. Chlorophyll a measurements
-------
often exceeded 100 yg/5, with associated primary productivities exceeding
100 yg C/Ji/hr. Secchi disc visibility averaged 1 meter in depth with a
minimum value of 0.3 meters observed. The bottom waters of the lake
were devoid of oxygen for as long as four months during the summer.
Black Creek was the most significant hydrologic input to Mona Lake, however,
prior to diversion Little Black Creek contributed more nutrients. The
principal sources of nutrients to Little Black Creek were municipal and
industrial discharges as well as urban runoff. It was estimated that the
prediversion point source loads represented 65% of the total phosphorus
load to the lake and 45 to 65% of the dissolved inorganic nitrogen load.
Since all of the point sources were not diverted by 1975 the potential
reduction in load as a consequence of the diversion project was 60% for
total phosphorus and 40 to 55% for dissolved inorganic nitrogen. The
actual 1972 to 1975 observed reduction was 65% for phosphorus and 30 to
45% for dissolved inorganic nitrogen. Nutrients loads from storm runoff,
urban drainage,and other unidentified sources were considered significant.
Spray site drainage did not have a dramatic effect on Black Creek water
quality. The nutrient loads from the drainage were 5 to 15% of the total
post diversion load.
Algal nutrient uptake, decomposition and sediment release, thermal strati-
fication, nitrification, and denitrification were observed to affect the
seasonal dynamics of limnological cycles in Mona Lake. The processes
were quite similar to those observed in White Und Muskegon Lakes. However,
Mona Lake algal dynamics were effected by the application of algicides
in the summer. As a consequence, the maximum phytoplankton population
occurred in the late fall in contrast with the summer maximum observed
in the other two lakes. Nutrient ratio analyses indicate that Mona Lake
has a potential for nitrogen limitation. Nitrogen fixing blue-green algae
were not observed to dominate in Mona Lake. All nutrient concentrations
were excessively high in Mona Lake waters and actual nutrient limitation
of growth was not expected.
Of the three lakes studied, Mona Lake experienced the largest reduction
in average surface water phosphorus concentrations (60-70%). Summer
bottom water ammonia and phosphorus concentrations also were reduced dra-
matically. Average surface water nitrogen concentrations increased
slightly. However, chlorophyll a concentrations were measured to be
markedly higher all three years following the diversion. This trend
could be the result of inconsistent year-to-year applications of algi-
cides. No improvements in water clarity were observed. Application
of simple eutrophication correlations suggest that further reductions
in nutrients are required before substantial improvements in chlorophyll a
and Secchi disc can be realized. Descriptions of changes in loading rates
and nitrogen, phosphorus and chlorophyll a concentrations are presented
in Figures 1 and 2.
-------
40
30
20
101-
1974
1973
- 1
972
1970
200
150
100
50
•
1974
1
-
972 1973
975
TOTAL PHOSPHORUS
DISSOLVED
INORGANIC NITROGEN
WHITE LAKE
200
150
100
50
1972
1975
19731974
1000
750
500
250
1
972
1
973
^^^MB
1
1974
975
TOTAL PHOSPHORUS
DISSOLVED
INORGANIC NITROGEN
MUSKEGON LAKE
20
10
1972
1973
200
150
100
- 1972
19731974
1975
TOTAL PHOSPHORUS
DISSOLVED
INORGANIC NITROGEN
MONA LAKE
Figure 1. Annual average nutrient loadings to the
Muskegon Lakes.
-------
20
15
10
5
0
r 20
"1972 IQT* l5
-
_.
1974 1975 10
5
0
r 200
" 197?
-
973
974
1975 '50
100
50
— 0
P
.
.
-
1973
974
1975
CHLOROPHYLL a (fj.g/1)
TOTAL DISSOLVED PHOSPHORUS
P/Jt)
DISSOLVED INORGANIC NITROGEN
WHITE LAKE
40
30
20
10
n
"
972
40
30
973 20
1974 1Q7^
— .21^ 10
_ o
-
1972
973
'
974 915
200
150
100
50
— 0
1975
-
972
-
1973
974
CHLOROPHYLL a
TOTAL DISSOLVED PHOSPHORUS
(fig PA!)
MUSKEGON LAKE
DISSOLVED INORGANIC NITROGEN
(fiQ
40
30
20
10
0
-
1972
1973
974
975
300
225
150
75
— 0
"
97?
600
450
973 300
975 150
197*4 IOU
n o
r 1973 974
-
972
975
CHLOROPHYLL a (fig/I)
TOTAL DISSOLVED PHOSPHORUS
P/l)
MONA LAKE
DISSOLVED INORGANIC NITROGEN
(fiQ N/J)
Figure 2. Annual average surface water concentrations of selected water quality
variables in the Muskegon Lakes.
-------
SECTION II
RECOMMENDATIONS
FUTURE WATER QUALITY STUDIES
This study represents a thorough investigation of nutrient and eutrophi-
cation related parameters for White, Muskegon, and Mona Lakes during the
years 1972 to 1975. Extensive data were also collected on tributary nu-
trient loads. There were, however, inherent limitations to the study and
as a consequence, additional research is necessary to more completely
understand the factors which affect water quality in the Muskegon Lakes.
The major limitations of this report evolve around its limited duration
and scope. The following studies are recommended in descending order of
priority.
First, it is important to continue to monitor the water quality in the
three lakes and their associated tributaries. The duration of the present
study was not sufficiently long to accurately observe the complete
response of the lakes following diversion. This limitation resulted
from the delayed implementation of the diversion spray-irrigation system
which shortened the actual post-diversion study period. An additional
two or three years of monitoring is recommended so that the extent of
additional improvements in water quality can be determined. Adequate
information is presently available on the seasonal and spatial dynamics
of the lakes. A limited sampling program is therefore recommended. Two
stations should be sampled for each lake on a biweekly basis during the
ice-free season. Monitoring should focus on nutrients (including kjeldahl
nitrogen), chlorophyll a, dissolved oxygen, biochemical oxygen demand, and
primary productivity.
A similar biweekly sampling program is recommended for tributary moni-
toring. Additional special studies should be conducted to accurately
quantify the sources of non-point contamination to each of the tributaries
and determine which of these sources are controllable. These studies must
include an assessment of storm sewer runoff, waste lagoon seepage, illegal
discharges, urban runoff, and septic field drainage. Estimates of the
importance of some of these sources were presented within this report
although detailed assessments were beyond the scope of the study. Data
from this study indicate that additional dramatic improvements in the
trophic status of the Muskegon Lakes can only be achieved through control
of these non-point and unidentified nutrient sources.
A major limitation of this report is the absence of complete taxonomic
analysis of phytoplankton, zooplankton, and benthos samples to support
the other chemical and biological data. However, preliminary analyses
-------
of these data generally support the conclusions of this report
(Meier, 1977). It is strongly recommended that these samples be thoroughly
analyzed. Continued sampling of phytoplankton, zooplankton, and benthos
is also recommended. Changes in species composition detected through
taxonomic analysis can often identify alterations in water quality which
may not otherwise be observed.
It is recommended that additional mathematical water quality models be
developed for Muskegon and Mona Lakes. These should be of the same level
of sophistication as the White Lake model. Development of these models
would permit more accurate, quantitative, and reliable evaluation of basin
and water management alternatives and their effects on lake water quality.
Use of such models will permit necessary cost-effectiveness evaluations.
A fourth recommendation for further research is to monitor various trace
organic and trace metal contaminants in the lakes. Although adequate
data are not available from a pre-diversion period, information may be
obtained by examining sediment concentrations and correlating sediment
depth with time. These investigations would permit an evaluation of trace
contaminant water quality problems in the lakes and could relate possible
changes to the diversion spray-irrigation system or other basin management
practices.
The last recommendation is for detailed process studies to evaluate mac-
rophyte ecology, sediment water interactions, epilimnetic and hypolimnetic
mixing, and algal growth potential in each of the lakes. These processes
have been found to be of varying importance in the lakes and need to be
further studied for accurate scientific understanding and rational manage-
ment.
MANAGEMENT RECOMMENDATIONS
Studies on White Lake have demonstrated that the major source of nutrient
contamination originates from unidentified sources in the White River up-
stream of the land disposal site. If further significant water quality
(nutrient and chlorophyll a) improvements are desired, then these
non-point sources must be identified, quantified and controlled where
feasible. This may require land-use management. Particular emphasis
should be focused on nutrient contamination from septic tank seepage,
celery farm drainage, and other sources of agricultural and forest run-off.
In Muskegon Lake, upstream nutrient sources were also determined to be
dominant. The control of the sources may require land use management.
First, however, more detailed quantification of the sources is required.
A limited (up to 10%) reduction in nutrient loads to Muskegon Lake may
be achieved by controlling storm-sewer runoff. Contamination of the
-------
lake by substances not studied in this research may have changed as a
result of the diversion, but additional urban sources may have to be
controlled to achieve further water quality improvements. Future studies
will help answer these management questions.
In the Mona Lake basin the most significant and immediate reduction in
remaining nutrient loadings would result from elimination of urban and
storm runoff, and industrial discharges to the Little Black Creek Basin.
This is the highest priority. Waste lagoon seepage to Black Creek may
also be an important nutrient source. Only after control of these sources
should the difficult task of land managment be addressed.
Direct lake rehabilitation programs such as dredging, aeration, and mixing
are not recommended for any of the lakes unless further reductions in
nutrient loads are achieved. Macrophyte harvesting and limited sediment
dredging may be helpful in White Lake to improve accessibility. However,
macrophytes represent a habitat for many lake fish and should not be en-
tirely eliminated. Full lake bottom dredging in White Lake is not recom-
mended. Detailed data concerning the effects of sediments and macrophytes
were not obtained for Muskegon and Mona Lakes. However, lake bottom
sediment dredging of Muskegon and Mona Lakes is not recommended unless
significant future nutrient load reductions are achieved. Macrophytes are
not a problem of sufficient magnitude in either Muskegon or Mona Lakes to
require harvesting.
10
-------
SECTION III
INTRODUCTION
Muskegon County, Michigan has recently been the focus of a considerable
amount of national attention. The region has had a history of uncontrolled
exploitation of its natural resources. Decades of resource degradation,
industrial sprawl, uncontrolled development, and pollution have forced
the county into a recent economic crisis. The county has now taken an
aggressive and innovative step in wastewater management. The county im-
plemented a wastewater management program whereby numerous municipal and
industrial waste discharges that were formerly discharged directly or
indirectly to Muskegon, White, and Mona Lakes are now diverted and trans-
ported to an inland spray-irrigation and disposal site. The wastes are
treated with secondary aeration in lagoons. The wastewater is then sprayed
on land where agricultural crops and soil act to filter and cleanse the
effluent through what has been termed a "living filter." This program
is based on the environmental concept that air, water, and land are one
interacting system. No wastes can be discarded without ultimate reper-
cussions and these wastes represent misplaced resources.
The concept of spray-irrigation of wastes to dispose of sewage and si-
multaneously raise farm crops is not new to the United States. Muskegon
County, however, was the first in the United States to attempt such a
system on a large scale to a regional population. The chief goal of the
system is to eliminate pollutional discharges efficiently and economically.
It is also hoped that implementation of the system would restore the
natural beauty of the lake environments degraded by pollution thus promoting
industrial growth and recreational development in the area.
A multidisciplinary research effort has been directed towards evaluating
the effectiveness of the new waste management system. This effort has
involved scientists and investigators from the U.S. Environmental Pro-
tection Agency, the University of Michigan, Michigan State University,
the Michigan Water Resources Commission, and Muskegon County. As part
of this program, the University of Michigan has been studying the impact
of the spray-irrigation system on surface water quality in the region.
White, Muskegon, and Mona Lakes are the most largely exploited lakes
of the region, and thus were the focus of the study. The objectives
of this study were:
1. To document pre-diversion water quality in the three
Muskegon County lakes and their tributaries.
2. To evaluate potential and actual reductions in
nutrient loads to the lakes following implementa-
tion of the sewage diversion, spray-irrigation
system.
11
-------
To assess potential and actual improvements in lake
water quality resulting from the implementation of the
system. In this study the water quality focus was on
phytoplankton growth nutrients, primary productivity,
and eutrophication related parameters.
12
-------
SECTION IV
DESCRIPTION OF STUDY AREA AND SOCIO-ECONOMIC HISTORY
Muskegon County is located on the eastern shore of Lake Michigan near
the midpoint of the western side of the lower peninsula in the State
of Michigan (see Figure 3). Muskegon County has a population of 157,000
which is principally concentrated in two urban areas. The larger of
the two areas is the Muskegon, Norton Shores, North Muskegon, and
Roosevelt Park region which includes 80% of the population. These muni-
cipalities are located in an area surrounding Mona and Muskegon Lakes.
Muskegon and Muskegon Heights are industrialized. The prominent in-
dustries are the S.D. Warren Company (paper mill); the Storey (Ott)
Chemical Company; and various other chemical, manufacturing, and foundry-
related industries. The other significant population center is White-
hall and Montague located at the eastern end of White Lake. This area
is much less industrialized. The only significant industries located
there are the Whitehall Leather Company, the Hooker Chemical Company,
and the Misco Division of Howmett Corporation (heavy manufacturing).
The lands outside of these urban areas, which include the remainder
of the drainage basins of the three lakes, are primarily forested and
rural.
The surface geology of the region is principally a reflection of glacial
effects. The surface features consist of glacial lake beds, outwash,
end moraines, ground moraines, sand dunes, delta deposits, abandoned
beaches, and waterlaid moraines. These features can be categorized
into four types: 1) moraine uplands, 2) outwash plains, 3) glacial
lake plains, and 4) alluvial lowlands. The moraine uplands are located
in the eastern and northwestern part of the county and are generally
associated with terminal moraines. The outwash plains are located
west of the uplands and exhibit an irregular and undulating topography.
The glacial lake plain is in the west and central portion of the county,
while the alluvial lowlands are associated with natural stream cuts in
the terrain. The glacial lake beds were formed primarily during the
Glenwood stage of Lake Chicago. The Muskegon and White Rivers are modern
counterparts of preglacial streams that flowed into Lake Chicago and
deposited sand and gravel to form deltas. Because of the sand and
gravel content of the surface glacial deposits, water infiltration rates
of the soil are high. The groundwater table in the area is also very
high, often only 5 or 10 feet from the surface. During extremely wet
periods or when lake levels are high, groundwater can cause basement
flooding, septic tank malfunction, and create marsh and wetland areas.
The climate of the region is typically midwestern although somewhat
modified by Lake Michigan. The area receives an average annual pre-
cipitation of 79.8 centimeters. The dominant winds are westerly. During
13
-------
STATE OF
MICHIGAN
Muskedon
Roosevelt Heiafits
Park
1mA LAKE
Muskegon
Spray
Site
LAKE MICHIGAN
Figure 3. The Muskegon Lakes study area.
-------
winter months warm westerly winds bring significant amounts of precipi-
tation. This is reflected by relatively high winter flows observed
in rivers, a consequence of snow melt and rain.
Muskegon County became a prosperous center of urban activity in 1840.
During the nineteenth century the economy was based almost entirely
on the exploitation of the valuable pine forests of the area. Rivers
cut deep into the forest providing cheap transportation of logs and
the dune impounded lakes at the river mouths provided excellent sites
for mills. Unfortunately, a half century of clear-cutting practices
stripped the area of its forest resources. At approximately the same
time industrialization was blooming in the region. Easy access to
Great Lakes water routes and railroad transportation, as well as an
abundant supply of foundry sands, encouraged heavy industry. Markets
for the goods produced were first the expanding railroads, followed by
the auto industry, and then national defense contracts—a vast market
heavily maintained by two world wars. Another natural resource that
boosted the economy of the area was oil, first discovered in 1927. By
1940, however, the wells were no longer profitable. Most oil reserves
had been depleted due to ravenous exploitation, inadequate regulation,
and inefficient extraction. Air and water pollution grew worse in the
area as urban and industrial development grew unchecked and discharged
wastes to the environment.
Attempts to introduce farming in 1930 were not highly successful. The
land had been left barren and was unsuited for farming because the soils
were very sandy and had little topsoil. As a consequence, recession
struck heavily in the area in the 1950fs and 1960's. By 1968 the un-
employment rate was double the national average and per capita income
was the third lowest in the state. Population growth in the county
between 1960 and 1970 was 4.2% compared to 13.4% for the entire state.
Industries could no longer compete with more modern plants elsewhere
and environmental degradation limited expansion. New industry was
not attracted to the area because of the largely unskilled work force
and pollution problems. Tourism, the third largest industry of the
county, was also threatened by air and water pollution, exploitation
of the coastal sand dunes, and uncontrolled urban sprawl.
As a result, Muskegon County took innovative steps to divert all waste
discharges from the lakes and pipe them inland for treatment and spray-
irrigation on the land. It was hoped that this scheme would meet the
increasingly strict government regulations on pollutional discharges
and would revitalize the polluted Muskegon County environment. The
plan was based on three considerations:
1. The environment is one system with interactions among
air, land, and water. Cultural development affects
and is affected by the system.
15
-------
2. The system is considered closed for planning purposes.
Nothing can be thrown away that could return to trouble
us later.
3. Wastewaters are potential resources out of place. If
relocated in the environment, they can take on new
values.
The goals and objectives of the diversion spray-irrigation project
were:
1. To protect Lake Michigan from materials that stimulate
excessive algal growth, toxic materials, and other
contamination.
2. To eliminate present sources of pollution in the prime
shoreline lakes (Muskegon, Mona, and White).
3. To maximize environmental improvement and facilitate
economic development, tourism, and other water-
oriented recreational activities.
4. To encourage programs that provide opportunities to
reclaim the large areas of unproductive land lying
dormant in the county.
5. To facilitate regional economic development by pro-
viding environmental management systems with long-range
economic efficiencies and required performance capa-
bilities.
16
-------
SECTION V
HISTORY AND OPERATION OF THE MUSKEGON
DIVERSION SPRAY-IRRIGATION SYSTEM
The Muskegon wastewater management system consists of six basic con-
ponents:
1. Collection and transportation of wastewater to the
inland treatment site.
2. Biological treatment of the wastes in aerated lagoons.
3. Storage of the treated wastes in holding basins.
4. Spray-irrigation of the treated wastewater on the land.
5. Filtration of the wastewater through the soil and
uptake by crops.
6. Collection of the drainage by underdrains and subse-
quent discharge to receiving streams.
The county has established two separate systems to handle wastes. The
larger of the two sites handles the wastes formerly discharged to
Muskegon and Mona Lakes. It presently accepts approximately 28 MGD
and has a 1992 design flow of 42 MGD. The drainage from this spray
system is discharged to both the Muskegon River via Mosquito Creek
and to Black Creek. A smaller system handles the wastewater formerly
discharged to White Lake. This 1.4 MGD system discharges its spray
drainage to the White River.
Construction of the system began in 1971 although full operation did not
begin until 1974. A detailed discussion of the history of the develop-
ment and operation of the system is available elsewhere (Muskegon County,
1976). Wastes from the communities of Muskegon, Norton Shores, and
Roosevelt Park were diverted on May 10, 1973. This eliminated the
Muskegon Wastewater Treatment Plant discharge to the Muskegon River
and a portion of the Muskegon Heights Wastewater Treatment Plant dis-
charge to Mona Lake. On May 30, 1973 Muskegon Heights diverted the
remainder of their discharge. The City of Whitehall diverted their
municipal wastes from White River to the spray site on July 18, 1973.
Also on June 4, 1973 the S.D. Warren Company diverted its wastewater
discharge from Muskegon Lake. In 1974 Storey (Ott) Chemical Company
diverted its wastewater discharge from the Muskegon River (April 18)
and on November 24 the Whitehall Leather Company diverted its waste
17
-------
from direct discharge to White Lake. Other industries have or are in
the process of diverting their waste discharge to the spray system.
However, many areas surrounding the Muskegon Lakes are still unsewered
and/or not connected. The status of areas surrounding each lake is
given in Figures 20, 59 and 87 and Appendix F. A chronology of waste-
water diversion is presented in Table 1.
In 1973 wastes were treated and stored in the large basins until 1974
when spraying of the wastes began. However, problems with clogging
of spray-irrigation equipment and waste transmission pipes, and elec-
trical and construction difficulties prevented full and regular spraying
during all of 1974. As a consequence, 247 million gallons of pretreated
and storad wastes were spilled directly into Mosquito Creek during the
summer of 1974 and 2,263 million gallons were again discharged directly
without spraying during the winter of 1974 to 1975. Since that time,
the system has performed well according to design. During 1975,
7,437 million gallons of waste were sprayed on the Muskegon-Mona site.
The drainage discharged 6,659 and 1,703 million gallons to the Muskegon
River (Mosquito Creek) and Black Creek, respectively. The differences
in the water balance are due to rainfall and natural drainage. Nitrogen
fertilizers were used on the irrigated crops during 1974 and 1975. The
efficiency of natural filtration and plant uptake to remove wastes and
nutrients was similar to the design expectations: 99% biochemical oxygen
demand removal, 99% suspended solids removal, 90% phosphorus, and 76%
nitrogen removal. The monitored nutrient content of the Mosquito Creek
drainage during 1975 was 50 yg P/£ total phosphorus, 600 yg N/£ ammonia,
2,000 pg N/£ nitrate, 3 mg/£ BOD,-, and 7 mg/£ suspended solids.
18
-------
Table 1. CHRONOLOGY OF SOME IMPORTANT EVENTS RELEVANT TO THE
MUSKEGON COUNTY WASTEWATER TREATMENT PROJECT
Date
Event
May 10, 1973
May 10, 1973
May 10, 1973
May, 1973
June 9, 1973
July 18, 1973
July 18, 1973
June, 1974
June, 1974
June, 1974
November 24, 1974
November, 1974
December, 1974
Muskegon municipal wastes are diverted to the
spray-irrigation facility.
Norton Shores municipal wastes are diverted to
the spray-irrigation facility.
Muskegon Heights municipal wastes are diverted
to the spray-irrigation facility.
Begin storage of diverted waste at Muskegon
site.
North Muskegon municipal wastes are diverted
to the spray-irrigation facility.
City of Whitehall municipal wastewaters are
diverted to the spray-irrigation facility.
Misco Division of Howmett Corporation (White-
hall) industrial wastewaters are diverted to
the spray-irrigation facility.
Spray irrigation begins with erratic operation.
Brown and Morse industrial wastewaters are
diverted to the spray-irrigation facility.
Johnson Products wastewaters are diverted to
the spray-irrigation facility.
Whitehall Leather industrial wastewaters are
diverted to the spray-irrigation facility.
Spray irrigation halted.
Direct discharge from storage lagoons begins.
19
-------
Table 1.—continued
Date
Event
February, 1975
April 15, 1975
November, 1975
Direct discharge from storage lagoons ends.
Spray-irrigation begins again with consistent
operation.
Spray-irrigation season ends.
20
-------
SECTION VI
METHODS AND MATERIALS
GENERAL
A program was devised to evaluate background water quality in Mona,
Muskegon, and White Lakes and to evaluate changes following nutrient
diversion. This study consisted of a comprehensive limnological sam-
pling program which monitored physical, chemical, and biological pa-
rameters in the lakes and their tributaries. Water quality sampling
began in the spring of 1972 with an abbreviated sample frequency and
station schedule. From 1973 to the fall of 1975 the sampling program
was at full intensity. A summary of the sampling cruise schedule is
given in Table 2. In general, the program consisted of biweekly sam-
pling of lake and tributary waters during the ice-free season and occa-
sional sampling during periods of ice cover. This sampling permitted
an assessment of lake water quality with respect to average annual
and seasonal dynamics. Although weekly or twice weekly sampling might
have provided better definition of the dynamics of the system, the
expense of such an effort could not be justified in view of the limited
goals and funds of the program. The biweekly schedule offered a rea-
sonable compromise between expense and sampling intensity which pro-
vided adequate information on seasonal dynamics and quantification of
season tributary loads.
The location of the lake sample stations are shown in Figures 4, 5, and
6. The establishment of two sample collection stations in both Mona
and White Lakes was considered adequate for the assessment of average
lake water quality and for the evaluation of spatial variations. In
Muskegon Lake four lake stations were sampled. The additional stations
were considered appropriate because of the larger size of the lake and
because of the diversity of land usage and tributary, municipal, and
industrial discharges. One station was added at the channel outlet
of each lake. This station provided information regarding the exchange
of waters (and their associated quality) between the individual lakes
and Lake Michigan.
In conjunction with the lake sampling program all major tributaries to
the three lakes were sampled. The sample station locations are shown
in Figure 7 and described in Table 3. The design of this sampling
scheme was selected to provide information on chemical loading to the
lakes and to provide information regarding the source of such loadings.
Sample stations were located to determine the effect of the wastewater
diversion and spray-irrigation system on the lakes.
21
-------
Table 2. SAMPLING CRUISE SCHEDULE
N>
Cruise No.
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
32
Dates
May 23-24
June 21-22
July 5-6
July 19-20
August 13-16
August 28-31
September 16
September 30-October 1
October 24
November 20-22
January 16
March 5-6
March 26-28
April 12-14
April 24-27
May 8-12
May 23-25
June 11-14
June 26-29
July 10-12
July 24-26
August 8-10
August 29- September 2
September 11-14
September 26-27
October 8-11
October 23-26
November 6-8
November 19-21
December 11-13
January 21-24
February 25-28
Year
1972
1972
1972
1972
1972
1972
1972
1972
1972
1972
1973
1973
1973
1973
1973
1973
1973
1973
1973
1973
1973
1973
1973
1973
1973
1973
1973
1973
1973
1973
1974
1974
Cruise No.
33
34
35
36
37
38
39
40
41
42
43
44
45
46
47
48
49
50
51
52
53
54
55
56
57
58
59
60
61
62
63
64
Dates
March 18-21
April 9-13
April 22-26
May 6-10
May 21-24
June 4-6
June 13-20
July 1-4
July 15-18
August 13-16
August 26-28
September 16-19
October 8-10
October 22-24
November 6-9
November 19-21
December 9-12
January 27-29
February 24-27
March 26-27
April 7-10
April 21-25
May 5-8
May 20-23
June 4-6
June 16-19
July 15-17
July 28-30
August 11-13
August 26-29
September 8-10
October 20-22
Year
1974
1974
1974
1974
1974
1974
1974
1974
1974
1974
1974
1974
1974
1974
1974
1974
1974
1975
1975
1975
1975
1975
1975
1975
1975
1975
1975
1975
1975
1975
1975
1975
-------
Table 3. LOCATION OF TRIBUTARY SAMPLING STATIONS
U)
Station
Number
2
25
26
27
102
143
144
145
146
147
Tributary
Name
Black Creek
Black Creek
Little Black Creek
Black Creek
Muskegon River
Muskegon River
Muskegon River
Muskegon River
Muskegon River
Muskegon River
Lake
System
Mona
Mona
Mona
Mona
Muskegon
Muskegon
Muskegon
Muskegon
Muskegon
Muskegon
Location
Sullivan Road
Swanson Road
Hoyt Street Bridge
Bus. Rte. 31 Bridge
Mill Iron Road
Maple Island Road
Bus. Rte. 31
Middle Branch
South Branch
At Confluence of
Middle & South
Comment
Downstream of spray drainage
Within the spray drainage
region; added in 1973
River mouth; added in 1973
River mouth; added in 1973
Downstream of spray drainage
Upstream of spray drainage;
added in 1973
North branch near the river
mouth; added in 1973
Abandoned during 1974
Abandoned during 1974
Sampled from boat; added in
1973
148
201
202
226
227
Bear Lake Channel
White River
White River
Mill Pond Creek
White River
Muskegon
White
White
White
White
Branches
Ruddiman Bridge
Fruitvale
US 31
At Pond Falls
Bus. Rte. 31
Near creek mouth; added in 1973
Upstream of spray drainage
Downstream of spray drainage
Near creek mouth; added in 1973
Near river mouth; sampled from
boat; added in 1973
-------
"t
Station Location
Montague
WHITE RIVER
St. 227
Whitehall
LAKE
MICHIGAN
226
MILL
CREEK
Wildcat Creek
0
I
WHITE LAKE
Kilometers
Depth in feet
Lake Survey 1972
Figure 4. White Lake sampling stations.
-------
LAKE
MICHIGAN
Muskegon River
' St. 144
North Branch
City of Muskegon
A Station Location
MUSKEGON LAKE
Miles
Contour locations approximate
Depth in feet
Figure 5. Muskegon Lake sampling stations.
-------
1
N
tt
MICHIGAN^!
Roosevelt
Park
Muskegon
Heights
Norton Shores
Norton Shores
MONA LAKE
A Station Location
o 0.5 1.0
Miles
0 0.5 1
I L_ 1
Kilometers
Figure 6. Mona Lake sampling stations.
-------
Whitehall
Site
st. 2057 WHITE LAKE
STATE OF
MICHIGAN
MUSKEGON LAKE\$
St.
St.
LAKE
MICHIGAN
St. 143
Muskegon
Site
• Sampling Stations
O Spray Site Discharge
^ Spray Irrigation Site
Figure 7. Tributary and lake sampling stations.
27
-------
Three sample stations were located on the White River and on Mill Pond
Creek. No other tributaries merited monitoring. The stations on the
White River were located at the mouth (Station 227) and upstream (Station
201) and downstream (Station 202) of the spray-irrigation site. The
Whitehall Wastewater Treatment Plant discharged a short distance upstream
of Station 227 before diversion. Two Muskegon Lake tributaries were
considered of sufficient significance to sample: The Muskegon River
and Bear Lake Creek. Station 148 was located on Bear Lake Creek.
The Muskegon River stations were located on both of the branches enter-
ing Muskegon Lake. Stations were also located upstream (Station 143)
and downstream (Station 102) of the spray-irrigation site. Pre-diver-
sion municipal and industrial discharges to the Muskegon River were
located between Station 102 and the mouth. Sample stations for Mona
Lake tributaries were located at the mouth of Black Creek (Station 27)
and Little Black Creek (Station 26) and at a site just downstream of
the discharge from the spray site to Black Creek (Station 2). A station
was also located in close proximity to the area at which the spray drain-
age is discharged (Station 25).
Sampling Methods
Routine samples were obtained from aboard a 21-foot outboard Boston
Whaler which was trailered between lakes. Occasionally special sampling
cruises were conducted from the University of Michigan R/V MYSIS. This
included cruises for sampling lake sediment. During periods of ice
cover an all-terrain vehicle with a plastic dinghy in tow provided
transportation on the lakes. Water samples were taken from the lake
stations using a four-liter polyvinyl chloride Van Dorn sampling bottle.
Samples were taken at all lake stations at 2 meters and at a depth 1
meter from the bottom. At one station in each lake (Station 4 in Mona
Lake, Station 106 in Muskegon Lake, and Station 204 in White Lake)
water samples were taken at a 1-meter depth and at mid-depth approximately
midway between the surface and bottom. The bottom water samples were
taken using a modified, inverted Van Dorn bottle designed to close when
a weight suspended 1 meter below the bottle made contact with the lake
bottom.
Tributary water samples were taken from surface waters only. When
access permitted, river mouths were sampled from the Boston Whaler
using Van Dorn sample bottles. Otherwise, samples were taken with plastic
buckets lowered from bridges or cast from the river banks.
Water samples were siphoned from the Van Dorn bottles or sampling
buckets into necessary containers for sample storage and preservation.
A small laboratory was located in Whitehall, Michigan where samples
were processed and prepared for transport to University of Michigan
laboratories for analysis. Specific methods of sample storage and
preservation are discussed in the next subsection on techniques of analysis.
28
-------
In general, samples were collected and then transferred to 1-liter
polyethylene containers with the appropriate preservatives added.
Waters intended for nutrient and ion analysis were temporarily stored
in ice water without preservatives. Aliquots were transferred to smaller
polyethylene bottles at the Whitehall laboratory and frozen for trans-
port to Ann Arbor. Other portions were pressure filtered through
0.45 y acid-washed Millipore filters and then frozen. Other operations
performed at the Whitehall laboratory included only those activities
not compatible with sample storage or later analysis. These included
filtration of chlorophyll a samples and titration of dissolved oxygen
samples.
The methods of analysis for water samples generally conformed to tech-
niques as described in Standard Methods (APHA, 1971). The methods of
analysis used are summarized in Table 4 along with their associated
uncertainty at concentrations typically measured in the Muskegon Lakes.
A detailed description of the physical, chemical, and biological methods
used is given in the following sections. Unless otherwise noted all
chemical analyses were performed on a Technicon Model II AutoAnalyzer.
Quality control tests were routinely performed. Periodically samples
having a known concentration were measured alongside lake water samples.
The frequency of occurrence was approximately once for each twenty-five
lake samples. Spike and recovery experiments were also routinely per-
formed. Studies were conducted to test storage and preservation tech-
niques. Results from all of the quality control procedures indicate
satisfactory precision and accuracy. In 1973 the analytical staff par-
ticipated in a U.S. Environmental Protection Agency interlaboratory
nutrient analysis comparison. The results of this study are shown in
Table 5. An additional analytical comparison study was conducted be-
tween the University of Michigan laboratories and the Michigan Depart-
ment of Natural Resources Water Resource Commission laboratories.
Collectively the above studies indicate high reliability of the Univer-
sity of Michigan analysis techniques.
PHYSICAL AND CHEMICAL METHODS OF ANALYSIS
Alkalinity
Unfrozen samples were stored in completely filled polyethylene bottles.
Analyses were completed immediately following the cruise using acidifica-
tion - pH measurement techniques (Strickland and Parsons, 1968). The
samples were titrated with 0.01 N hydrochloric acid to a pH below 4.
Biochemical Oxygen Demand
Biochemical oxygen demand (BOD) was measured on a limited number of
samples from White Lake. Samples were stored under refrigeration in
29
-------
Table 4. SUMMARY OF METHODS OF ANALYSIS
Parameter
Alkalinity
Ammonia Nitrogen
Biochemical
Oxygen Demand
Chloride
Chlorophyll a
Method
Acid titration
AutoAnalyzer
phenate reaction
Incubation
Standard Methods
AutoAnalyzer
thiocyanate method
Fluorometry
Remarks
Uncertainty:
LD: 10 yg N/£.
Uncertainty:
LD: 0.15 mg/A
Uncertainty :
LD: 0.2 mg/Ji
Uncertainty :
LD: 0.01 yg/Jl
0.02 meq/£
15 yg N/£
20%
3%
Chemical Oxida-
tion Demand
Dissolved Oxygen
Iron
Nitrate &
Nitrite
PH
Phosphorus
Primary Productivity
Silicon
Specific Conductance
Total Organic Carbon
Temperature
Transparency
Dichromate oxidation
Azide-Winkler titra-
tion or potentiometric
electrode
AutoAnalyzer
TPTZ method
AutoAnalyzer
diazotization and
cadmium reduction
Submersible electrode
AutoAnalyzer ascorbic
acid
reduction, persulfate
digestion
In situ C14
AutoAnalyzer silicomo-
lybdate complex
formation
Conductivity Meter
Digestion & gas chro-
matographic deter-
mination of C0~
Submersible Thermister
Secchi disc
Uncertainty:
LD: 1 mg/£
Uncertainty: 10%
Uncertainty: 0.05 mg/£
D:
20
Uncertainty: 2-3%
LD: 10 yg N/fc
Uncertainty: 10 yg N/fc
Uncertainty: 0.05 units
LD: 5 yg P/£
Uncertainty:
20% @ 10 yg P/&
2% @ 60 yg P/£
Uncertainty: 10-20%
LD: 0.03 mg
Uncertainty: 1%
Uncertainty: 5-7%
LD: 1 mg/Jl
Uncertainty: 10%
Uncertainty: 0.1°C
Uncertainty: 20%
L : lower limit of detection
30
-------
Table 5. USEPA INTERLABORATORY COMPARISON STUDY
Total
Species
P mg/£
Soluble Reactive P mg/£
NH-3N
N03-N
mg/£
mg/£
U
0.
0.
0.
0.
Sample
of M
069
010
038
268
A
0
0
0
0
... .
EPA
.064
.010
.041
.252
U
0.
0.
0.
0.
Sample
of M
043
008
021
631
B
0
0
0
0
=
EPA
.038
.008
.026
.610
-------
amber bottles. BOD was measured using standard incubation techniques
as outlined in Standard Methods (APHA, 1971). A Precision Instruments
galvanic cell oxygen analyzer was used to measure oxygen uptake. Seeding
and dilution of water samples was not necessary.
Chemical Oxygen Demand
Analysis for chemical oxygen demand (COD) was conducted on 250 mH water
samples preserved with 0.5 mJl concentrated sulfuric acid and refrigerated.
Only a limited number of samples for White Lake were analyzed. The
method of analysis used is described in Standard Methods (APHA, 1971).
The samples were refluxed with 0.025 N dichromate with sulfamic acid
added to prevent nitrate interference. The sample was titrated with
ferrous ammonium sulfate.
Chloride
Frozen filtered water samples were used for the determination of chloride
concentration. Analyses were done on the Technicon AutoAnalyzer. A
colorimetric determination was used which depended on the liberation of
the thiocyanate ion from mercuric thiocyanate caused by the formation of
an unionized but soluble mercuric chloride compound. In the presence
of ferric ions the liberated thiocyanate forms a highly colored compound,
the color of which is proportional to the original chloride concentra-
tion (Technicon Instrument Corp., 1971, O'Brien, 1962, Zall et al.3 1956).
Dissolved Oxygen
Samples for dissolved oxygen (DO) were analyzed using the sodium azide
modification of the Winkler titration (APHA, 1971). Samples were fixed
immediately in the field in standard glass BOD bottles. The samples
were acidified and titrated with thiosulfate aboard ship or at the end
of the day in the Whitehall laboratory. The titrant was standardized
daily with a biniodate solution. Additional dissolved oxygen measure-
ments were made at 1-meter depth intervals at each lake station using a
Martek Instrument Corporation submersible electrode. Measurements were
calibrated using the results from the Winkler titrations.
Hydrogen Ion Activity
pH was determined using a Leeds and Northrup Model 7417 pH meter with
temperature correction. A glass pH electrode with a calomel reference
electrode was used. The meter was calibrated with two different pH
buffer solutions each day. In A-utu measurements were also taken at
each lake station at 1-meter depth intervals using a Martek Instruments
Corporation submersible electrode.
32
-------
Iron
Nutrient water samples were measured for Iron concentrations using a
wet chemical automated procedure. The method is based on the formation
of a violet complex of ferrous iron with 2, 4, 6 tri (2-pyridyl) - s -
triazine (TPTZ). Hydroxylamine was used to insure reduction of any
trivalent iron to its divalent state and a sodium acetate buffer was
used to provide the proper pH for maximum color development (Technicon
Instrument Corp., 1973a). Measurements were made on a Technicon Auto-
Analyzer II. Dissolved iron was measured from filtered water samples.
To measure total iron, samples were first digested in a persulfate solu-
tion. The detection limit of the test was 20 yg Fe/Jl and the uncertainty
was 10 yg Fe/£. In some cases, precipitation of oxidized iron compounds
before analysis might have occurred due to the introduction of oxygen
to anaerobic waters. This oxidation could occur during shipboard storage
or pressure filtration. Consequently, peak summer hypolimnetic iron
measurements are possibly low.
Ammonia Nitrogen
Ammonia concentrations were determined on the AutoAnalyzer utilizing
the Berthelot reaction. In this technique a blue compound forms when a
solution of an ammonium salt is added to sodium phenoxide (Technicon
Instrument Corp., 1973b, USEPA, 1974). EDTA was used to prevent precipi-
tation of hydroxides of calcium and magnesium. The accuracy of the
test at low concentrations was highly sensitive to ammonia contamination
in the laboratory air.
Nitrate, Nitrite Nitrogen
Nitrate was determined on the AutoAnalyzer utilizing a procedure whereby
nitrate is reduced to nitrite in a cadmium column and then reacted with
sulfanilamide under acid conditions to form a diazo compound. This com-
pound then couples with N-l napthylethylenediamine dihydrochloride to
form a reddish purple azo dye, the color of which is proportional to
the nitrite concentration (Technicon Instrument Corp., 1972, USEPA,
1974). Nitrite was measured separately by foregoing the reduction.
All data presentations of nitrate values include nitrite.
Phosphorus
Total dissolved phosphorus was determined on filtered nutrient samples
after digestion in a persulfate solution (Menzel and Corwin, 1965). The
resulting released soluble reactive phosphorus was determined on the
AutoAnalyzer using the Murphy and Riley (1962) ascorbic acid reduction
technique (Technicon Instrument Corp., 1973c, USEPA, 1974). A
33
-------
phosphomolybdenum complex is formed and reduced by ascorbic acid to form
a blue compound, the color of which is directly proportional to the
phosphorus concentration. Total phosphorus was determined similarly
except that the analysis was done on an unfiltered nutrient water sample.
Measured concentrations of phosphorus from anaerobic waters may be lower
than actual concentrations if oxidation of iron and manganese compounds
occurs during storage, filtration, and transport.
Relative Irradiance
A submersible T.S. submarine illuminance meter equipped with two photo-
cells and direct readout was used to measure relative light extinction.
Readings were generally made at 0.5-meter intervals.
Solar Radiation
A Weather-Measure Corporation Model RA01 solar radiation recorder was
used to determine incident solar radiation. The unit was mounted on a
hill top located next to the Whitehall laboratory.
Silicon
Dissolved silicon concentrations were determined on filtered nutrient
water samples using a colorimetric AutoAnalyzer technique. This method
is based on the formation of a silicomolybdate complex which is reduced
by an ascorbic acid solution to form moloybdenum blue. Oxalic acid was
used to prevent phosphate interference (Technicon Instrument Corp.,
1973d, APHA, 1971).
Specific Conductance
Electrical conductivity was measured on alkalinity samples prior to
titration using a YSI Model 31 conductivity bridge calibrated in ymho
units. All measurements were corrected to 25°C. Measurements were also
made in situ at 1-meter depth intervals at all lake stations using a
Martek Instrument Corporation submersible electrode.
Total Organic Carbon
Occasional water samples were measured for total organic carbon (TOG).
Samples were preserved by adding 0.5 m& concentrated sulfuric acid to
250 m£ of sample. Analysis was done with an Oceanography International
carbon analyzer. Samples were digested overnight in sealed ampules in
a solution of potassium persulfate. The resulting carbon dioxide pro-
duced was measured.
34
-------
Temperature
Water temperatures were measured using a standard mercury thermometer.
In situ measurements were also made using a Martek Instruments Corpora-
tion submersible thermister.
Transparency
A standard Secchi disc (20 cm diameter) was used to measure water trans-
parency. Readings were the average of the levels of disappearance and
reappearance of the disc recorded in meters from the surface.
BIOLOGICAL METHODS OF ANALYSIS
Chlorophyll a
Samples for chlorophyll a analysis were collected and stored in 2-liter
amber polybottles containing 5 m£ of magnesium carbonate suspension.
In the Whitehall laboratory 200 m£ of the stored sample was filtered
through a 0.45ji Millipore filter. The filters were folded and then frozen
in plastic centrifuge tubes. All storage was done in complete darkness.
The samples were transported to Ann Arbor and then analyzed for chlorophyll a
as outlined in Strickland and Parsons (1968). A Turner Model 110
Fluorometer was used for the analysis. The unit was periodically cali-
brated using standardized chlorophyll a samples and checked against spec-
trophotometric techniques.
Primary Productivity
Primary production was determined using an in situ C bicarbonate up-
take technique. Two clear and one opaque 250 m£ glass stoppered Pyrex
reagent bottles were filled with water from specified depths. Each bottle
was stored in the dark and then individually inoculated with two
microcuries of C1^ bicarbonate solution (Strickland and Parsons, 1968).
Transfer of the inoculum from the ampules to the bottles was done with
a syringe followed by rinsing. The bottles were then mounted on Plexi-
glas racks, lowered to their respective depths, and anchored to a sta-
tion located by a separately attached buoy. Following three to four
hours of incubation the bottles were retrieved and fixed with a formaldehyde
solution. The contents of the bottles were later filtered onto 0.45 y
Millipore filters and rinsed with distilled water. The filters and
associated suspended solids were then exposed to fuming hydrochloric
acid for ten minutes to remove inorganic carbonate particles which might
contain C1^ (Wetzel, 1965). The filters were subsequently placed in
20 m£ polyethylene liquid-scintillation vials and covered with a
dioxane-based water miscible solution. The radiocarbon was determined
35
-------
using a Unilux I liquid scintillation counter. The carbon uptake
rate was then computed considering the C14, pH, and alkalinity measure-
ments (Strickland and Parsons, 1968).
36
-------
SECTION VII
GENERAL LIMNOLOGIGAL OBSERVATIONS
INTRODUCTION
In any limnological study it is useful, at the outset, to provide a
characterization of the lakes under investigation and to compare them
to other, more intensively studied lakes. This allows both the researcher
and reader to place these systems in perspective against a reference
framework. In this case, the Muskegon Lakes will be compared with
southern Lake Michigan (to which they discharge), to Green Bay and
other areas on the Great Lakes, and among themselves. The maximum,
minimum, and average values for various physical, chemical, and biological
parameters measured in surface and bottom samples are presented in
Table 6. In this preliminary discussion no discrimination will be made
with respect to pre- and post-diversion data, the objective of this
section being a general categorization of the lakes.
PHYSICAL AND CHEMICAL PARAMETERS
pH and Alkalinity
The pH of water is an expression of the molar concentration of the
hydrogen ion (H+) in solution and controls such phenomena as solubility,
degree of dissociation, and acid-base equilibria. Changes in pH will
occur both spatially and temporally as a result of biologic processes
(C02 production or uptake and biodegradation) and mineral processes.
The State of Michigan water quality standard for recreational waters
with partial or total body contact is 6.5-8.5. The measured pH values
for White Lake ranged from 7.35 to 9.06; for Muskegon Lake from 7.15
to 9.09; and for Mona Lake from 6.77 to 9.48. This range of pH as pre-
sented in Table 6 is normal for aquatic systems and represents a slightly
alkaline system.
Average surface pH values were higher in Mona Lake than in White or
Muskegon Lakes. This phenomenon reflects the higher rates of primary
productivity in Mona Lake. Bottom water pH values were generally lower
than surface values, again to a greater extent in Mona Lake. The low
pH values of the bottom waters are a function of lower primary produc-
tivity and high rates of biochemical decomposition.
Alkalinity is a measure of the ability of water to neutralize acids
and is an indicator of buffer capacity or the ability to resist changes
in pH. A source of alkalinity is the weathering of limestone soils and
37
-------
Table 6. WATER QUALITY CHARACTERISTICS—AVERAGES OF ALL DATA*
co
Parameter (Units) Depth
PH
Alkalinity (meq/Jl)
Conductivity
(ymhos/cm2)
Chlorides (mg/£)
Dissolved Oxygen (mg/£)
Biochemical Oxygen
Demand (mg/&)
Chemical Oxygen
Demand (mg/&)
Ammonia (yg N/£)
Nitrate (yg N/£)
S
B
S
B
S
B
S
B
S
B
S
S
S
B
S
B
White Lake
Min. Avg. Max.
7.61
7.35
2.04
2.24
271
280
13.3
15.8
5.0
0
0.7
3
0
6
0
0
8.49
7.94
2.67
2.68
380
402
35.1
41.0
9.9
7.5
2.3
19
65
204
82
101
9.06
8.64
3.44
3.20
460
893
53.4
171.0
13.4
13.1
4.7
42
199
1300
430
359
Muskegon Lake
Min. Avg. Max.
7.90
7.15
2.10
1.95
260
250
9.7
1.3
5.8
0
1.1
8
4
4
0
0
8.46
7.88
2.74
2.65
329
322
20.1
18.5
9.6
7.3
1.8
24
43
147
89
105
9.09
8.76
3.89
3.70
427
421
27.7
28.7
14.4
14.9
3.4
47
180
1514
453
545
Mona Lake
Min. Avg.
7.65
6.66
1.79
1.73
331
318
18.8
21.0
5.8
0
1.2
7
8
10
0
0
8.92
8.60
2.26
2.36
456
461
36.9
37.0
10.7
7.8
2.4
28
161
775
365
386
Max.
9.48
8.97
2.96
3.30
566
670
49.1
86.0
18.6
17.9
3.0
39
731
9484
1189
1325
-------
Table 6.—continued
Parameter (Units)
Total Dissolved
Phosphorus (yg P/£)
Soluble Reactive
Phosphorus (yg P/£)
Total Phosphorus
(yg P/fc)
Silicon (mg/£)
Dissolved Iron (yg/£)
Chlorophyll a (yg/&)
Primary Productivity
(yg C/A/hr)
Secchi Disc (m)
Depth
S
B
S
B
S
B
S
B
S
B
S
1m
2m
-
White Lake
Min. Avg. Max.
4
4
0
1
8
16
0.09
0.25
0
0
0.1
0.1
0
1.0
14
29
5
17
35
47
1.75
2.21
46
48
9.7
24.8
12.5
1.8
43
155
15
156
83
275
4.67
4.54
149
178
69.1
179.7
89.3
3.8
Muskegon Lake
Min. Avg. Max.
4
4
0
0
17
17
0.05
0.17
0
0
1.0
1.0
0
0.9
18
21
6
9
49
56
1.43
1.59
47
49
13.8
28,5
14.9
1.5
74
120
29
99
316
271
4.16
4.10
196
401
57.4
109.6
174.6
3.3
Mona Lake
Min. Avg. Max.
9
7
1
2
29
26
0
0
0
0
.3
0.1
0
0.3
107
262
56
166
185
312
1.54
1.80
61
79
30.7
28.2
7.0
1.0
476
2180
237
1628
535
2411
4.60
4.60
275
1096
189.8
114.7
62.6
2.0
K
Data are averages of all data collected between 1972-1975.
S = 2m below surface
B = 1m above bottom
-------
rocks. Alkalinities generally ranged from 2-3 meq/£ for all three lakes.
These levels of alkalinity are similar to those average values reported
for southern Lake Michigan (2.22 meq/£) and higher than those observed
in the other Great Lakes (0.92-1.92 meq/£) (Auer et at., 1976). In
this range of alkalinities the buffer capacity is high and changes in
pH should be minimal.
Conductivity and Chlorides
Conductivity is a measure of the ability of water to conduct an electri-
cal current, and, as such, reflects the ionic strength of the solution.
Maximum and minimum values varied widely, but generally ranged from 270-
500 ymhos/cm2. The higher average conductivities observed for Mona Lake
(surface water average of 456 ymhos/cm2 as opposed to 380 and 329
ymhos/cm2 in White and Muskegon Lakes) reflect more concentrated and
productive conditions. These values are well above those reported for
southern Lake Michigan (260 ymhos/cm2, Auer et al.3 1976).
The chloride ion is a common constituent of natural waters; sources in-
clude runoff, groundwater, and wastewater discharge. Since chlorides
contribute to conductivity (and both are often associated with urban and
industrial contamination), it might be expected that trends in ranking
among lakes would be similar; this is not entirely the case since White
Lake receives chloride contamination from natural and industrial sources.
Chloride values in the Muskegon Lakes (38.0 mg/£ for White Lake, 19.3 mg/£
for Muskegon Lake, and 37.0 mg/5, for Mona Lake) are higher than average
southern Lake Michigan levels (7.2 mg/Jl, Auer et at., 1976).
Oxygen and Oxygen Demanding Substances
The maintenance of adequate levels of dissolved oxygen is important in
lakes because of the effect on fish and benthic macroinvertebrate popu-
lations. Dissolved oxygen concentrations in the Muskegon Lakes vary
widely, both with season and with depth. All three lakes exhibit hypo-
limnetic oxygen depletion in the summer months; Mona Lake to a greater
extent than the others. As would be expected, dissolved oxygen concen-
trations above the hypolimnion are near saturation. No severe winter
depletion was observed in any lake, although a reduction of 4-5 mg/£
was noted for the bottom water of Mona and White Lakes.
The depletion of oxygen in hypolimnetic waters is largely the result
of the aerobic decomposition of organic material (oxygen demanding
substances) within the water column and from the consumption of oxygen
by lake sediments and the oxidation of ammonia in the nitrification pro-
cess. Two general classes of substances contribute to this oxygen
demand: allochthonous and autochthonous materials. The former group
is composed largely of wastewater input plus organic material occurring
naturally in the basin. The latter group is composed of oxygen demanding
material generated within the lake, largely plankton biomass.
40
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A study by Sands (1974) reported that the five-day biochemical oxygen
demand (BOD^) and chemical oxygen demand (COD) were positvely correlated
with chlorophyll a levels (and thus phytoplankton) in the Muskegon Lakes.
This suggests that autochthonous oxygen demanding materials are of pri-
mary importance in the Muskegon Lakes. The average BOD5 magnitude
rankings were: Mona, 2.4 mg/£; White, 2.3 mg/£; and Muskegon, 1.8 mg/&.
For COD the average values were: Mona, 28 mg/£; White, 19 mg/£; and
Muskegon, 24 mg/£; this may reflect the input of industrial waste to
Muskegon Lake. The largely autochthonous nature of the oxygen demand-
ing substances alludes to the prospect of significant improvement in
dissolved oxygen levels if the quantity of phytoplankton is reduced by
the wastewater diversion.
Nitrogen
The nitrogen cycle in lakes is highly complex and interfaces importantly
with several facets of phytoplankton nutrition. Among the phenomena
involving the nitrogen cycle observed in lakes are: fixation, nitrifica-
tion, denitrification, ammonification, and uptake and assimilation of
nitrogen. The transformations of nitrogen are closely linked to dissolved
oxygen availability with nitrification and ammonification being aerobic
processes. Nitrogen fixation and assimilation may be aerobic or anaerobic
depending on the organisms involved.
Ammonia-nitrogen concentrations vary widely with depth and season in the
Muskegon Lakes, but generally result in very high average levels, espe-
cially in Mona Lake. On the other hand, it should be noted that surface
depletion of ammonia-nitrogen occurs in all three lakes during the summer
and that high concentrations develop in the hypolimnion. Concentrations
of ammonia in all White Lake waters varied from 0 to 1300 yg N/£, for
Muskegon Lake from 4 to 1514 yg N/£, and for Mona Lake from 8 to 9484
yg N/A.
Nitrate-nitrogen concentrations also reach extremely high levels in the
Muskegon Lakes, especially Mona Lake. Maximum nitrate concentrations for
the three lakes were 430 yg N/£ for White Lake, 545 yg N/£ for Muskegon
Lake, and 1325 yg N/£ for Mona Lake. The presence of nitrite is largely
a function of the nitrification process of which nitrite is an inter-
mediate; when a large increase in nitrate is observed a concommitant
increase in nitrite is usually noted. The nitrite/nitrate ratios vary
widely, but are generally less than 1:5.
Average levels of ammonia and nitrate are 33 and 173 yg N/£ for southern
Lake Michigan and 172 and 90 yg N/& for lower Green Bay (Auer et al.3
1976). Mona Lake levels are 2-5 times higher than this while Muskegon
and White Lake levels are generally similar. Surface values in the
Muskegon Lakes, where algal uptake is important, do not always reflect
the tremendous amounts of nitrogen present; bottom water values provide
a better indication. The magnitude of productivity of the Muskegon
41
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Lakes is reflected by the fact that the dissolved inorganic nitrogen
concentrations, often observed to approach or exceed 1 mg N/& in the
winter, are depleted near zero in the summer months, revealing a tre-
mendous potential production of phytoplankton. The surface water deple-
tion of dissolved inorganic nitrogen in White Lake and Muskegon Lake
encourage the dominance of the phytoplankton by nitrogen-fixing blue-
green algae such as Anobaena sp., and Aphanizomenon Flos-aquans
(USEPA, 1975a,c, Auer and Canale, 1976).
Phosphorus
Phosphorus, like nitrogen, is an important plant nutrient. The dynamics
of phosphorus in aquatic systems revolve largely around phytoplankton
uptake with subsequent decomposition and release and sediment-water
interchange. The former process is to a large extent seasonal and the
latter is closely tied to the oxygen status of the hypolimnion.
Three forms of phosphorus were measured in this study: total phosphorus,
total dissolved phosphorus, and soluble reactive phosphorus. Average
total phosphorus concentrations in Muskegon and White Lakes are 2-3 times
greater than those reported for southern Lake Michigan (14.6 Ug P/&) but
less than those observed for lower Green Bay (304 yg P/£). Mona Lake
average total phosphorus levels (248 yg P/&) are an order of magnitude
greater than those reported for southern Lake Michigan. The release of
large quantities of dissolved phosphorus to the bottom waters of all
three lakes from sediments and phytoplankton settling and decomposition
is evident from the data. The bottom water total dissolved phosphorus
maximum in Mona Lake (2411 yg P/&) was an order of magnitude greater
than that for either Muskegon Lake (271 yg P/Jl) or White Lake (275 yg P/&) ,
Additionally, the 2m average total dissolved phosphorus concentration
for Mona Lake exceeds that of the particulate fraction, the only lake
in which this happens. This observation may indicate that dissolved
phosphorus levels in Mona Lake are at times in excess of that which can
be utilized by the organisms. Two-meter total dissolved phosphorus is
depleted to near the analytical limit of detection at times in all lakes,
but never to zero.
Silicon
Silicon is an element required for growth by a number of aquatic organisms,
most notably the diatoms (Bacillariophyceae). Silicon, as silicon
dioxide, generally occurs abundantly in natural waters and is seldom
introduced in high levels as a result of man-generated pollution. Since
this element is required by diatoms, its availability serves to control
species succession in the phytoplankton. Silicon levels in the Muskegon
Lakes are, on the average, quite high (1.4-1.7 mg Si/5,). The silicon
42
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depletion observed in all three lakes reflects the large diatom popula-
tions observed at certain times of the year. Average dissolved silicon
values for the Muskegon Lakes are approximately 3 times those observed
for southern Lake Michigan (0.43 mg/£) and similar to those observed
for lower Green Bay (Auer et al., 1976).
Iron
Iron is also an element required, in small quantities, for algal growth.
Iron participates in a number of complex chemical reactions in aquatic
systems, often those associated with changes in oxygen concentrations
and redox potential. Large differences were noted between maximum and
minimum levels of iron in the Muskegon Lakes; these are the result of
precipitation and dissolution reactions. Under aerobic conditions,
ferric iron undergoes reactions involving phosphorus and hydroxyl ions
which result in the formation of ferric compounds existing in the solid
phase. Some of this material remains suspended as colloidal particles
in the water, while the remainder becomes part of the sediment. Addi-
tionally, iron is taken up by the phytoplankton and transferred to the
sediment upon the death and settling of the organisms. During strati-
fication, under anaerobic conditions, the ferric iron is reduced to
the more soluble, ferrous form. At this point the iron is released to
the water column and continues the cycle. Dissolved iron concentrations
are an order of magnitude higher in the Muskegon Lakes than in Lake
Michigan (6 yg/fc) (Auer et al., 1976).
BIOLOGICAL PARAMETERS
Chlorophyll a
Chlorophyll a concentrations, although variable with the physiological
state of the organism, provide a measure of the standing stock of phyto-
plankton present in a lake at any point in time. High levels of chlor-
ophyll a, in excess of 20 l-ig/£ especially when contributed by blue-green
algae (Cyanophyceae), may lead to reduction in water quality for many
uses. The average values for the Muskegon Lakes are 5-15 times those
observed for southern Lake Michigan and bracket that of lower Green Bay
(Auer et at., 1976), with Mona Lake averaging 2-3 times more pigment
than the other lakes at 30 yg/£. Concentrations were observed as high
as 69 yg/fc in White Lake, 57 yg/i, in Muskegon Lake, and 189 yg/£ in Mona
Lake.
Primary Productivity
Primary productivity,
the phytoplankton growth rate actually occurring at a specific depth
14
Primary productivity, as measured by C uptake, is an indication of
43
-------
and time. As such, this uptake is a function of specific conditions
of light, nutrient availability, and the standing stock of phytoplankton.
Again these values are 5-10 times greater than those measured for
southern Lake Michigan (Auer et al.s 1976). The distinct range ob-
served for chlorophyll a levels (ranking the lakes by greatest average
concentration: Mona, Muskegon, White) is not observed for primary
productivity. The reason for this is the presence of a self-shading
feedback mechanism which reduces the average primary productivity in
lakes with extremely large standing stocks of phytoplankton. Maximum
primary productivity measurements were 179 yg C/£/hr for White Lake,
174yg C/£/hr for Muskegon Lake, and 144 yg C/£/hr for Mona Lake.
Secchi Disc
The depth at which the Secchi disc is visible is a measure of water
transparency. It is influenced by changes in phytoplankton standing
crop, suspended solids, and other turbidity components which scatter,
reflect, and absorb light. The trend in Secchi disc among lakes is
identical to that observed for chlorophyll a. Average Secchi disc measure-
ments were 1.82 for White Lake, 1.54 for Muskegon Lake, and 1.01 for
Mona Lake. By way of comparison, southern Lake Michigan Secchi disc
values average 5.2 m (Auer et al.3 1976).
Phytoplankton, Zooplankton, and Benthos
Data on biologic taxonomy were available from studies by the USEPA
(1975a, 1975b, 1975c, 1975d). The phytoplankton of the Muskegon Lakes
is dominated by eutrophic forms of blue-green algae (Cyanophyceae)
and diatoms (Bacillariophyceae). Nitrogen-fixing blue-greens and pennate
diatoms are found largely in Muskegon and White Lakes while non-nitrogen-
fixing blue-greens (primarily Micpooystis aevuginosa) and centric diatoms
are found in Mona Lake. The zooplankton of all three lakes is dominated
by Bosmina longirostris., a eutrophic form. Numbers of zooplankton decrease
in abundance among Mona and Muskegon and Muskegon and White Lakes. The
dominant benthic macroinvertebrate in Mona Lake is the phantom midge,
Chaoborus. Oligochaetes dominate the bottom fauna of Muskegon and White
Lakes.
SUMMARY
In summary it can be said that the Muskegon Lakes are highly productive
lakes, with ample phytoplankton growth nutrients (N, P, Si) to permit
massive algal blooms. That such events occur is evidenced in surface
water nutrient depletion and extremely high levels of chlorophyll a and
primary productivity with concommitant reduction in Secchi disc depth
and hypolimnetic dissolved oxygen concentrations.
44
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SECTION VIII
WHITE LAKE
INTRODUCTION
The discussion of the effect of the wastewater diversion project on the
water quality of the Muskegon Lakes will be presented in two major
parts. The first of these will involve tributary-related considera-
tions, e.g., hydrology, contaminant concentrations and loading. The
evaluation of the response of water quality in White, Muskegon, and
Mona Lakes to the wastewater spray-irrigation project, requires infor-
mation on the past and present pollutant loads to the system. Con-
taminant loads from direct municipal and industrial discharges and
from tributary and non-point sources must be quantified separately.
The changes in pollutant loads to the lakes and the subsequent response
of lake water quality can, in this manner, be properly related to the
implementation of the diversion project. Information is also needed
regarding the hydrology of the system. Hydrological characteristics
dictate the rate at which water, nutrients, and algae are flushed from
the lakes.
The second part of the discussion involves lake-related considerations,
e.g., spatial, seasonal, and long-term trends in lake water quality.
This section of the report will deal with lake chemistry and biology,
primarily focusing on major algal growth nutrients (N, P, Si) and phyto-
plankton indicators, since these materials are those expected to change
as a result of the diversion program.
An evaluation of spatial and temporal trends in major phytoplankton
growth nutrients is fundamental to an understanding of variation in
plankton populations. In order to determine if changes in water quality
are a result of the diversion, their relation to the annual cycles in
the lake must be studied. Since the vertical distribution of chemical
and biological species are closely related to seasonal phenomena, both
spatial and seasonal characteristics will be discussed together. Long-
range trends and their relation to the wastewater diversion project will
be analyzed subsequently. A brief discussion of the biological char-
acteristics of each lake and summaries of specialty studies (where
applicable) are presented.
White Lake is the northernmost of the three study lakes. It is approx-
imately 7 kilometers long and 0.7 to 1.0 km wide with a southwest to
northeast orientation (see Figure 7). The lake receives flow from nine
tributaries, dominanted by the White River. The lake empties into Lake
Michigan through a narrow channel. The channel is dredged and is navi-
gable, qualifying White Lake as a shelter for ship refuge.
45
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2 73
The lake has a surface area of 10.4 km , a volume of 7.6 x 10 m , and
a mean depth of 7.3 meters. The lake is naturally divided into three
basins: east, central, and west. The central basin is the deepest
with a maximum depth of approximately 23 meters. The lake has extensive
shallow areas which support prolific macrophyte growth. Figure 4
describes lake morphology.
The region surrounding White Lake is principally residential. The lake
received discharges from three major industries prior to diversion.
(Hooker Chemical Company, Misco Division of Howmett Corporation, and the
Whitehall Leather Company). Two of these industries have not yet fully
diverted into the system. One municipal wastewater treatment plant
(Whitehall) discharged to White Lake prior to diversion.
TRIBUTARY-RELATED CONSIDERATIONS
2
Hydrology—The White Lake drainage basin contains 1,319 km of land
in Muskegon, Newaygo, and Oceana Counties. The White River drainage
area accounts for 94% (1,245 km ) of the total lake drainage basin (see
Table 7). The remaining area includes minor lake tributaries and direct
drainage to the lake. The White River contributes an important share of
the flow to White Lake. This is seen in hydrologic data collected by
the Michigan Water Resource Commission in 1967 (see Table 8) (MWRC,
1967). This publication reports that the White River accounts for
approximately 99% of the total flow to White Lake.
The White River begins in north central Newaygo County and flows south-
west to the mouth. Although technically direct drainage to White Lake
is considered part of the river basin, in this report, discussion of
the White River will only include the drainage up to its entry into
White Lake. The White River basin is primarily rural with approximately
40% of the land forested and 39% agricultural (MWRC, 1967). The flow in
the White River has been monitored by the USGS since 1958. The 17-year
average flow at this location is 11.4 m /sec. However, the annual average
flow varies significantly (see Figure 8). During the period of this
study the annual flow was observed to vary. During the first year (1972)
a low flow was recorded, a moderate flow was measured in 1973, and high
flows in 1974 and 1975. The average monthly flows measured during the
investigation are presented in Figure 9. These data reveal that the
seasonal effects of runoff exert a significant influence on the White
River flow.
The flow as measured at the USGS station does not represent the total flow
of the White River into White Lake. Between the USGS station and White
Lake the river receives additional direct drainage from 11 tributaries.
Flow at the river mouth was estimated by multiplying the flow at the
gauging station by a factor of 1.4. The factor was obtained by comparing
USGS measured flows to flows measured at the mouth during this study.
46
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Table 7. WHITE LAKE DRAINAGE BASIN AREAS
Description
Area
(km2)
Percentage
of Total
White River
Pierson Dam
Mill Pond Creek
Miscellaneous
Tributaries & Direct
Drainage
Lake Surface Area
Total
1245.1
27.0
21.4
15.4
10.4
1319.3
94.4%
-2.0%
1.6%
1.2%
0.8%
100.0%
47
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Table 8. WHITE LAKE TRIBUTARY FLOW DATA, JULY 11 AND 12, 1967
(MWRC, 1967)
Name
Unnamed Creek from City
Solid Waste Disposal Site
Unnamed Creek
Mill Pond Creek
Wildcat Creek
Birch Creek
Strawberry Creek
Pier son Drain
Coon Creek
White River
Discharge
(m^/sec)
0.018
0.0004
0.079
0.021
0.027
0.010
0.026
0.007
13.28
Percentage
of Total
0.2%
trace
0.6%
0.2%
0.2%
trace
0.2%
trace
98.6%
48
-------
16
14
.FLOW
mVsec
12
Il.4lm3/sec
17 Year Average
J L
J » »
=0.
1961 1962 1963 1964 1965 1966 1967 1968 1969 1970 1971 1972 1973 1974 1975
YEAR
Figure 8. White River average annual flow at Whitehall,
Michigan (USGS Station # 04122200).
3O
20
FLOW
m3/sec
10
nl 1 1 1 1 1 1 1 1 1 1 1 1 n 1 1 1 1 1 1 1 1 1 1 ..... 1 1 1 1 1 1 1
J 1972 J 1973 J
1 1 1 .....
YEAR
Figure 9. Mean monthly flow of the White River at Whitehall,
Michigan (USGS Station # 04122200).
49
-------
Direct municipal and industrial discharges do not significantly affect
the hydrologic characteristics of White Lake.
The significance of the river flow to White Lake can be estimated if
the ratio of lake volume to tributary flow, or mean hydraulic retention
time, is calculated. Dividing the total lake volume of 7.6 x 10' cubic
meters by the total average flow, the retention time in the lake is
calculated to be 55 days. On the average, the flow coming into White
Lake is capable of exchanging the total lake water volume seven times
each year. This calculation does not account for short-circuiting,
stratification, and stagnation in littoral zones, nor does it describe
the seasonal variation of river flow and retention time.
Concentration of Chemical Species in Tributaries — Various water quality
parameters were monitored in the White River and Mill Pond Creek. A
summary of these results is given in Table 9. The average concentrations
measured in the two tributaries were of the same order of magnitude
although certain White River parameters had higher concentrations. The
three-year average concentrations of chemical species for the White
River at the mouth were 17.6 mg Cl/£ chloride, 60 yg N/£ ammonia,
136 yg N/& nitrate, 46 yg P/& total phosphorus, 2.8 mg Si/5, dissolved
reactive silicon, and 223 ygA iron. The Mill Pond Creek concentrations
were half as high for chlorides, approximately equal for nitrate and
ammonia, one-third to one-half as high for phosphorus, approximately
the same for silicon and slightly lower for iron. Because Mill Pond Creek
has such a small flow relative to the White River and its concentrations
are generally lower than those in the White River, it is not considered
to have a significant influence on White Lake water quality. This is
assumed true for other lake tributaries as well. These streams have
drainage basins of similar character to that of Mill Pond Creek and
receive no direct wastewater discharges. This similarity in water
quality was verified by a Michigan Water Resources Commission (1967)
study. All future discussion of river water quality will be focused on
the White River.
Water quality in White Lake, particularly subsequent to the wastewater
diversion, is affected by the tributary water quality. The White River
upstream of the influence of the diversion and spray-irrigation project
at station 201 is rich in algal nutrients. Monitored total phosphorus
concentrations of approximately 46 yg P/£, dissolved inorganic nitrogen
concentrations of 244 yg N/&, and dissolved silicon concentrations
of 3.3 mg Si/5, are sufficient to support algal growth at nuisance levels.
Although only about one-half of the total phosphorus is in the soluble
reactive form, and considered immediately available for algal growth,
all of the phosphorus is potentially available through bacterial and
enzymatic action.
50
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Table 9.
AVERAGE CONCENTRATIONS OP SELECTED CHEMICAL SPECIES IN TRIBUTARIES TO WHITE LAKE, 1972-1975
Tributary
White River (at mouth)
(Station 227)
White River
(Station 201)
White River
(Station 202)
Mill Pond Creek.
(Station 226)
Year
1973
1974
1975
1973-1975
1972
1973
1974
1975
1972-1975
1972
1973
1974
1975
1972-1975
1973
1974
1975
1973-1975
Chloride
(og Cl/t)
19.1
17.2
16.7
17.fr
18.5
18.3
17.8
16.2
17.8
8.9
7.2
7.3
7.2
7.5
10.6
9.7
7.0
9.5
Anaemia
(US N/i)
45
52
87
60
86
37
32
37
43
56
23
31
31
33
45
57
38
49
Nitrate
(ug N/£)
118
142
147
136
260
108
133
171
155
335
167
182
217
211
107
183
177
154
Soluble
Reactive
Phosphorus
(ug f/i)
16
14
15
15
11
16
13
14
28
29
23
27
6
9
9
8
Total
Dissolved
Phosphorus
(ug P/O
29
25
27
27
16
22
25
25
23
21
31
41
36
33
16
14
16
15
Total
Phosphorus
(ug f/i)
51
42
45
46
26
46
37
46
40
28
49
51
49
46
25
24
28
25
Silicon
(ng Si/1)
2.9
2.9
2.7
2.8
4.1
3.1
3.3
3.0
3.3
3.9
3.2
3.2
3.1
3.3
2.6
2.7
2.9
2.7
Dissolved
Iron
(ug Fe/1)
104
87
88
92
113
95
68
91
58
76
68
68
58
64
48
59
Total
Iron
(ug Fe/t)
368
179
162
223
489
154
199
261
342
123
144
190
265
123
104
162
-------
Figures 10 to 19 show plots of the concentrations of various parameters
measured in the White River. Total phosphorus concentrations were low
(approximately 20 yg P/£) during periods of low flow and runoff (fall and
winter) when the river water originates principally from groundwater or
snow melt. Groundwater is generally low in phosphorus due to soil ad-
sorption. Beginning in the spring concentrations of phosphorus increase
to levels approaching 100 yg P/£. This elevation is a consequence of
runoff from forest and agricultural lands carrying nutrient rich soil
and other allochthonous materials into the river. Nitrate concentra-
tions were observed to be highest during the winter months at times
exceeding 500 yg N/£ and lowest during the summer (approximately 50 yg N/£).
Ammonia concentrations show less variation than phosphorus or nitrate
but appear to be lower in the spring. Concentrations averaged about
50 yg N/£. The nitrate increase in the winter is probably the consequence
of low uptake by plants and the influx of nitrate rich groundwaters.
Lower spring ammonia concentrations may reflect dilution by high spring
runoff. Nitrate and ammonia concentrations decrease simultaneously in
the spring.
Comparisons of the yearly average concentrations of chemical species at
the mouth of the White River (Station 227) before and after the waste-
water diversion reveal only a few perceptible changes. Iron concentrations
were noted to increase during 1975; and nitrate concentrations were ob-
served to increase subsequent to 1973. Other parameters such as phos-
phorus, silicon, and chloride concentrations were not observed to change
significantly. It is difficult to determine if the observed changes
in concentration were a consequence of the sewage diversion spray-irri-
gation project because of the lack of sufficient data. No observations
were made at the river mouth (Station 227) during 1972. Sample data
were available for 1972 from Station 202 located upstream of the former
Whitehall Wastewater Treatment Plant. Only the 1975 data reflect full
implementation of the spray-irrigation project. Attempting to draw con-
clusions regarding changes in nutrient concentrations resulting from the
diversion project at Station 227 can be misleading because short-term
alterations in upstream concentration may be important. Comparison of
upstream and downstream concentrations in the White River is therefore
important.
Stations 201 and 202 are located upstream and downstream, respectively,
of the spray-irrigation site and Stations 202 and 227 are located up-
stream and downstream, respectively, of the former Whitehall Wastewater
Treatment Plant discharge (see Figures 7 and 20). An evaluation of the
effects of the spray-irrigation drainage and non-point sources can be
made by comparing concentrations among these stations.
Significant changes in phosphorus concentrations were not observed spa-
tially or temporally during the period of study. This is true with
52
-------
600
400
Ul
Co
c
0)
en
o
200
972
White River
Statbn 201
° Ammonia
a Nitrate
1973
1974
1975
Figure 10. Dissolved inorganic nitrogen concentrations at Station 201 in White
River, 1972-1975.
-------
1000
800-
400-
cn
e
200-
White River
Station 202
o Ammonia
a Nitrate
1972
1973
1974
1975
Figure 11. Dissolved inorganic nitrogen concentrations at Station 202 in White River,
1972-1975.
-------
500
CT
.
LJ
CD
O
cr
Ln i__
Ui Li
250
WHITE RIVER
Station 227
a Nitrate
o Ammonia
nl I I I I I I I I I I I I I I I I I I I M I | I i |W
1972 I973
1974
1975
Figure 12. Dissolved inorganic nitrogen concentrations at Station 227 in White River
1973-1975.
-------
Ul
O'"
White River
Station 201
n Total Phosphorus
o Total Dissolved Phosphorus
A Soluble Reactive Phosphorus
' I ' I 1 I I I I I I I I I I I I I I I I I I i I—L__i_J—' ' i i ' I '
Figure 13. Phosphorus concentrations at Station 201 in White River, 1972-1975.
-------
White River
Station 202
a Total Phosphorus
Total Dissolved Phosphorus
A Soluble Reactive Phosphorus
0
1972
1973
1974
1975
Figure 14. Phosphorus concentrations at Station 202 in White River, 1972-1975.
-------
s/l
30
1972
1973
1974
1975
Figure 15. Phosphorus concentrations at Station 227 in White River, 1973-1975.
-------
White River
Station 201
0 Silicon
CO
Ui
vo
'(n
O
V)
en
Q
O1
I II I I 1 I I I I I I I
1972
1973
1974
1975
Figure 16. Silicon concentrations at Station 201 in White River,
1972-1975.
-------
in
01
()
T3
-------
20
en
cu
•a
.c
O
o
White River
Station 201
o Chloride
I i i i i i . i i i i i
' I ' i i — I I I — L_1_J — I I I — I
I — I— J — I I I — I— i— I
1972
1973
S974
1975
Figure 18. Chloride concentrations at Station 201 in White River,
1972-1975.
-------
40
NJ
30
CD
•
O
20
10
White River
Station 202
o Chloride
''—I—I—I—L
i i i i i i i i til—I—L_J L_J—I—I—1—1—I—L.
1972
1973
1974
1975
Figure 19. Chloride concentrations at Station 202 in White River,
1972-1975.
-------
respect to all forms of phosphorus measured. During the period of 1973
prior to diversion slightly higher phosphorus concentrations were ob-
served at times at the rivermouth as compared to the upstream stations.
Consistent trends were not observed, however, and statistical support
for this observation cannot be demonstrated due to limited data. In
general, it appears that upstream non-point sources are the main factor
determining phosphorus concentrations in the White River. No increase
in phosphorus levels in White River were observed to result from the
spray-irrigation drainage. Only limited effects on phosphorus concen-
trations can be attributed to the former Whitehall Wastewater Treatment
Plant discharge. Had more data been available from the river mouth (Station
227) prior to diversion (1972 and earlier), the latter effect may have
been more noticeable.
Spray drainage is discharged from the Whitehall spray-irrigation site
to the White River after ground infiltration. Concentration in wells
surrounding the area then characterize the spray drainage. Measure-
ments from these wells reveal concentrations similar to those from the
upstream White River (Appendix E). Average total phosphorus concentrations
were approximately 50 yg P/£; ammonia was 200 yg N/5, in 1974 and 50 yg N/A
in 1975; and nitrate-nitrite was approximately 60 to 70 yg N/£. As a con-
sequence, no significant concentration changes were observed to result
from the spray drainage in the White River.
Significant spatial and temporal variations in nitrate concentrations
were observed. Ammonia concentrations were also observed to fluctuate.
Analysis of these data is complicated by the processes of nitrification,
denitrification, ammonification, and algal uptake. Also complete mass
balance considerations cannot be conducted without data on total nitrogen.
It appears, however, that the nitrate concentrations are highest at the
upstream Station (201); no changes in nitrate were observed to result
from nutrient (fertilizer) runoff at the spray-irrigation site. The
high upstream nitrate is possibly groundwater derived. Ammonia concentra-
tions increased downstream. The largest increases in ammonia were observed
to occur between Stations 202 and 227. This occurrence is considered to
be an effect of non-point loadings, decomposition, and ammonification of
organics in the river. It appears that unidentified non-point sources
of inorganic nitrogen possess sufficient inherent variation to mask the
effects of known point sources.
Silicon concentrations were not observed to vary temporally but did appear
to decrease spatially between Stations 202 and 227. This might be a
consequence of dilution by lower basin tributaries. The influence of
White Lake on the integrity of lower White River waters must also be con-
sidered. Because of the dominant westerly winds, the lake at times has
a tendency to mix with White River waters and alter their normal char-
acter. This problem may exist not only for silicon but also for all
63
-------
concentration measured at the river mouth station (227). Hence, the
absence of any strong measurable effect from the wastewater treatment
plant discharge could have been partially a consequence of the close prox-
imity of Station 227 to the lake. (Logistics and geographical restric-
tions prevented the designation of a station further upstream, yet still
downstream of the former wastewater treatment plant.)
Chloride concentrations were not observed to change year to year, but
a large increase in concentration was observed spatially between Stations
201 and 202. This increase also was noted prior to the spraying period.
Because no known discharges of chloride exist in this portion of the
basin, the increase may be an effect of urban runoff or groundwater
infiltration. The Whitehall area is known to lie over brine deposits
and local chemical companies rely on these deposits for their operation.
Concentrations of iron were observed to vary between stations and among
years. Higher concentrations of iron were measured in 1973. No explana-
tion is proposed for this observation, except variation in unidentified
non-point contamination and the relative influence of groundwater high
in iron.
No significant alterations in White River chemistry could be observed
to result from the diversion spray-irrigation project because the spray
discharge has concentrations similar to those in the upper river.
Furthermore, occasional influences of White Lake water on tributary samples
at the lowermost White River Station (227), variability in upstream
non-point loads, and limited pre-diversion river mouth data prevent detailed
statistical analysis of the data. Calculations comparing non-point and
point nutrient loads are required to evaluate the effectiveness of the
system. This analysis will follow.
Nutrient Loads — Nutrient loads to White Lake originate from tributary,
industrial, and municipal sources. Of the nine tributaries discharging
to White Lake, the White River is the dominant hydrologic and nutrient
source. In past studies on White Lake tributaries, the White River was
estimated to contribute 98% of the total phosphorus loading and 96% of
the total nitrogen load (MWRC, 1967). The focus of this investigation
of tributary monitoring and load calculations was therefore on the White
River with minor emphasis on Mill Pond Creek, the next largest hydrologic
and nutrient source.
There are four significant municipal and industrial discharges within the
study area. The location of these and other discharges are portrayed in
Figure 20 and described in Appendix F. The locations of these discharges,
estimates of their loads, and information regarding the times of their
diversion to the spray-irrigation system are given in Table 10. The
Whitehall Wastewater Treatment Plant and Plant Number One of the Misco
Division of Howmett Corporation diverted their discharges on July 18, 1973;
the Whitehall Leather Company diverted its discharge beginning November 24,
1974.
64
-------
St227,fs'-2oa
o*. o™* J i Old Treatment Plant
or. c\j$f &
.Whitehall Waste Water
Land Treatment Site
Lake
Michigan
Lake
Michigan
WHITE LAKE
Montague
\\
rt if ied Concrete, Inc.
hitehall Lafher
owmet Corp./
bt.
A203
Strawberry
Creek
kilometers
A station location
Communities
7///.J in system
V0\y = out of system
XNNX but to enter
within 20 yr.
I I = out, no plan
Figure 20. Location and diversion status of point sources and municipalities
in the White Lake basin.
65
-------
Table 10. ESTIMATED MUNICIPAL AND INDUSTRIAL LOADS TO WHITE LAKE PRIOR TO DIVERSION IN KILOGRAMS PER DAY*
Source & Location
of Discharge Receiving Water
Hooker Chemical Com-
pany, Montague White Lake
Misco Division of
Howmett Corporation, White Lake
Whitehall
Whitehall Leather Com-
pany, Whitehall White Lake
Whitehall Wastewater
Treatment Plant, White River
Whitehall
Soluble
Chemical Biochemical Reactive Total
Oxygen Oxygen Suspended Phosphorus Phosphorus
Demand Demand Solids as P as P
949 — 1842 — 1.72
91.0 15.3 66.2 1.1 , 1.5
1478 845 388 0 1.64
13.5 128 13.8 14.1
Dissolved
Inorganic
Nitrogen
as N
4.0
4.4
87.6
29.0
Total
Nitrogen Date of
as N Diversion Source
7.9 MWRC 1973
5.3 7/18/73 MWRC 1969
1970
t
116 11/24/74 MWRC 1962,
1964, 1965,
1967
32.2 7/18/73 MWRC 1967
EPA 1975
&
*This table does not include minor business and industrial concerns in the area which have unmonitored small contributions. Also not included i" this
table are celery farm runoff, lagoon seepage, and septic tank drainage from Fruitland Township. Lakewood Club, Montague, Montague Township, and Whitehall
Township. Other industries are listed in Appendix F.
-------
Estimates of the nutrient loads to White Lake were obtained from operating
reports and Michigan Water Resource Commission industrial and municipal
waste surveys.
Tributary nutrient loads were calculated by multiplying concentrations
of nutrients in the river by the specific daily flow as calculated from
the USGS White River measurements (USGS 1971, 1972, 1973, 1974). Esti-
mates of White River flows at the various stations were derived by
multiplying the USGS measured flow by a factor to account for the increase
in total drainage area. Estimates of the flows in Mill Pond Creek were
obtained by multiplying the USGS White River gauged flow by a correlation
factor derived from current measurements. The focus of the loading calcu-
lations was on phosphorus and nitrogen because they are believed to be
the nutrients limiting algal growth in White Lake and are also the two
parameters most likely to be affected by the diversion spray-irrigation
project. A summary of the calculated loads from the White River and
Mill Pond Creek is presented in Table 11. Plots of White River loads
are given in Figures 21 through 24.
A comparison of nutrient loads from Mill Pond Creek with those of the
White River demonstrate the insignificance of the smaller tributary.
The White River load was over a thousand times greater than the Mill
Pond Creek load. Since the water quality in Mill Pond Creek is similar
to that of the other minor tributaries (MWRC, 1967), no further analysis
was conducted on minor tributary loads. In subsequent discussions on
lake loadings the minor tributaries were usually ignored.
Some patterns were observed in the seasonal variation of nutrient loads
from the White River. Phosphorus loads were closely correlated with
flow. During periods of high flow, concentrations increased due to
higher non-point runoff, and the associated nutrient load showed a
dramatic increase. Dissolved inorganic nitrogen loads were highest
during winter periods when nitrate concentrations were high. Chloride
and dissolved silicon loads showed a slight seasonal pattern with loads
increasing with increases in flow.
One objective in calculating the various nutrient loads to White Lake
was to separate the point and non-point sources, quantify their relative
influences, and then to evaluate the potential and actual effectiveness
of the wastewater diversion spray-irrigation system. Several additional
computations were useful for this evaluation. Table 12 is an annual
breakdown of the point versus non-point loads to White Lake. The point
discharges were calculated from Table 10 and adjusted to reflect their
period of actual operation. The non-point White River sources were more
difficult to estimate because municipal discharges prior to diversion
influenced the load determined at the river mouth. The non-point White
River load was therefore estimated using loads calculated from Station 202.
Corrections were made for differences in flow at the river station and
at the mouth and for spray-irrigation drainage which began in August 1974
67
-------
Table 11. ANNUAL AVERAGE WHITE LAKE TRIBUTARY LOADS IN KILOGRAMS PER DAY
00
Station
White River
Station 227
White River
Station 202
White River
Station 201
Year
1972*
1973
1974
1975
1972
1973
1974
1975
1972
1973
1974
1975
Total
Phosphorus
as P
45.5
59.9
88.4
80.1
31.4
55.8
70.5
71.9
30.6
52.1
80.7
75.7
Nitrate
+
Ammonia
as N
194
223
314
424
165
185
248
376
392
211
267
386
*Estimated from known point sources and estimated non-point loads.
-------
69
DISSOLVED SILICON LOAD (thousand kgms/day)
ro
bi
T~
ui
b
~r
ui
p
b
ID
l-t
tsi
O
o
O
pi
a
o
l-h
ct
sr
ps
H-
to
H1
VO
OJ
I
VO
Ui
CD
->l
CM
CD
31
CO
->J
en
-------
x
tn
6
-D 40
o
V)
o
£ 30
£ 20
E
3
5 10
0
WHITE RIVER
Station 227
i i i i i i i i i i i I i i i | | | | |
1972
1973
1974
1975
Figure 22. Chloride load of the White River, 1973-1975.
-------
li
DISSOLVED INORGANIC NITROGEN (N03+NH3) LOAD (kgms/day)
OP
l-l
NJ
>o to
U) CO
I O
•vj (0
Ui Cu
3
O
t-t
OQ
3
H-
O
3
O
TO
Q
3
O
O-
O
(B
(D
-------
300
to
WHITE RIVER
Station 227
O
•o
X
o
§
to
a:
o
O
Q.
I
200
100
0
JLJL
I I I I I I I I I I I I I I I I I l I I l I l I I i i i i i i I i i i i i i i i i
1972 1973 1974 1975
Figure 24. Total phosphorus load of the White River, 1973-1975.
-------
Table 12. ESTIMATED TOTAL YEARLY NUTRIENT LOADS TO WHITE LAKE,
1972-1975 IN THOUSAND KILOGRAMS PER YEAR
Total Phosphorus
Year
1972
1973
1974
1975
Municipal &
Industrial
6.92
(37.2%)
4.13
(16.6%)
0.63
(1.9%)
0.63
(2.1%)
Non-Point
White River
11.7
(62.8%)
20.8
(83.4%)
32.2
(98.1%)
29.05
(97.8%)
Spray-Site
Drainage Total
0 18.6
0 24.9
.002 32.8
(0)
•015 29.7
(0.1%)
Dissolved Inorganic Nitrogen
Municipal &
Industrial
45.6
(42.5%)
40.1
(36.7%)
30.7
(21.1%)
1.5
(0.9%)
Non-Point
White River
61.6
(57.5)
69.0
(73.3%)
114.6
(89.9)
154.67
(99%)
Spray-Site
Drainage
0
0
.002
(0)
.033
(.1%)
Total
107.2
109.1
145.3
156.2
-------
(see Appendix E). The above calculations do not consider certain nutrient
sources, such as septic tank drainage, minor tributary discharges, and
atmospheric precipitation. Estimation of the contribution by these
sources is difficult. Johnson (1975) measured atmospheric inputs of
phosphorus to Saginaw Bay to be an average of 20 kg P/km2/yr. Using this
measured rate the atmospheric inputs of phosphorus to White Lake are
calculated to be less than 1% of the total tributary load. A 1972-73
study by the USEPA on White Lake estimated the influence of minor sources
to be less than 2% (USEPA, 1975a); these sources were therefore not
included in further analysis.
A second calculation used in evaluating the changes in nutrient loads
to White Lake was normalization of river loads to average flow conditions.
Comparison of the loads between years can be confusing if there exist
significant differences in total river flow because non-point sources
are important. To normalize the loads for an average flow period, each
yearly load was multiplied by the ratio of the 17-year average flow to
the specific flow of each year. This method can normalize changes in
flow but cannot normalize the effect of the changing non-point loads
associated with the flow. The results of the normalized load calculations
are given in Table 13.
The potential effectiveness of the sewage diversion can be estimated
using the above calculations. If 100% of the 1972 point discharge loads
to White Lake were eliminated, the expected reduction in the total phos-
phorus load would be 23% and for the dissolved inorganic nitrogen load
it would be 31%. These estimates were obtained by averaging the non-
point White River loads displayed in Table 12 and comparing these with
the 1972 point discharges. If the normalized loading data are used, the
respective percentage reductions are calculated to be 24.5% for total
phosphorus and 27% for dissolved inorganic nitrogen. The nutrient load
reduction expected to occur in the White River itself would be 19% for
total phosphorus and 8% for dissolved inorganic nitrogen because all
the loads shown in Table 12 do not discharge to the river (see Table 10).
It should be noted that the reduction in phosphorus load is primarily
with respect to the soluble reactive fraction. Almost 98% of the
phosphorus discharged by the Whitehall Wastewater Treatment Plant was in
this form. In contrast (see Table 9) only about 25-35% of the river
phosphorus is in the soluble reactive form. The expected reduction
in the White River soluble reactive phosphorus load would be approximately
50%.
The above comparison of municipal and industrial loads to the White River
background loading is in good agreement with comparisons made from other
data sources (MWRC, 1976, USEPA, 1975d). The Michigan WRC data indicate
that total phosphorus point loads were approximately 20% of the total
lake load and dissolved inorganic nitrogen point loads were 25% of the
74
-------
Table 13. NORMALIZED YEARLY AVERAGE WHITE RIVER LOADS IN KILOGRAMS PER DAY
Ui
Station
White River Station 227
White River Station 202
White River Station 201
Year
1972
1973
1974
1975
1972
1973
1974
1975
1972
1973
1974
1975
Total
Phosphorus
51.7
55.7
61.0
60.8
36.7
51.9
48.6
59.2
35.8
48.4
55.7
57.5
Nitrate
+
Ammonia
226
207
217
322
193
172
171
286
458
196
184
293
-------
total. Estimates derived from USEPA data suggest a similar reduction
(20%) for total phosphorus. The USEPA data on total nitrogen indicated
that point sources represented less than 15% of the total nitrogen load.
Although the percentages between the various studies do not agree exactly
(because of differences in sampling period and frequency and estimates
of the point loads), the conclusions that can be drawn from each are
similar. Even if the diversion is 100% effective, the reduction in
nutrient loads to White Lake will not be dramatic. The exact percentage
is difficult to determine because of variability in flow and non-point
discharges.
To evaluate the actual effectiveness of the diversion spray-irrigation
project a comparison among yearly average nutrient loads is necessary.
An increase is seen in the total phosphorus and dissolved inorganic
nitrogen loads when the raw load data for the river and the total lake
examined (Tables 11 and 12). This increase is also seen, but to a lesser
extent, in the normalized load data. However, the increase in total
phosphorus and inorganic nitrogen loads observed is not a consequence of
the spray-irrigation system. An examination of the upstream calculated
loads at Stations 201 and 202 demonstrates that the observed increase
is a reflection of increases in upstream loads. These loads do not
originate within the study region which included the drainage from the
spray-irrigation site. The spray-irrigation began in 1974; no observable
effect on White River water quality was noted to result from the drain-
age. The observed increase in the upstream loadings for 1975 may have
been because of peculiarities of the data available for that sampling
year. The sampling program ended in October of 1975. The calculated
1975 loads were therefore biased towards periods of higher flow and
nutrient loads. In addition, the sampling frequency in the winter and
spring of 1975 was more thorough than in other years.
As was the case with inorganic nitrogen and total phosphorus, the yearly
average silicon and chloride loads did not show decreases subsequent to
implementation of the diversion project. Chloride yearly average loading
fluctuated between 20 and 30 thousand kilograms per day. Dissolved
silicon loads ranged between 3 and 5 thousand kilograms per day with some
evidence of increased upstream loading subsequent to diversion.
In all prior discussions average yearly loadings were evaluated. This
approach was used for several reasons including: 1) it provided the
most statistically useful data set; 2) it was consistent with year-round
lake sampling; 3) lake water quality problems (algal blooms) occurred
during spring, summer, and fall periods; and 4) the effects of nutrient
recycle and lake retention necessitated this approach. If loading data
were evaluated seasonally, the calculated percent reduction from the
sewage diversion project would be slightly different. The load data for
76
-------
total phosphorus for the months June, July, August, and September for
1972 to 1975 was averaged and compared to the diverted load. The average
calculated reduction for this period was again approximately 25-30%.
The percentage was much higher in 1972 and 1973 and lower in 1974 and 1975.
This was a consequence of the varying upstream nutrient concentrations
and flow. A similar calculation was made for the spring period. In
this case the potential reduction in total phosphorus load to result from
the diversion was approximately 20%.
In general, the measured nutrient loads to White Lake did not change as
a result of the wastewater diversion spray-irrigation project. The anti-
cipated reduction may have been masked by variability in upstream non-
point loads. The baseline used in this study was 1972, a low flow year;
other years of the study were high or moderate flow years. The flow
normalization technique may not have been adequate in adjusting these
loads to normalized conditions particularly with respect to total phos-
phorus. The anticipated dissolved inorganic nitrogen reduction of 8%
in the White River was small in comparison to fluctuations in the overall
load. Additional insight regarding the effectiveness of the diversion
project can be gained by comparing calculations of the yearly, flow-
weighted, average tributary concentration of nutrients, incorporating all
of the point and non-point loads. The result from this calculation can
give a rough indication of the potential effect of each yearly nutrient
load on lake concentrations. It is not an accurate prediction of concen-
trations and ignores many phenomena such as mixing in the lake, physical,
chemical and biological reactions, and various other source or sink
mechanisms. The results from these calculations are presented in Table 14.
These data further suggest that no large-scale improvement in water quality
(nutrients, productivity, etc.) would be expected in White Lake during
this investigation.
A more sophisticated analysis of the effect of nutrient loads on White
Lake can be achieved using a model developed by Vollenweider (1975).
This model was designed to relate nutrients (specifically total phos-
phorus loads) to trophic status. The details of the model are too complex
for presentation in this report, however, the important conclusions of
the model are depicted in Figure 25 and accompanying Table 15. The model
correlates phosphorus loading rate in grams P/m2/year to hydraulic load
(the lake mean depth divided by the lake hydraulic retention time). The
dangerous loading rate depicted on the graph represents the rate at
which the receiving water would become or remain eutrophic. The permissible
rate is a rate which would result in oligotrophic conditions. A load
between the two is considered a mesotrophic rate.
The calculated average phosphorus loading rate for White Lake prior to
diversion is approximately 2.4 grams P/m2/year. At this loading rate the
Vollenweider model suggests that eutrophic conditions would persist.
Even the anticipated 25% reduction in total phosphorus load expected as
a result of the diversion project (which has not yet been observed in
the data) will not effect the trophic status of the lake according to
77
-------
Table 14. FLOW WEIGHTED AVERAGE CONCENTRATIONS OF TOTAL PHOSPHORUS AND
DISSOLVED INORGANIC NITROGEN IN TRIBUTARIES TO WHITE LAKE
Year
1972
1973
1974
1975
Total Phosphorus
(yg P/A)
45
48
47
47
Dissolved Inorganic Nitrogen
(yg N/&)
259
209
210
246
78
-------
IOO
">» in
^* i \j
'E
^
o:
!?
1 |JO
-1
13
o
CL
cn
o
01 0.1
/"\ 01
U.UI
(
1 1 — | 1 1 III j 1 1 — 1 1 1 1 ll| 1 1 1 1 1 1 M| 1 lilt II
A Pred i version Load
n Observed Postdiversion Load
• Expected Postdiversion Load
E" A Lake A.Muskegon
: '67/701 a Lake
!
I EUTROPHIC M°kneQ . Ko(main) ^Dangerous
r vVhiteglea Gr wt J i ijeo/rff
Lake • • • wa Nv zii ,'* Permissable
Pf* t »Ze S •„-"*" ! *«"'
Erie 4- Jff ^'''
: * t'65 \\0f •LN<*^'"
: F ivje ^^ jv^' Rix
j .-'''' Vn ^'"''
"'m'dP. /A.& *** A
/-MiShl ^-';'239 * OLIGOTROPHIC
_ -^"' '67* ^'"' «227
j ^«' +Hur
" *'30
1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 I L I _Ll
D.I 1.0 10 100
_
.
"
-
]
-
_
_
-
—
-
w
~
—
M
IOC
Z/TW (meters/year)
Figure 25. Vollenweider Model relating phosphorus loading per unit of
surface to hydraulic load (mean depth divided by lake re-
tention time) for Muskegon Lakes (Vollenweider, 1975).
79
-------
Table 15. KEY TO SYMBOLS USED IN FIGURE 25
(AFTER VOLLENWEIDER, 1975)
Lakes Plotted: (o - oligotrophic; m - mestrophic; e - eutrophic)
1) Europe:
Ae - Aegerisee (o)
Tu - Turlersee (m)
Ha - Hallwilersee (e)
Bo - Bodensee (m)
Pf - Pfafflkersee (e)
Zu - Zurichsee (m-e)
Gr - Greifensee (e)
Ba - Baldeggersee (e)
Le - Lac Leman (m)
Ze - Zellersee (e)
LN - Lough Neagh (e)
F - Fures (e)
Va - Vattern (o)
Vn - Vanern (o-m)
Hj - Hjalmaren (e)
Ma - Malaren (e)
Wb - Wahnbachtalsperre (e)
Ri - Riverissperre (o)
2) North America:
Me - Lake Mendota (e)
Mn - Lake Monona (e)
Wa - Lake Washington (e)
Sup - Lake Superior (o)
Mich - Lake Michigan (o-m)
Hur - Lake Huron (o)
Erie - Lake Erie (e)
Ont - Lake Ontario (m)
Ta - Lake Tahoe (o)
Cl - Clear Lake (m)
227 - ELA Lake Nr. 227 (o; ex-
perimentally eutrophied)
239 - ELA Lake Nr. 239 (o)
Ko - Lake Kootenay (main basin,
m-e)
80
-------
the model. The model defined permissible loading rate is 0.73 grams
P/m^/year and the dangerous rate is defined as 1.43 grams P/m /year.
Further, it can be noted from data displayed in Figure 25 that the phos-
phorus loading rate for White Lake is equal to or greater than rates
of other lakes which have been classified as eutrophic.
In addition to calculations of nutrient loads to White Lake, estimates
of the rate at which nutrients are leaving the system can be made by
multiplying the measured White Lake channel concentration by the channel
flow which is assumed equal to the total tributary flow. A summary of
these flux calculations, including comparisons with nutrient loads to
White Lake is presented in Table 16. In the case of total phosphorus
a major percentage of this nutrient appears to remain in the lake although
the results could be effected by intrusion from Lake Michigan. If this
is true, then there must exist a significant pool of phosphorus at the
bottom of White Lake which could have the potential for future nutrient
release.
Summary — The White River has been demonstrated to be the major hydro-
logic and nutrient source to White Lake. Estimates of the nutrient
reduction expected to result from the diversion spray-irrigation project
suggest a reduction in total phosphorus of 23% and dissolved inorganic
nitrogen of approximately 31%. During the study period no reduction in
nutrient loads or in tributary nutrient concentrations was measured.
Reductions were not observed because of varying upstream non-point
loads, the magnitude of which was equal to or greater than the point
source reduction. The variation in upstream non-point loads is of sufficient
magnitude to entirely mask the observed reduction. Future improvements
in lake trophic status and water quality are only expected to be minor
with respect to phosphorus and nitrogen. Reductions in loads for other
water quality parameters such as heavy metals, organic matter, suspended
solids, fecal coliform, and toxic organics were not investigated in this
study.
No effect on water quality in the White River was observed as a result
of spray-irrigation drainage. Nutrient concentrations flowing from the
drain field were only slightly larger than those of the river. However,
since this point source is relatively minor hydrologically, no effect on
water quality was observed.
LAKE-RELATED CONSIDERATIONS
Spatial and Seasonal Distributions — The presence of any horizontal
variation in chemical characteristics in White Lake was examined by
comparing total inorganic nitrogen and total dissolved phosphorus concen-
trations at a depth of 2 meters at Stations 203 and 204 (see Figures 26
and 27). With the exception of three points in the first year of study
(1972), concentration patterns of total inorganic nitrogen and total
81
-------
Table 16. YEARLY AVERAGE FLUX OF NUTRIENTS LEAVING AND ENTERING
WHITE LAKE IN KILOGRAMS PER DAY
Year
Total
Phosphorus
as P
Nitrate
+
Ammonia
as N
Silicon
as Si
White Lake Channel
Station 205
1972
1973
1974
1975
13.1
16.1
30.7
19.9
144
264
380
401
1276
2154
3371
2206
Total Tributary and
Point Loads
1972
1973
1974
1975
50.9
68.2
89.8
81.6
293
298
397
424
3473
5330
4705
Percent Retained in
White Lake
1972
1973
1974
1975
75%
76%
66%
76%
51%
12%
5%
37%
53%
82
-------
oo
OJ
WHITE LAKE
Station 203
Station 204
2 Meter
1972
1973
1974
1975
Figure 26. Dissolved inorganic nitrogen concentrations at Stations 203 and 204 in White Lake,
1972-1975.
-------
oo
WHITE LAKE
o Station 203
Station 204
2 Meter
1972
1973
1974
1975
Figure 27- Total dissolved phosphorus concentrations at Stations 203 and 204 in White Lake,
1972-1975.
-------
dissolved phosphorus followed each other very closely at both White Lake
stations. Total dissolved phosphorus concentrations at Station 203 were
usually greater than those at Station 204 although in most instances
the difference amounted to less than 30%. The greatest spread occurred
during May of 1974, when the total dissolved phosphorus concentration at
Station 203 was almost two times that at Station 204. Less difference
in total inorganic nitrogen concentrations was noted than in total
dissolved phosphorus levels. Higher dissolved inorganic nutrient concen-
trations would be expected at Station 203, due to the influence of the
White River. Later, as these materials move through the lake, they are
transformed into organic nitrogen and phosphorus (via algal uptake),
resulting in lower concentrations at Station 204. Due to the horizontal
homogeneity of the system, no further discussion of horizontal distri-
bution is considered necessary.
Vertical distributions in physical, chemical, and biological character-
istics are closely tied to seasonal phenomena. The fluctuations in nitro-
gen, phosphorus, and silicon in the surface waters are largely a function
of uptake by the phytoplankton. The phytoplankton populations, in turn,
are governed by light, temperature, and the nutrient recharge associated
with spring and fall thermal circulation periods. Concentrations of
various chemical species in the bottom waters respond to changes in
dissolved oxygen and oxidation-reduction potential; these, in turn, being
influenced by the autochthonous supply of oxygen-demanding organic material
provided by the plankton and macrophyte communities.
Surface water (2m) concentrations of nitrate (NC>2 + NO^) as shown in
Figure 28 vary directly as a function of the phytoplankton populations.
Maximum surface values of nitrate (200-400 yg N/fc) are recorded in the
winter (December, January, February) and are rapidly depleted as a con-
sequence of the spring (March, April, May) diatom blooms to near zero
levels in the summer (July, August, September). After fall turnover,
surface nitrate concentrations then increase towards their winter peak.
Surface ammonia concentrations follow a pattern similar to that observed
for surface nitrate (see Figure 29). Peak surface concentrations
(200 yg N/£) occur in December and January, due to a combination of high
loads and low uptake, declining to a minimum in August and September.
The reduction of total inorganic nitrogen to near-zero levels during the
summer months (July, August, September) allows the nitrogen-fixing
forms of the Cyanophyceae (blue-green algae) to dominate the phytoplankton
community. Several of these algae are considered to be among the most
noxious components of the plankton. The depletion of ammonia and nitrate
during the spring and summer months indicates nitrogen limitation. Auer
and Canale (1976) and USEPA (1975b), using bioassay techniques, found
nitrogen to be limiting phytoplankton growth during this period. When
nitrogen is depleted to zero in the surface waters of the lake, nitrogen-
fixing forms of algae become dominant. Since these algae are able to
fix atmospheric nitrogen, nitrogen should not, in a practical sense, be
considered unavailable for growth during these periods. Phytoplankton
growth is most probably limited by the availability of light or phosphorus.
85
-------
500-
400-
Jl 300
UJ
*
cc
00 \_
200h
100-
WHITE LAKE
Station 204
ZMeter
Bottom
1972
1973
1974
1975
Figure 28. Nitrate concentrations in White Lake, 1972-1975.
-------
1200
1000
800
oo
WHITE LAKE
Station 204
o 2 Meter
a Bottom
1972
1973
1974
1975
Figure 29. Ammonia concentrations in White Lake, 1972-1975.
-------
At certain times of the year in the bottom waters of the lake, well below
the photic zone, concentrations of dissolved inorganic nitrogen are
dramatically different than those observed in the surface waters. Nitrate
(N0~ + NO^) levels in the bottom waters respond not to phytoplankton
densities, but rather to the processes carried on by nitrifying bacteria.
These organisms convert ammonia to nitrate with nitrite being an inter-
mediate, as follows:
NH_ N-Ltrosomonas group
N0~ Nitrobaeter group
. . . w "*J f)
J* 2.
NO'
Since inorganic nitrogen production through ammonification and deamina-
tion processes exceeds uptake in the bottom waters, this region of the
lake acts as a source of replenishment of dissolved inorganic nitrogen.
Bottom water concentrations of nitrate were observed to increase rapidly
between December and March (see Figure 28). During this period concen-
trations of ammonia and dissolved oxygen are adequate to permit nitrifica-
tion (see Figures 29 and 30). Bottom water nitrate concentrations are
reduced in the period March-June as the bottom waters are mixed with
nitrogen poor surface waters and the spring phytoplankton increase begins.
Further nitrification in the bottom waters is halted at this point by
the onset of hypolinmetic anoxia. It would be expected that nitrification
would be non-existent in the bottom waters during the summer months, due
to the lack of dissolved oxygen, regardless of high ammonia levels.
Intrusion of well-oxygenated (and high-nitrate) waters from Lake Michigan,
however, and the sporadic disruption of thermal stratification, provide
sufficient oxygen to produce short-lived peaks of nitrate in the bottom
waters during the summer months. With the occurrence of fall turnover,
bottom water nitrate is mixed with the nitrate-poor waters of the epil-
imnion and assimilated by the phytoplankton, thus completing the seasonal
cycle.
Evidence of intrusion was observed in the dissolved oxygen data for 1973
and 1974 and in the bottom water nitrate data for 1973-1975. This is
depicted by the dashed line in the dissolved oxygen plot (see Figure 30).
The dashed line represents the lowest concentration of dissolved oxygen
in the hypolimnion whereas the solid line represents the concentration
of dissolved oxygen 1 meter from the bottom. Higher dissolved oxygen at
the bottom suggests intrusion of Lake Michigan waters. This explanation
is also supported by the associated increase in bottom water nitrate
(see Figure 28). The presence of nitrate in the bottom waters can also
be related to the presence of hypolimnetic oxygen at depths greater
than 1 meter from the bottom (which are designated in this report as
bottom water samples). This prevents denitrification and will at times
permit nitrification.
88
-------
00
20
UJ
o
X
o
Q
LJ
en 10
Q
WHITE LAKE
Station 204
Bottom Water
1972
1973
1974
1975
Figure 30. Dissolved oxygen in the bottom waters of White Lake, 1972-1975.
-------
Ammonia concentrations in the bottom waters tend to provide a mirror image
of the nitrate concentrations (see Figures 28 and 29). Highest levels
of ammonia occur during the summer when decomposition processes are most
active and nitrification is essentially halted by anoxia. The peaks
in bottom water ammonia observed in October of 1974 and 1975 and in August
of 1973 are the result of this process. Bottom water ammonia concen-
trations are severely reduced during the periods of nitrification (i.e.,
December-March). The nitrate cycle (depletion, decomposition, nitrifi-
cation, and replenishment) in White Lake cause fluctuations of up to
250-400 Ug N/£ in a given season. It was observed that ammonia concen-
trations in the lake were higher than those of the White River, the major
tributary. This is due to the contribution to the nitrogen pool by
nitrogen-fixing organisms in the lake and decomposition of organic
nitrogen.
The phosphorus cycle in White Lake is, as was the case with nitrogen,
tied to the seasonal cycles of dissolved oxygen and the phytoplankton.
Additionally, dissolved inorganic phosphorus is closely related to the
iron cycle. Three phosphorus fractions were measured in the Muskegon
Lakes: soluble reactive phosphorus, total dissolved phosphorus, and
total phosphorus. While many components of total dissolved phosphorus
are ultimately utilizable by phytoplankton, only the soluble reactive
phosphorus is believed to participate in precipitation reactions with
iron.
Surface water soluble reactive phosphorus and total dissolved phosphorus
(see Figures 31 and 32) follow similar seasonal patterns, although the
latter is usually two to three times more abundant. This dominance
is expected since soluble reactive phosphorus is more readily assimilated
by phytoplankton. Variation in surface total dissolved and soluble
reactive phosphorus is much less than that observed for the dissolved
inorganic nitrogen species. Peak surface water levels of soluble reactive
phosphorus and total dissolved phosphorus occur in late fall and winter,
following the replenishment provided by turnover, the low winter produc-
tivity periods and spring loading. Surface levels of total dissolved
and soluble reactive phosphorus are reduced rapidly from March to June,
with soluble reactive phosphorus levels in the surface waters approaching
zero in September due to uptake by the phytoplankton. Following this
short period, increases in soluble reactive phosphorus were observed
due to turnover. Auer and Canale (1976) and the USEPA (1975a) using
bioassay techniques found phosphorus to be limiting phytoplankton growth
in the fall. Concentrations of phosphorus then continue the cycle
toward the winter maximum. Surface water total phosphorus levels reach
a maximum during August and September (see Figure 33) suggesting both
high levels of particulate phosphorus (organisms and detritus) and a
possible transfer of the high concentrations of hypolimnetic phosphorus
to the surface waters. Hypolimnetic peaks in total phosphorus are a con-
sequence of sediment nutrient release. Summer peaks in surface water
total phosphorus concentrations also appear to be largely a function of
90
-------
vo
70
£60
w 50
o:
o
a.
g40
x
a.
LJ
> 30
o
LoJ
or
LJ
_l
CO
_J
O
20
10
0
WHITE LAKE
Station 204
0 2 Meter
a Bottom
0(I53.5)
~th~(78.1)
1972
1973
1974
1975
Figure 31. Soluble reactive phosphorus concentrations in White Lake,
1972-1975.
-------
VD
N3
CP
77)
S 50
o
I
a.
CO
g 40
a.
Q
LJ
> 30
O
CO
Q
I
20
10
(95)
(120)
WHITE LAKE
Station 204
o2Meter
a Bottom
(88)
1972
1973
1974
1975
Figure 32. Total dissolved phosphorus concentrations in White Lake, 1972-1975.
-------
u>
260-
WHITE LAKE
Station 204
2 Meter
Bottom
1972
1973
1974
1975
Figure 33. Total phosphorus concentrations in White Lake, 1972-1975.
-------
of sediment release with a lesser dependence on loads. The White River
peak total phosphorus concentration and load were observed in the spring
and did not coincide with lake maximum concentrations. Further, the
observed increases in summer concentrations were too rapid to be pri-
marily attributed to loading.
Bottom water phosphorus concentration patterns are essentially identical
to surface values except during the months July through September when
extremely high concentrations are observed. The period when departure
annually begins varies slightly but generally corresponds to the time
of hypolimnetic anoxia. During stratified periods, phosphorus released
to the bottom waters from decomposition and sediment exchange accumu-
lates to extremely high levels. This increase is accentuated due to
the limited exchange between strata and thus algal uptake. The fact
that 70 to 90% of this phosphorus is present as soluble reactive phos-
phorus suggests the iron precipitation and dissolution phenomenon as
a mechanism controlling transport.
Iron-phosphorus interactions are, at this time, imperfectly understood
but may be generally explained as follows. During periods when the lake
waters are oxygenated, iron is in the ferric (III) oxidation state.
In this form iron is only sparingly soluble and reacts to form carbon-
ate, hydroxide, or possibly phosphorus precipitates. If the compounds
are formed, the phosphate ions may be adsorbed onto the surface of these
materials. The result is the transfer of both iron and phosphorus from
the soluble to the particulate form. Phosphorus released through the
decomposition of organic matter in the sediment can be scavenged and
trapped by oxidized iron in the sediment.
During the summer, when anoxic conditions prevail in the hypolimnion,
iron is reduced to the more soluble ferrous (II) form. The compounds
formed earlier are dissolved resulting in dramatic increases in the
dissolved iron and dissolved phosphorus concentrations. Such occurrences
were observed regularly during the summer in White Lake (see Figure 34).
At the end of the summer, these chemical species are mixed through the
water column (during fall turnover) and a portion of the soluble phos-
phorus is assimilated by the plankton. Some of the phosphorus is flushed
from the system while the remainder reacts and is returned to the sedi-
ments.
Silicon is important because it is a major nutrient required for growth
by certain phytoplankton, particularly the diatoms (Bacillariophyceae).
These organisms are primarily of importance in White Lake during the
spring and the fall. The silicon cycle in White Lake consists largely
of a period of algal depletion in late winter and spring (February to
June) with surface replenishment occurring in late fall and winter
(November-February) (see Figure 35). Late summer surface concentrations
of silicon are low and variable (0.5 - 1.0 mg Si/ #•) indicating that
94
-------
vo
Ui
WHITE LAKE
Station 204
°2 Meter
a Bottom
I I I l l i i I i i i i i i i i{ i I I
1973
1974
1975
Figure 34. Dissolved iron concentrations in White Lake, 1972-1975.
-------
6.0
3 5.0
(7>
o>
I 4.0
o
o
cr>
Q
LJ
o 2.0
(T)
cn
1.0-
0
WHITE LAKE
2 Meter Average
I I I I I i I I I I I
1972
1973
1974
1975
Figure 35. Dissolved silicon concentrations in White Lake, 1972-1975.
-------
diatoms are an important component of the phytoplankton during this
period. No severe depletion indicating a fall diatom peak was observed;
the spring bloom on the other hand was significant. The failure of
the phytoplankton populations to lower the levels of silicon closer
to limiting values during the spring diatom bloom is unusual. This
may be due to other types of growth limitation (e.g., nitrogen) or to
the fact that rather high concentrations of silicon (4 - 4.5 mg Si/£)
are present during the winter months. Summer silicon concentrations are
reduced below 0.5 mg/£, but these levels are not believed to be growth
limiting.
Chlorophyll a and primary productivity have been discussed in relation
to nutrient cycles. The maximum values for chlorophyll a and primary
productivity occurred simultaneously in the summer (see Figures 36 and
37). This is expected since the latter is in part a function of the
former. The data indicate that peak phytoplankton populations for 1973
and 1974 occur during mid-July. The peak could not be determined with
certainty for 1975 since there was no cruise during July; however, it
appears that the highest chlorophyll levels may have occurred in September.
The peak phytoplankton population is composed to a large extent to blue-
green algae, a significant fraction of which are nitrogen-fixing forms.
The abundance of nitrogen-fixing forms is related to the severe deple-
tion of inorganic nitrogen in the surface waters. Michigan Department
of Natural Resources (personal communication, 1976) reported that
algicide was applied to White Lake in June of 1974. This action was
not observed to have an effect on average chlorophyll levels.
An analysis of nutrient ratios can provide information regarding stoi-
chiometric nutrient limitation of the phytoplankton in the lake. Stoi-
chiometric nutrient limitation must be differentiated from actual growth
limitation. If a nutrient is determined to be stoichiometrically limit-
ing, this means that this will be the first nutrient which will become
totally depleted if growth is unrestricted. However, it is possible
for total depletion to fail to occur due to restraints imposed by time
(seasonality or washout), light, temperature, algicides, etc. Only
when the nutrient becomes depleted to a level below which phytoplankton
uptake cannot occur will actual growth limiting conditions exist.
The^average dissolved inorganic nitrogen to total dissolved phosphorus
ratios (N/P ratio) can be calcualted for various circumstances. The
winter N/P ratio in the surface waters varied from 17 to 32:1 between
1974 and 1975. For bottom waters the ratios were 37:1 (1974) and 25:1
(1975). Published estimates (Allen and Kramer, 1972) report that a
typical non-limited ratio would be 10:1 to 13:1 by weight but occassionally
as low as 3:1. Ratios larger than this indicate phosphorus limitation,
lesser ratios indicate nitrogen limitation. By these calculations, White '
Lake would become phosphorus limited in the winter. The winter period
was chosen as an example because of the characteristic low biological
activity. In this circumstance, sources of available nutrients remain
97
-------
00
60
o>
50
ai 40
o
a:
o 30
LJ
o
<
or
20
10
0
WHITE LAKE
Stations 203,204
2 Meter Average
1972
1973
1974
i i i i i I i I l
1975
Figure 36. Chlorophyll a concentrations in White Lake, 1972-1975.
-------
120
^100
o
J^80
>-
H
>
H 60
o
13
O
£ 40
a:
E 20
1972
WHITE LAKE
A 1 Meter Average
°2 Meter Average
1973
1974
1975
Figure 37. Primary productivity rates in White Lake9 1972-1975.
-------
in their original form and analysis of the system is not complicated by
uptake and conversion.
A more germane ratio would be that of summer surface N/P ratios. This
ratio is difficult to calculate, however, since summer dissolved inor-
ganic nitrogen levels approach the limit of detection because of algal
uptake. In this case then, with dissolved inorganic nitrogen depleted,
nitrogen would be found to be stoichiometrically limiting and growth
limitation would occur if nitrogen-fixing algae were not present.
Another approach to nutrient ratio analysis is to develop the ratio of
winter dissolved inorganic nitrogen in the bottom waters to summer total
dissolved phosphorus in the bottom waters. This ratio describes the chem-
ical conditions that might develop if there was no phytoplankton uptake
and thus establishes a baseline nutrient status. Each of the two periods
represents the maxima for the respective nutrient. For White Lake this
ratio is 10:1 in 1974 and 7:1 in 1975. These ratios marginally indicate
a relatively well-balanced nutrient supply.
A fourth approach to evaluating nutrient limitation through nutrient ratio
analysis is to examine the ratios from the system loads. These average
yearly calculations are 5.7:1, 6.28:1, and 8.6:1 for 1973, 1974, and
1975 respectively. These data suggest a well-balanced nutrient load or
a possible tendency towards stoichiometric nitrogen limitation. The
latter interpretation is supported by bioassay studies by Auer and
Canale (1976) and the USEPA (1975b). A calculation of nutrient loading
ratios for the period June through September (which excludes the periods
of high dissolved inorganic nitrogen loading) show the ratios to be sig-
nificantly less, on the order of 3:1. This further supports the hypo-
thesis of summer stoichiometric nitrogen limitation.
The vertical distributions and seasonal variations observed for physical,
chemical, and biological parameters in White Lake are consistent with
what would be expected for a shallow, eutrophic lake in the temperate
zone. One of the most impressive phenomenon observed for this, and the
other Muskegon Lakes, is the tremendous seasonal fluctuations of nutrients
in the surface and bottom waters. Variations in the magnitude of this
flux should provide information regarding the effects of the diversion
program on the lake.
Long-Term Changes— This portion of the report deals with observations
of long-term changes in physical, chemical, and biological parameters.
It was anticipated by Chaiken et al. (1973) and Bauer Engineering (1971)
that the diversion of wastewater from the Muskegon Lakes, followed by
an on-land treatment and disposal system would result in an improvement
in lake conditions (e.g., dissolved oxygen, nitrogen and phosphorus
levels, phytoplankton densities). The objectives of this section are
first to define trends in water quality and second to relate them, if
possible, to the wastewater diversion.
100
-------
The effects which could result from the diversion of wastewater would
be the following: reduction of nitrogen and phosphorus concentrations
resulting in lower phytoplankton populations and, ultimately, shorter
periods of hypolimnetic anoxia. A reduction in the duration of hypo-
limnetic anoxia has benefits both with regard to direct effects on
the biota and an influence on the flux of phosphorus from the sediments.
To evaluate such changes, average annual values for various chemical
and biological parameters at the surface and bottom waters were calcu-
lated (see Table 17). Annual averages were used as a principal tool
for two basic reasons: 1) the annual average provided the most statis-
tically valid data base and is not influenced by changes in yearly sea-
sonal dynamics; and 2) water quality problems, e.g., algal blooms, occur
in all ice-free seasons. Focus on one particular period would ignore
others.
There were no observable consistent trends in the average surface or
bottom water concentrations of soluble reactive, total dissolved, or
total phosphorus in White Lake over the period 1972-1975 (see Table 17).
Similarly, summer maxima of soluble reactive and total dissolved phos-
phorus in the bottom waters appear to be generally unchanged, although
1972 data are incomplete. The maximum summer values (both surface and
bottom) for total phosphorus -may have declined slightly over the three-
year period. The surface and bottom water maxima are respectively for
1972, 49 and 127 Ug P/A; for 1973, 82 and 275 yg P/fc; for 1974, 75 and
136 yg 7/1; and for 1975, 60 and 190 yg P/£. This change is a reflection
of the particulate fraction since the dissolved fraction remains rela-
tively unchanged. It can be said that any changes which may have occurred
in phosphorus concentrations were, in relative magnitude, insufficient
to dramatically affect the phytoplankton populations for the following
reasons. The minimum summer surface total dissolved phosphorus concen-
tration in 1975 was no lower than in previous years. Additionally,
average total dissolved phosphorus concentrations in the surface and
bottom waters remain unchanged from pre-diversion levels and are sufficient
to support 10-15 yg/£ of chlorophyll a (assuming 1 ug Chi a/yg P).
More fluctuation was observed in average concentrations of dissolved
inorganic nitrogen than for phosphorus. The most distinct trends were
in bottom water concentrations of ammonia which decreased markedly from
373 yg N/£ in 1972 to 137 yg N/£ in 1975; nitrate concentrations in
the bottom water varied, but with no discernable trend. Surface water
concentrations of nitrate increased markedly over this period also from
56 yg N/fc in 1972 to 104 yg N/A in 1975 while ammonia levels decreased
from 69 yg N/£ to 37 yg N/£ during the same period. These changes may
indicate an increase in oxidative conditions in the lake. Surface water
levels of dissolved inorganic nitrogen continue to be depleted to near
zero in the summer.
101
-------
Table 17. AVERAGE ANNUAL VALUES FOR SELECTED WATER QUALITY
PARAMETERS IN WHITE LAKE, 1972-1975
o
IS3
Year
Ammonia
(yg N/A)
Nitrate
(yg N/A)
Dissolved
Inorganic
Nitrogen
(yg N/n)
Total
Dissolved
Phosphorus
(yg P/A)
Total
Phosphorus
(yg P/i)
Soluble
Reactive
Phosphorus
(yg P/A)
Chlorophyll a
(yg/*)
Secchi
Disc
(m)
Surface
1972
1973
1974
1975
1972
1973
1974
1975
69
69
81
37
373
195
192
137
56
76
83
104
110
92
116
84
125
145
164
141
483
287
308
221
12
14
15
13
Bottom
34
31
25
30
30
39
31
40
51
53
39
52
9
5
6
4
6
21
15
17
12.4
11.4
8.6
8.6
1.83
1.92
1.72
1.79
-------
The occurrence of bottom water anoxia is an important aspect of the
depressed water quality in White Lake. Although no significant or con-
sistent reduction in the period of bottom water anoxia was observed in
White Lake, an overall oxygen budget on the lake would likely reveal
improved oxygen conditions. This is consistent with the ammonia and
nitrate trends. The rate of bottom water deoxygenation shows a poten-
tially decreasing trend during the study period. Thorough analyses of
the oxygen resources of White Lake would require detailed studies on
biochemical oxygen demand (BOD) and sediment oxygen demand. These were
beyond the scope of this study. An improvement of oxygen conditions
in White Lake might be a significant positive effect of the diversion
of wastewater.
As mentioned earlier, the peak summer phytoplankton population could
not be determined with certainty in 1975 due to sampling frequency.
Consistent trends in phytoplankton density and activity were not observed
in either the Secchi disc or primary productivity data. Although nutrient
concentrations were relatively unaltered, improvements in average 2m
chlorophyll a measurements were noted between 1972 and 1975 (12.4 to
8.6 yg/£). There was no difference between 1974 and 1975. It is believed
that nutrient concentrations have not been reduced sufficiently to be
responsible for changes in phytoplankton densities.
Dillon and Rigler (1974, 1975) have developed relationships between
spring total phosphorus at turnover and summer average chlorophyll a
and chlorophyll a and Secchi disc transparency. Illustrations of these
relationships are presented in Figures 38 and 39. According to these
data, the average summer chlorophyll a levels in White Lake would need
to be reduced by approximately 50 to 80% from the 1972 levels to gain a
1-meter increase in Secchi disc transparency. Furthermore, according
to these calculations, an additional 30 to 50% reduction in total phos-
phorus levels would be necessary to achieve the required chlorophyll a
reduction.
Summary — The potential impact of the wastewater diversion on White
Lake is largely a function of the percentage reduction in nitrogen
and phosphorus loads which would be expected. The total phosphorus
input to White Lake should decrease by 23% while the dissolved inorganic
nitrogen reduction should be 31% as a result of the diversion project.
The actual average nutrient and water quality conditions for White
Lake in 1972 and 1975 are presented in Figure 40 along with data from
Lakes Michigan and Erie for comparison. Although nutrient concentrations
in White Lake have not changed significantly, reductions in chlorophyll a
were noted. Secchi disc depths remained unchanged. It would not be
expected that the small alterations in the loads to the lake would have
a dramatic effect on the trophic status, although the rate of hypolimnetic
oxygen depletion may be decreasing.
103
-------
° Dillon and Rigler
White Lake, 2 meter
summer overage
10 20
CHLOROPHYLL a
Figure 38. Correlation between chlorophyll a and Secchi disc
(after Dillon and Rigler, 1975).
104
-------
1000
looL
o:
3
X
O
o:
UJ
10
1.0
•
O.I
a
1972^1973
a Dillon and Rigler
A White Lake
.
10 100
TOTAL PHOSPHORUS (/ig
1000
Figure 39.
Correlation between phosphorus and summer chlorophyll 0.
(after Dillon and Rigler, 1974).
105
-------
100
80
60
40
20
0
- .-
50
40
\
Wh
. Wh "975
1972 rn
-n
VL
30
20
SLM 10
nGTB
. . n
~ Wh
1972
~n
TOTAL PHOSPHORUS {/ig P/Jt) TOTAL
250
200
150
100
50
0
r I5f Wh
WLE
Wh
1975
" Wh
1972
VMM
^™ *
o... 10-
SLM
"1 GTB
5-
.
0 -
1972
I50r W^E
WLE I0°
Wh
1975
n
•M
50
SLM
II
176
Wh
-1972
Wh
1975
- n
SLM
nGTB
n
DISSOLVED PHOSPHORUS " AMMONIA Uig N/Z)
(fj.g P/J.)
I2p
Wh WLE a
1975 T
w
4
SLM
fin
GTB
Ql M
"wh wh
.'972 1975 WLE
n n n
«•*»..•»'
NITRATE (fig N/^} CHLOROPHYLL a (fj.q/1) SECCHI DISC (m)
LEGEND: Wh 1972 » White Loke 1972 , Wh 1975 » White Lake 1975, WLE = Western Lake Erie
SLM = Southern Loke Michigan , GTB "Grand Traverse Bay
WHITE LAKE
Figure 40. Pre- and post-diversion status of selected two-meter, yearly average water quality
parameters in.White Lake.
-------
SPECIALTY STUDIES
Algal Growth Nutrient Bioassays — Phytoplankton nutrient chemistry has
been the subject of intense research efforts by a large segment of the
scientific community. Several nutrients have been found to be of particular
importance in limiting phytoplankton growth, among these: nitrogen
(Thomas, 1970a, 1970b), phosphorus (Edmondson, 1972), carbon (Kerr &t al.,
1970), iron (Schelske, 1962), silicon (Schelske and Stoermer, 1971),
colbalt and molybdenum (Goldman, 1972), and manganese (Shapiro and Glass,
1975). It seems logical then to suggest that if the chemistry of certain
of these nutrients is understood, and the state of nutrient limitation
in a particular lake is known, manipulation of nutrient concentrations
should result in control of the phytoplankton population. This is,
of course, the case as has been demonstrated in a number of instances,
the most notable being that of Lake Washington (Edmondson, 1972).
Preliminary to the manipulation of nutrient concentrations, a study of
nutrient limitation in the lake phytoplankton population is necessary.
The algal growth nutrient bioassay provides a method for such a determina-
tion. Algal bioassays are conducted for the purpose of determining the
nutrient status of algal populations. Generally, it is wished to deter-
mine which nutrient, if any, limits the growth of that population. In
most bioassays, a series of nutrient solutions are added to separate
aliquots of lake water and the resultant growth is measured. The element,
whose addition stimulates growth to the greatest extent, is described
as the limiting nutrient. The following is a summary of nutrient
bioassay studies conducted on White Lake. A full discussion of these
results is given in Appendix A.
Water samples were collected from White Lake (Station 203) at intervals
chosen to represent seasonal variations (November 2, 1973; April 27, 1974;
July 18, 1974; and October 25, 1974). The samples were filtered to reduce
the numbers of predatory organisms (zooplankton). The lake water, with
its natural assemblage of phytoplankton, was placed in each of six 14-
liter pyrex carboys. Each carboy, with the exception of the control,
received a nutrient addition: ammonia, nitrate, ammonia plus nitrate,
phosphorus, or a trace metal mixture. The carboys were outfitted with
submerged air diffusers and magnetic stirrers. Each reactor was placed
in a constant temperature bath equipped with a fluorescent light bank.
The lighting was provided in a diurnal cycle. Samples were taken daily
for chlorophyll a, pH, temperature, and chemistry. Samples of water in
the reaction vessels were taken, typically every third day, and analyzed
for cell enumeration and identification. A more detailed discussion of
the experimental methods is contained in Appendix A.
The addition of orthophosphate phosphorus to White Lake water stimulated
algal growth markedly, particularly during the fall (see Figure 41). The
addition of nitrate nitrogen to White Lake water resulted in increased
algal growth (Fragilaria, Cyclotella, Asterionella) in the spring which
had a longer and more evenly distributed nature than did additions of
phosphorus (see Figure 42). While the magnitude of growth was not as
high with nitrogen as with phosphorus additions, neither were the crashes
as severe. Trace metals appeared to be associated with the enhancement
107
-------
40
35
30
«v
o»
o Control
o Nitrote-N
• Ammonia -N
* Nitrate+Ammonia-N
• Phosphorus
* Trace Metals
o
oo
0 5 10 15 20 25
TIME (DAYS)
Figure 41. Chlorophyll a. concentrations - 2 November 1973 bioassay.
-------
60T
CHLOROPHYLL a
H-
00
c
>-(
ro
4^
N>
O
O
"O
3"
o
o
§
rt
rt
H-
O
3
w
-a
i
H-
O
o
Ci
CO
en
to
-------
of the metabolism of available nitrogen. The addition of trace metals
mixture also increased the algal uptake of nitrogen over the period of
the bioassay. The addition of phosphorus usually resulted in rapid popu-
lation peaks of 'Fragitaria and Melosi-ra. The species of these genera
observed to bloom are considered opportunists and would not be expected
to dominate following nutrient reduction. Nitrogen limitation was most
important during the spring and summer. The dominant phytoplankton in
the summer in White Lake are nitrogen-fixing forms and therefore, reduc-
tions in phosphorus will be required before these species can be controlled.
Ammonia nitrogen was, in all cases, found to be inferior to nitrate nitro-
gen as a nitrogen source. In reactors receiving ammonia and exhibiting
nitrification, growth was often inhibited even with copious quanities of
nitrification-produced nitrate nitrogen available. The nitrogen uptake
and transformation associated with the nitrifying organisms was very much
greater than that associated with algal populations.
Macrophytes — Extensive research has been directed towards evaluating
various aspects of aquatic macrophyte ecology in lakes and other systems
(Westlake, 1968). This research, however, has not adequately described
the significance of macrophytes to total lake ecology in a broadly appli-
cable manner. The significance of macrophytes to lake nutrient budgets
and cycling remains unclear. The nutrient content of plant tissues has
been analyzed by several investigators. Although wide variability in
nitrogen and phosphorus concentrations have been reported (Caines, 1965,
Anderson et al., 1966, Gerloff, 1973, Neel et al.} 1973) aquatic plants
generally average about 3% nitrogen and 0.4% phosphorus as dry weight.
Results from laboratory studies by DeMarte and Hartman (1974) suggest
that aquatic plants can play a significant role in recycling nutrients
within aquatic systems. This occurs not only when the plants die and
decompose but also during periods of active growth. Such an occurrence
is the result of the active transport of nutrients along the substrate-
root-stem-leaf-water pathway. Data obtained by Neel et al. (1973)
from plant tissue meausrements suggest, however, that in Lake Sallie,
Minnesota, macrophyte control programs such as harvesting, would not
be effective in decreasing nutrient concentrations in the lake. Macro-
phytic nitrogen and phosphorus were insignificant when compared with
the river nutrient loading and total lake water content.
The objective of this phase of the research was to assess the significance
of submerged aquatic macrophytes in White Lake. This indues evaluation
of the biomass and species distribution of the lake macrophytes, measure-
ment and assessment of the significance of plant tissue nutrients to the
total lake nutrient budget, and analysis of the potential of the macro-
phytes to respond to the sewage diversion project. A detailed discussion
of these findings is presented in Appendix B.
110
-------
Field and laboratory techniques were employed to investigate the impor-
tance of the submerged aquatic macrophytes in White Lake. The experimen-
tal methods are described in detail in Appendix B. Seven sampling cruises
were conducted between June and October of 1974. The lake macrophyte
community was mapped with respect to species, areal, and biomass distri-
bution. Species distribution of the White Lake macrophyte community are
illustrated in Figure 43. The species composition of the community in
the late summer of 1974 is shown. At each keyed location all species
identified are listed according to their relative abundance. Although
a total of fourteen species were identified in the system, the relative
abundance of species varied widely. Myriophyllum vertioillatum, Ceratophy Hum
demerswn, and VafLisneria ameriaana were the prominent species at most
locations, and represented the overwhelming majority of the biomass.
The results of macrophyte harvesting in White Lake indicate wide varia-
bility in plant densities both spatially and temporally with plant con-
centrations often approaching 150 g dry weight/meter2 (typical for shallow
eutrophic lakes). The observed extent of the macrophyte beds ranged
from a 6% coverage of the lake bottom in June to a maximum coverage
of 18% in August. The integrated results of the areal and biomass cal-
culations derived from the seven macrophyte samplings are shown in
Figure 44. The significance of these calculated biomass estimates can
be evaluated if a comparison is made with the other major primary pro-
ducer in the lake, the phytoplankton. Estimates of total chlorophyll a
in the lake were made by multiplying the depth weighted average measured
concentrations by the lake volume. An approximate stoichiometric dry
weight to chlorophyll a ratio was used to estimate the phytoplankton
biomass. A comparison of these results indicates that during much of
the year the biomass standing crops of the macrophytes and the phytoplankton
are approximately the same.
Samples of plant tissue were also analyzed for carbon, hydrogen, nitrogen,
potassium, and phosphorus. These results suggest that the White Lake
macrophytes community is not limited by phosphorus or nitrogen, and is
probably restricted only by light and space requirements. Nutrients
associated with the macrophytes are an order of magnitude smaller than
the total nutrient content of the lake but are approximately one-half
the magnitude of the estimated nutrient content of the phytoplankton.
However, studies by Denny (1972) and calculations detailed in Appendix
B indicate that macrophytes are capable of extracting significant quan-
tities of phosphorus from the sediments. Because of this and other phe-
nomena, it is important to consider the potential response of the community
to the nutrient diversion program and reductions in lake levels. The
possibility exists that the community will increase in size if light
penetration of the water improves due to reduced levels of algae and
detritus. In addition, lowered lake levels will increase the extent of
the shallow water areas available for growth. Macrophytes can derive
their essential nutrients from the rich bottom sediments; consequently,
subsequent recycling of these nutrients to the overlying waters could
result in the persistence of high nutrient and nuisance plankton levels.
A program of direct macrophyte control may then be necessary.
Ill
-------
LEGEND
(A) Abundant
(C) Common
(U) Uncommon
(R) Rare
M. Myriophyllum
.C. Ceratophyllum
JP. Potamoqeton
V. Vallisneria
L. Lemna
EL Elodeo
S. Scirpus
1. M. verticillatum with
filamentous algae (A)
2. C. demersum (C)
3. P. zosteriformis (U)
1. M. yerticillatum with
filamentous algae (A)
2. y americona (C)
3. S. americanus (C)
1. M. verticillatum with
filamentous algae (A)
2. V. americano (C)
M. verticillaturn (A)
1. M. verticillatum (A)
2. C. demersum (A)
3. P. praelongus (U)
t. M. verticillatum (A)
2. C. demersum (A)
3. R zosteriformis (C)
4. V americana (C)
5. L triscula (C)
6. L minor (C)
7. Nymphae tuberosa (U)
8. E. canadensis (U)
•Typha sp (A)
1. M. verticillotum (A)
2. C. demersum (A)
3. P zosteriformis (C)
4. V. americana (C)
1. V_. omericana (A)
2. M. verticillatum (C)
5. L minor (C)
6. L. triscula (C)
M. verticil lotum (A)
2. V. americana (C)
3. P^ zosteriformis (U)
4. (X demersum (R)
_1. verticillatum wilh
filamentous algae (A)
1. M. verticillatum with
filamentous algae (A)
2. C. demersum (U)
I.M. verticillatum (A)
2. V. americana (A)
3. C. demersum (A)
4. R_ zosteriformis (C)
5. E. canadensis (C)
6. P.'crispus (U)
7. P. pectinuatus (U)
8.Najas flexilus (R)
9. P proelongus (R)
figure 43. Distribution of macrophytes in White Lake.
112
-------
O>
"g200
o
en
O
JZ
CO
C/)
o
QQ
X
a_
o
a:
100
0
V
/ \ phytoplankton
Y
macrophyte
biomass
&c\
£K.
/ /i/x^X \
/ /^macrophyte x\ \
/ rf/ areal coverage Vi \
I A v^
u
L
1
L
Jun Jul Aug Sep Oct
4.0
CVJ
3.0
LU
X
LU
2.0%
LJ
Q.
O
0
Figure 44. Macrophyte and phytoplankton content in White Lake, 1974.
113
-------
Sediment-Nutrient Relationships — The importance of lake sediments in
controlling nutrient concentrations in overlying waters has long been a
subject of concern. Mortimer (1941, 1942) concluded from his studies
on English lakes that various mechanisms exist (e.g., adsorption, and
complexation) in superficial oxidized sediment layers which may prevent
the transport of materials from the sediments to overlying aerobic waters.
More recently, it has been demonstrated that the disappearance of this
oxidized microzone (as might occur during hypolimnetic anoxia) results
in a substantial release of nutrients from the sediment (Mortimer, 1971).
Barter (1968) found that eutrophic lake sediments have a large capacity
to temporarily absorb phosphorus and later release it. In laboratory
experiments, Porcella et at., (1970) also demonstrated that sediments
possess a large potential for nutrient release. Despite these studies,
and numerous others, there does not now exist sufficient information to
quantitatively predict the magnitude of nutrient release or uptake by
sediments in White Lake (Lee, 1970, Byrnes et al,3 1972).
The purpose of the efforts summarized in this section was to conduct a
study to assess the significance of sediment nutrient release under
anaerobic conditions in White Lake. A detailed discussion of these find-
ings is presented in Appendix C. A three-phase plan was devised to
achieve the objectives of this study. The first task was to measure nu-
trient concentrations in the sediments and assess their potential for
release and exchange with overlying waters. Investigations of the sedi-
ment revealed high nutrient concentrations in the interstitial waters.
Results from these chemical analysis are shown in Figure 45. Examination
of the data from the top five centimeters of sediments reveals significant
concentration gradients between the sediments and the overlying waters.
Maximum nutrient concentrations in this sediment zone were 22.0 mg Si/£
of silicon, 12.5 mg N/£ of ammonia, 3.6 mg P/H soluble reactive phosphorus,
and 5.2 mg P/5, total dissolved phosphorus. The calculated concentration
gradients between the sediment and overlying waters were 6.1 mg Si/£/cm
silicon, 3.4 mg N/£/cm ammonia, 2.36 mg P/Jl/cm soluble reactive phosphorus,
and 3.4 mg/£/cm total dissolved phosphorus.
The second phase of the work involved a laboratory study to simulate the
lake bottom and measure the sediment-water nutrient flux. The experiments
were conducted on sediments and hypolimnetic water collected in a benthic
corer. These experiments revealed significant nutrient release from the
sediments to the overlying waters under anaerobic conditions. The results
from this experiment are shown in Figure 46. Observed concentrations of
nutrients in the overlying waters increased drastically. Soluble reactive
phosphorus concentrations increased from 0.05 to 0.56 mg P/£, while total
dissolved phosphorus increased from 0.05 to 0.67 mg P/£. Ammonia increased
from 0.23 to 0.78 mg N/& and silicon increased from 2.2 to 8.7 mg Si/£.
Nutrient flux rates were calculated from nutrient release data by use
of graphical and analytical techniques incorporating the area and volume
of the experimental apparatus.
The third phase of this work consisted of measurements of actual nutrient
release rates in a chamber placed at the bottom of White Lake. The re-,
suits from the in situ chamber study also revealed high sediment-water
114
-------
SOLUBLE REACTIVE
PHOSPHORUS, mgP/l
1 23 4
8 5
x"
I-
Q_
UJ
010
15
o
o
TOTAL DISSOLVED
PHOSPHORUS, mgP/l
w
x"
Q.
UJ
010
1 ' ' " ' 'o
o
o
0
o
o
1 L_o 1 1 1
AMMONIA.mgN/l
0
§ 5
x"
CL
UJ
Q 10
1^;
4 ^8 12 16 2(
o
o
0
o
o
o
.1 o I I I
SILICON.mgSiA?
u
§ 5
x"
t
UJ
1*S
0
o
0
o
0
q
1 1 — _ L ln I
Figure 45. Concentrations of nutrients in White Lake sediment
interstitial waters.
115
-------
SILICON, mg Si/I AMMONIA, mgN/J
ro ^ _
P P P P
TOTAL DISSOLVED
PHOSPHORUS, mgP/f
P P P P
ORTHOPHOSPHATE,
mgP/l
P P p P
ro -
en -
CD
3^ Ui Oi bi <
"O | | |
o
0
o
— —
o
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o
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0
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o
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0
3 p
ro
o
^ •£»
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en
m
D ro ^ en c
T° 1 1
o
wo
o
—
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o
0
o
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0
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o'
(III
30 p
ro
o
CO
en
m
q i ho :* m bo _c
^ i i i
o
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— -
o
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o
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8
1 1 1
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u i i i
0
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h o
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0
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1 1 1
Figure 46. Nutrient release from White Lake sediments-laboratory studies.
-------
nutrient exchange rates. A plot of the change of nutrient concentrations
in the chamber is shown in Figure 47. Concentrations of soluble reactive
phosphorus increased from 0.04 to 0.20 mg P/& during the three-day study,
ammonia increased from 0.33 to 0.61 mg N/£, and silicon increased from
1.1 to 4.5 mg
The results of these studies were used to calculate a flux rate between
the sediment and water. General agreement among methods was obtained for
both nitrogen and phosphorus. The average sediment nutrient release
rates for the three methods were 25.1 mg P/m2/day soluble reactive
phosphorus and 36.2 mg N/m^/day ammonia. The associated net diffusion
coefficient across the sediment-water interface was calculated to be
1.0 to 1.5 x 10~5 cm^/sec. Theoretical and experimental results for
silicon release were not in good agreement. Speculations regarding this
discrepancy are discussed in Appendix C.
The measured flux rates of nitrogen and phosphorus suggest that the sedi-
ments have the potential to contribute nutrients to the overlying waters
at levels sufficient to support algal growth. As a result, improvements
in water quality resulting from the White Lake sewage diversion project
could be delayed or reduced.
Modeling — One goal of the Muskegon Wastewater Management System is
to improve the water quality of White, Muskegon, and Mona Lakes so that
they may be more effectively used for recreation and navigation. This
usage is a function of the levels of algae, macrophytes, dissolved oxygen,
and fecal coliform in the lake. The limnological sampling program has
been conducted to document changes in water quality following land
disposal treatment. Data from this sampling program has also been used
to develop mathematical models which can be used to predict the long-term
impact of the waste management program. Mathematical models are important
because they allow a quantitative evaluation of the relative importance
of several factors which may effect water quality in lakes. For example,
algal blooms in lakes are a function of nutrient loading from non-point
sources such as urban and agricultural runoff, domestic and industrial
wastes, nutrients released from the bottom sediments, nutrients pumped
into the water by rooted aquatic macrophytes, and the rate of nutrient
recycle in the water column. All of these processes must be quantitatively
evaluated before improvements in levels of phytoplankton productivity
and other parameters related to water quality can be predicted following
a decrease in nutrient loading or implementation of other restorative
measures such as sediment dredging and macrophyte harvesting. Experience
in Lakes Washington and Sammamish has shown that the effectiveness of
nutrient diversion cannot always be intuitively predicted and that mathe-
matical models can explain otherwise unexpected results.
The goal of the modeling studies was to predict long-term phosphorus
concentrations in White Lake. Most previous phosphorus and trophic
status models (Vollenweider, 1969, Vollenweider, 1975, and Dillon and
Rigler, 1974) have considered a single component of the phosphorus cycle
(total phosphorus) . Most of these models have been applied to less
eutrophic waters for cases where sediments play a minor role in regulating
117
-------
00
SILICON, mg Si/I
AMMONIA, mgN/f
Q Q p
SOLUABLE REACTIVE
PHOSPHORUS, mg P/l
«
O
H
m
*
a.
Q
k<
Vt
po
(1.1
-0 ro w 4>
^ i ii
O
O
O
O
-
O
O
1 1 1
J1 f
O
H
;p
S»
jn
Q.
o
^^f
CO
ro
fki
N) bi, 4^ C7l Cn
i O 1 1 1
O
0
o
o
o
-
o
o
1 1 1 1
oc
H
jn
Q.
o
(A
ro
LIJ
D 0 '- r
o
o
o
o
o
-
o
0
1 1 1
Firure 47. Nutrient release from White Lake sediments-^tn -6>c£u studies,
-------
the phosphorus cycle. Under many circumstances, such as in White Lake,
other phenomena, such as phosphorus regeneration from the sediments to
the overlying water and phosphorus transformation within the sediments
may complicate the system response and require more comprehensive models.
Therefore, a model which incorporates the water and the sediment systems
and considers two forms of phosphorus (particulate and dissolved) has
been developed for White Lake. A significant amount of phosphorus release
has been observed in the hypolimnion of the lake during anaerobic condi-
tions in the summer. The model quantifies the dynamic interactions of
phosphorus between sediments and water by taking into account the sinking
of particulate phosphorus and diffusion of dissolved phosphorus across
the sediment-water interface. Other model mechanisms include vertical
eddy diffusion in the water, phosphorus transformation between the
particulate form and the dissolved form in both the water and the sedi-
ment, diffusion of phosphorus in the interstitial water, and sedimentation
in the sediments. The components of the model are displayed in Figue 48.
Extensive field data were used to determine the coefficients and param-
eters defined in the model formulations. The vertical eddy diffusion
coefficient characterizing vertical mixing between the epilimnion and
the hypolimnion was calculated using temperature and nutrient conditions.
The sinking velocity of particulate phosphorus in the lake was determined
through mass balance considerations. The diffusion coefficient in the
interstitial water was determined from the chloride profile in the sediment.
The kinetic coefficient in the upper sediment layers was found to correlate
with the seasonally variable dissolved oxygen level at the bottom of the
lake. A detailed discussion of the model formulation is contained in
Appendix D.
Model calibration produced close agreement between the model calculations
and observed data for 1974 (see Figure 49). Sensitivity analysis further
substantiated the model results. The model was then verified against
an independent set of data taken in 1973 with the parameters and coeffi-
cients determined in the 1974 calibrations. The model is able to explain
the significant release of phosphorus from the sediment to the hypolimnion
of White Lake in summer. Inclusion of two separate forms of phosphorus
into the model was necessary to gain detailed insight into the dynamics
of phosphorus cycling in White Lake.
One immediate application of the model was to assess the effect of nutrient
reduction resulting from the sewage diversion program on White Lake. The
simulation results shown in Figure 50 indicate a slight decrease of phos-
phorus levels in the first year after nutrient reduction and virtually no
improvement after that. It is concluded, therefore, that the lake will
not undergo dramatic improvement in water quality (i.e., reduction
119
-------
tl
Li
1
K
1
§
PARTICULATE
PHOSPHORUS
1
1
1
^ Diffusion ^
k
o»
c
co
7 1
i
PARTICULATE
PHOSPHORUS
c
*-
co
\
i
PARTICULATE
PHOSPHORUS
jj
2
"c
, _a_ t _ IM._M .. flj
(/)!
\
PARTICULATE
PHOSPHORUS
-1!
il
£T
"•6
O)
CO
_ Reaction
Reaction
Reaction
Reaction
DISSOLVED
PHOSPHORUS
/
o
"to
»•-
H-
5
^
\
'
DISSOLVED
PHOSPHORUS
/
0
'to
««—
*»-
5
^
\
'
DISSOLVED
PHOSPHORUS
I
Diffusion
S* • IS
VI »""
Sedimentation
[
DISSOLVED
PHOSPHORUS
Diffusion
^ IN.
vi 1*"
Sedimentation
i
EPILIMNION
HYPOLIMNION
SEDIMENT
SEDIMENT
Figure 48. White Lake phosphorus model.
120
-------
CO
a:
o
OL
CO
o
I
CL
UJ
Z)
o
h-
o:
2
70
60
50
40
30
20
10
0
50
40
I I I I I I I I
Epilimnion
I I I
Hypolimnion
I I I I I I
Epilimnion
Hypolimnion
i i i i i t »» I I I
50
40
30
20 §
-------
NJ
f-O
330
fc
z 25
CONTINUED WITH THE 1974 LOADING
Present Nutrient Diversion (Mean Load)
/Aeration
T '
^Dilution/Flushing
Aeration and Circulation
Control of Non-Point Sources
2 3
YEARS
Figure 50. Comparison of rehabLlitation schemes for White Lake.
-------
in algal concentrations). The model was also used to evaluate the addi-
tional schemes of lake rehabilitation for the possibility of further
improvement of water quality in White Lake. Figure 50 demonstrates that
further reduction of the present non-point phosphorus loading is necessary
for addition recovery, although some improvements would also be expected
to result from aeration, mixing, dredging, and flow augmentation.
123
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SECTION IX
MUSKEGON LAKE
INTRODUCTION
Muskegon Lake is the largest of the three study lakes (see Figure 3).
The lake has a surface area of 16.8 km2, a volume of 12.0 x 107 m3 and
a mean depth of 7.1 meters. The maximum lake depth is 23 meters. There
exist shallow littoral areas in the lake; however, these are not as
extensive or as over-grown by macrophytes as those of White Lake.
The lake has a roughly east-west orientation and is approximately 8
kilometers long by 1.5 to 3.5 kilometers wide.
Muskegon Lake receives flow from six identified tributaries of which
the Muskegon River and Bear Lake Creek are the most significant. The
lake discharges into Lake Michigan through a narrow channel. The
channel and the lake are dredged permitting the commercial navigation
important to various industries.
The area surrounding Muskegon Lake is mixed urban, industrial, and
residential. The major segment of the industry and the urban center
lies to the southeast and east of the lake. The southwest and north
shores are primarily residential. In the past, the lake has received
numerous industrial and municipal discharges which are described in
detail in subsequent sections. The most notable of these discharges
were from the Muskegon and North Muskegon Sewage Treatment Plants, the
S.D. Warren Paper Company, and the Storey (Ott) Chemical Company.
TRIBUTARY-RELATED CONSIDERATIONS
Hydrology — The Muskegon Lake drainage basin has an area of 6,819 km2
and drains lands from Muskegon, Newaygo, Montcalm, and Mecosta Counties.
Six identified tributaries empty into Muskegon Lake, with the Muskegon
River dominating the system (see Figures 5 and 7). The Muskegon River
drains 97.5% of the Muskegon Lake basin with the next largest tributary
Bear Lake Creek, accounting for only 1.1% (see Table 18). Hydrologically
the Muskegon River is also dominant. In a 1972 to 1973 study by the
USEPA (1975c) the Muskegon River was observed to contribute an estimated
95% of the total flow to Muskegon Lake.
The Muskegon River basin begins in northern Mecosta County and flows
southwesterly to Lake Michigan. Because the focus of this study is on
Muskegon Lake, all references to the Muskegon River and its basin will
be with regards to the drainage upstream of the river entry to Muskegon
Lake. Tributary and direct drainage to the lake will be considered
124
-------
Table 18. MUSKEGON LAKE DRAINAGE BASIN CHARACTERISTICS
Description
Muskegon River
Green Creek
Bear Lake Creek
Four Mile Creek
Ryerson Creek
Ruddiman Creek
Minor Tributaries
& Immediate
Drainage
Muskegon Lake
Total
Area
(km2)
6645.7
30.3
74.0
8.8
19.7
8.8
15.0
16.8
6819.1
Percentage
of Total
97.5%
0.4%
1.1%
0.1%
0.3%
0.1%
0.2%
0.2%
100%
Discharge
(m-Vsec)
58.86
0.33
0.84
0.09
0.20
0.09
0.27
60.68
Percentage
of Total
97.00%
0.54%
1.38%
0.15%
0.33%
0.15%
0.44%
100%
(Modified from USEPA, 1975c)
125
-------
separately. The 52-year average flow in the Muskegon River as measured
at USGS station 04122000 at Newaygo is 54.9 m3/sec. The annual average
flow can vary significantly (see Figure 51). Between 1972 and 1973
the river changed from a moderately low flow period to a high flow period.
The monthly average flows as measured at the USGS station during this
study are shown in Figure 52.
The flow at the USGS station does not represent the total flow of the
Muskegon River to Muskegon Lake. Between the USGS station and the river
mouth the Muskegon River receives drainage from six identified tributaries
(Cedar Creek, Mosquito Creek, Brooks Creek, Maple River, Minnie Creek,
and Sand Creek), several minor tributaries, and direct drainage sources.
To estimate the total river flow entering Muskegon Lake, the USGS flows
were multiplied by 1.23. This factor was derived from miscellaneous
USGS flow data (USEPA, 1975c), flow data collected during this study, and
drainage area considerations. The total 52-year average flow entering
Muskegon Lake is then calculated to be 67.5 m3/sec. Direct municipal
and industrial discharges do not significantly alter the hydrologic char-
acteristics of the river.
The significance of the Muskegon River flow to Muskegon Lake can be cal-
culated if the ratio of lake volume to tributary flow or mean hydraulic
retention time is calculated. The lake volume is 12.0 x 10' m3. The
retention time is calculated to be 21 days. This indicates that on the
average the Muskegon River has the capability of flushing the total
volume out of the lake over 16 times per year. This hydraulic retention
time is, of course, an average estimate which does not consider short-
circuiting, stratification, etc., nor does it consider the seasonal varia-
tion in flow which would cause the retention time to vary at different
times of the year.
Concentrations of Chemical Species in Tributaries — Measurements of
various water quality parameters were made in the Muskegon River and
Bear Lake Channel. Only these tributaries were chosen for monitoring.
Hydrologic evaluations demonstrated that all other tributaries were
insignificant and relatively uncontaminated. Bear Lake Channel was
assumed representative of general water quality in the minor tributaries.
A summary of the water quality measurements in the Muskegon River and
Bear Lake Channel is given in Table 19. The Muskegon River discharge
concentrations displayed in this table represent an average of the con-
centrations measured in the three branches of the river. Each of the
branches originate from interconnected sources and the relative propor-
tion of flows in each branch could not be distinguished.
A comparison of the concentrations of chemical species at the Muskegon
River mouth with those in the Bear Lake Channel show the two to be of
similar magnitude except for chloride and nitrogen. The Bear Lake Channel
126
-------
30
1961 1962 1963 1964 1965 1966 1967 1968 1969 1970 1971 1972 1973 1974 1975
YEARS
Figure 51. Muskegon River average annual flow at Newaygo, Michigan
(USGS Station #04122000).
150
100
FLOW
m3/sec
50
pi M 1111111111111..,
1972 J 1973 J 1974 J 1975
YEAR
Figure 52.
Muskegon River mean monthly flow at Newaygo, Michigan
(USGS Station #04122000).
127
-------
Table 19. AVERAGE CONCENTRATIONS OF SELECTED CHEMICAL SPECIES IN TRIBUTARIES TO MDSKEGON LAKE, 1972-1975
S3
00
Tributary
Muskegon River
(average of all
branches)
Muskegon River
(Station 143)
Muskegon River
(Station 102)
Bear Lake Channel
(Station 148)
Year
1973
1974
1975
1973-1975
1973
1974
1975
1973-1975
1972
1973
1974
1975
1972-1975
1973
1974
1975
1973-1975
Chloride
(mg Cl/t)
19.0
20.9
21.5
20.3
18.6
18.4
18.9
18.6
15.4
17.9
25.5
27.7
22.0
43.1
39.7
38.6
40.6
Ammonia
(vg N/l)
85
35
33
54
17
30
24
24
57
18
45
31
35
42
37
41
40
Nitrate
(ug N/i)
101
151
200
144
102
163
211
156
409
97
174
228
196
50
90
91
77
Soluble
Reactive
Phosphorus
(Mg P/D
18
11
9
13
5
6
5
5
..
14
14
13
14
4
3
4
3
Total
Dissolved
Phosphorus
(wg P/*)
40
22
23
29
15
13
13
14
18
30
22
26
25
14
12
17
14
Total
Phosphorus
(Mg P/*)
63
46
43
51
32
27
33
30
29
36
41
67
44
70
43
60
57
Silicon
(ng Si/t)
2.3
2.6
3.1
2.6
2.2
2.5
2.9
2.6
3.1
2.7
2.7
3.1
2.8
2.1
1.7
3.1
2.3
Dissolved
Iron
(yg Fe/t)
76
63
57
66
61
41
33
44
64
70
79
71
52
49
70
56
Total
Iron
(ug Fe/t)
485
149
157
260
461
111
124
220
454
170
148
250
310
146
154
194
-------
chlorides were approximately twice those in the Muskegon River. This
elevation in chloride concentrations is postulated to be an effect of
the high salt content of the groundwater inflow. No other explanation
is proposed. No point discharges are known to exist in the Bear Lake
basin. Nitrate and ammonia concentrations in the Bear Lake Channel
were 30-50% less than those in the Muskegon River. This is considered
a consequence of point discharges to Muskegon River waters. Since
the concentrations of chemical species in the Bear Lake Channel were not
excessive and because of its hydrologic insignificance, all subsequent
discussions of water quality are focused on Muskegon River.
The Muskegon River is the dominant tributary to Muskegon Lake and thus
the lake water quality can be expected to be a function of tributary
water quality. This assumption ignores any direct point discharges to
the lake which could change concentrations. The average river concen-
trations of dissolved inorganic nitrogen (199 yg N/A), total phosphorus
(.52 yg P/A), and dissolved silicon (2.6 mg Si/A) are capable of supporting
significant algal growth. Although only 25% of the total phosphorus is
in the readily available soluble reactive form, all of the phosphorus
is expected to be potentially available through bacterial and enzymatic
action.
Figures 53 to 58 are plots of concentrations of various parameters measured
in the Muskegon River. The seasonal patterns observed are similar to
those found in the White River. Higher phosphorus concentrations were
found in the late spring and summer and are associated with higher runoff
while higher nitrate concentrations were measured during the winter
and reflect low plant uptake.
Yearly average concentrations of chemical species measured in the Muskegon
River display a significant variability. Explanations for this variation
must include analysis of upstream concentrations as they relate to down-
stream water quality. This isolates the effects of the diversion system
from changes in upstream boundary condition influence. Concentrations
of plant nutrients measured at the river mouth reflect upstream water
quality (including spray drainage) during all years except 1973. During
1973 observed ammonia and phosphorus concentrations were higher at the
river mouth, a result of industrial and municipal discharges. In 1972
no measurements were made at the river mouth. The two most significant
discharges to the river, the Muskegon Wastewater Treatment Plant and
the Storey (Ott) Chemical Company, diverted their wastes in May 1973
and April 1974, respectively.
A reduction of the ammonia and phosphorus concentrations at the Muskegon
River mouth was observed after 1973. Average yearly concentrations
between 1973 and 1974 dropped from 62.7 yg P/* to 45.8 yg p/A for total
phosphorus and 85.5 yg N/A to 35.4 yg N/A for ammonia. Total iron also
showed a decrease from 485 yg Fe/£ to 149 yg Fe/A. Other parameters
did not significantly change. The river mouth data were compared
129
-------
u>
o
MUSKEGON RIVER
at the mouth (avg.)
° Nitrate
o Ammonia
500
o»
UJ
o
o
DC
250
1972
1973
1974
1975
Figure 53. Dissolved inorganic nitrogen concentrations
in the Muskegon River, 1973-1975.
-------
Muskegon River
Station 102
o Ammonia
a Nitrate
1972
1973
1974
1975
Figure 54. Dissolved inorganic nitrogen concentrations in
the Muskegon River, 1972-1975.
-------
100
tr
o
x
Q.
cn
o
50
0
,(238)
.(174)
MUSKEGON RIVER
at the mouth (avg.)
a Total Phosphorus
o Total Dissolved Phosphorus
l I I i i i 1 I I i i i i l ' ' ' ' ' '
1972
I i l l I I I I I
1975
Figure 55. Phosphorus concentrations in the Muskegon River, 1973-1975.
-------
ri 100
Muskegon River
Station 102
D Total Phosphorus
o Total Dissolved Phosphorus
A Soluble Reactive Phosphorus
UJ
ID
i_
O
.C
CL
(f)
o
50
1972
1973
1974
1975
Figure 56. Phosphorus concentrations in the Muskegon River, 1972-1975.
-------
Muskegon River
Station 102
0 Silicon
LO
CO
en
"-
o
o
CO
T3
S
§
Q
0
I I I 1 1 I I I I I I.
J L
' ' '—L
' ' ' ' ' '
I I
1972
1973
1974
1975
Figure 57. Silicon concentrations in the Muskegon River, 1972-1975.
-------
Ui
60
o>
TJ
20
Muskegon River
Station 102
o Chloride
I I I I I I I—I'll
J L
-1—I—I—I—L-J—I—I—I—J—I—i ' I ' i ' '' i ' i ' i '
1972
1973
1974
1975
Figure 58. Chloride concentrations in the Muskegon River, 1972-1975.
-------
to upstream data from Station 102. Prior to the summer of 1973 the
Muskegon River received the discharges from the Muskegon and North
Muskegon Wastewater Treatment Plants between these stations, and hence
a comparison can relate cause and effect. A drop in iron concentrations
between 1973 and 1974 was also observed at Station 102. This suggests
that the decrease in concentration was a consequence of upstream condi-
tions not diversion. The decrease in iron was also observed at Station
143 which is upstream of the spray site; this rules out any cause-and-
effect relation to the spray diversion project for iron. On the other
hand, the phosphorus and ammonia data suggest that the observed reduc-
tions for these parameters may have been a direct consequence of the
waste diversion because similar decreases in phosphorus and ammonia con-
centrations were not observed at upstream stations between the years
of 1973 and 1974.
The Storey (Ott) Chemical Company diverted high ammonia containing
wastes in early 1974. No subsequent significant reduction in ammonia
was observed subsequent to diversion. Part of the observed reduction
in 1973 and 1974 in ammonia could have been caused by this diversion.
However, as will be noted later, the municipal waste discharge loads
were much greater than those originating from Storey (Ott) Chemical
Company. It is difficult therefore to directly distinguish the effect
of the Storey (Ott) Chemical Company dishcarge.
Limited effects on Muskegon River concentrations were observed to result
from the drainage from the spray-irrigation site. This can be evaluated
by examining the yearly averages at Stations 143 and 102. An increase
in nitrogen concentrations might have been expected to result from
the application of urea fertilizer to the spray site. This was not
observed. Either this effect was minimal or the sampling dates did not
coincide with fertilization periods. No specific information was avail-
able on the amounts and dates of fertilization. Total phosphorus con-
centrations were observed to increase between Stations 143 and 102 from
26.7 to 41.4 yg P/fc in 1974 and 32.6 yg P/fc to 67.4 yg P/& in 1975.
During 1975, the average concentrations of nitrogen and phosphorus
measured in Mosquito Creek (which receives the drainage from the spray
site) were 50 yg P/Jl total phosphorus, 1.9 mg N/& nitrate, and 0.6 mg N/£
ammonia (Muskegon County, 1976). Concentrations measured in other years
were of similar magnitude or less (see Appendix E). The total phosphorus
concentrations were not significantly different than upstream Muskegon
River concentrations. This illustrates the effectiveness of the soil
to adsorb phosphorus from percolating water. Nitrate and ammonia, on
the other hand, were significantly higher in the drainage than in up-
stream locations. The potential effect of the irrigation drainage on
the Muskegon River can be evaluated by comparing the spray drainage flow
and the Muskegon River flow. The average 1975 drainage from the spray
site was approximately 1 m /sec which represents less than 2% of the
136
-------
total Muskegon River flow. Given this consideration and the similarity
between drainage phosphorus and river phosphorus concentrations, the
observed increase in phosphorus between Stations 143 and 102 cannot
be readily explained.
The distribution of phosphorus among its various forms was noted to have
changed during the investigation. During 1973, solible reactive phos-
phorus concentration represented approximately 33% of the total phos-
phorus concentration at the river mouth. During subsequent years this
fraction dropped to about 25%. The percentage may have been higher
prior to 1973 when industtial discharges were at their maximum; however,
no information is available on this aspect. The point industrial discharges
of phosphorus, particularly from the wastewater treatment plant, are
principally in the soluble reactive form, hence the trend was as expected.
Phosphorus data also showed the soluble reactive form of phosphorus to
increase in percentage with distance downstream. This was particularly
evident between Stations 143 and 102. This could be an effect of differ-
ences in non-point loads or due to bacterial and enzymatic conversion of
organic forms of phosphorus to the soluble reactive form.
Dissolved silicon was noted to decrease in concentration at the river
mouth as compared to upstream levels. This could be an effect of algal
uptake or dilution from intruding Muskegon Lake waters. Average chloride
concentrations were observed to increase downstream of the spray site
(Station 102) as compared to Station 143. This increase did not appear
in the Muskegon River mouth data. Higher chlorides might be expected
from the spray drainage; however, the downstream disappearance of this
increase is inconsistent.
In general, the wastewater diversion project has resulted in improve-
ments in Muskegon River water quality. Prior to diversion, the industrial
and municipal discharges caused elevated levels of phosphorus and ammonia
in the river. The effect of diversion could have been portrayed more
clearly if additional pre-diversion river mouth data were available. The
spray site drainage did not appear to have a deleterious influence on
Muskegon River water quality. However, variation in upstream concentra-
tions resulting from non-point sources is a dominant factor in determining
nutrient concentrations in the Muskegon River during the post-diversion
period.
Nutrient Loads — The major sources of nutrients to Muskegon Lake have
been from municipal, industrial, and tributary discharges (see Figure 59).
Other loads are described in Appendix F. Six tributaries empty into
Muskegon Lake; of these the Muskegon River is the only significant source
of nutrients. A 1972-73 study by the USEPA (1975c) indicated that the
Muskegon River accounted for 94% of the total phosphorus load from the
tributaries and 96% of the total nitrogen load.
137
-------
V
North Branch
A/
o^Storey Chemical \
\\\\\ \.Teledyne Continenfal
\\\\\V^ Motors
\ \ \ VJaph-Sol Refining Co.
Mu$kec/ori Ri
U)
00
Former
North
Muskegon
WWTP '
City of Muskegon
147 Former WWTP
°Amstead Industries //A \
/Michigan Celery Promotion Co-op
'/t.
eledyn'e/
nt. Motors
West Michigan Dock and Market
o'Shaw Walker/VQ. ////////////
Mich. Foundry/"Geerpres
Howmet #2 / / / ' K—
Wire and Cable?
3/.W I IUWI 11C I HC. /I I
///Port City Paints
rei
>tr
S.D.'Warron'
. - . —,
Breneman lnc/////
. /////
Muskegon Piston Ring
'
Sealed Power
o Standard Oil Car
, Wyatt and Cannon
o"//n* Cannon Muskegon Corp
// Great Lakes Plating
Lake
Michigan
Industries .
o =in
•=out
0 1 2
kilometers
Communities \ '
////= in systerA
\\v=out, butto\
enter within ^
20 years
1 |- out, no plan
Figure 59. Location and diversion status of point sources and municipalities in the Muskegon
Lake basin.
-------
Information regarding the major industrial and municipal discharges
to Muskegon Lake is summarized in Table 20. Estimates of the nutrient
loads were obtained from operating reports and Michigan Water Resources
Commission industrial and municipal waste surveys. The four most signifi-
cant pre-diversion discharges were the S.D. Warren Paper Company, the
Storey (Ott) Chemical Company, and the Muskegon and North Muskegon Waste-
water Treatment Plants. These discharges were diverted to the spray-
irrigation system on the dates shown in Table 1.
Nutrient loads in the tributaries were calculated by multiplying the
monitored river concentrations by the specific daily flow as calculated
from the USGS measurements on the Muskegon River and Bear Lake Channel.
The USGS flows were corrected to represent the total flow at a specific
sample station. A multiplication factor was used to compensate for
the increase in flow below the USGS station. This was derived from
miscellaneous flow measurements and drainage area considerations.
Because no consistent or reliable information was available regarding
the split in flow between the various branches of the Muskegon River,
concentrations were averaged from the different branches and multiplied
by the total flow to obtain the loads. A summary of the calculated trib-
utary loads is given in Table 21. Plots of the calculated Muskegon
River loads are given in Figures 60 through 63. The emphasis of the
load calculations was on total phosphorus and dissolved inorganic nitrogen
because they were believed to be most important in evaluating the effec-
tiveness of the diversion program. Emphasis has usually been placed
on yearly averages, for reasons previously outlined in discussion related
to White Lake. All conclusions derived from the yearly averages were also
supported by seasonal analysis of the data.
The tributary nutrient loads from Bear Lake Channel were compared with
those of the Muskegon River. This comparison demonstrated the insig-
nificance of the load from Bear Lake Channel. The Bear Lake Channel
load was typically 1% or less of the total phosphorus tributary load
and less than 2% of the chloride load (approximately 3 kg P/day and 2500
kg Cl/day). No further consideration of its influence was pursued.
Patterns were observed in the seasonal variation of nutrient loads
from the Muskegon River. The seasonal variation in nitrogen and phos-
phorus loads was consistent with the variation in concentrations. The
chloride and silicon loads were highest in early spring and were assoc-
iated with high river flows.
The primary focus in this investigation was to examine point and non-
point nutrient sources to Muskegon Lake and evaluate the effects of the
wastewater diversion on water quality. The sources of nutrients to
Muskegon Lake and the potential and actual effectiveness of the sewage
spray-irrigation system were also evaluated. To this end several
additional computations were useful. Table 22 is an annual breakdown
of point and non-point nutrient loads to Muskegon Lake. The point discharges
139
-------
Table 20. ESTIMATED MUNICIPAL AND INDUSTRIAL LOADS TO MUSKEGON LAKE PRIOR TO DIVERSION IN KILOGRAMS PER DAY*
-P-
O
Source & Location
of Discharge
Campbell, Wyant, &
Cannon Company, Muskegon
Continental Motors,
Muskegon
Misco Division of How-
net t Corporation,
Muskegon
Kaydon Bearing Keene
Corporation, Norton
Shores
Michigan Foundry Supply
Company, Muskegon
Muskegon Piston Ring
Company, Muskegon
Naph Sol Refinery,
North Muskegon
Ott (Storey) Chemical
Company, Muskegon
S.D. Warren Paper
Company, Muskegon
Sealed Power Corpora-
tion, Muskegon Heights
Westran Corporation,
Muskegon
Muskegon Wastewater
Treatment Plant
North Muskegon**
Wastewater Treatment
Plant
Receiving Water
Ruddiman Creek
Muskegon Lake
Ruddiman Creek
Ruddiman Creek
Muskegon Lake
Ruddiman Creek
North Branch
Muskegon River
Middle Branch
Muskegon River
Muskegon Lake
Ruddiman Creek
Muskegon Lake
Middle Branch
Muskegon River
Muskegon Lake
Chemical
Oxygen
Demand
121
418
4.2
4.0
8.4
3.7
561
3387
—
34
29.7
—
—
Soluble
Biochemical Reactive
Oxygen Suspended Phosphorus
Demand Solids as P
28.1 158 0.62
134 391 1.16
1.27 0.01
0.6 0.01
18.6 0.0
0.5 1.6 0.01
72.6 — 1.86
1328 95 0.13
5625 5041 —
358 5.4
19.5
—
—
Total
Phosphorus
as P
1.99
2.06
0.04
0.07
0.0
0.01
2.88
0.81
37.4
6.5
0.08
93.2
15.9
Dissolved
Inorganic
Nitrogen
as N
8.39
2.7
0.71
0.32
0.41
0.03
0.0
425
113.5
10.4
2.3
562
95.9
Total
Nitrogen
as N
>8.39
14.4
>0.71
>0.32
>0.41
0.09
13.4
>425
>113.5
>10.4
>2.3
1278
218
Date of
Diversion Source
— MWRC 1973
MWRC 1967-69
— MWRC 1973
— MWRC 1973
MWRC 1973
— MWRC 1973
MWRC 1967
4/18/74 MWRC 1969
6/4/73 MWRC 1966-67
— MWRC 1973
MWRC 1973
Muskegon Co.
5/10/73 1970 & 1975
6/9/73 Muskegon Co.
1970 & 1975
*This table does not include industrial outfalls which prior to 1973 discharged to a municipal treatment system. It also does not include Industrial
outfalls discharging to private lagoons or septic systems. Nutrients loading to Muskegon Lake from these latter sources could not be quantified.
Several other industries are known to discharge to surface waters in the area; however, no data on the quality of their discharges were available.
Appendix F contains additional data.
**Load estimate baaed on Muskegon Waatewater Treatment Plant effluvnt quality and North Muikagon Uattevatcr Plant capacity.
-------
Table 21. AVERAGE MUSKEGON LAKE TRIBUTARY LOADS IN KILOGRAMS PER DAY
Nitrate
Total +
Phosphorus Ammonia
Station Year as P as N
Muskegon River 1972* 273 1744
(at mouth) 1973 421 1268
1974 274 1403
1975 389 2306
Muskegon River 1972 154 686
(Station 102) 1973 189 71?
1974 314 1250
1975 444 2189
Muskegon River 1973 166 ?23
(Station 143) 1974 188 127g
1975 258 1970
*
Estimated based on upstream water quality and point loads.
-------
N:
O
T3
3
C
O
(O
O
O
.C
O
O
25
en
Q
LJ
Z
O
CO
to
Q
MUSKEGON RIVER
at the mouth (avg.)
I 1 I I I I I I I I I I I I ! I I I I I I I I I I t I I I I I I I
1972
1973
1974
1975
Figure 60. Silicon load of the Muskegon River, 1973-1975.
-------
500
-P-
U>
C
o
to
o
Q
<
Q
Q 250
o:
3
a
MUSKEGON RIVER
at the mouth (avg.)
I I I I I i I I I I I i i i i i i i i i i I i i i i i i i i i i i I i i i i i i i i i
1972
1973
1974
1975
Figure 61. Chloride load of the Muskegon River, 1973-1975,
-------
DISSOLVED INORGANIC NITROGEN (N03+NH3) LOAD (kgms/day)
OQ
c
to
S O
C H-
01 CO
7? CO
n> o
00 M
o <
3 (D
a.
< a
ro o
» 00
M a
-J O
Co
I 3
I-1 H-
vo rt
Ui O
" 1
I-1
o
(X
o
M>
rf
(D
I I I 1 I I I I
-------
MUSKEGON RIVER
at the mouth
1972
1973
1974
1975
Figure 63. Total phosphorus load of the Muskegon River, 1973-1975.
-------
Table 22. ESTIMATED TOTAL YEARLY NUTRIENT LOADS TO MUSKEGON LAKE,
1972-1975 IN THOUSAND KILOGRAMS PER YEAR
M
-P-
Total Phosphorus
Municipal & Non-Point
Year Industrial Muskegon River
1972
1973
1974
1975
58.7
(47.1%)
27.9
(26.9%)
5.1
(4.8%)
5.0
(3.4%)
65.8
(52.9%)
75.3
(72.6%)
98.95
(93.7%)
140.8
(95.5%)
Spray-Site
Drainage Total
0 124.5
.5 103.7
(.5%)
1.55 105.6
(1.5%)
1.55 147.4
(1.1%)
Dissolved Inorganic Nitrogen
Municipal &
Industrial
445
(61.8%)
264
(47.8%)
45
(8.1%)
9
(1.1%)
Non-Point
Muskegon River
275
(38.2%)
282
(51.1%)
454
(81.4%)
747
(87.8%)
Spray- Site
Drainage Total
0 720
6 552
(1.1%)
59 558
(10.5%)
94 850
(11.1%)
-------
were estimated from Table 19 and adjusted to reflect their actual dura-
tion of discharge. Spray-site loads were estimated from operating data
presented in Appendix E. The non-point sources of nutrient loads from
the Muskegon River were estimated using Muskegon River data which was
not influenced by point industrial or municipal sources. The loads
represent unidentified upstream loads which the authors chose to charac-
terize as non-point. The calculations of the total loads to Muskegon
Lake in this table did not include minor tributary drainage, urban run-
off, or atmospheric inputs. A 1972-73 investigation by the USEPA (1975c)
estimated that these nutrient sources amounted to only 1 or 2% of the
total nitrogen and phosphorus load to Muskegon Lake.
The contribution of atmospheric inputs can be estimated from data collected
by Johnson (1976). Using an average atmospheric phosphorus input of
20 kg P/km2/yr, the total yearly contribution from the atmosphere is
calculated to be 336 kg P/yr. This is an insignificant amount. The
source of nutrients originating from storm runoff have been roughly
estimated (without supporting data) by the Western Michigan Shoreline
Federal 208 Planning Agency. This discharge into Muskegon Lake was
through two primary drains, Four Mile Creek and Ruddiman Creek. This
preliminary data suggest that the urban storm-runoff phosphorus load could
be as much as 9% (9200 kg P/yr) of the total system load (Weaver, 1976).
This is not in agreement with the USEPA estimate. Direct measurements
are needed to quantify this source.
A second calculation performed on the data was intended to normalize the
river loads to average flow conditions. The loads were normalized by
multiplying each yearly average load by the ratio of the 52-year average
annual flow to the specific annual average flow. This technique will
normalize the effects of changing flow, but it does not normalize the
effect of the variable intensity of the non-point source loads associated
with changes in flow. The results of the normalized flow calculations
are given in Table 23.
The potential effectiveness of the sewage diversion can be evaluated
based on the four years of data collected on nutrient loads to Muskegon
Lake. If 100% of the measured point discharge loads were eliminated, a
38% reduction in total phosphorus and 50% reduction in dissolved inorganic
nitrogen is expected. These estimates were derived by averaging the
non-point Muskegon River loads for'1972 to 1975 (Table 22 and comparing
this to the industrial and municipal pre-diversion point discharges.
(This does not include the unquantified storm water source or spray
site drainage). If the normalized tributary loading data are used in
this calculation instead of the observed loads, the percentage reductions
calculated are 39% for total phosphorus and 52% for dissolved inorganic
nitrogen. The nutrient load reduction expected in the Muskegon River
load alone was 27% for phosphorus and 47% for dissolved inorganic nitrogen.
These estimates were calculated using the normalized tributary loads.
A comparison of the above calculation with data collected by the USEPA
147
-------
Table 23. NORMALIZED YEARLY AVERAGE MUSKEGON RIVER LOADS IN KILOGRAMS PER DAY
Nitrate
Total +
Phosphorus Ammonia
Station Year as P as N
Muskegon River 1972 290 1970
(at mouth) 1973 340 1030
1974 210 1090
1975 320 I860
Muskegon River 1972 180 770
(Station 102) 1973 150 580
1974 240 970
1975 360 1790
Muskegon River 1973 130 590
(Station 143 1974 140 990
1975 210 1610
-------
(1975c) was not possible because the USEPA incorrectly surveyed and iden-
tified the municipal discharges and had no information on industrial
discharges. It should be emphasized that a large share of the phosphorus
reduction resulting from the Muskegon Wastewater Treatment Plant diver-
sion was soluble reactive phosphorus. This form is considered to be
immediately available for algal uptake.
Silicon and chloride loads were observed to increase between 1973 and
1975. The silicon loading from the Muskegon River was 14,200 kg/day
in 1973; 20,600 kg/day in 1974; and 28,600 kg/day in 1975. The
chloride load was 110,000 kg/day in 1973; 150,000 kg/day in 1974; and
197,000 kg/day in 1975. These increases are primarily a reflection
of the increased flow.
The actual measured yearly average nutrient loads were compared to eval-
uate the effectiveness of the diversion spray-irrigation project. Exam-
ining the non-normalized load data in Table 22, a decrease in nutrient
(total phosphorus and inorganic nitrogen) loads is seen in 1973 and 1974
but an increase is observed in 1975. This trend is also observed if
normalized load data are used. The approximate 20 to 25% reduction is
probably a reflection of the sewage discharge diversion. The percentage
reduction was not the anticipated 39% phosphorus and 50% dissolved
inorganic nitrogen reduction. Differences in flow and in non-point
loads cause this deviation. A low flow year occurred in 1972 and thus
the pre-diversion calculated loads are likely to be lower than the aver-
age. The increase in load observed during 1975 is coincidental to the
nutrient spray-irrigation project. An evaluation of the calculated loads
at the two upstream stations on the Muskegon River demonstrate this.
This is further supported by previous analysis of river concentration
data. The increase in the 1975 load is a consequence of increased
flow and increased concentration upstream of the discharge site.
The nutrient load calculated at Station 143 represents nutrients derived
from unidentified upstream sources. The differences between the loads
at Stations 143 and 102 should reflect the effect of the spray-irrigation
drainage. From these data it is seen that the increase in loads observed
in 1975 at the river mouth can be accounted for by an increase in load
from upstream sources. No dramatic change in load was observed below
Station 143 except for the influences of former point discharges. A
small portion of the 1975 increase in load could be a consequence of
the availability of loading data for 1975, which did not include the
fall period. The 1975 loading increase is also observed in a seasonal
analysis of the data.
No conclusive effects on receiving water quality were observed to result
from the spray-irrigation drainage. Dissolved inorganic nitrogen loads
did not increase downstream of the Mosquito Creek discharge. Total phos-
phorus loads were noted to increase but this was not definitely related
149
-------
to the diversion project. The drainage from the irrigation site was
measured by Muskegon County and found to be relatively low in phosphorus
with a concentration similar to that of the upstream Muskegon River waters.
The increase in load from the high nitrogen waters of Mosquito Creek
was not dramatic because of the low flow contribution. Calculations of
yearly and monthly nutrient loads from the spray site drainage is avail-
able in Appendix E. These loads are compared to the other point and
non-point loads in Table 22. The spray drainage phosphorus load was at
most 1.5% of the total lake load; the dissolved inorganic nitrogen load
was at most 11%.
In all prior discussions average yearly loading data were used for an-
alysis. The reasons for this approach have been previously described.
If loading data were evaluated seasonally, the calculated percentage
reduction from the sewage diversion project would vary slightly. Exam-
ining the loading data for the months June through September, the
potential percentage reduction is calculated to range from approximately
30 to 45% depending on the year. Averages for the spring period show
potential percentage reductions of the same order of magnitude. Similar
calculations for dissolved inorganic nitrogen show potential reductions
in the summer to be as much as 50 to 60% depending on the year and in
the spring a much lesser percentage.
An additional evaluation of the effectiveness of the diversion project
was made by comparing the flow weighted average tributary concentrations
resulting from the calculated nutrient loads (see Table 24). These data
indicate that a reduction in nutrient concentrations in Muskegon Lake
is expected as a consequence of the diversion. The increase in calculated
concentration for 1975 is not believed to be a consequence of the diver-
sion spray-irrigation program.
An additional quantitative evaluation of the effect of the observed nu-
trient loads to Muskegon Lake can be obtained using the Vollenweider
(1975) model. This model was briefly discussed in the section on nu-
trient loads to White Lake. A load greater than the model-defined danger-
ous rate represents one causing or maintaining eutrophic conditions
while a loading rate below the permissible rate represents a condition
suitable for maintaining oligotrophic conditions. A loading rate be-
tween tha two would be considered consistent with a mesotrophic system.
In Muskegon Lake the permissible rate is calculated to be 1.08 g P/
while the dangerous rate is 2.16 g P/m^/year. The pre-diversion phos-
phorus load to Muskegon Lake is 3.7 times greater than the dangerous
rate and 7.4 times greater than the permissible rate. According to this
model the reduction in phosphorus load resulting from the diversion pro-
ject is not sufficient to correct the eutrophication problem in Muskegon
Lake.
150
-------
Table 24. FLOW WEIGHTED AVERAGE CONCENTRATIONS OF TOTAL
PHOSPHORUS AND DISSOLVED INORGANIC NITROGEN
IN TRIBUTARIES TO MUSKEGON LAKE
Year
Total Phosphorus
(yg P/A)
Dissolved Inorganic Nitrogen
1972
1973
1974
1975
65.8
39.8
38.2
56.0
382
213
204
325
151
-------
The rate at which nutrients are leaving the system can be calculated by
multiplying the channel concentration by the flow from the lake. A
summary of these flux calculation with comparisons to the nutrient loads
to Muskegon Lake is given in Table 25. The calculated lake retention
of phosphorus is low, particularly in contrast to White Lake and other
eutrophic systems. This may be a response of the system to non-steady
state conditions, intermittent mixing, or shipping traffic. It is
possible that the effects of reduction in nutrient load can be affected
by phenomena such as sediment nutrient release which tend to buffer
the system. This may have been observed in 1973 when a reduction in
phosphorus load to the lake occurred. The percent retention in 1973
was negative indicating a nutrient contribution from within the lake.
The dissolved inorganic nitrogen retention was calculated to be less
during the post-diversion period. This observation is impossible to
evaluate without information on total nitrogen because of the effects
of algal uptake and ammonification. No change in retention of dissolved
silicon was observed. The high retention of silicon was a likely conse-
quence of algal uptake of the dissolved silicon.
Summary — The Muskegon River is the major hydrologic and tributary nu-
trient source to Muskegon Lake. The former municipal and industrial
discharges were found to be significant contributors of nutrients to
Muskegon Lake. Estimates of the potential nutrient load reduction result-
ing from the diversion program are 38% for phosphorus and 50% for dissolved
inorganic nitrogen. Approximately 20 to 25% reduction in nutrient loads
was actually observed following diversion. The difference is attributed
to variation in river flow and non-point loads during the period of the
investigation. Lower phosphorus, ammonia, and iron concentrations were
observed immediately subsequent to diversion. The effects of changing
non-point nutrient loads to Muskegon Lake were observed (particularly
in 1975) to have the potential to partially or completely mask the
nutrient reduction resulting from the diversion project. Calculations for
Muskegon Lake using the Vollenweider model suggest no anticipated change
from its present eutrophic status.
LAKE-RELATED CONSIDERATIONS
Spatial and Seasonal Distributions — In a manner similar to that for
White Lake, two stations in Muskegon Lake (Stations 103 and 106) were
selected for the evaluation of horizontal variation in chemical char-
acteristics. The total dissolved phosphorus and total inorganic nitrogen
data were evaluated (see Figures 64 and 65). Station 103 is located
in the extreme eastern portion of Muskegon Lake and is influenced by the
Muskegon River, an important tributary. Station 106 is located in the
western portion of the lake and should reflect overall conditions.
152
-------
Table 25. A SUMMARY OF THE YEARLY AVERAGE FLUX OF NUTRIENTS
LEAVING AND ENTERING MUSKEGON LAKE
IN KILOGRAMS PER DAY
Nitrate
Total +
Phosphorus Ammonia Silicon
Year as P as N as Si
Leaving 1972 260 1100 5400
1973 360 700 6200
1974 260 1200 10000
1975 340 2100 18900
Entering 1972 340 1900
1973 280 1500 14200
1974 290 1500 20600
1975 400 2300 28600
Percent 1972 24% 43%
Retained in 1973 -28% 46% 49%
Muskegon Lake 1974 11% 20% 49%
1975 15% 9% 34%
153
-------
MUSKEGON LAKE
Station 103
Station 106
2 Meter Average
1972
1973
1974
1975
Figure 64. Total dissolved phosphorus concentrations at
Stations 103 and 106 in Muskegon Lake, 1972-1975.
-------
Ul
J500
UJ
0400
^300
<
o
cr
o
2200
Q
UJ
CO
Q
100
0 I—1—I—I—I—I—1
A
MUSKEGON LAKE
o Station 103
o Station 106
2 Meter Average
1972
1973
1974
1975
Figure 65. Dissolved inorganic nitrogen concentrations at Stations
103 and 106 in Muskegon Lake, 1972-1975.
-------
An examination of total dissolved phosphorus data reveals that concen-
trations at Station 103 are generally higher than those at Station 106.
Levels are usually 30 to 50% higher at Station 103, but twofold elevations
were observed. The higher concentrations at Station 103 reflect the in-
fluence of the Muskegon River, the largest contributor of phosphorus
to the lake and algae uptake between Stations 103 and 106.
Dissolved inorganic nitrogen concentrations were quite similar at Sta-
tions 103 and 106. The exception was during the summer months when
Station 103 had concentrations of total inorganic nitrogen 100-150 ug N/£
greater than Station 106. It is postulated that this is also a result
of the influence of the river. The Muskegon River contributes waters
with very high levels of nitrate and ammonia. The excess dissolved
inorganic nitrogen is utilized by algae with passage through the lake
and has disappeared by the time it reaches Station 106. The difference
is not as notable during the spring and fall because of the large influx
of inorganic nitrogen from the bottom waters due to mixing.
Surface water (2m) concentrations of nitrate (N0~ + N0~) in Muskegon
Lake are a function of loading, algal uptake, and replenishment from the
bottom waters. Maximum concentrations (200-400 yg N/£) of nitrate
occur in the winter (December through March) during high load and low
uptake periods. These levels are rapidly reduced during the spring
(March to June) (see Figure 66). Surface water nitrate concentrations
approach zero during the summer due to algal uptake. Peak surface water
ammonia concentrations occur during the winter months when phytoplankton
uptake is low (see Figure 67). During the spring and summer months algal
assimilation reduces ammonia concentrations to near the limit of detec-
tion. Short-term increases in summer surface water ammonia concentra-
tions are probably due to the transfer of ammonia from the bottom waters
during temporary periods of disruption of thermal stratification resulting
from storms or ship traffic. At times higher surface water concentra-
tions of ammonia were observed for Muskegon Lake than for the Muskegon
River, its major tributary.
Nitrogen-fixation, thermocline disruption, and other processes are the
likely cause of this phenomenon. The surface water inorganic nitrogen
depletions observed in Muskegon Lake present the possibility that, like
White Lake, the Muskegon Lake system is nitrogen limited. This is supported
to an extent by the presence of nitrogen-fixing blue-green algae. A
USEPA (1975c) bioassay study also confirmed this hypothesis.
Nitrate concentrations in the bottom waters follow a cycle of depletion
and replenishment. The pattern is closely tied to surface water dynamics.
Bottom water nitrate concentrations start from very high levels
(200 - 400 yg N/£) which are a result of elevated winter loads, nitri-
fication and low plant uptake. Nitrate then rapidly decreases to near
zero levels in the spring due to algal uptake. The spring phytoplankton
156
-------
Ul
MUSKEGON LAKE
2 Meter
Bottom
Station 106
1972
1973
1974
1975
Figure 66. Nitrate concentrations in Muskegon Lake, 1972-1975.
-------
CO
800
600
g 400
O
5
< 200
MUSKEGON LAKE
o 2 Meter
a Bottom
Station 106
1972
1973
1974
1975
Figure 67. Ammonia concentrations in Muskegon Lake, 1972-1975.
-------
bloom has an effect on the bottom waters only until such time as strati-
fication occurs. With the onset of stratification bottom waters are no
longer effected by uptake. Nitrate concentrations are occasionally
replenished by nitrification. Dissolved oxygen was often available in
the hypolimnion at depths greater than 1 meter from the bottom. Waters
significantly above the lake bottom are affected less by sediment oxygen
demand and more by sporadic mixing with the epilimnion. Temporary but
frequent disruptions of the thermocline were observed resulting from
ship traffic, storms, or other environmental phenomena (See Figure 68).
The introduction of oxygen containing epilimnetic waters and intrusion
of Lake Michigan waters (high in dissolved oxygen and nitrate) were
sufficient to support nitrate concentrations in the bottom waters,
permit some nitrification and retard or prevent significant denitrifica-
tion. Later in the period of stratification the oxygen content of the
hypolimnion is further reduced and some denitrification may occur. The
result is a short-lived decrease in bottom water nitrate concentrations.
During and after turnover nitrate is replenished in both surface and
bottom waters through nitrification of hypolimnetic ammonia.
Ammonia concentrations in the bottom waters increase as a result of or-
ganic decomposition (largely during the anoxic summer months) and de-
crease with nitrification, and the mixing and assimilation period. Very
high levels of ammonia (400 - 700 yg N/Jl) are generated in the bottom
waters of Muskegon Lake during the summer months. Nitrogen flux (trans-
fer between forms) in Muskegon Lake approaches 1 mg N/£ in a given
season. The magnitude of the nitrogen dynamics (winter nitrate peaks,
ammonia buildup in summer, assimilation, nitrification) is notably
similar for Muskegon and White Lakes.
As was the case with White Lake, three forms of phosphorus were measured
for Muskegon Lake: soluble reactive, total dissolved, and total phos-
phorus. Generally the soluble reactive phosphorus accounted for much
less than half of the dissolved component and the total dissolved
phosphorus represented approximately one-third of the total phosphorus
in the lake. The remaining two-thirds, the particulate fraction, in-
cludes organisms and detritus.
Concentrations of soluble reactive phosphorus and total dissolved phos-
phorus in the surface waters at 2 meters followed similar seasonal
patterns (see Figures 69 and 70). Levels of total dissolved phosphorus
are highest (30 - 40 yg P/£) during the winter months (December through
March) and then decrease during the spring and summer to concentrations
of 5-10 yg P/£. The supply of total dissolved phosphorus in the sur-
face water is never reduced below 5 - 10 yg P/SL, indicating that this
nutrient may not become limiting in Muskegon Lake. Soluble reactive
phosphorus concentrations, although following a similar pattern, are
generally lower (below 7 yg P/&). The levels of soluble reactive
159
-------
MUSKEGON LAKE
Station 106
Bottom Water
Intrusion
I I I I II
1972
1973
1974
1975
Figure 68. Dissolved oxygen in the bottom waters of Muskegon Lake, 1972-1975.
-------
-*
fc
o>
Jt
D
a:
o
Q_
cn
o
Q.
UJ
50
Ld
or
y
00
MUSKEGON LAKE
Station 106
o 2 Meter
o Bottom
25
0
1972
1973
1974
1975
Figure 69. Soluble reactive phosphorus concentrations in Muskegon Lake, 1972-1975,
-------
f50
or
o
EL 40
(/)
o
0
i ' i i I ' l l l i I I I I
MUSKEGON LAKE
o 2 Meter
o Bottom
Station 106
1972
1973
1974
1975
Figure 70. Total dissolved phosphorus concentrations in Muskegon Lake, 1972-1975.
-------
phosphorus in surface waters are reduced to zero. The question of limi-
tation by phosphorus then becomes one of the availability of the
dissolved organic phosphorus fraction. This phenomenon is thought to
be species specific (Keenan and Auer, 1974) and would require further
investigation before any conclusions could be made.
Surface water total phosphorus data are somewhat incomplete. It is
observed that surface water total phosphorus peaks occur at approxi-
mately the same time as peaks in phytoplankton abundance (see Figure 71).
Concentrations through the remainder of the year are relatively stable.
Since total phosphorus is the sum of the dissolved and particulate frac-
tions, it should remain somewhat constant through the year while the
relative contribution of the components change. Flux of phosphorus
from the sediments to the biota and back to the sediments later in the
year accounts for some of the seasonal variation in this parameter, along
with variations in loads.
Bottom water concentrations of dissolved phosphorus in Muskegon Lake
do not fluctuate as radically as those observed in White Lake. Summer
peaks in dissolved (both total and soluble reactive) phosphorus were
noted, but the frequency and particularly the magnitude of the peaks were
reduced in comparison to White Lake. It is postulated that the reason
for this is that the disruption of stratification by storms and the in-
trusion of well-oxygenated Lake Michigan water reduced both the duration
and extent of oxygen depletion in the hypolimnetic waters; this results
in the iron being maintained in the sparingly soluble ferric form.
During the summers of 1973-1975 the release of dissolved iron to both the
surface and bottom waters was noted (see Figure 72). This phenomenon
was noted earlier in relation to nitrification processes in the bottom
waters of Muskegon Lake. During the spring, late fall, and winter, bottom
and surface dissolved phosphorus concentrations are quite similar. The
fall peak in total phosphorus in 1973 is due to the particulate fraction;
it is not clear why this peak is so much larger than peaks in other
years.
Silicon concentrations in Muskegon Lake follow one of the most consistent
seasonal patterns observed. Surface water values increase through the
fall and winter months to a peak of 3 to 4 mg/£ in March. The spring
diatom bloom then depletes this concentration through the spring and
early summer to a minimum value of 0.5 to 1.0 mg/& in June or July.
Silicon levels remain low during the summer and early fall and then
begin the replenishment period. Silicon barely reaches levels approach-
ing limitation in Muskegon Lake (30 - 50 yg/£) (see Figure 73).
Peaks in primary productivity did not follow chlorophyll a patterns in
Muskegon Lake nearly as well as in White Lake (see Figures 74 and 75).
Chlorophyll a, instead of producing a single (unimodal) peak, varied
throughout the spring and summer of 1973-1975 in a more polymodal fashion.
163
-------
240
~ 200
CJ>
~ 160
en
ID
cc.
o
CL 120
en
o
CL
-J 80
40
i i i i i I i I I I I I I i i i I I I l
MUSKEGON LAKE
o 2 Meter
o Bottom
Station 106
1972
1973
1974
1975
Figure 71. Total phosphorus concentrations in Muskegon Lake, 1972-1975,
-------
140
120
-100
80
60
Q
LU
cn 40
en
20
I I I i I l l l i i i I
MUSKEGON LAKE
o 2 Meter
D Bottom
Station 106
1972
1973
1974
1975
Figure 72. Dissolved iron concentrations in Muskegon Lake, 1972-1975.
-------
MUSKEGON LAKE
2 Meter Average
1972
1973
1974
1975
Figure 73, Dissolved silicon concentrations in Muskegon Lake, 1972-1975,
-------
MUSKEGON LAKE
2 Meter Average
1972
1973
1974
1975
Figure 74. Chlorophyll a concentrations in Muskegon Lake, 1972-1975.
-------
.
120
100
> 80
o
M g 60
Q\ L_J
oo o
OC
Q-
> 40
CE
20
0
-------
Data for 1972 showed only a single peak; however, sampling frequency
may not have been adequate to identify other peaks. From an examination
of chlorophyll a data alone, one might suggest the development of a
bimodal (fall/spring), diatom dominated phytoplankton. The primary pro-
ductivity values, however, display unimodal (late summer, early fall)
peaks. The unimodal primary productivity patterns, at the peak, repre-
sent the point in time where the combination of standing stock, light,
and nutrients is optimum. Obviously, it is not required that this match
the chlorophyll a peaks.
Nutrient ratios of dissolved inorganic nitrogen to total dissolved phos-
phorus were calculated for Muskegon Lake as they were for White Lake.
The winter N/P ratio in the surface waters was 13-14:1 in 1974 and 1975
The bottom water winter N/P ratios were 27-30:1 for this same period.
These ratios indicate stoichiometric phosphorus limitation in the euphotic
zone but are approaching nitrogen limitation in the surface waters.
Nitrogen levels are generally higher than phosphorus levels in the winter
since the iron-phosphorus dissolution mechanism is inoperative with
oxygen present.
The summer surface N/P ratios in Muskegon Lake reach levels of 1:1 or
less. This is due to the total depletion of nitrate and the reduction
of ammonia to levels below the limit of detection. Muskegon Lake waters
are then nitrogen limited in the summer months. The ratio of winter
dissolved inorganic nitrogen to summer total dissolved phosphorus in the
bottom waters was 19:1 in 1974 and 15:1 in 1975. Again these are values
slightly indicating phosphorus limitation but approaching nitrogen limi-
tation.
Another analysis of N/P ratios can be made by examining the system loads.
Although this does not consider such factors as system recycle or reten-
tion, it is still a useful technique. Calculation of the N/P ratio
based on average yearly loads result in ratios of 5 to 10:1 This
indicates a well-balanced to nitrogen limited nutrient status. Analyses
of the spring loading data suggest slightly higher ratios favoring
stoichiometric nitrogen limitation. The summer nitrogen limitation
which was suggested by summer loading N/P ratios and lake surface water
N/P ratios is further supported by USEPA (1975c) bioassay studies and
the presence of nitrogen-fixing blue-green algae.
Long-Term Changes — Average annual values for selected major phytoplankton
nutrients were calculated for Muskegon Lake (see Table 26) and significant
temporal trends were observed. Average surface water ammonia levels
decreased 44x! in the period following wastewater diversion while average
surface nitrate concentrations increased 98%. Bottom water average
concentrations decreased 53% and nitrate concentrations increased
This resulted in a net increase in surface dissolved inorganic
169
-------
Table 26. AVERAGE ANNUAL VALUES FOR SELECTED WATER QUALITY
PARAMETERS IN MUSKEGON LAKE, 1972-1975
—I
o
Ammonia
Year (yg N/A)
1972
1973
1974
1975
1972
1973
1974
1975
68
42
37
38
237
141
146
111
Nitrate
(yg N/A)
68
64
91
135
90
77
111
146
Dissolved
Inorganic
Nitrogen
(yg N/A)
136
106
128
173
327
218
257
257
Total
Dissolved Total
Phosphorus Phosphorus
(yg P/A) (yg P/A)
Surface
33
20
13
15
Bottom
44
25
16
14
67
58
37
42
77
73
42
45
Soluble
Reactive Secchi
Phosphorus Chlorophyll & Disc
(yg P/A) (yg/A) (m)
20 25.2
7 16.5
5 11.0
4 9.5
13
15
1.47
1.53
1.57
1.58
-------
nitrogen and a net decrease in same in the bottom waters. Analysis of
river loadings indicates that the changes in dissolved inorganic nitrogen
reflect an increase in oxidation. This may result either from improved
nitrification of the ammonia in wastewater aeration lagoons or by soil
microorganisms on the disposal site. The net result of this would be
favorable as a reduction in nitrogenous biochemical oxygen demand in the
lake should be realized. A reduction in oxygen demand could reduce the
duration of hypolimnetic anoxia and ultimately lessen phosphorus flux
from the sediments. Analysis of the lake dissolved oxygen data show
a possible improvement in hypolimnetic dissolved oxygen concentrations
(see Figure 68).
A significant reduction in phosphorus concentrations was observed. Total
dissolved and soluble reactive phosphorus were reduced 55 and 80% in the
surface waters and 68 and 69% in the bottom waters. The reduction in
phosphorus concentrations is supported by loading data. Such reductions
may be the result of the ability of soils (at the disposal site) to
retain phosphorus, a process not applicable to inorganic nitrogen.
These levels of dissolved phosphorus are approaching the point where
they may govern phytoplankton production.
No significant changes were observed in primary productivity levels in
the period following diversion. Significant reductions in chlorophyll a
levels were noted, although this had limited effect on water clarity
(Secchi disc). This observation is supported by data from studies
by Dillon and Rigler (1974 and 1975). As shown in Figure 76 Secchi disc
is insensitive to fractional changes in chlorophyll a at the levels
observed in Muskegon Lake. The system has» however, moved to a condition
which is more sensitive to further change. The chlorophyll a reduction
required to increase the average summer Secchi disc reading by one meter
would be an additional 50 to 70% over 1975 values (see Figure 76).
The total phosphorus reduction necessary (see Figure 77) would be approx-
imately 40 to
Summary — The reduction in nutrient load to Muskegon Lake as a result
of the diversion project was expected to be 38% for total phosphorus and
48% for dissolved inorganic nitrogen. The actual observed load reductions
were only 20 to 25% for total phosphorus and inorganic nitrogen because
upstream loads had increased. The average nutrient and water quality
conditions for Muskegon Lake for 1972 and 1975 are presented in Figure 78
along with data from Lakes Michigan and Erie for comparison.
Muskegon Lake data on nutrients, chlorophyll a, and Secchi disc reveal
that significant reductions, particularly in phosphorus were achieved.
This resulted in a large reduction in chlorophyll a. The reduction in
chlorophyll a was not reflected in water clarity. The system has, however,
been shifted into a more sensitive condition where further changes will
increase Secchi disc depths. The change in chlorophyll a coupled with
the expected reduction in biological oxygen demand load has resulted in
increased levels of dissolved oxygen in the hypolimnion.
171
-------
a Dillon and Rigler
Muskegon Lake,
2 meter summer —
average
1975 ~ a
I973AAI974
a A a
10 20
CHLOROPHYLL a (/ig/1)
Figure 76. Correlation between chlorophyll a and Secchi disc
(after Dillon and Rigler, 1975).
172
-------
SUMMER CHLOROPHYLL a
00
C
n
n>
VJ
O rt
L •l ^t
(-> O
M 3
O
3 O*
(D
(U rt
3 <
CL n>
(D
pd 3
H-
00 T)
(T> O
1 W
(-• O
VD i-(
•^ C
*^ CO
»— '
• (U
en
O
3-
O
I
3
r~ _
?°
o
O)
~D
O
3D
O
o
o
O
O
O
O
O
^ D
S5
S 6"
a
Q
O 3
3 CL
-------
100
80
60
40
20
o
-
50
- Mu 40
1972
r—i WLE
-
Mu
1
97
5
30
20
SLM -__ 10
nGTB
n
_
- Mu
1972
-
-
Mu
197
I3U
V
5
/LI
r 100
50
SLM
nGTB
n
r n
i 1
176
Mu
-1972
Mu
:ni
>LM
nGTB
n
TOTAL PHOSPHORUS (/tg P/J) TOTAL DISSOLVED PHOSPHORUS AMMONIA (fj.g N/l)
250
200
150
100
50
O
-
—
—
-Mu
30
WLE
Mu
1975
1972
-n
•••
SLM 20
n PTR
p— i
10
o
" Mu
1972
r-
—
_
—
Mu
12
8
1975 WLE 4
SLMrTB
nGTB
n n
-
-
s
_
• M mil i
Mu ™"f-
-1972 '975 WLE
nnn
GTB
LM
NITRATE (
CHLOROPHYLL a
SECCHI DISC (m)
LEGEND: Mu 1972* Muskegon Lake 1972 , Mu 1975 = Muskegon Lake 1975, WLE= Western Lake Erie
SLM'Southern Lake Michigan, GTB *Grand Traverse Bay
MUSKEGON LAKE
Figure 78. Pre- and post-diversion status of selected two-meter, yearly average
water quality parameters in Muskegon Lake.
-------
SECTION X
MONA LAKE
INTRODUCTION
Mona Lake is the smallest and southernmost of the three study lakes (see
Figure 6). It is a very narrow, riverine lake, with a length of about
6.5 kilometers and a maximum width of 0.5 kilometers. The lake covers
an area of 2.8 km2 and has a mean depth of 4.1 meters and a volume of
1.15 x 107 m3. The maximum lake depth is 12.8 meters (USEPA, 1975d).
The lake has very limited shallow littoral areas due to rapid shoreline
drop off.
The lake receives flow from several tributaries of which Black Creek
and Little Black Creek are the most significant. Mona Lake is connected
to Lake Michigan via a small channel. The channel is barely navigable,
even by small pleasure boats.
The area surrounding Mona Lake is primarily residential. The lake is
influenced by the urbanized area of Muskegon Heights. Little Black Creek
flows through this area. Numerous industries and the Muskegon Heights
Wastewater Treatment Plant have discharged to the lake by this creek.
Detailed information on these discharges is given in Appendix F.
TRIBUTARY-RELATED CONSIDERATIONS
Hydrology — The Mona Lake drainage basin is the smallest of the Muskegon
Lakes' basins with an area of 212.4 km2. The entire basin is within
Muskegon County. Although several small creeks empty into the lake,
only Black Creek and Little Black Creek are of sufficient size to merit
monitoring. Black Creek is the largest tributary to Mona Lake; it drains
159.5 knr and discharges an average flow of 1.28 m3/sec (see Table 27).
Little Black Creek drains 15.5 km2 and discharges an average flow of
0.15 nrYsec. The remainder of the drainage, 34.6 km2, is estimated to
contribute a yearly average flow of 0.30 m3/sec. The average tributary
discharge flows given in Table 27 were extrapolated by USGS from data
collected on 14 dates during 1972 and 1973. Average flows during the
data collection period were nearly double the reported long-term average.
Information regarding the daily flow in Black and Little Black Creeks
has not been gathered regularly by the USGS. No regular USGS gauging
stations exist on rivers in the Mona Lake basin. To calculate the Black
Creek flows on specific dates during this investigation, USEPA data were
correlated with USGS flow measurements of the Muskegon River at Newaygo.
A factor was then used to convert Muskegon River USGS gauged flow to an
estimate for Black Creek flow on a specific date. The factor used was
0.025. A similar correlation for Little Black Creek was developed using
175
-------
Table 27. MONA LAKE DRAINAGE BASIN CHARACTERISTICS
(PROJECTED LONG-TERM AVERAGE)
Description
Area Percentage Discharge Percentage
(km2) of Total (m3/Sec) of Total
Black Creek
159.5
75.1%
1.28
74.1%
Little Black Creek
15.5
7.3%
0.15
8.6%
Miscellaneous
Tributaries & Direct
Drainage
34.6
16.3%
0.30
17.3%
Lake Surface Area
2.8
1.3%
Total
212.4
100.0%
1.73
100.0%
(Modified from USEPA, 1975d).
176
-------
the Black Lake Creek USGS gauged flow. A factor of 0.769 was derived.
The precision and accuracy of these factors is complicated by numerous
variable point discharges in the Little Black Creek basin and by the
drainage effects of the spray-irrigation site. Corrections for these
effects are extremely difficult and were not attempted. The accuracy
of the correlation is sufficient for evaluation of relative flows and
nutrient loads.
The mean hydraulic retention time for Mona Lake is 76 days (USEPA, 1975d).
This implies that the average hydrologic tributary input to Mona Lake
is sufficient to exchange the total water volume in the lake about five
times each year. This calculation does not account for seasonal varia-
bility or incomplete mixing in the lake.
Concentrations of Chemical Species in Tributaries — The concentration
of various water quality parameters was measured in Black Creek and
Little Black Creek. No other tributary or drainage sources were considered
large enough to monitor. A summary of the water quality findings is
given in Table 28. The concentrations measured in the two creeks were
significantly different and, as such, merit individual discussion.
The water quality observed at the Black Creek mouth was distinctly
different from that observed in the Muskegon and White Rivers. Measured
concentrations of phosphorus and dissolved silicon were similar to the
other rivers; however, nitrogen, iron, and chloride concentrations were
much higher. The total study period averages at the Black Creek mouth
were 50.8 yg P/A, 3.5 yg Si/A, 260 yg NH3-N/£, 651 yg N03-N/fc, 746 yg Fe/A,
and 35.9 yg Cl/£. The elevated nitrate, iron, and chloride concentra-
tions were believed to be an influence of groundwater and non-point sources.
Black Creek is a much smaller tributary than the Muskegon and White Rivers
and is suspected to be dominated more by groundwater infiltration.
Groundwater generally has relatively high nitrate and iron concentrations
compared with surface waters. This is a consequence of a number of
factors including ammonification, nitrification, and redox potential.
The high chloride in the water could also originate from groundwater
or urban runoff. In addition, Black Creek receives seepage from industrial
waste lagoons.
The influence of groundwater on Black Creek is also observed in plots
of the nutrient concentrations measured at Station 27 (Figures 79 and 80).
The seasonal variation in chemical concentrations in Black Creek was less
than that observed for the Muskegon and White Rivers. Figures 81 to
84 are plots of concentrations of various parameters measured at stations
in Black Creek.
During the period of this investigation no significant or conclusive
trends in Black Creek water quality were observed. Major improvements
in water quality were not expected because there were no diversions
of municipal or industrial discharges from Black Creek. The only industrial
177
-------
Table 28. AVERAGE CONCENTRATIONS OF SELECTED CHEMICAL SPECIES IN TRIBUTARIES TO MONA LAKE, 1972-1975
—I
CO
Tributary
Black Creek (at mouth)
(Station 27)
Black Creek
(Station 2)
Black Creek
(Station 25)
Little Black Creek
(Station 26)
Year
1973
1974
1975
1973-1975
1972
1973
1974
1975
1972-1975
1973
1974
1975
1973-1975
1973
1974
1975
1973-1975
Chloride
. (ng Cl/l)
36.9
34.2
36.9
35.9
16.6
11.0
12.8
18.9
14.2
11.7
12.4
10.6
11.6
69.9
86.7
67.0
75.0
Ammonia
(wg N/t)
272
289
207
260
113
107
149
195
141
54
93
102
81
2608
630
436
1314
Nitrate
(wg N/l)
650
646
659
651
811
453
721
719
651
600
785
617
650
5716
5811
4538
5424
Soluble
Reactive
Phosphorus
(ng P/O
10.5
11.7
9.3
10.6
4.9
3.5
2.6
3.7
4.7
5.7
9.7
6.5
530
588
87
429
Total
Dissolved
Phosphorus
(wg P/l)
25
19
18
21
11
11
9
10
10
15
12
18
15
683
585
101
489
Total
Phosphorus
(Wg P/*)
73
37
42
51
20
49
29
27
34
32
35
41
35
1022
922
234
755
Silicon
(mg Si/I)
3.2
3.6
3.5
3.5
4.4
3.6
3.7
3.7
3.8
3.3
3.4
3.1
3.3
3.7
2.9
2.6
3.1
Dissolved
Iron
(wg Fe/t)
246
152
162
182
—
105
353
205
232
123
126
170
138
101
44
57
66
Total
Iron
(wg Fe/1)
796
753
695
746
—
1978
3018
2356
2497
902
1057
871
952
1245
509
661
786
-------
1000
2
LU
O 500
QL
h-
BLACK CREEK
Station 27
o Nitrate
o Ammonia
1972
1973
1974
1975
Figure 79. Dissolved inorganic nitrogen concentrations
in Black Creek, 1973-1975.
-------
oo
o
BLACK CREEK
Station 27
DTP
1972
1973
1974
1975
Figure 80. Phosphorus concentrations in Black Creek, 1973-1975.
-------
230
Black Creek
Station 2
a Total Phosphorus
Total Dissolved Phosphorus
Soluble Reactive Phosphorus
1972
1973
1974
1975
Figure 81. Phosphorus concentrations in Black Creek, 1972-1975.
-------
3000
2600-
2000 -
c
CD
cn
o
oo •*
NJ U
1000-
Black Creek
Station 2
o Ammonia
n Nitrate
1972
973
1974
1975
Figure 82. Dissolved inorganic nitrogen concentrations in Black Creek,
1972-1975.
-------
00
UJ
CO
en
c
o
(
ID
O
to
en
Q
Black Creek
Station 2
° Silicon
JL_i
' ' ' «—I i I I I I
' ' I t I .1—l_l—I—I—J-
1972
1973
1974
1975
Figure 83. Dissolved silicon concentrations in Black Creek, 1972-1975.
-------
00
60
E. 40
o>
O
20
Black Creek
Station 2
o Chloride
O I ' ' ' '' I ' I I I ' I ' ' ' ' ' ' I' I I I I I I I I I I i II I I I I I 8 I till
1972 1973 1974 1975
Figure 84. Chloride concentrations in Black Creek, 1972-1975.
-------
or municipal contamination that Black Creek is known to receive originates
from industrial waste lagoon seepage. Black Creek also receives drain-
age from the spray-irrigation site. One possible temporal trend was
observed for phosphorus. Phosphorus concentrations at both up and
downstream stations were observed to be higher in 1973. This was
not a consequence of the diversion project. No changes in Black Creek
water quality were observed to result from spray-site drainage.
An evaluation of the spatial variation in Black Creek water quality can
provide more information on the relative influence of sources which
contribute materials to the river. Station 27 represents water quality
at the mouth of Black Creek. Station 2 represents upstream water quality
and includes the effects of the spray-irrigation drainage. Station 25
represents the water quality of the headwaters of Black Creek and is a
measure of the effect of the spray-irrigation drainage closer to its
entry to the river. Sample collection upstream of the spray site was
not possible because of the limits of the drainage basin. As a con-
sequence, the influence of the spray-site drainage could not be observed
directly.
Observations of upstream water quality reveal the strong influence
of groundwater. Iron and nitrate concentrations at Station 25 were
very high (approximately 1,000 pg Fe/£ and 650 Ug N/£). As the water
moved downstream however, iron concentrations increased at Station 2
and then dropped at Station 27. This is likely associated with non-point
sources, dilution, oxidation and precipitation. Ammonia concentrations
increased with distance downstream with an associated increase in
ammonia concentrations. This may be a result of biologic activity or
additional contributions of ammonia. Phosphorus concentrations were
noted to increase by 25 to 50% downstream. This is a result of the
increased influence of runoff and possibly seepage from industrial lagoons.
Chloride concentrations also increased with distance downstream again
suggesting groundwater infiltration, salt deposits, urban runoff, or
lagoon seepage.
Concentrations in Little Black Creek were distinctly different from that
observed in Black Creek. During 1973 (the only year including any
observations on Little Black Creek prior to diversion), the concentration
of phosphorus, nitrogen, and chloride were all observed to be much
higher than those measured in Black Creek. Chlorides were approximately
twice as high while phosphorus and nitrogen were an order of magnitude
higher. The average total phosphorus concentration was 1,022 pg P/£
while the ammonia and nitrate concentrations were 2,608 ug N/£ and
5716 yg N/& respectively (see Figures 85 and 86). Little Black Creek
flows through a high industrialized area of Muskegon and, prior to diversion,
received numerous industrial and municipal waste discharges as well as
urban runoff and storm sewer drainage. This influence will be discussed
in more detail in the following section on nutrient loads. The influence
185
-------
12000-
10000 -
8000-
o 6000
4000-
2000-
LITTLE BLACK CREEK
° Nitrate
a Ammonia
1972
1973
1974
1975
Figure 85, Dissolved inorganic nitrogen concentrations
in Little Black Creek, 1973-1975.
-------
oo
2400
Q.
o>2000
g 1600
x
Q.
(f)
§ 1200
800
400
0
LITTLE BLACK CREEK
Station 26
I I I I I I I I I I | I I I I I I I I I I I I I I I I I I II I I I I ! I I I I I
1972
1973
1974
1975
Figure 86. Total phosphorus concentrations in Little Black Creek, 1973-1975.
-------
of these discharges can be readily seen in the data for 1974 and 1975.
During this period the Muskegon Heights Wastewater Treatment Plant was
diverted and other industrial discharges reduced their nutrient input
to the creek. Concentrations of nutrients were much less in 1975; this
was particularly true for phosphorus and iron. No data on upstream water
quality or river mouth water quality were available prior to 1973 to
accurately assess the specific influences of the various municipal and
industrial discharges.
Nutrient Loads — The primary sources of nutrients to Mona Lake are Black
and Little Black Creeks. Municipal and industrial discharges have con-
tributed significantly to the nutrient budget of the lake, although
none discharged directly to the lake, instead Little Black Creek has
received these discharges. The location of these industries is presented
in Figure 87. Other data on these discharges is given in Appendix F.
Other nutrient sources such as minor tributaries, septic tank seepage, and
atmospheric precipitation are difficult to quantify but were considered
minor (USEPA, 1975d).
The tributary nutrient loads to Mona Lake from Black Creek and Little
Black Creek were calculated by multiplying measured concentrations by
flows. The measured concentrations from Little Black Creek were below
the locations of point discharges, urban runoff, and storm runoff. The
water quality measurements, therefore, included the effects from these
sources. Measurements of Black Creek water quality at Station 27 included
the effects of waste lagoon seepage. All flow estimates were based on
limited direct measurements but are acceptable for establishing reasonable
estimates of the nutrient loads. A summary of the yearly tributary
nutrient loads is given in Table 29. Plots of nitrogen and phosphorus
loads to Mona Lake from Black and Little Black Creek are presented in
Figures 88 through 91. No direct monitoring of Little Black Creek water
quality was conducted in 1972.
Nutrient loads from urban storm runoff were suspected to be significant
although direct monitoring of these sources was beyond the study scope.
The Western Michigan Shoreline Federal 208 Planning Agency has roughly
estimated (without site specific data) the contribution of total phosphorus
from storm runoff to Mona Lake to be 4.4 thousand kg P/year (Weaver,
1976). This represents a significant fraction of the total load.
However, over 75% of the storm runoff drains into Little Black Creek
above Station 26. Tributary monitoring at Station 26 was conducted in
both clear and rainy conditions; therefore, this source was included
in the tributary monitoring.
Estimates of the atmospheric nutrient inputs to Mona Lake can be calcu-
lated using data from Johnson (1976) for Saginaw Bay. These data show
that calculated total phosphorus atmospheric inputs to Mona Lake would
be much less than 1% of the total load.
188
-------
N
.Thomas Solvent Co.
////////////////// "ft"""'////// ^Th°TSolve
M W'W////W
Muskegon/^^^^/^^Coil Anodize>\\\
Peerless Products)* \\oAmerican Coil Springs
son D-oducts<>///^vmerjcan\ V\9Fleet Engineers
and Johnsono.\Porcelain \\Y " " '
VEast Shore Chemical^ v x« \\ Enamel
Roosevelt Park//^^/^01"^;1!^0" and Cann-on*'
^Umco \nc.9/// Bennett
Tekmold?. /^^Universal Camshflfto^/^,.^ WJ?r^ ^Cnm-n^H «,„„„ nnlt Cannon^-4
Creek
Industries Communities
o
•
0
-in %
= out \s
1
1 1
80 = in system
Jv=out, but to
xx enter within
20 years
= out, no plan
kilometers
Figure 87. Location and diversion status of point sources and municipalities in the Mona
Lake basin.
-------
Table 29. AVERAGE MONA LAKE TRIBUTARY LOADS IN KILOGRAMS PER DAY
Station
Black Creek
(Station 27)
Black Creek
(Station 2)
Little Black
Creek (Station
26)
Year
1973
1974
1975
1972
1973
1974
1975
1973
1974
1975
Total
Dissolved
Phosphorus
as P
3.6
3.3
3.0
0.5
0.7
0.8
0.7
23.5
7.8
4.0
Total
Phosphorus
as P
9.1
6.9
7.6
1.1
2.9
2.6
2.5
31.9
14.2
8.6
Nitrate
+
Ammonia
as N
121
140
154
55.5
37.2
73.2
83.1
131
133
183
Silicon
as Si
379
505
630
212
215
283
295
66.3
74.3
91.4
Chloride
as Cl
4319
4835
6066
737
658
901
1543
1355
2544
2295
-------
(A
O>
§ 3°°
to
O
z
10
I
Z
200
LLJ
CD
O
o:
f-
o
e>
QL
o
z
Q
UJ
O
to
100
BLACK CREEK
Station 27
i i i i i i i i i i i
I i i i i
i i i i
i i i i i i i i
i i i i i i i
J I
1972
1973
1974
1975
Figure 88. Dissolved inorganic nitrogen load of Black Creek, 1973-1975.
-------
BLACK CREEK
Station 27
1972
1973
1974
1975
Figure 89. Total phosphorus load of Black Creek, 1973-1975.
-------
LITTLE BLACK CREEK
Station 26
1972
1973
1974
1975
Figure 90. Dissolved inorganic nitrogen load of Little Black
Creek, 1973-1975.
-------
LITTLE BLACK CREEK
Station 26
1972
1973
1974
1975
Figure 91. Total phosphorus load of Little Black Creek, 1973-1975.
-------
An evaluation of specific municipal and industrial discharges is diffi-
cult. None are known to have discharged directly into Black Creek except
for the drainage from the spray-irrigation site which began in 1974.
Unquantified sources of contamination originate from industrial lagoon
seepage. Little Black Creek flows through a highly industrialized area
of Muskegon and receives numerous discharges from storm sewers, drains,
etc., not all of which are monitored. Table 30 is a summary of the data
available for discharges from some of these industries and municipalities.
The important discharges are those of the Muskegon Heights Wastewater
Treatment Plant and the Kersman Company (Coil Anodizers). The Muskegon
Heights Wastewater Treatment Plant diverted its discharge in May of 1973.
The Kersman Company discharges high loads of phosphorus to Little Black
Creek and had not diverted its wastes during this study. Since December
of 1974 the Kersman Company has maintained a much reduced phosphorus
loading consistent with federal (NPDES) requirements. The specific data
at which loads were reduced from the 1970 to 1975 level is not known
because operating reports on discharge water quality are not available
prior to December 1974. Information on the other industrial discharges
for the study period is presented in Appendix F. Many of these discharges
have plans to divert to the spray-irrigation system. Loading data was
only available for major industrial discharges.
Yearly average nutrient loads to Mona Lake demonstrate a significant
phosphorus reduction (approximately 60%) between 1973 and 1975. No
1973 to 1975 reduction in load was observed for nitrogen, silicon, or
chloride. Measurements of the actual reduction since 1972 and a subse-
quent comparison between the measured and the anticipated reductions
are difficult because of insufficient pre-diversion data. The original
study plan did not include monitoring on Little Black Creek or the
mouth of Black Creek. An estimate of the 1972 to 1975 reduction can be
obtained from other available data.
The upstream Black Creek nutrient measurements are considered represen-
tative of non-point (non-urban) contamination. Upstream measurements
do, however*include the effects of spray-irrigation drainage. This has
been calculated as 0.44 kg P/day and 7.36 kg N/day for 1973; 0.76 kg P/day
and 40.0 kg N/day for 1974; and 1.07 kg P/day and 52.4 kg N/day for 1975
(see Appendix E). The average of the upstream non-point loads from Black
Creek are 1.8 kg P/day and 37 kg N/day. These loads were also used to
estimate hypothetical Little Black Creek nutrienc loads uneffected by
urban runoff and industrial municipal discharges. The load was corrected
based on a drainage area ratio. The resulting total non-point loads
are for total phosphorus 2.0 kg/day and for dissolved inorganic nitrogen
41 kg N/day. These estimates do not include storm and urban runoff or
waste lagoon seepage.
A comparison of Station 2 and Station 27 loading data indicate that on
the average 5.2 kg P/day of total phosphorus and 75.0 kg N/day of
dissolved inorganic nitrogen are contributed to Black Creek within this
reach. This could result from waste lagoon seepage or other non-point
sources such as storm runoff.
195
-------
Table 30. ESTIMATED MUNICIPAL AND INDUSTRIAL LOADS TO MONA LAKE PRIOR TO DIVERSION IB KILOGRAMS PER DAY*
ON
Source & Location
of Discharge
American Coil Spring
Company, Muskegon
American Porcelain
Enamel Company,
Muskegon
Browne-Morse Com-
pany, Muskegon
Heights
Campbell, Wyant, &
Cannon Company,
Plant tl, Muskegon
Heights
Campbell, Wyant, &
Cannon Company,
Plant #4, Muskegon
Heights
East Shore Chemical
Company , Muskegon
Johnson Products
Company, Muskegon
Kersman Company,
Coil Anodizers
Muskegon**
Muskegon Heights
Wastevater Treatment
Plant, Muskegon
Heights***
Sealed Power Corpora-
tion, Muskegon
Receiving Water
Keating Drain
(Little Black Creek)
Keating Drain
(Little Black Creek)
Merriam St. Sewer
(Little Black Creek)
Little Black Creek
Little Black Creek
Little Black Creek
Keating Drain
(Little Black Creek)
Keating Drain
(Little Black Creek)
Little Black Creek
Little Black Creek
Soluble
Chemical Biochemical Reactive
Oxygen Oxygen Suspended Phosphorus
Demand Demand Solids as P
1.104 0.65 0.78 0.39
3.66 0.81 6.28 0.005
6.85 0.43 0.67 0.97
5.90 — 53.1 0.01
2.54 — 2.22 0.005
3.36 0.74 1.83 0.006
0.56 0.70 0.84 0.005
__ __ _- 24.7
—
5.83 1.94 49.5 0.05
Total
Phosphorus
as P
0.41
0.02
2.27
0.08
0.01
0.006
0.01
35.44
1.59
25.2
96.0
0.02
Dissolved
Inorganic
Nitrogen
as N
1.05
0.06
0.11
1.77
>0.16
1.02
0.07
>30.0
208
193
0.74
Total
Nitrogen
as N
1.09
0.12
0.16
>1.77
>0.16
1.04
0.24
>30.0
319
309
1.14
Date of
Diversion Source
1/75 MWRC 1973
MWRC 1973
4/74 MWRC 1973
MWRC 1973
— MWRC 1973
MWRC 1973
74-75 MWRC 1973
— MWRC 1973
5/73 Musfcegon Ca'75
Muskegon Ca'75
MWRC 1973
*TM.s table does not include industrial outfalls which prior to 1973 discharged to a municipal treatment system. It also does not include Industries which
discharge to private lagoons or septic systems. Nutrient loads to Mona Lake from these latter sources could not be directly quantified. Appendix F con-
tains more information about other industrial outfalls.
**Treatment of wastes improved between 1970 and 1974.
***Two levels of discharge load represent plant operation with and without lime treatment.
-------
The pre-diversion total industrial and municipal point loads are calcu-
lated to be 29.8 kg P/day of total phosphorus and 231 kg N/day of dis-
solved inorganic nitrogen. These were estimated assuming improved treat-
ment of wastes for the Muskegon Heights Wastewater Treatment Plant and
the Kersman Company. Of these discharges all except 33 kg N/day and
1.7 kg P/day were diverted by 1975.
The total average pre-diversion phosphorus load can be calculated by
adding the following components: 1) upstream non-point Black and Little
Black Creek loads, 2) Black Creek downstream non-point loads, 3) direct
discharges, and 4) Little Black Creek storm runoff loads (25% of the
total storm runoff is already included in the Black Creek downstream
loading). The resultant total phosphorus load is 46 kg P/day. The waste
diversion should reduce the phosphorus load by approximately 60%. A
comparison of the 1975 Mona Lake phosphorus loads to the calculated 1972
pre-diversion load shows a reduction of 65%. Using this same methodology
to calculate the post-diversion load the phosphorus load is calculated
to be 19 kgms P/day. This estimate includes storm runoff, non-point
sources, spray drainage, and undiverted point sources. This calculated
load is similar to the 1974 and 1975 measured loads.
Based on the former calculations, future abatement of urban and storm
runoff and waste lagoon seepage could reduce the phosphorus load by
an additional 50%. Future diversion of the remaining point sources
would 'reduce phosphorus loads by an additional 10%.
Calculations of the pre-diversion dissolved inorganic nitrogen load
were conducted using the same techniques. However, only data on total
nitrogen were available for storm runoff (Weaver, 1976). As an approx-
imation, the estimated total storm runoff load of 11.7 thousand kg
N/year was multiplied to 0.75 to estimate the total dissolved inorganic
load. The 1972 pre-diversion load was calculated to be 365 kg N/day.
On this basis the diversion project should have reduced the nitrogen
load by 55%. Abatement of storm and urban runoff and waste lagoon
seepage could reduce the nitrogen load by an additional 50 to 60%.
Abatement of the remaining point sources would reduce the nitrogen
loads by an additional 15 to 20%.
A comparison of the calculated pre-diversion dissolved inorganic nitro-
gen load to the 1975 measured load shows a reduction of only 10%. A
portion of the reduction was negated by the 50 kg N/day load from spray-
site drainage (see Appendix E). Without this the reduction would have
been 25%. An additional portion of the reduction was masked by varying
non-point loads.
The post-diversion dissolved inorganic nitrogen load was calculated
using the above load component analysis; the result was 167 kg N/day.
The measured 1975 load was 337 kg N/day. A large portion of this
discrepancy results from an underestiraation of the non-point nitrogen
load to Little Black Creek. The estimated load was 22 kg N/day; the
197
-------
calculated load obtained by subtracting undiverted point loadings from
the measured Little Black Creek load was 149 kg N/day. The difference
represents unidentified point or non-point sources. Considering this
measured but unidentified load the 1972 pre-diversion load is calcula-
ted to be 492 kg N/day; the potential reduction in nitrogen load as a
consequence of the diversion is then 43%. The observed reduction be-
tween this load and the 1975 measured load is 32%.
Summarized in Table 31 are the calculated annual average nutrient loads
to Mona Lake for 1972 to 1975 based on observed water quality monitor-
ing data, calculated river flows, wastewater discharge data, and the
previous analysis of non-point loading which was used to calculate the
1972 loads because 1972 data on Little Black Creek were limited. The
data in Table 31 depicts a 63% reduction in phosphorus loading and a
32% to 45% (1975 vs. 1974) reduction in nitrogen loading. The exact
percentages of nutrient load reductions are difficult to calculate for
Mona Lake because of uncertainties in non-point loading and the applied
river flow correlations.
Spray-irrigation drainage had small effects on loads to Mona Lake. The
average load expected to originate from this drainage can be calculated
based on Muskegon County measurements of drainage water quality and
estimates of the drainage volume (see Appendix E) . For 1974 and 1975
these calculations suggest a total phosphorus load addition of 0.6 kg
P/day and 45.2 kg N/day of dissolved inorganic nitrogen. The phosphorus
load increase was not observed in any of the yearly comparisons of
Black Creek data; in fact, a reduction was observed. Part of the
anticipated increase in nitrogen load was observed although part of
this increase could have been unrelated to the spray-irrigation program.
A simple and approximate evaluation of the reduction in nutrient input
to Mona Lake can be achieved by calculating the weighted average tribu-
tary concentration resulting from each yearly load. The calculated
concentrations are presented in Table 32. As can be seen from these
data, a significant reduction in lake phosphorus concentrations are
expected. Little can be said regarding nitrogen without information
on total nitrogen.
Further evaluation of the reduction in nutrient loads to Mona Lake can
be conducted using the Vollenweider model (Vollenweider, 1975).
According to this model the minimum eutrophic or dangerous load rate
is 0.92 g P/m /year while the maximum permissible or oligotrophic
loading rate is 0.46 g P/m^/year. The pre-diversion 1972 phosphorus
load to Mona Lake was approximately 6.0 g P/m^/year. It is apparent
that the system is still being loaded with phosphorus at a rate one
order of magnitude greater than the maximum loading rate calculated
to be necessary to achieve oligotrophic conditions. According to this
model the system will maintain in its eutrophic condition despite the
diversion of wastes. A comparison of the Mona Lake load to loads
for other lakes considered eutrophic reveals the pre- and post-diversion
Mona Lake rate to be equal to or larger than those for the other lakes.
198
-------
Table 31. ESTIMATED TOTAL YEARLY NUTRIENT LOADS TO MONA LAKE,
1972-1975 IN THOUSAND KILOGRAMS PER YEAR
Total Phosphorus
Year
1972
1973
1974
1975
Municipal &
Industrial
10.81
(64.7%)
5.45
(36.4%)
1.06
(13.8%)
0.63
(10.6%)
Non-Point
White River
5.9
(33.3%)
9.35
(62.5%)
6.36
(82.6%)
4.89
(82.7%)
Spray-Site
Drainage Total
0.0 16.71
(0%)
0.16 14.96
(1.1%)
0.28 7.70
(3.6%)
0.39 5.91
(6.6%)
Dissolved Inorganic Nitrogen
Municipal &
Industrial
83.21
(46.3%)
42.14
(45.8%)
12.73
(12.8%)
12.32
(10.0%)
Non-Point
White River
96.37
(53.7%)
47.15
(51.3%)
72.29
(72.5%)
91.54
(79.4%)
Spray- Site
Drainage
0.0
2.69
(2.9%)
14.62
(14.7%)
19.14
(15.6%)
Total
179.58
91.98
99.64
123.00
-------
Table 32. FLOW WEIGHTED AVERAGE CONCENTRATIONS OF TOTAL PHOSPHORUS
AND DISSOLVED INORGANIC NITROGEN IN TRIBUTARIES
TO MONA LAKE
Year
1972
1973
1974
1975
Total Phosphorus
(yg P/fc)
379
203
104
83
Dissolved Inorganic Nitrogen
(yg N/a)
3903
1320
1353
1820
200
-------
Table 33 is a total nutrient budget for Mona Lake. The most notable
observation from these calculations is the negative retention observed
for phosphorus in 1975. This suggests a response of the lake attempt-
ing to buffer the effect of the nutrient reduction. It is possibly a
result of sediment nutrient release. This is occurring because of the
reduction in the concentration of phosphorus in the water, which in turn
disturbed the former sediment-water nutrient balance.
Summary — Black Creek is the major hydrologic contributor to Mona Lake.
Little Black Creek was the most significant nutrient source to Mona Lake
prior to diversion and during the post-diversion period was equally as
important as Black Creek. Very high nutrient concentrations were observed
in Little Black Creek which originated from industrial and municipal
discharges and urban runoff. Significant reductions in phosphorus loads
to Mona Lake were observed during the investigation. These were a conse-
quence of the diversion of the Muskegon Heights Wastewater Treatment Plant
discharge and improved treatment by the Kersman Company. The approximate
65% reduction in phosphorus observed was similar to that predicted. For
dissolved inorganic nitrogen a 40 to 55% reduction was expected and the
observed reduction was calculated to be approximately 30 to 45%. The
Vollenweider model predicts no change in the trophic status of Mona Lake.
LAKE-RELATED CONSIDERATIONS
It is important to note at the onset of any discussion of Mona Lake that
the physical, chemical, and biological parameters measured are generally
many times greater than those observed in either White or Muskegon Lakes
which are comparatively much less productive. Additionally, the dominant
species of phytoplankton differ from those observed in Muskegon and White
Lakes: non-nitrogen fixing blue-green algae and centric diatoms for Mona
Lake and nitrogen-fixing blue-greens and pennate diatoms for White and
Muskegon Lakes (USEPA 1975 a,c,d). This is, certainly, a result of chem-
ical differences among the lakes.
Spatial and Seasonal Distributions — To evaluate horizontal distribu-
tions in Mona Lake, the concentrations of total dissolved phosphorus and
total inorganic nitrogen were observed at Stations 3 and 4. The former
station is located at the east end of the lake near the mouth of Black
Creek ( a major tributary to Mona Lake) while the latter station is at
the west end and reflects average lake conditions.
Total inorganic nitrogen values at Stations 3 and 4 fluctuated, but
neither station consistently recorded higher or lower values than the
other (see Figure 92). In the case of total dissolved phosphorus,
surface values at the two stations were quite similar (see Figure 93).
Occasional peaks were observed during the summer and fall in the sur-
face waters of Station 4; probably due to the influence of Little Black
Creek, a major source of nutrients.
201
-------
Table 33. A SUMMARY OF THE YEARLY AVERAGE FLUX OF NUTRIENTS LEAVING
AND ENTERING MONA LAKE IN KILOGRAMS PER DAY
NJ
o
Entering
Leaving
Percent
Retained in
Mona Lake
Year
1973
1974
1975
1973
1974
1975
1973
1974
1975
Total
Dissolved
Phosphorus
as P
27.1
11.1
7.0
16.2
3.8
17.2
41%
66%
-140%
Total
Phosphorus
as P
38.8
21.1
16.2
26.7
13.5
20.3
31%
64%
-25%
Nitrate
+
Ammonia
as N
252
273
333
74
114
141
71%
58%
58%
Silicon
as Si
445
579
721
69
161
438
85%
63%
39%
Chloride
as Cl
5674
7379
8361
4401
5802
8385
23%
21%
0%
-------
S3
O
OJ
1400
1200
2 1000
LU
O
O
cc
t 800
(1617) (1550)
9o o
MONA LAKE
2 Meters
o Station 3
o Station 4
y
z
o
2
o
CO
600
400
200
0
I I I I I I
1972
1973
1974
1975
Figure 92. Dissolved inorganic nitrogen concentrations
at Stations 3 and 4 in Mona Lake, 1972-1975,
-------
N>
O
-P-
MONA LAKE
° Station 3
Station 4
2 Meter
1972
1973
1974
1975
Figure 93. Total dissolved phosphorus concentrations at
Stations 3 and 4 in Mona Lake, 1972-1975.
-------
Vertical and seasonal distribution of chemical and biological parameters
in Mona Lake follows to a large extent many of the classic patterns ob-
served in White and Muskegon Lakes. Surface nitrate levels peak in March
(exceeding 1,000 yg N/£) and then rapidly decline with increasing phyto-
• a?n,?? Producti°n in the spring and early summer. By July (August
in 1974) the nitrate has been depleted (to the limit of detection) and
remains low into the fall. There is no replenishment of surface nitrate
through the summer months (see Figure 94).
Surface water ammonia concentrations vary somewhat, but are generally
quite low compared to bottom water levels (see Figure 95). Spring and
fall peaks in ammonia concentration respond to peaks in loading and
mixing with bottom waters high in ammonia. Accumulation of ammonia in
the surface waters is observed during the period October through February.
This is the result of the introduction of ammonia from the bottom waters
during a period of low phytoplankton activity. Nitrification and phyto-
plankton assimilation quickly reduces these levels to concentrations
approaching the limit of detection. Although nitrate concentrations
are reduced to zero in the surface waters in the summer, this is not
the case for ammonia. The minimum reported summer surface ammonia con-
centrations were: 28.5 yg N/l in 1972, 8.3 yg N/£ in 1973, 9.0 yg N/£
in 1974, and 16.7 yg N/A in 1975. The average summer concentrations
in the surface waters were 2-10 times this value. The surface summer
minimum and surface summer average for ammonia in Mona Lake was twice
the value reported for either White or Muskegon Lakes. The lack of com-
plete depletion of ammonia in the surface waters in the summer may account
for the absence of the nitrogen-fixing blue-green algae as observed
in Muskegon and White Lakes (USEPA, 1975d).
The hypolimnetic waters of Mona Lake become anoxic rapidly during the
spring and remain totally anoxic throughout the summer (see Figure 96)
The occurrence of denitrification of nitrate to nitrogen gas is considered
a possibility. This is more the case in Mona Lake than in White or Muskegon
Lakes because of the more severe conditions of hypolimnetic anoxia.
Nitrate concentrations during the spring, late fall, and winter in the
bottom waters are high and are generally comparable to surface values
Ammonification on the other hand may be an important process in the bottom
waters of Mona Lake especially during the summer months. Extremely high
tT™ , ^onia-nitrogen were reported in the bottom waters during 1972
(8,536 yg N/£) and 1973 (9,484 yg N/£). Significantly smaller peaks were
reported during 1974 (1,907 yg N/£) and 1975 (2,109 yg N/£). Bottom
water concentrations of ammonia fall rapidly in October (turnover) and
remain low until anoxia and ammonia production begin again in June.
Three forms of phosphorus were measured in Mona Lake; soluble reactive,
total dissolved, and total. Surface water concentrations of both soluble
reactive and total dissolved phosphorus followed a similar pattern. In
Mona Lake, as opposed to Muskegon and White Lakes, the soluble reactive
phosphorus is the major component of the dissolved fraction. This may
indicate a rapid turnover or mineralization of the organic fraction
205
-------
1400
ro
o
MONA LAKE
2 Meter
0 Bottom
Station 4
1972
!973
1974
1975
Figure 94. Nitrate concentrations in Mona Lake, 1972-1975.
-------
0>
M 2 3000
9, O
1000
MONA LAKE
2 Meter
Bottom
Station 4
1972
1973
1974
1975
Figure 95. Ammonia concentrations in Mona Lake, 1972-1975.
-------
1400
ho
o
MONA LAKE
0 2 Meter
0 Bottom
Station 4
1972
1973
1974
1975
Figure 94. Nitrate concentrations in Mona Lake, 1972-1975.
-------
transfer of soluble reactive phosphorus from the bottom waters or an
amount of phosphorus present in excess of that which can be used by the
phytoplankton. Surface water soluble reactive and total dissolved phos-
phorus concentrations are generally highest during the late fall (100 -
400 yg P/£), after replenishment from the hypolimnetic waters. Concen-
tration of phosphorus then decrease slowly until they are depleted in
the summer (see Figures 97 and 98). The severity of depletion has in-
creased from 1972-1975, but sufficient phosphorus remains to support
large populations of phytoplankton. The increased depletion is probably
a result of less total available phosphorus not necessarily greater
algal growth.
Peak total phosphorus concentrations in the surface waters of Mona Lake
occurred at approximately the same time as peaks in primary productivity
(see Figure 99). The total phosphorus is, however, probably responding
to load variation and sediment release. Dissolved phosphorus concentra-
tions in Mona Lake are much in excess of what can be assimilated by the
phytoplankton and the particulate fraction therefore accounts for much
less than half of the total phosphorus. It would be expected that the
phytoplankton would convert the dissolved phosphorus to the particulate
form if this were not the case.
The dynamics of the phosphorus cycle in the bottom waters are dominated,
as in the other lakes, by soluble reactive phosphorus-iron interactions.
Except during periods of anoxia, bottom water soluble reactive phosphorus
concentrations follow those of the surface waters. During the summer
months when no oxygen exists in the hypolimnion, tremendous quantities
of phosphorus and dissolved iron are released from the sediment according
to the mechanism discussed earlier (see Figures 97 and 100). Soluble
reactive phosphorus concentrations approaching or exceeding 1 mg P/&
were reported on numerous occasions during the summer. Such large amounts
of organic matter are generated in Mona Lake that hypolimnetic oxygen
depletion can occur, even in the winter months. Although complete deoxy-
genation was not observed (1-5 mg/& remains), conditions could have
been met in the sediments for the release of phosphorus and iron to the
bottom waters.
Silicon concentrations in Mona Lake follow a pattern of depletion asso-
ciated with spring phytoplankton uptake. Silicon concentrations are re-
duced to zero in Mona Lake as early as April and May. Replenishment
(through tributary loads) is very rapid and begins in June. A second
period of depletion begins in September which is equivalent to the spring
depletion period. Concentrations then increase to the winter maximum
(see Figure 101).
The silicon cycle is in marked contrast to that observed in either White
Lake or Muskegon Lake. For these lakes there was only one, much less
rapid silicon uptake period which did not result in concentrations ap-
proaching zero. A slight replenishment occurred in mid-summer followed by
209
-------
NJ
M
O
MONA LAKE
Station 4
o2 Meter
° Bottom
1972
1973
1974
1975
Figure 97. Soluble reactive phosphorus concentrations
in Mona Lake, 1972-1975.
-------
TTZ
c
f-t
ro
vo
CO
p> a.
H-
tr1 co
(11 CO
ff o
(B M
- <
ro
(-• P.
VO
I O
I-1 CO
VO "O
Oi O
e
CO
o
o
3
o
ro
O
rt
P>
rt
H-
O
CO
TOTAL DISSOLVED PHOSPHOROUS (Mg P/Jt)
(0
->l
r\>
CD
-Nl
OJ
(D
r\>
O
o
T~
o
o
1—r
Ol
o
o
oo
o
o
o
o
o
r\>
o
o
i i—i—i—r
o
o
a CD ro o
?Ssg
r> o
-------
Q_
CO
ID
tr
o
x
Q.
CO
O
O
h-
2400
2000
1600
1200
800
400
MONA LAKE
° 2 Meter
° Bottom
Station 4
1972
1973
1974
1975
Figure 99. Total phosphorus concentrations in Mona Lake, 1972-1975.
-------
CO
240
200
en
O
cr
Q
o
(D
160
120
80
40
0
^(300)
MONA LAKE
o 2 Meter
o Bottom
Station 4
I I I I I I I I I I
1972
1973
1974
1975
Figure 100. Dissolved iron concentrations in Nona Lake, 1973-1975.
-------
DISSOLVED SILICON (mg Si /I)
O
T
ro
b
~r
OJ
b
~T
en
b
T
H
a
CD
CO
CO
o
(D
Pu
CO
o
o
o
o
3
o
s
OJ
CO
rt
H-
O
9
CO
5-
t-1
(a
vo
««j
to
Ul
-------
a fall uptake. The comparative magnitude of the dynamics of the two
less productive lakes and Mona Lake is notable and reflects the higher
productivity in Mona Lake.
Chlorophyll a and primary productivity levels are elevated for a longer
part of the year in Mona Lake than in either White or Muskegon Lakes;
average levels in Mona Lake are also much higher (see Figures 102 and 103).
Only partial data are available for 1972 and 1975 in the mid-summer period,
From data gathered in 1973 and 1974, however, it is apparent that
the only time when chlorophyll a values are not high is in the winter
months from January through March. Peak chlorophyll a values generally
occur during the month of October. Primary productivity values follow
a similar trend except that peak values generally occur in August.
Interpretation of trends in chlorophyll a concentration is complicated
by the fact that algicides were applied to Mona Lake during the summers
of 1970 and 1975. The algicide, month of application, and quantity
applied are presented in Table 34.
The application of algicides has had two effects on phytoplankton levels
in Mona Lake. First, the populations during the peak summer recreation
months have been controlled. Second, the peak phytoplankton bloom has
been "postponed" until October or November. The use of algicides may
make the average chlorphyll a levels appear lower than they would be
without algicide and thus obscure the influence of the diversion project.
Nutrient ratios were calculated for Mona Lake as for Muskegon and White
Lakes. The winter N/P ratio in the surface waters was 39-47:1 in 1974
and 1975. The bottom water winter N/P ratios were 16-26:1 for this same
period. These ratios indicate phosphorus limitation. The summer sur-
face N/P ratios in Mona Lake were <1:1 for all years sampled (1972-1975)
except 1974 when it was 4:1; these ratios are indicative of nitrogen
limited conditions. The low N/P ratios result from very high phosphorus
levels; ammonia nitrogen does not become completely depleted in the
surface waters. The ratio of winter dissolved inorganic nitrogen to
summer total dissolved phosphorus in the bottom waters was 14:1 in 1974
and 4:1 in 1975. These values indicate nitrogen limitation. Calculations
of N/P ratios in the Mona Lake loads demonstrate generally high nitrogen
levels. The ratios were 9:1, 24:1, and 42:1 for 1973, 1974, and 1975.
Insufficient data were available to calculate a 1972 ratio. The higher
ratios in 1974 and 1975 indicate the phosphorus diversion. It is,
however, perhaps useless to calculate any of these ratios for Mona Lake
due to the extremely high nitrogen and phosphorus levels. Growth in
Mona Lake was likely limited by other environmental factors (light,
time, etc.) or the algicide application.
Long-Term Changes — In the period since diversion there has been a sig-
nificant change in the phytoplankton nutrient concentrations in Mona Lake.
Calculations of changes in various parameters are presented in Table 35.
215
-------
140
120
100
0>
80
I 60
DC
0 40
20
MONA LAKE
2 Meter Average
I I I I 1*1 I I I I I I ' I I ' I ' ' I '
1974
1975
Figure 102. Chlorophyll a. concentrations in Mona Lake, 1972-1975.
-------
MONA LAKE
1 Meter Average
0 2 Meter Average
0
1972
1973
1974
1975
Figure 103. Primary productivity rates in Mona Lake, 1972-1975.
-------
Table 34. ALGICIDE APPLICATION TO MONA LAKE
(Michigan DNR, 1976)
Year
Month
Algicide
Quantity
1970
1971
1972
1973
1974
1975
June & August
June & August
June & August
June & August
June, July, & August
June, July, & August
Copper Sulfate
Copper Sulfate
Copper Sulfate
Copper Sulfate
Endothall
Endothall
4200 pounds
4200 pounds
4200 pounds
4200 pounds
75 gallons
300 gallons
218
-------
Table 35. AVERAGE ANNUAL VALUES FOR SELECTED WATER QUALITY
PARAMETERS IN MONA LAKE, 1972-1975
K>
M
kQ
Year
1972
1973
1974
1975
1972
1973
1974
1975
Ammonia
(yg N/A)
126
183
160
156
1374
1199
389
476
Nitrate
(yg N/A)
321
367
417
337
321
362
451
353
Dissolved
Inorganic
Nitrogen
(yg N/A)
447
550
577
493
1695
1561
840
829
Total
Dissolved Total
Phosphorus Phosphorus
(yg P/A) (yg P/A)
Surface
261
128
34
68
Bottom
661
344
72
194
338
226
108
134
675
380
158
259
Soluble
Reactive
Phosphorus
(yg P/A)
86
95
25
49
116
302
64
172
Secchi
Chlorophyll a. Disc
(ygM) (m)
17.6 1.21
40.0 0.92
34.4 1.05
29.8 0.92
-------
Although nitrate concentrations and surface ammonia concentrations have
remained relatively constant, a 65% reduction in bottom water ammonia
concentrations has been observed. More importantly, similar and more
striking reductions in total dissolved and total phosphorus were noted.
Levels of total dissolved phosphorus in both surface and bottom waters
decreased by more than 70% while concentrations of total phosphorus
were reduced by more than 60%. This change has not had a measured
effect on primary productivity. Average chlorophyll a levels in 1973-
1975 were markedly higher than in 1972. There is a slight yearly reduc-
tion in chlorophyll a levels between 1973 and 1974 and again between 1974
and 1975. This reduction may be a result of the diversion project, but
this is unlikely due to the tremendous amounts of nutrients remaining.
It is more likely that variation in average chlorophyll a levels between
1972 and 1975 was a result of algicide applications and changes in sampling
frequency. Because of the algicide application, all analysis regarding
primary productivity and chlorophyll a is complicated. Seasonal cycles
were distorted and the maximum phytoplankton growth occurred late in the
fall. The effect of the diversion on algal growth cannot be easily
discerned.
As discussed earlier, Dillon and Rigler (1974, 1975) have related water
clarity (Secchi disc), chlorophyll a, and total phosphorus (see Figures
76 and 77). Because of the particularly high nutrient levels in Mona
Lake and the application of algicides, these relationships cannot be
directly applied to the Mona Lake data. Summer chlorophyll a levels
predicted using these correlations were twice or more than those observed.
Based strictly on these concentrations, 1975 phosphorus levels would have
to be reduced an additional three-quarters or more to gain a one-meter
increase in Secchi disc under natural conditions.
The dissolved oxygen resources of Mona Lake may have changed slightly
during the period of this study. The duration of anoxia appeared to be
slightly less in 1975 than in 1974 and 1973. This could be a result
of lessened biological oxygen demand loading and autochthonous production.
However, significant amounts of nitrate were not observed in the summer
bottom waters. This suggests denitrification or inhibition of nitrifi-
cation. Both occurrences are related to anoxic conditions. Bottom water
ammonia concentrations were less in 1974 and 1975.
Summary — A calculated 60% reduction in total phosphorus load for Mona
Lake was predicted and observed. A 40 to 55% reduction in dissolved
inorganic nitrogen load was predicted and an estimated 30 to 45% reduc-
tion was observed. The actual nutrient and water quality conditions for
1972 and 1975 are presented in Figure 104 along with data from Lakes
Michigan and Erie for comparison. The large reduction (65%) in phosphorus
levels in Mona Lake may have resulted in a slight decrease in chlorophyll a;
this is not clear due to the use of algicides in the lake. Nutrient
concentrations remained very high compared to other lakes. Some slight
improvements in hypolimnetic anoxia were observed. It may be expected
that further improvement in water quality could result from reduced
phytoplankton growth leading to shorter periods of hypolimnetic anoxia.
This would retard phosphorus release from the sediments and thus further
reduce algal growth.
220
-------
N)
Mo
™« '972
300
200
100
0
m
"338
-
M
-
"
B •
Mo
1975
WLE
n
SLM
300
200
100
GTB
- Mo
1972
Mo
1975
300
200
100
nWLE
n ^ GTB
••
-
Mo WLE
Mo I9lp f
1972
.
SLM
TOTAL PHOSPHORUS (/ig P/Z) TOTAL DISSOLVED PHOSPHORUS AMMONIA (u.gN/1)
(fig P/M
Mo Mo
300
200
100
0
1972 1975
M 337
-321
WLE
SLM
Mo
30 -
.
20 -
GTB
10 -
0 -
1
Mo
1972
37
V
/Lf
12
8
4
SLM r
n m 0
-
.
GTB
SLM
-
Mo Mo
"1972 K^ WLE
n I9n n
NITRATE (fj.g N/J) CHLOROPHLL a (fiq/Jl) SECCHI DISC (m)
LEGEND: Mo 1972 = Mono Loke 1972, Mo 1975= Mono Loke 1975 , WLE= Western Loke Erie
SLM s Southern Loke Michigon , GTB = Grand Traverse Boy
MONA LAKE
Figure 104. Pre- and post-diversion status of selected two-meter,
yearly average water quality parameters in Mona Lake.
-------
LITERATURE CITED
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Interscience, New York. 457 pp.
Anderson, R.R., R.G. Brown, and R.D. Rappleye. 1966. The mineral content
of Myriophyllum spicatum L. in relation to its aquatic environment.
Ecology, 47^ (5): 844-846.
APHA, AWWA, and WPCF. 1971. Standard Methods for the Examination of Water
and Wastewater. 13th Edition. American Public Health Association,
Washington, D.C. 874 pp.
Auer, M.T. and R.P. Canale. 1976. Muskegon Algal Nutrient Bioassay Study—
White Lake Project. The University of Michigan, Ann Arbor. 110 pp.
Auer, M.T., R.P. Canale, and P.L. Freedman. 1976. The Limnology of Grand
Traverse Bay. Michigan Sea Grant Technical Report No. 47. Ann Arbor,
Michigan. 244 pp.
Bauer Engineering, Inc. 1971. The Muskegon County Wastewater Management
System. Pamphlet, privately published. Chicago, Illinois. 16 pp.
Byrnes, B.H., D.R. Keeney, and D.A. Graetz. 1972. Release of ammonium-N
from sediments to waters. Proc. 15th Conference Great Lakes Res.,
pp. 249-259.
Caines, L.A. 1965. Phosphorus content of some aquatic macrophytes with
special emphasis on seasonal fluctuations and application of phos-
phorus fertilizers. Hydrobiologia, XXV:289-301.
Chaiken, E.I., S. Poloncsik, and C.D. Wilson. 1973. Muskegon Sprays
Sewage Effluents on Land. ASCE-Civil Engineering Reprint. 5 pp.
DeMarte, J.A. and R.T. Hartman. 1974. Studies on absorption of 32P, 50Fe
and ^Ca by water-milfoil (Myriophyllum exalbescens) . J. Ecology, _5JL:
189-194.
Denny, P. 1972. Sites of nutrient adsorption in macrophytes. J. Ecology,
60:819-829.
Dillon, P.J. and F.H. Rigler. 1974. The phosphorus-chlorophyll relation-
ship in lakes. Limnol. Oceanogr., 19:767-773.
Dillon, P.J. and F.H. Rigler. 1975. A simple method for predicting ca-
pacity of a lake for development based on lake trophic status. J.
Fish. Res. Bd. Canada, 32:1519-1531.
Edmondson, W.T. (ed). 1959. Ward and Whipple's Fresh Water Biology. 2nd
Edition. John Wiley & Sons, New York. 1248 pp.
222
-------
Edmondson, W.T. 1972. Nutrients and phytoplankton in Lake Washington.
pp. 172-188. In: G.E. Likens (ed), Nutrients and Eutrophication:
The Limiting Nutrient Controversy. ASLO, Lawrence, Kansas.
Gerloff, G.C. 1973. Plant analysis for nutrient assay of natural waters.
Office of Research and Monitoring, U.S. Environmental Protection
Agency, Washington, B.C. 66 pp.
Goldman, C.R. 1972. The role of minor nutrients in limiting the produc-
tivity of aquatic ecosystems, pp. 21-33. In: G.E. Likens (ed), Nu-
trients and Eutrophication: The Limiting Nutrient Controversy. ASLO,
Lawrence, Kansas.
Harter, R.D. 1968. Adsorption of phosphorus by lake sediment. Soil
Sci. Amer. Proc., 32:514-518.
Johnson, D.M. 1976. Atmospheric Inputs of Trace Metals and Nutrients to
Saginaw Bay. The University of Michigan, Ann Arbor (Ph.D. disserta-
tion) .
Keachie, P. 1967. Personal communication.
Keenan, J.D. and M.T. Auer. 1974. The influence of phosphorus luxury
uptake on algal bioassays. J. Water Poll. Contr. Fed., 4_6(3) : 532-542.
Kerr, P.C., D.F. Paris, and D.L. Brockway. 1970. The Interrelation of
Carbon and Phosphorus in Regulating Heterotrophic and Autotrophic
Populations in Aquatic Ecosystems. Water Poll. Contr. Res. Ser. 16050
FGS 07/70, Fed. Water Qual. Admin., Dept. Interior, Washington, D.C.
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226
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APPENDIX A
MUSKEGON ALGAL NUTRIENT BIOASSAY STUDY
WHITE LAKE PROJECT
by
M. T. Auer and R. P. Canale
Department of Civil Engineering
The University of Michigan
Ann Arbor, Michigan 48105
for
Michigan Water Resources Commission
Department of Natural Resources
Lansing, Michigan 48926
EPA Grant No. G005104
SECTION 108 (a) PROGRAM
OFFICE OF GREAT LAKES COORDINATOR
U.S. ENVIRONMENTAL PROTECTION AGENCY, REGION V
CHICAGO, ILLINOIS 60604
227
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ABSTRACT *
Algal nutrient bioassays were conducted on White Lake, Muskegon
County, Michigan in November 1973, and April, July, and October 1974.
Ammonia and nitrate nitrogen (both singly and combined), orthophosphate,
and a trace metals mixture were added to large volumes of lake water
possessing the natural phytoplankton assemblage. Growth, as measured
by chlorophyll ji concentration, was followed for a period of 24-28 days.
Water chemistry and cell numbers were monitored throughout the course
of the experiment.
Nutrient limitation in White Lake phytoplankton populations displayed
a marked seasonality. Stimulation due to the addition of orthophosphate
was observed to be most important in the fall. Nitrogen limitation was
observed during the spring and summer.
The effect of supplying different forms of nitrogen is discussed. Obser-
vations and measurements of nitrification are presented and their
importance is considered. A discussion of the interpretation of bioassay
results is provided with reference to lake management objectives.
The complete Appendix may be obtained from the National Technical
Information Service, Springfield, VA. 22151.
228
-------
APPENDIX B
SUBMERGED AQUATIC MACROPHYTES
IN WHITE LAKE, MICHIGAN
by
P. L. Freedman and R. P. Canale
Department of Civil Engineering
The University of Michigan
Ann Arbor, Michigan 48105
for
Michigan Water Resources Commission
Department of Natural Resources
Lansing, Michigan 48926
EPA Grant No. G005104
SECTION 108 (a) PROGRAM
OFFICE OF GREAT LAKES COORDINATOR
U.S. ENVIRONMENTAL PROTECTION AGENCY, REGION V
CHICAGO, ILLINOIS 60604
229
-------
ABSTRACT *
A field and laboratory study was conducted to investigate the
importance of the submerged aquatic macrophytes to the White Lake
ecosystem. Seven sampling cruises were conducted between June and
October of 1974. The lake macrophyte community was mapped with respect
to areal and biomass distribution. Samples of plants were later
analyzed for carbon, hydrogen, nitrogen, potassium and phosphorus. The
findings reveal that the areal extent of the macrophtes approaches one
fifth of the lakes total surface area and the macrophyte biomass is
equal in magnitude to that of the phytoplankton. The White Lake macro-
phyte community does not appear to be limited by phosphorus or nitrogen,
and is probably restricted only by light and space requirements. The
significance of the macrophyte nutrient content seems to be minor in
comparison with other components of the lake nutrient content. The
importance of macrophyte nutrients is, however, realized when compared
with stream nutrient loads. If White Lake water quality improves as a
consequence of the recently initiated wastewater diversion program, the
macrophyte problem could become greater. Increased water clarity would
increase the areal extent and possibly the density of the macrophyte
community. The impact of the suspected sediment nutrient pumping by
the macrophytes could also lessen or retard the lake response to the
diversion.
The complete Appendix may be obtained from the National Technical
Information Service, Springfield, VA. 22151.
230
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APPENDIX C
NUTRIENT RELEASE FROM
ANAEROBIC SEDIMENTS
IN WHITE LAKE, MICHIGAN
by
P. L. Freedman and R. P. Canale
Department of Civil Engineering
The University of Michigan
Ann Arbor, Michgian 48105
for
Michigan Water Resources Commission
Department of Natural Resources
Lansing, Michigan 48926
EPA Grant No. G005104
SECTION 108 (a) PROGRAM
OFFICE OF GREAT LAKES COORDINATOR
U.S. ENVIRONMENTAL PROTECTION AGENCY, REGION V
CHICAGO, ILLINOIS 60604
231
-------
ABSTRACT *
A multiphase study was conducted to assess the significance of
sediment nutrient release under anaerobic conditions in White Lake.
This involved field monitoring, laboratory experiments, and -In situ
measurements. The results of these phases were in general agreement
for both nitrogen and phosphorus. The average sediment nutrient
release rates were 25.1 mg P/m2/day soluble reactive phosphorus,
38.0 mg P/m /day total dissolved phosphorus and 36.2 mg N/m2/day
ammonia. The associated net diffusion coefficient across the sedi-
ment-water interface was calculated to be 1.0 to 1.5 x 10 5 cm2/sec.
Theoretical and experimental results for silicon release were not in
good agreement. Speculative explanations for the discrepency were
given.
Assessment of the influence of the sediments in lake water quality
improvements suggest that the sediments can contribute nutrients to
the overlying waters at levels sufficient to support troublesome
plant growth. Consequently, improvements in water quality, resulting
from the recent White Lake sewage diversion, could be delayed or
reduced until after the lake sediments release the nutrients accumulated
previously during the period of higher nutrient loading and until
the sediments attain a new balance with the reduced loading
conditions.
The complete Appendix may be obtained from the National Technical
Information Service, Springfield, VA. 22151.
232
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APPENDIX D
MODEL PROJECTIONS OF PHOSPHORUS CONCENTRATIONS
by
R. P. Canale and W. S. Lung
Department of Civil Engineering
The University of Michigan
Ann Arbor, Michigan 48105
for
Michigan Water Resources Commission
Department of Natural Resources
Lansing, Michigan 48926
EPA Grant No. G005104
SECTION 108 (a) PROGRAM
OFFICE OF GREAT LAKES COORDINATOR
U.S. ENVIRONMENTAL PROTECTION AGENCY, REGION V
CHICAGO, ILLINOIS 60604
233
-------
ABSTRACT *
Most previous phosphorus and euthrophication models have considered a
single component (total phosphorus) and have been applied to lakes in
which sediments play a minor role in regulating the phosphorus cycle.
However, under many circumstances, other phenomena, such as phosphorus
regeneration from the sediments and transformation of phosphorus within
the sediment may complicate the response of the lake and require more
comprehensive models.
A model which incorporates the water and the sediment systems and
considers two forms of phosphorus (particulate and dissolved) is de-
veloped for White Lake, Michigan. Dynamic interactions between phos-
phorus in the sediments and the water are quantified by taking account
of particulate phosphorus sinking to the sediment-water interface and
diffusion of dissolved phosphorus across the interface. Other model me-
chanisms include vertical eddy diffusion in the water, phosphorus trans-
formation between the particulate form and the dissolved form in both
the water and the sediment, diffusion of phosphorus in the interstitial
water, and sedimentation in the sediments.
Extensive field data have been used to determine the coefficients
and parameters defined in the model formulations. Temperature data are
used to estimate the vertical eddy diffusion coefficient. A non-linear
biological production model and field data are used to calculate equiva-
lent first-order kinetic coefficients in the water system. Literature
is consulted to obtain the sinking velocity of particulate phosphorus in
the lake. The diffusion coefficient in the interstitial water is
determined by matching a calculated chloride profile with observed data
in the sediment. The kinetic coefficients in the sediment are obtained
by model tuning to match the observed phosphorus profiles in the sediment.
The kinetic coefficient in the upper sediment layers correlates with the
dissolved oxygen level of the bottom of the lake.
Close agreement has been obtained between the model calculations
and the observed data, especially for the upper layers of the sediment.
Sensitivity analysis for the model further substantiates the model cal-
culations. It is found that two separate forms of phosphorus are neces-
sary to gain detailed insight into the dynamics of phosphorus cycling
in White Lake. The model also explains massive releases of phosphorus
from the sediment to the hypolimnion of White Lake in summer. It appears
that the model may be applied to lakes having different degrees of
eutrophication.
The model has been used to calculate long-term trends of phosphorus
concentrations in White Lake. The results indicate some decreases of
phosphorus levels in the first year after implementation of a nutrient
reduction program and virtually no improvement after that. However,
234
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the lake will probably not experience dramatic changes in phosphorus
concentration because upstream non-point sources of phosphorus are
important. Furthermore, year-to-year variations of these loadings over-
shadow the effect of nutrient reduction. Therefore, additional schemes
of the lake rehabilitation are evaluated using the model in order to
achieve further decreases of phosphorus concentrations in White Lake.
It is found that further reduction of the present non-point phosphorus
loading is necessary for full recovery, although significant additional
improvements are also expected from aeration and mixing.
The complete Appendix may be obtained from the National Technical
Information Service, Springfield, VA. 22151.
235
-------
APPENDIX E
WATER QUALITY AND LOADING RATE DATA
FOR THE MUSKEGON COUNTY TREATMENT SYSTEM
236
-------
The following ten tables summarize water quality and load-
ing rate data for the Muskegon and Whitehall Spray-Irrigation
Treatment Sites.
Table 1 lists the average annual reduction in concentrates
of selected parameters between the treatment site influent and
spray drainage affluent at Muskegon spray site. Table 2 defines
the associated annual average flows and loads. Tables 3 through
8 give similar data expressed on a monthly basis. Tables 9 and
10 contain average annual concentration and estimated flow and
loading data for the Whitehall Spray Treatment System.
237
-------
Table 1. AVERAGE ANNUAL CONCENTRATIONS OF SELECTED POLLUTANTS IN INFLUENT
AND EFFLUENT AT THE MUSKEGON TREATMENT SITE
P04-P
TP
NH4-N
(N02+N03)-N TKN
Cl
LO
oo
Fe
S04
Influent
1973*
1974
1975
Effluent, Mosquito Creek
1973*
1974
1975
Effluent, Big Black Creek
1973*
1974
1975
1.28 1.79
1.83 2.70
1.56 2.38
0.03
0.03
0.03
0.02
0.02
0.02
3.58
7.91
6.12
0.35
0.48
0.59
0.34
0.50
0.48
0.03
0.07
—
0.18
1.20
2.09
0.15
1.04
0.95
6.30 154
10.60 176
8.24 182
57.0
60.0
78.0
21.0
16,0
32.0
0.94
1.02
0.79
2.13
1.68
1.03
. 14.6
22.0
17.4
80.0
82.0
75.0
78.0
83.0
81.0
214
327
284
''six-month period (July-December).
-------
Table 2. ANNUAL WASTEWATER FLOWS AND LOADS OF NITROGEN AND PHOSPHORUS
INFLUENT AND EFFLUENT AT THE MUSKEGON TREATMENT SITE
Nutrient
1973*
Year
1974
1975
Influent
Flow,
Load,
TCM/year
kgms/year PO^-P
TP**
NH4-N
TKN**
18,798
24,061
33,648
67,297
118,427
37,755
69,091
101,938 .
298,642
400,203
36,529
56,985
86,939
223,557
300,999
Effluent, Black Creek
Flow,
Load,
Effluent
Flow,
Load,
TCM/year
kgms/year P04~P
rrp***
(NH4 + N02 + N03)-N
, Mosquito Creek
TCM/year
kgms/year PO^-P
TP***
(NH4 + N02 + N03)-N
5,494
110
160
2,692
11,443
343
500
6,065
9,494
190
277
14,620
35,105
1,053
1,537
58,976
13,385
268
391
19,141
35,193
1,056
1,541
94,317
* TCM flow for six-month period (July-December in 1973).
** Limited data, therefore missing values estimated by linear regression
with P04-P and NH4 estimators for TP and TKN.
*** Based on a 1.46 TP:P04 ratio obtained from plant influent data.
239
-------
Table 3. MONTHLY INFLUENT CONCENTRATIONS OF PHOSPHORUS
AND NITROGEN TO MUSKEGON WASTEWATER SYSTEM
Month/ Year
7/73
8/73
9/73
10/73
11/73
12/73
MEAN 1973
1/74
2/74
3/74
4/74
5/74
6/74
7/74
8/74
9/74
10/74
11/74
12/74
MEAN 1974
1/75
2/75
3/75
4/75
5/75
6/75
7/75
8/75
9/75
10/75
11/75
12/75
MEAN 1975
P04-P
mg/£
1.02
0.91
2.61
1.15
0.85
1.28
1.30
1.12
1.60
1.52
1.88
1.70
1.91
2.16
2.15
2.33
2.13
2.19
1.87
1.88
1.86
1.83
1.89
1.41
1.74
1.66
1.50
1.23
1.05
0.96
1.72
1.86
1.56
NH4
mg/£
3.39
3.33
3.87
3.72
3.03
4.15
3.58
3.95
5.96
4.63
7.08
9.06
7.15
10.70
8.30
10.96
9.19
8.61
9.32
7.91
9.29
8.56
12.90
7.80
8.40
7.25
5.85
3.27
2.27
1.56
2.94
3.34
6.12
240
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Table 4. MONTHLY INFLUENT CONCENTRATIONS OF PHOSPHORUS AND NITROGEN
TO MUSKEGON WASTEWATER SYSTEM.
Month/Year
7/73
8/73
9/73
10/73
11/73
12/73
TOTAL 1973
1/74
2/74
3/74
4/74
5/74
6/74
7/74
8/74
9/74
10/74
11/74
12/74
TOTAL 1974
1/75
2/75
3/75
4/75
5/75
6/75
7/75
8/75
9/75
10/75
11/75
12/75
TOTAL 1975
Flow
TCM
3,278
3,353
3,133
3,176
2,965
2,893
18,798
3,155
2,808
3,277
3,198
3,301
3,411
3,115
3,453
3,014
3,145
2,087
2.791
37,755
2,984
2,659
2,779
2,928
3,188
3,245
2,872
3,190
3,135
3,380
3,083
3,086
36,529
P04-P
kg
3,344
3,051
8,177
3,652
2,520
3.703
24,447
3,534
4,493
4,981
6,012
5,612
6,515
6,728
7,424
7,023
6,699
4,571
5.219
68,811
5,550
4,866
5,252
4,128
5,547
5,387
4,308
3,924
3,292
3,245
5,303
5,740
56,542
NH4
kg
11,112
11,165
12,125
11,815
8,984
12,006
67,207
12,462
16,736
15,173
22,642
29,907
24,389
33,331
28,660
33,033
28,903
17,969
26,012
289,217
27,721
22,761
35,849
22,838
26,779
23,526
16,801
10,431
7,241
5,273
9,064
10,307
218,591
241
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Table 5. MONTHLY CONCENTRATIONS OF PHOSPHORUS AND NITROGEN
IN EFFLUENT AT MOSQUITO CREEK OUTFALL
Month/Year
7/73
8/73
9/73
10/73
11/73
12/73
MEAN 1973
1/74
2/74
3/74
4/74
5/74
6/74
7/74
8/74
9/74
10/74
11/74
12/74
MEAN 1974
1/75
2/75
3/75
4/75
5/75
6/75
7/75
8/75
9/75
10/75
11/75
12/75
MEAN 1975
(NH4 + N02 + N03)-N
mg/£
0.31
0.41
0.40
0.57
0.61
0.89
0.53
0.81
1.04
0.99
1.21
1.32
1.50
2.23
2.34
2.20
2.59
2.50
1.42
1.68
2.50
2.50
2.08
1.99
2.50
2.35
3.41
3.49
3.12
2.93
2.94
2.37
2.68
P04-P
mg/£
0.033
0.027
0.023
0.060
0.034
—
0.029
—
0.064
0.064
0.032
0.047
0.049
0.023
0.006
0.013
0.026
0.075
0.033
est .
0.03
0.03
0.03
0.03
0.03
0.03
0.03
0.03
0.03
0.03
0.03
0.03
0.03
242
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Table 6. MONTHLY EFFLUENT FLOW AND LOADS OF PHOSPHORUS AND NITROGEN TO
MOSQUITO CREEK FROM THE MUSKEGON TREATMENT SITE
Month/Year
7/73
8/73
9/73
10/73
11/73
12/73
Flow
TCM
1,927
1,926
1,869
1,926
1,869
1,926
(NH4 + N02 + N03)-N
kg
597
790
748
1,098
1,140
1,714
PO^-P
kg
63.6
52.0
43.0
115.6
63.6
—
TOTAL 1973 11,443 6,087 338.8
1/74 1,476 1,195
2/74 1,333 1,387
3/74 1,828 1,810 117.0
4/74 2,337 2,828 149.6
5/74 2,180 2,878 69.8
6/74 3,586 5,379 168.5
7/74 5,348 11,927 262.1
8/74 4,292 10,044 98.7
9/74 4,040 8,888 24.2
10/74 3,471 8,990 45.1
11/74 2,564 6,410 66.7
12/74 2,650 3,762 198.8
TOTAL 1974 35,105 65,498 1,200.5
1/75 3,599 8,998 108.0
2/75 3,252 8.127 97.5
3/75 1,956 4,069 58.7
4/75 1,893 3,768 56.8
5/75 1,956 4,891 58.7
6/75 2,461 5,784 73.8
7/75 2,895 9,872 86.8
8/75 2,426 8,466 73.1
9/75 4,846 16,087 • 145.4
10/75 2,191 6,420 65.7
11/75 5,527 16,249 165.8
12/75 2,191 5,193 65.7
TOTAL 1975 35,193 97,924 1,056.0
243
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Table 7. MONTHLY CONCENTRATIONS OF PHOSPHORUS AND NITROGEN
IN EFFLUENT AT BLACK CREEK OUTFALL
Month/Year
7/73
8/73
9/73
10/73
11/73
12/75
MEAN 1973
1/74
2/74
3/74
4/74
5/74
6/74
7/74
8/74
9/74
10/74
11/74
12/74
MEAN 1974
1/75
2/75
3/75
4/75
5/75
6/75
7/75
8/75
9/75
10/75
11/75
12/75
MEAN 1975
P04-P
0.03
—
0.01
0.04
—
0.00
0.02
__
—
—
—
—
—
0.04
0.01
0.04
0.02
0.02
0.02
0.02
0.03
0.04
0.01
0.01
—
0.01
0.01
0.03
0.01
0.01
0.03
0.01
0.02
(NH4 + N02 + N03)-N
0.41
0.37
0.31
0.45
0.45
0.97
0.49
0.98
1.15
1.08
1.53
1.68
1.62
1.43
2.04
1.52
2.17
1.91
1.40
1.54
1.48
1.40
1.42
1.45
1.56
1.45
1.81
1.60
1.67
1.27
0.95
1.14
1.43
244
-------
Table 8. MONTHLY EFFLUENT FLOW AND LOADS OF PHOSPHORUS AND NITROGEN
TO BLACK CREEK FROM MUSKEGON TREATMENT SITE
Month/Year
Flow
TCM
P04-P (NH4 + N02 + N03)-N
kg kg
7/73
8/73
9/73
10/73
11/73
12/73
TOTAL 1973
1/74
2/74
3/74
4/74
5/74
6/74
7/74
8/74
9/74
10/74
11/74
12/74
TOTAL 1974
1/75
2/75
3/75
4/75
5/75
6/75
7/75
8/75
9/75
10/75
11/75
12/75
TOTAL 1975
1,408
1,604
1,348
516
276
342
5,494
475
535
625
864
1,096
676
758
1,885
782
504
874
420
9,494
1,181
42.2
13.5
20.6
76.3
30.3
18.8
31.3
10.0
17.5
8.4
116.4
18.0
37.0
10.5
9.8
11.5
12.8
35.4
18.0
12.
31,
,3
.4
577
593
418
232
124
332
2,276
466
615
675
1,322
1,841
1,095
1,084
3,845
1,189
1,094
1,669
588
15,483
13,385
12.0
209.7
19,365
245
-------
Table 9. AVERAGE ANNUAL CONCENTRATIONS OF SELECTED POLLUTANTS IN INFLUENT
AND EFFLUENT (WELLS) AT THE WHITEHALL TREATMENT SITE
P04-P
TP
NH4-N
(N02 + N03)-N
TKN
Cl
S04
- mg/fc -
Influent
N, 1974 — — 10.46
OS
1975 0.35 0.65 38.22 0.67
Effluent, (wells)*
1974 0.04 -- 0.20 0.07
1975 0.02 0.05 0.05 0.06
—
48.27
5.4 18.3
3.3 44.5
*Average of parameter concentration in perimeter wells at Whitehall.
-------
Table 10. ANNUAL WASTEWATER FLOWS AND LOADS OF NITROGEN AND PHOSPHORUS,
INFLUENT AND EFFLUENT AT THE WHITEHALL TREATMENT SITE
Influent
Flow, TCM/year
Load, kgms/year
Effluent (wells)*
Flow, TCM/year
Load, kgms/year
Year
Nutrient 1974 1975
733 1,505
P04-P — 533
TP — 978
NH4-N 7,667 57,521
(N02 + N03)-N — 1,007
TKN — 72,646
6.32 298.41
P04-P 0.25 5.97
TP — 14.92
NH4 1.26 14.92
(N02 + NOo)-N 0.44 17.90
247
-------
APPENDIX F
INDUSTRIAL AND MUNICIPAL DISCHARGE INVENTORY
248
-------
Tables 1, 2, and 3 list the industrial discharge for Muskegon,
Mona, and White Lake basins. The industries in these tables are
restricted to those which have filed National Permit Discharge Elimination
System (NPDES) reports with the State of Michigan Environmental Protection
Bureau. Included in these tables is documentation of the industry,
NPDES discharge number, discharge type and character, and waste flow.
Table 4 documents the status of various Muskegon County communities
with respect to their participation in the Muskegon County wastewater
treatment system. In all tables industries and municipalities have been
categorized into those with more than 50% and less than 50% correction
to the wastewater treatment system.
249
-------
Table 1. INDUSTRIAL NFDES WASTEWATER DISCHARGES TO MUSKEGON LAKE
Industry
Year
State
Outflow Discharge
Number Type*
Z Z
Processing Cooling
Z Flow
Sanitary (Mgd)
Industries with more than
50Z connected to the Spray-
Irrigation Treatment System
Amstead Industries Inc.
Standard Automotive Parts
Anaconda Wire and Cable Co.
Division of Anaconda Co.
Breneman, Inc.
Muskegon Division
Great Lakes Plating Corp.
Michigan Celery Promotion'
Co-op, Inc.
Michigan Spring Co.
Muskegon Piston Ring Co.
Muskegon Plant
S.D. Warren Co.
1975
1974
1973
1975
1974
1973
1974
1973
1975
1974
1973
1975
1973
1975
1974
1973
1975
1974
1973
1974
1973
610185
610186
610234
610235
980537
610185
610186
610234
610235
980537
971832
971833
971834
971835
610156
610156
619156
610158
970042
610158
970042
610165
610165
610165
610233
970730
970731
940222
940223
970716
970717
610179
940240
610179
610179
970609
610232
980451
980452
610071
610072
970346
970347
970348
970349
970350
6
6
6
2
8
6
6
6
2
6
2
2
2
2
8
8
8
6
8
8
6
8
8
8
8
8
4
8
8
8
8
1
8
1
1
8
1
8
8
1
1
1
1
1
8
8
6
0
99
100
0
100
0
95
100
0
0
100
0
100
5
5
5
100
46
46
100
75
80
82
65
80
0
0
100
100
0
0
35
0
0
98
0
0
100
100
70
100
100
100
0
100
94
100
1
0
45
0
100
5
0
43
1
0
100
0
82
82
82
0
19
19
0
20
10
10
25
20
0
100
0
0
100
100
55
100
100
0
100
0
0
0
30
0
0
0
0
0
0
0
0
0
55
0
0
0
0
57
99
0
0
0
13
13
13
0
35
35
0
5
10
8
5
0
100
0
0
0
0
0
10
0
0
2
0
100
0
0
0
0
0
0
100
0
0.0005
0.0240
0.0006
0.0004
0.0290
0.0030
0.0060
0.0040
0.0009
0.0510
0.0020
0.0020
0.0040
0.0005
0.1152
0.1459
0.0136
0.0001
0.0245
0.0243
0.0001
0.025
0.050
0.018
0.0246
0.071
0.001
0.002
0.009
0.008
0.002
0.0002
0.5222
0.064
0.064
0.470
4.1
0.14
15.4
4.2
11.67
0.045
0.35
0.18
0.14
14.0
Standard Oil Car Wash
1975 880970
95
0.0118
-------
Table 1.—continued
Industry
Storey Chemical Co.
Ott Division
Teledyne Continental
Shaw Walker Co.
Year
1975
1974
1973
Motors 1975
1974
1973
1975
1975
1974
. 1973
State
Outflow Discharge
Number Type*
610085
980563
610085
980563
610084
610085
610063
980785
980786
610063
980785
980786
970849
970850
980280
980282
980283
980284
980285
980286
980237
980288
980280
980282
980283
980284
980285
980286
980287
970128
970129
970130
970131
970132
970133
970134
2
8
2
8
1
2
1
8
8
1
8
8
1
1
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
Z Z
Processing Cooling
0
68
0
90
60
0
0
0
100
0
0
100
100
100
28
0
0
0
0
90
90
93
25
25
0
0
0
87
90
10
0
0
0
0
88
90
100
30
100
60
40
100
100
0
0
100
0
0
0
0
45
0
0
0
0
0
0
57
47
47
0
0
0
2
0
72
0
0
0
0
12
0
Z Flow
Sanitary (Mgd)
0
2
0
0
0
0
0
100
0
0
100
0
0
0
27
100
100
100
100
10
10
0
28
28
100
100
100
11
10
18
100
100
100
100
0
10
0.55
0.75
0.7
0.8
0.75
0.55
0.25
0.05
0.70
0.25
0.1
0.6
0.77
0.77
0.06
0.007
0.004
0.0004
0.0007
0.0110
0.0680
0.0490
0.056
0.100
0.005
0.0004
0.0009
0.0720
0.0096
0.1548
0.0127
0.0060
0.0003
0.0009
0.0715
0.0105
Industries with less than
50Z connected to the Muske-
gon Wastewater Treament
System
Campbell, Wyatt & Cannon
Cannon-Muskegon Corp.
Clark Gravely Corp.
Geerpres Winger', Inc.
1975
1974
1973
1975
1974
1973
1975
1974
1973
1975
1974
1973
610125
610125
610125
610214
610214
610214
610213
610213
610213
610224
610224
610224
1
1
1
2
2
2
1
1
1
4
4
1
0
10
0
0
0
0
0
0
7
7
7
100
100
90
99
99
99
100
100
100
80
80
80
0
0
0
1
1
1
0
0
0
13
13
13
0.79
0.5
0.58
0.20
0.123
0.123
0.0024
0.0024
0.0057
0.0078
0.0078
0.0078
251
-------
Table 1.—continued
Industry
Enterprise Brassworks
Hovmett Corp.
Hlsco Division
Plant 12
Keene Corp . , Kaydon
Bearing
Michigan Foundry Supply
Naph-Sol Refinery Co.
Port City Inc.
Sealed Power Co.
Stanford Street
Seal Tex Co.
Teledyne Continental
Motors, N. Getty
•
West Michigan Dock
& Market Corp.
Western Corp.
Year
1975
1974
1973
1975
1974
1973
1975
1974
1973
Co. 1975
1974
1973
1975
1974
1975
1974
1973
1975
1974
1973
1974
1973
1975
1974
1973
1975
1974
1973
1975
1974
1973
State
Outflow Discharge X X
Number Type* Processing Cooling
610216
610216
610216
Inactive
610154
610231
610154
610231
610101
610239
610101
610239
610101
610239
970446
970447
660099
610099
610099
610123
610123
610219
970213
610219
980208
610219
970213
610261
980779
980780
610261
980779
980780
971267
927883
927883
610076
610102
980927
610076
610102
980927
610076
610102
970797
610418
610918
610418
610255
610255
610222
610223
970157
1
1
1
1
1
1
1
1
2
1
2
1
2
2
8
2
2
1
1
1
1
8
1 .
8
1
8
1
8
8
1
8
8
1
1
1
1
2
8
1
2
8
1
2
8
1
1
1
1
1
1
1
8
0
0
0
10
20
20
10
0
100
0
100
0
100
100
0
15
15
15
100
100
0
6
0
6
0
0
28
0
6
28
0
6
28
0
0
0
100
0
0
100
0
0
100
0
0
0
0
0
0
0
0
0
100
100
100
90
80
80
90
100
0
100
0
100
0
0
0
84
84
85
0
0
100
0
100
0
100
6
72
0
28
72
0
28
72
100
100
100
0
0
100
0
0
100
0
100
100
100
100
100
100
100
100
89
I Flow
Sanitary (Mgd)
0
0
0
o
0
0
0
0
0
0
0
0
0
0
100
1
1
0
0
0
0
94
0
94
0
94
0
100
66
0
100
66
0
0
0
0
0
100
0
0
100
0
0
0
0
0
0
0
0
0
0
11
0.003
0.014
0.0204
0.2
0.3
0.3
0.24
0.06
0.04
0.06
0.04
0.11
0.001
0.008
0.0039
0.056
0.056
0.056
0.066
0.005
0.0004
0.0001
0.0004
0.0001
0.0004
0.0001
0.97'
0.02
0.059
1.034
0.0575
0.0575
1.142
0.001
0.001
0.05
0.028
0.035
0.30
0.028
0.03
0.26
0.028
0.03
0.154
0.2
0.2
0.5
0.5
0.452
0.013
0.078
The State of Michigan Environmental Protection Bureau categorizes the discharge types as
follows: 1) surface; 2) lagoon; 3) spray; 4) septic tile field; 5) deep well; 6) surface
overground flow; 7) other; 8) municipal (sanitary sewer).
252
-------
Table 2. INDUSTRIAL NPDES WASTEWATER DISCHARGES TO MONA LAKE
Industry
Year
State
Outflow Discharge Z Z Z rlow
Number Type* Processing Cooling Sanitary (Mgd)
Industries with more than
SOZ connected to the Mus-
kegon Wastewater Treatment
System
American Coil Spring Co.
Bennett Pump Co.
Brown-Morse Co.
Plant #1
110 E. Broadway
Brown-Morse Co.
6th Street
Brunswick Corp.
Burdick & Jackson
Laboratories
Johnson Products
Division Sealed Power Corp.
Tek Mold Inc.
Universal Canshaft Co.
1975
1974
1973
1975
1973
1973
1975
1974
1973
1975
1974
1973
1975
1974
1973
1975
1974
1973
1975
1974
1973
1975
1974
1973
610246
980092
610150
980092
610150
970023
610157
610157
610159
970440
610242
980277
610242
980277
610242
970441
610168
610168
610168
610160
610160
610160
610166
980447
610166
980447
610166
970742
610208
610208
610208
924374
980441
924374
980441
924374
970659
1
8
1
8
1
8
8
8
1
8
1
8
1
8
1
8
8
8
8
8
8
8
1
8
1
8
1
8
8
8
8
8
7
8
4
8
4
30
70
30
70
5
70
1
1
21
28
27
28
27
28
27
28
35
46
46
5
5
5
0
71
0
40
60
24
10
10
10
35
100
35
100
35
100
52
5
52
5
70
5
80
80
79
6
73
6
73
6
73
6
20
21
21
92
92
92
100
12
100
43
40
26
86
86
86
60
0
60
0
60
0
18
25
18
25
25
25
19
19
0
66
0
66
0
66
0
66
45
33
33
3
3
3
0
17
0
17
0
10
4
4
4
5
0
5
0
5
0
0.115
0.120
0.09
0.02
0.103
0.038
0.07
0.06
0.0082
0.0159
0.0056
0.0165
0.0089
0.0165
0.0089
0.0106
0.27
0.42
0.42
0.0629
0.0336
0.0290
0.034
0.256
0.115
0.173
0.076
0.114
0.03
0.1387
0.1864
0.0335
0.0006
0.8335
0.0001
0.0335
0.0001
Industries with less than
SOZ connected to Muskegon
Wastewater Treatment
System
American Porcelain Enamel 1975
1974
1973
610155
980455
610155
980455
610155
970251
100
0
100
0
100
0
0
0
0
0
0
0
0
100
0
100
0
100
0.612
0.0026
0.0538
0.0018
0.0564
0.0011
253
-------
Table 2*—continued
Industry
Campbell, Wyatt & Cannon
Plant 11
Campbell, Wyatt & Cannon
Plant 14
Coil Anodizers
Division of Locin
Industries (Kersman Co.)
East Shore Chemical Co.
Fleet Engineers, Inc.
Hazekomp Bert & Son
Lakeway Chemicals, Inc.
Peerless Plating Co.
Punches & Son
Slaughter House
Ryerson Creek Produce Inc.
Sealed Power Corp.
Harvey St.
State
Outflow Discharge
Year Number Type*
1975
1974
1973
1975
1974
1973
1975 .
1974
1973
1975
1974
1973
1975
1974
1973
1975
1974
1975
1974
1973
1975
1974
1973
1975
1973
1975
1973
1975
1974
1973
610073
610073
610073
610126
610126
610126
610057
610059
980008
610057
610059
980008
610057
610059
970300
610162
940264
610162
980877
610162
970475
610241
940245
610241
970456
970457
610119
610119
610095
980751
610095
980757
610095
970029
610200
980073
610200
980073
610200
970138
610120
610120
610218
610218
610248
610170
980777
980778
971270
1
1
1
1
1
1
1
2
8
1
2
8
1
2
2
1
8
1
8
1
8
2
8
2
2
8
2
2
2
4
2
4
2
4
2
4
2
4
2
4
2
2
1
1
1
1
8
a
i
Z I
Processing Cooling
20
20
5
0
0
1
50
100
0
50
100
0
50
100
0
0
95
0
95
0
95
100
0
100
100
0
11
11
13
0
13
0
13
0
49
0
33
0
42
0
50
25
99
98
0
0
0
36
5
80
80
95
100
100
99
50
0
0
50
0
0
50
0
100
100
0
100
0
100
0
0
0
0
0
0
88
88
87
0
87
0
87
0
51
0
67
0
58
0
40
25
1
1
100
100
0
57
95
X Flow
Sanitary (Hgd)
0
0
0
0
0
0
0
0
100
0
0
100
0
0
0
0
5
0
5
0
5
0
100
0
0
100
1
1
0
100
0
100
0
100
0
100
0
100
0
100
10
50
0
1
0
0
100
7
0
0.28
0.28
0.28
0.08
0.08
0.11
0.250
0.002
0.001
0.400
0.002
0.0001
0.500
0.011
0.144
0.029
0.006
O.OB
0.005
0.05
0.005
0.0016
0.0008
0.0001
0.0001
0.0008
0.01
0.01
1.3
0.002
0.76
0.002
0.78
0.002
0.012
0.0001
0.0082
0.0001
0.0165
0.0000
0.0005
0.001
0.0010
0.0005
?
0.0504
0.0013
0.0618
0.055
254
-------
Table 2.—continued
State
Outflow Discharge
Industry
Stresscr Joseph Laundry
Thomas Solvent Co.
Thermal Chemical Inc.
Dnico Inc.
Year
1975
1974
1973
1975
1974
1973
197S
1974
1973
Number
610053
610053
610053
610078
610078
610078
610228
970012
610228
610228
970012
Type*
2
2
2
2
2
2
2
8
2
2
8
Z
Processing
0
100
0
1
1
1
100
0
100
100
0
z
Cooling
0
0
0
98
98
98
0
0
0
0
0
Z
Flow
Sanitary (Mgd)
100
0
100
1
1
1
0
100
0
0
100
0.0028
0.001
0.002
0.0045
0.0045
0.0045
0.0015
0.0001
0.0021
0.0021
0.0002
The State of Michigan Environmental Protection Bureau categorizes the discharge types as
follows: 1) surface; 2) lagoon; 3) spray; 4) septic tile field; 5) deep wall; 6) surface
overground flow; 7) other; 8) municipal (sanitary sewer).
255
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Table 3. INDUSTRIAL NPDES WASTEWATER DISCHARGES TO WHITE LAKE
Industry
Year
State
Outflow
Number
Discharge
Type*
Z Z Z Flow
Processing Cooling Sanitary (Mgd)
Industries with more than
50Z connected to Whitehall
Wastewater Treatment System
Whitehall Leather Co. 1975
Division Genesco Industries 1974
Industries with less than
50Z connected to Whitehall
Wastewater Treatment System
Certified Concerete Inc.
Happs Wash King
Booker Chemical Corp.
Howmett Corp., Misco Div.
Plant #1
1973
1975
1974
1974
1973
1975
1974
1973
610047
610062
980565
610062
970706
924137
924137
610049
610049
610094
610094
610094
1973 610091
85
85
0
85
0
100
100
0
100
1
1
1
20
4
15
0
15
0
0
0
0
0
98
98
98
80
1
0
100
0
100
0
0
100
0
1
1
1
0.4960
0.5
0.004
0.491
0.004
0.0005
0.0005
0.0005
0.0005
11.7
12.2
14.1
0.02
Howmett Corp., Misco Div.
Plant #3
Howmett Corp., Misco Div.
Plant 04
Pin Key Manufacturing Co.
Tech Cast Inc.
1975
1974
1973
1975
1974
1973
1975
1974
1973
1975
1974
610092
610092
610093
610217
980357
610217
980357
610217
980357
927739
980640
927739
980640
927739
970786
927742
927742
1
1
1
2
8
2
8
2
2
4
2
4
2
4
2
2
20
20
20
10
30
10
30
10
100
0
0
100
100
0
0
0
80
80
80
90
10
90
10
90
0
0
0
0
0
0
100
100
0
0
0
0
60
0
60
0
0
100
100
0
0
100
0
0
0.10
0.104
0.092
0.200
0.022
0.33
0.036
0.033
0.0002
0.0002
0.0002
0.0002
0.0002
0.0002
0.02
0.04
The State of Michigan Environmental Protection Bureau categorizes the discharge types as
follows: 1) surface; 2) lagoon; 3) spray; 4) septic tile field; 5) deep well; 6) surface
overground flow; 7) other; 8) municipal (sanitary sewer).
256
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Table 4. STATUS OF MUSKEGON COUNTY MUNICIPALITIES PARTICIPATION
IN THE SPRAY-IRRIGATION WASTEWATER TREATMENT SYSTEM
Muskegon Lake Municipalities
Communities with more than 50% connected to the Muskegon Wastewater System
1. Muskegon
2. North Muskegon
Communities with less than 50% connected to the Muskegon Wastewater System
1. Dalton Township
2. Egelton Township
3. Laketon Township
4. Muskegon Township
Mona Lake Municipalities
Communities with more than 50% connected to the Muskegon Wastewater System
1. Muskegon Heights
2. Roosevelt Park
Communities with less than 50% connected to the Muskegon Wastewater System
1. Egelton Township
2. Fruitport Township
3. Muskegon Township
4. Norton Shores
5. Sullivan Township
White Lake Municipalities
Communities with more than 50% connected to the Whitehall Wastewater System
1. Whitehall
Communities with less than 50% connected to the Whitehall Wastewater System
1. Fruitland Township
2. Lakewood Club
3. Montague
4. Montague Township
5. Whitehall Township
6. White River Township
257
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APPENDIX G
AVAILABILITY OF DATA FROM U.S. EPA STORAGE
AND RETRIEVAL COMPUTER SYSTEM "STORET"
258
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Much of the data collected has been entered into the U.S. Environ-
mental Protection Agency's storage and retrieval computer system called
"STORE!". Access to STORE! and use of this data may be obtained directly
by authorized users or indirectly through any of the ten different EPA
Regional Offices or STORET User Assistance, U.S. EPA, 401 M Street, S.W.,
Washington, D. C. 20460, phone (202) 426-7792. The applicable codes
for gaining access to this data are: Agency Code No. 21 MI MUSK;
State Code No. 26; County Code No. 121.
259
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TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1. REPORT NO. 2-
EPA-905/9-79-006-A
4. TITLE AND SUBTITLE
Applicability of Land Treatment of Wastewater in The
Great Lakes Area Basin - Impact of Wastewater Diver-
sion Spray Irrigation on Water Oualitv in Muskeaon
7. AUTHOR(S) county, Michigan Lakes
P.L. Freedman, R.P. Canale , and M.T. Auer
9. PERFORMING ORGANIZATION NAME AND ADDRESS
Department of Civil Engineering
The University of Michigan
Ann Arbor, Michigan 48105
12. SPONSORING AGENCY NAME AND ADDRESS
U.S. Environmental Protection Agency
Great Lakes National Program Office
536 South Clark Street, Room 932
Chicago, Illinois 60605
. RECIPIENT'S ACCESSION NO.
. REPORT DATE
Mav 1979
6. PERFORMING ORGANIZATION CODE
8. PERFORMING ORGANIZATION REPORT NO.
10. PROGRAM ELEMENT NO.
2RA645
11. CONTRACT/GRANT NO.
G005104 01
13. TYPE OF REPORT AND PERIOD COVERED
Final April 197° June 1Q76
14. SPONSORING AGENCY CODE
15. SUPPLEMENTARY NOTES
EPA Project Officers: Dr. John M. Walker and Stephen Poloncsik
16. ABSTRACT ipne Muskegon County Wastewater Management System is a lagoon impoundment,
spray irrigation facility which treats about 102,000 cubic meters of wastewater per
day and irrigates 2,160 hectares of corn land. Irrigated treated water channels back
to the surface water via subsurface drains, percolation through the soil, wells and
open ditches. A significant amount of the wastewater was diverted to the treatment
site in 1974 from out-dated inefficient treatment plants which had previously dis-
charged poorly treated wastewater directly to the County's surface waters.
Data was collected from 1972 to 1975 to determine the impact of the diversion of
wastewater and subsequent treatment as the site on improved quality of surface waters.
Within this study, particular emphasis was placed on an analysis of the effect of the
diversion project on the trophic status and associated nutrient budgets of three major
County lakes. Organics, trace metals and suspended solids were not measured. In this
effort, tributary data was combined with information on municipal and industrial
nutrient loads.
The Data shows improvement of water quality in two of the three lakes where non-point
sources of pollution were not dominant. Eutrophication models show that the current
reduction in nutrient loadings will not be sufficient to change the eutrophic status
of the lakes. However, additional improvement in water transparency, oxygen conditions1
and other water quality parameters are expected. . —
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
b.IDENTIFIERS/OPEN ENDED TERMS
COSATI Field/Group
Water Quality
Land Use
Land treatment of Wastewater
Lake Renovation
Eutrophic
Muskegon
18. DISTRIBUTION STATEMENT AVailatlleEo
Municipal Construction Div. Denver, CO,
Great Lakes National Program Office Chgo.,
IL and NTIS, Springfield, VA 22151
19. SECURITY CLASS (This Report)
21. NO. OF P.
260
20. SECURITY CLASS (Thispage)
22. PRICE
EPA Form 2220-1 (Rev. 4-77)
PREVIOUS EDITION IS OBSOLETE
260
6 U.S. GOVERNMENT PRINTING OFFICE. 1979-652-042
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