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.

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                              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

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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

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                              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

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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

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                              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

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                                        STATE OF

                                        MICHIGAN
                          Muskedon
                 Roosevelt Heiafits
                     Park

                        1mA LAKE
                                                            Muskegon
                                                            Spray
                                                            Site
LAKE MICHIGAN
               Figure 3.   The Muskegon Lakes  study area.

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 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

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     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

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                               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

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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

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 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

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                      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

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                             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

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                                          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

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                                   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

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                                "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.

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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.

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            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.

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                        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

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 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

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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

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 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

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                               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

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                          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

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                                        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

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 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

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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

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      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

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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

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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.

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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.

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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

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                    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.

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                                  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.

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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

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(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

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                      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

-------
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n Observed Postdiversion Load
• Expected Postdiversion Load

E" A Lake A.Muskegon
: '67/701 a Lake
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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.

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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

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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.

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  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.

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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

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 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

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                              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






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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

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                             ° 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

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 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

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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
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5-

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1972
















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WLE I0°

Wh
1975
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SLM
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176

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-1972
Wh
1975
- n







SLM
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n
DISSOLVED PHOSPHORUS " AMMONIA Uig N/Z)




(fj.g P/J.)
I2p


Wh WLE a
1975 T





















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fin



GTB

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.'972 1975 WLE
n n n
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     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.

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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

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                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.

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                                 60T
                           CHLOROPHYLL a
H-
00
c
>-(
ro

4^
N>
O
O
"O
3"
 o

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 §
 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
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o

— —
o
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o
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0
3 p




ro


o
^ •£»
CO


en


m
D ro ^ en c
T° 1 1
o
wo
o

—
o
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
_ o


— -
o
o
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- o -
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o
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8
1 1 1
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ro


0

CO


0)


m
D0 ho i& en c
u i i i
0
_ o

o

0
o
h o
o
0

o
0
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o
o
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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

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         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

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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

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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

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                                        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

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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.

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               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.

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                                                                     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.

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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

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 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

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                         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

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                                      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.

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                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.

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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.

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       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,

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           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.

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                          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%)

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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

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           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

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 (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

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     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

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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

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     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

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                                         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.

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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

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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

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                                          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

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                            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
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  (D
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H-
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  O


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                                                           a
                 Q
               O 3
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-------

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

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       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

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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

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                                      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

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   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.

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oo
o
                                                                       BLACK CREEK

                                                                       Station 27
                                                                       DTP
                   1972
1973
1974
1975
                        Figure 80.  Phosphorus concentrations in Black Creek, 1973-1975.

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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

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   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.

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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

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                                 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

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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

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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

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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

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                       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%

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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

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       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

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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
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  H-
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(11 CO
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  CO

  o
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  3
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  ro
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  P>
  rt
  H-
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                   TOTAL DISSOLVED PHOSPHOROUS (Mg P/Jt)
           (0
           ->l
           r\>
           CD
           -Nl
           OJ
          (D
                    r\>
                    O
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                   T~
                           o
                           o
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-------
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
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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

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   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.

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               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

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                            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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Anderson, R.R., R.G. Brown, and R.D. Rappleye.  1966.  The mineral content
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APHA, AWWA, and WPCF.  1971.  Standard Methods for the Examination of Water
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Auer, M.T. and R.P. Canale.  1976.  Muskegon Algal Nutrient Bioassay Study—
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Auer, M.T., R.P. Canale, and P.L. Freedman.  1976.  The Limnology of Grand
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Bauer Engineering, Inc.  1971.  The Muskegon County Wastewater Management
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Caines, L.A.  1965.  Phosphorus content of some aquatic macrophytes with
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Dillon, P.J. and  F.H.  Rigler.   1974.  The  phosphorus-chlorophyll  relation-
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 Gerloff,  G.C.   1973.  Plant analysis for nutrient assay of natural waters.
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 Goldman,  C.R.   1972.  The  role of  minor nutrients in limiting  the produc-
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 Harter,  R.D.   1968.  Adsorption of phosphorus by lake sediment.  Soil
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 Johnson,  D.M.   1976.  Atmospheric  Inputs of Trace Metals and Nutrients  to
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 Keachie,  P.  1967.  Personal  communication.

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 Lee, G.F.  1970.   Factors  Affecting the Transfer of  Materials  Between
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 Meier, P.  1977.   Summary  of  Benthic Macroinvertebrates, Phytoplankton, and
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 Menzel, D.W. and  N. Corwin.   1965.  The measurement  of total phosphorus
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 Michigan Department of Natural Resources.  1976.  Personal communication
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 Michigan Water Resources Commission.  1967.  White Lake Nutrient Survey.
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 Michigan Water Resources Commission.  1976.  Industrial Wastewater Surveys,
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 Mortimer, C.H.   1941.   The exchange of dissolved substances between mud
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                                 223

-------
Mortimer, C.H.  1971.  Chemical exchanges between sediments and water in
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Murphy, J. and J.P. Riley.  1962.  A modified single solution method for
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Muskegon County.  1976.  Muskegon County Wastewater Management System,
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O'Brien, J.E.  1962.  Automatic  analysis of chlorides  in sewage.  Wastes
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Porcella,  D.B., J.S. Kumagai, and E.J. Middlebrooks.   1970.   Biological
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Powers,  C.F.  and A.  Robertson.   1965.  Some Quantitative Aspects of the
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    pp.  153-159.

Powers,  C.F.  and A.  Robertson.   1967.  Design  and  Evaluation  of  an  Ail-
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Sands,  H.D.   1974.   A Study  of  the  Biochemical Oxygen Demand, Chemical
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 Schelske,  C.L.   1962.   Iron,  organic  matter,  and other factors limiting
     primary  productivity in  a marl  lake.   Science, 136:45-46.

 Schelske,  C.L.  and E.F. Stoermer.  1971.   Eutrophication,  silica,  and
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 Schwoerbel,  J.   1970.  Methods of Hydrobiology.   Pergamon Press, New York,
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 Shapiro, J.  and G. Glass.  1975.  Synergistic effects of P and Mn on
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 Strickland,  J.D.H. and T.R.  Parsons.   1968.   A Pratical Handbook of Sea-
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 Technicon Instrument Corporation.  1971.  Chloride  in Water  and Waste-
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                                  224

-------
 Technicon  Instrument  Corporation.   1972.  Nitrate and Nitrite in Water
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 Technicon  Instrument  Corporation.   1973a.  Iron in Water and Seawater,
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                                225

-------
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                                 226

-------
                  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

-------
                              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

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                   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

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                              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

-------
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

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               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

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                      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

-------
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

-------
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

-------
 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

-------
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

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     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

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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

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                                  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

-------
     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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