Phase I Diagnostic / Feasibility Study of Campus Lake, Southern Illinois

Illinois EPA Clean Lakes Program

Phase I

Diagnostic / feasibility Study of Campus Lake, Southern Illinois University Carbondale, Jackson County, Illinois

Prepared by

Southern Illinois University Carbondale

Charles Muchmore - College of Engineering John Stahl - College of Science Erik Talley - Center for Environmental Health and Safety Frank M. Wilhelm - College of Science

in cooperation with

Illinois Environmental Protection Agency

Illinois Clean Lakes Program

Phase I Diagnostic/Feasibility Study of Campus Lake, Jackson County, Illinois

Prepared by:

C. Muchmore1, J. Stahl2, E. Talley3 and F. M. Wilhelm2

Southern Illinois University, Carbondale

1College of Engineering 2College of Science 3Center for Environmental Health and Safety

in cooperation with

Illinois Environmental Protection Agency

March 2004

This report was financed in part by a grant from the Illinois Environmental Protection Agency under the Illinois Clean Lakes Program. The contents do not necessarily reflect the views of that agency.

ACKNOWLEDGEMENTS

This report was funded by a grant from the Illinois Environmental Protection Agency (IEPA) under the Clean Lakes program and Southern Illinois University at Carbondale (SIUC). It was conducted primarily under the supervision of faculty from the College of engineering and the College of Science, with support from the Center for Environmental Health and Safety (CEH&S).

The water samples from the lake were taken primarily by Amy Ruffing of CEH&S, as a more intensive sampling program than the voluntary lake sampling effort CEH&S has conducted for several years. Storm event sampling and data entry and analysis were aided by two graduate students in the Department of Mechanical Engineering and Energy Processes, Hongfei Liu and Adam Kaiser. Limnological data entry and analysis was aided by two graduate students in the Department of Zoology, Myra Miyoshi and Mary Kandl. Mary Kandl also aided in obtaining general background information on the region’s recreational facilities. Roy Frank and some of his students from the Department of Civil Engineering conducted the bathymetric survey.

William McMinn, Director of Intramural Recreational Sports at SIUC, provided historical data on the recreational aspects of Campus Lake. Dr. Roy Heidinger of SIUC performed the fisheries survey of Campus Lake. Several representatives from the SIUC Physical Plant contributed suggestions for improvements to the lake.

Dr. Gary B. Dreher of the Illinois State Geological Survey performed the sediment analysis. The phytoplankton analysis was completed by Dr. Larry M. O’Flaherty of Western Illinois University. Analyses of water samples were performed by the IEPA Laboratory in Springfield, IL. Several members of the IEPA including Teri Holland and Gregg Good of the Springfield office and Mike Bundren of the Marion Regional Office contributed to the report. Appreciation is also extended to others who contributed to the project.

ii Table of Contents

PART A: DIAGNOSTIC STUDY - INTRODUCTION ...... 1

1. LAKE IDENTIFICATION AND LOCATION ...... 2

2. GEOLOGICAL AND SOILS DESCRIPTION ...... 7 2.1. GEOLOGICAL AND TOPOGRAPHICAL DESCRIPTION ...... 7 2.2. GROUNDWATER HYDROLOGY ...... 7 2.3. DESCRIPTION OF SOILS ...... 7

3. DESCRIPTION OF PUBLIC ACCESS ...... 14

4. DESCRIPTION OF POPULATION SIZE AND ECONOMIC STRUCTURE ...... 15 4.1. PER CAPITA PERSONAL INCOME (PCPI) ...... 15 4.2. DEMOGRAPHICS OF REGION SURROUNDING CAMPUS LAKE ...... 15

5. SUMMARY OF HISTORICAL LAKE USE ...... 22 5.1. ACTIVITIES AT CAMPUS LAKE ...... 22 5.2. LAKE-ON-THE-CAMPUS BOAT DOCK ...... 22 5.3. CAMPUS BEACH ...... 23 5.4. CAMPUS LAKE TRAIL ...... 23 5.5. FISHING OPPORTUNITIES ...... 23 5.6. CAMPUS LAKE RETREAT AND PICNIC AREAS ...... 23 5.7. SPECIAL EVENTS ...... 24 5.8. PROGRAMMING ...... 24

6. POPULATION SEGMENTS ADVERSELY AFFECTED BY LAKE DEGRADATION ...... 25

7. COMPARISON OF LAKE USES TO OTHER LAKES IN REGION ...... 26

8. DESCRIPTION OF POINT SOURCE POLLUTION DISCHARGES ...... 29

9. LAND USES AND NON-POINT SOURCE POLLUTION LOADINGS ...... 30 9.1. CURRENT AND PAST RESTORATION ACTIVITIES ...... 30

10. BASELINE AND CURRENT LIMNOLOGICAL DATA ...... 33

10.1. HISTORICAL AND CURRENT LAKE WATER QUALITY ...... 33 10.1.a. Water transparency ...... 33 10.1.b. ph and Alkalinity ...... 36 10.1.c. Conductivity ...... 40

iii 10.1.d. Turbidity ...... 42 10.1.e. Suspended Solids ...... 44 10.1.f. Nitrogen ...... 48 10.1.g. Phosphorus ...... 55 10.1.h. Chlorophyll ...... 59 10.1.i. Dissolved Oxygen and Temperature ...... 61 10.2. TROPHIC CONDITION ...... 66 10.3. LIMITING ALGAL NUTRIENT ...... 68 10.4. SEDIMENT QUALITY AND SEDIMENTATION ...... 69 10.4.a. Sediment quality ...... 69 10.4.b. Shoreline erosion in and around Campus Lake ...... 74 10.5. HYDROLOGIC BUDGET ...... 77 10.6. PHOSPHORUS AND NITROGEN BUDGETS ...... 80 10.6.a. Direct wet and dry deposition to the lake ...... 80 10.6.b. Runoff entering the lake from the shoreline and storm drains during storms ...... 81 10.6.c. Waterfowl ...... 83 10.6.d. Groundwater flow to the lake ...... 83 10.6.e. Macrophytes ...... 83 10.6.f. Leaves and other shoreline vegetation that falls into the lake ...... 84 10.6.g. Bottom sediments ...... 84 10.7. SEDIMENT BUDGET ...... 86 10.8. STORM WATER RUNOFF ANALYSIS ...... 87

11. BIOLOGICAL RESOURCES AND ECOLOGICAL RELATIONSHIPS ...... 91

11.1. PHYTOPLANKTON ...... 91 11.2. BACTERIAL DENSITIES ...... 95 11.3. ZOOPLANKTON AND BENTHIC MACROINVERTEBRATES ...... 97 11.3.a. Zooplankton ...... 97 11.3.b. Profundal Benthos ...... 101 11.4. FISHERIES POPULATION ...... 108 11.4.a. Urban Fishing Program ...... 108 11.4.b. Stocking History ...... 108 11.4.c. Fish Community Study ...... 109 11.5. WATERFOWL ...... 113 11.6. AQUATIC VEGETATION ...... 116

iv PART B: FEASIBILITY STUDY ...... 119

1. INTRODUCTION ...... 120

2. FACTORS IMPAIRING THE QUALITY OF CAMPUS LAKE ...... 120 2.1. EXCESSIVE NUTRIENT INPUTS / ALGAE BLOOMS, BLUE-GREENS ...... 120 2.2. POOR ZOOPLANKTON COMMUNITY ...... 121 2.3. BANK EROSION ...... 121 2.4. UNBALANCED FISH POPULATIONS AND LACK OF LONG-TERM MONITORING 122 2.5. INADEQUATE RECREATIONAL ACCESS FOR THE DISABLED ...... 123

3. OBJECTIVES OF THE CAMPUS LAKE IMPROVEMENT PLAN ...... 123

4. ALTERNATIVES FOR ADDRESSING FACTORS IMPAIRING CAMPUS LAKE .124 4.1. IMPROVE WATER QUALITY OF CAMPUS LAKE ...... 124 4.1.a. Watershed level approaches ...... 124 4.1.b. In-lake approaches ...... 126 4.2. REDUCE SHORELINE EROSION ...... 130 4.2.a. Vegetation establishment ...... 130 4.2.b. Physical structures ...... 130 4.3. MAINTAIN HIGH QUALITY FISHING OPPORTUNITIES ...... 130 4.3.a. Manual predator removal ...... 131 4.3.b. Harvest regulations ...... 131 4.3.c. Chemical controls ...... 132 4.3.d. Long-term fish population monitoring ...... 132 4.4. IMPROVE RECREATIONAL ACCESS ...... 132 4.4.a. Renovate existing facilities ...... 132 4.4.b. Develop new access point ...... 133 4.5. ENHANCE PUBLIC KNOWLEDGE ABOUT CAMPUS LAKE ECOSYSTEM ...... 133

5. PROPOSED IMPLEMENTATION STRATEGIES ...... 134

5.1. EROSION CONTROL AND BANK STABILIZATION ...... 134 5.2. RENOVATION OF HORTICULTURE POND ...... 134 5.3. CONSTRUCTION OF SEDIMENT BASINS ...... 135 5.4. CONSTRUCTION OF STORMWATER WETLAND ...... 135 5.5. LAKE AERATION ...... 136 5.6. ZOOPLANKTON MONITORING ...... 136 5.7. LONG-TERM FISH POPULATION MONITORING ...... 137 5.8. INSTALL HANDICAP ACCESSIBLE FISHING PIER ...... 137

v 5.9. WATER QAULITY MONITORING ...... 137 5.10. ENHANCE PUBLIC EDUCATION ...... 138

6. PHASE II WATER QUALITY MONITORING ...... 139

7. PROPOSED PHASE II BUDGET ...... 140 7.1. EXPLANATION OF BUDGET ...... 145

8. SOURCES OF MATCHING FUNDS ...... 146

9. RELATIONSHIP TO OTHER POLLUTION CONTROL PROGRAMS ...... 146

10. PUBLIC INPUT / /PARTICIPATION SUMMARY ...... 147

11. OPERATION AND MAINTENANCE PLAN ...... 147

12. ENVIRONMENTAL EVALUATION ...... 148

13. CAMPUS LAKE IMPLEMENTATION SCHEDULE ...... 151

14. REFERENCES ...... 152

APPENDICES

APPENDIX 1 SAMPLING PROGRAM PROCEDURES ...... 159 A1. BATHYMETRIC MAP ...... 160 A1.1. GENERAL ON-LAKE SAMPLING PROCEDURE ...... 160

A1.2. STORM EVENT SAMPLING ...... 162

A1.3. SEDIMENT CORE SAMPLE COLLECTION AND ANALYSIS ...... 163

A1.4. ZOOPLANKTON AND BENTHOS COLLECTIONS ...... 166

A1.5. MACROPHYTE SAMPLING ...... 166

A1.6. PHYTOPLANKTON ENUMERATION METHODS ...... 166

A1.7. STATISTICAL METHODS ...... 168

APPENDIX 2 SEDIMENT ANALYSIS AND QUALITY ASSURANCES ...... 169

APPENDIX 3 PHYTOPLANKTON REFERENCES AND TABLES ...... 177

APPENDIX 4 DETAILED ZOOPLANKTON AND BENTHOS COUNT DATA ...... 193

vi LIST OF FIGURES

PART A: DIAGNOSTIC STUDY

Figure 1-1. Location of Campus Lake in Carbondale, Illinois...... 3 Figure 1-2. Watershed and sub-watershed map of Campus Lake...... 4 Figure 1-3. Bathymetric contour map of Campus Lake ...... 5 Figure 2.3-1 Surface soil map for the Campus Lake watershed ...... 8 Figure 9.1-1. Map showing location of storm drains to Campus Lake ...... 31 Figure 10.1.a-1. Seechi depths in Campus Lake ...... 34 Figure 10.1.b-1. pH in Campus Lake ...... 37 Figure 10.1.b-2. Alkalinity in Campus Lake ...... 38 Figure 10.1.c-1. Conductivity in Campus Lake ...... 41 Figure 10.1.d-1. Turbidity in Campus Lake ...... 43 Figure 10.1.e-1. Total suspended solids (TSS) in Campus Lake ...... 46 Figure 10.1.e-2. Volatile suspended solids (VSS) in Campus Lake ...... 47 Figure 10.1.f-1. Ratio fo organic to toal nitrogen in Campus Lake ...... 50 Figure 10.1.f-2. Nitrate and nitrite nitrogen in Campus Lake ...... 51 Figure 10.1.f-3. Un-ioninzed ammonia in Campus Lake ...... 52 Figure 10.1.f-4. Ammonium in Campus Lake ...... 53 Figure 10.1.f-5. Total Kjeldahl nitrogen in Campus Lake ...... 54 Figure 10.1.g-1. Total phosphorus in Campus Lake ...... 57 Figure 10.1.g-2. Dissolved phosphorus in Campus Lake ...... 58 Figure 10.1.h-1. Chlorophyll in Campus Lake ...... 60 Figure 10.1.i-1. Isopleths of dissolved oxygen concentrations in Campus Lake ...... 63 Figure 10.1.i-2. Temperature isopleths in Campus Lake ...... 65 Figure 10.2-1. Trophic status index (TSI) trends in Campus Lake ...... 67 Figure 10.4.b-1. Map of erosion around Campus Lake ...... 76 Figure 11.1-1. Density of algal species in Campus Lake ...... 94 Figure 11.2-1. Densities of fecal coliform bacteria in Campus Lake ...... 96 Figure 11.3.a-1. Densities of zooplankton in Campus Lake ...... 98 Figure 11.4.c-1. Relative weight of Largemouth bass and bluegill in Campus Lake ...... 111 Figure 11.4.c-2. Proportional stock densities of fish in Campus Lake ...... 112 Figure 11.5-1. Total number of waterfowl visiting Campus Lake ...... 114 Figure 11.5-2. Waterfowl dropping accumulation for one night at Campus Lake ...... 115

vii APPENDICES Figure A1.3-1. Sediment corer used to sample sediment in Campus Lake ...... 163 Figure A1.3-2. Locations of sediment core samples in Campus Lake ...... 164

viii LIST OF TABLES

PART A: DIAGNOSTIC STUDY Table 1-1. Designated uses for Campus Lake based on Illinois Environmental Protection Agency section 305b Report ...... 6 Table 2.3-1. Campus Lake watershed soil types ...... 9 Table 4.2-1. Estimates of population and age distribution of residents of counties in Illinois within an 80-km (50-mile) radius of Campus Lake, 1990 ...... 16 Table 4.2-2. Estimates of population and age distribution of residents of counties in Illinois within an 80-km (50-mile) radius of Campus Lake, July 1, 1996...... 17 Table 4.2-3. Estimates of population and age distribution of residents of counties in Illinois within an 80-km (50-mile) radius of Campus Lake, July 1, 1997...... 18 Table 4.2-4. Population estimates for towns in Jackson County (1990) ...... 19 Table 4.2-5. Selected social characteristics of the population in Jackson County for 1989-1990...... 20 Table 7.1-1. Public access lakes $4 ha (10 acres) within an 80-km (50-mile) radius of Campus Lake ...... 27 Table 10.1.e-1. Mean lake-wide contribution of volatile suspended solids to total suspended solids ...... 45 Table 10.2-1. Relationship between Carlson’s (1977) trophic state index (TSI) and lake condition ...... 66 Table 10.4.a-1. Current and historical sediment quality data for Campus Lake ...... 70 Table 10.4.a-1. Classification of Illinois Lake sediments ...... 71 Table 10.4.b-1. Areas of shoreline erosion around Campus Lake ...... 75 Table 10.5-1. Sub-watershed rainfall flow volume into Campus Lake ...... 77 Table 10.5-2. Sub-watershed and their associated discharge points for Campus Lake ...... 78 Table 10.5-3. Spillway gauge heights and seasonal flow volumes ...... 79 Table 10.6.b-1. Mean storm water runoff parameter for each sub-watershed around Campus Lake ...... 81 Table 10.6.b-2. Annual discharge amount for each sub-watershed from Campus Lake ...... 82 Table 10.6.b-3. Nutrient outflow over spillway for spring, summer and fall in Campus Lake .. 83 Table 10.6.g-1. Nutrient budget for total phosphorus and nitrogen for Campus Lake ...... 85 Table 10.8-1. Mean concentrations of constituents in storm water runoff entering Campus Lake ...... 88 Table 10.8-2. Ranking of 15 sites which contribute the highest concentration of each constituent to Campus Lake ...... 89 Table 10.8-3. Weight factor for calculating importance of storm drain contribution to the mass of constituents entering Campus Lake ...... 89 Table 10.8-4. Storm drain discharge point ranking based on weights ...... 90 Table 11.1-1. Summary of algae found in Campus Lake ...... 93

ix Table 11.1-2. Biovolume summary of algae in Campus Lake ...... 93 Table 11.3.b-1. Population density of principal benthic groups at sampling Site 1 in Campus Lake ...... 102 Table 11.3.b-2. Population density of principal benthic groups at sampling Site 2 in Campus Lake ...... 103 Table 11.3.b-3. Population density of principal benthic groups at sampling Site 3 in Campus Lake ...... 104 Table 11.3.b-4. Population density of other benthic taxa at Sites 1, 2 and 3 in Campus Lake 107 Table 11.6-1. Summary of dry weights and percentages of macrophytes from Campus Lake surveys ...... 117

PART B: FEASIBILITY STUDY Table 6.1. Detailed Phase II water quality monitoring program for Campus Lake ...... 139 Table 7. Budget ...... 140 Table 13. Campus Lake Phase II Implementation Schedule ...... 151

APPENDICES Table A1-2. Parameters and constituents analyzed for storm water runoff entering Campus Lake ...... 162 Table A1.3-1. Depth and location of sediment cores from Campus Lake ...... 165 Table A2-1. Quality control assurance for major and minor elements ...... 170 Table A2-2. Quality control assurance for trace elements ...... 171 Table A2-3. Historic sediment quality parameters for Campus Lake Site 1 ...... 172 Table A2-4. Historic sediment quality parameters for Campus Lake Site 2 ...... 174 Table A2-5. Historic sediment quality parameters for Campus Lake Site 3 ...... 175 Table A3.2-1. List of taxa of algae found at Site 1 in Campus Lake ...... 181 Table A3.2-2. Size, volume, density and biovolume of individual organisms found in Campus Lake ...... 185 Table A4.1-1. Summary of taxa means and total number of organisms on each sampling date for three stations in Campus Lake ...... 195 Table A4.1-2. Summary of Daphnia counts and station means for Campus Lake ...... 196 Table A4.1-3. Summary of Ceriodaphnia counts and station means for Campus Lake ...... 197 Table A4.1-4. Summary of Bosmina counts and station means for Campus Lake ...... 198 Table A4.1-5. Summary of adult and copepodid Copepoda counts and station means for Campus Lake ...... 199 Table A4.1-6. Summary of adult and copepodid Calanoid copepod counts and station means for Campus Lake ...... 200 Table A4.1-7. Summary of cyclopoid and calanoid nauplii counts and station means for Campus Lake ...... 201

x Table A4.1-8. Summary of rotifer counts and station means for Campus Lake ...... 202 Table A4.1-9. Dates on which rotifer species occurred in samples taken from Campus Lake ...... 203

xi PART A

DIAGNOSTIC STUDY OF CAMPUS LAKE, JACKSON COUNTY, ILLINOIS

INTRODUCTION

Southern Illinois University Carbondale (SIUC) was awarded a grant from the Illinois Environmental Protection Agency (IEPA) in 1997 to conduct a Phase 1 Study of Campus Lake under the Clean Lakes Program of Conservation 2000. The study was primarily a joint effort of the Department of Mechanical Engineering and Energy Processes in the College of Engineering and the Department of Zoology in the College of Science. Assistance was provided by the Center for Environmental Health and Safety at SIUC. The major objectives of this study were to establish the current quality of the lake and to determine the source(s) of any water-borne pollutants to the lake. Based on the findings, potential corrective measures were proposed. The grant also provided support for the direct involvement and training of graduate and undergraduate students, increasing their knowledge of and appreciation for the quality of the lake and the lake management profession in general. Publicity in the local newspapers, radio and TV stations further enhanced the educational mission of the study.

1 1. LAKE IDENTIFICATION AND LOCATION

Campus Lake is located in the Big Muddy River Watershed in southern Illinois (Figure 1- 1). It is located in the southern portion of the SIUC campus in Carbondale, Jackson County, Illinois (Figure 1-2) and is thus a full access public lake. Campus Lake is located in the municipality of Carbondale at a location of 37/7'N and 89/2'W and was originally named Thompson Lake, the label found on older topographic maps. On the SIUC campus, Campus Lake is located within the Southeast Quarter of the Northwest Quarter; the Southwest Quarter of the Northwest Quarter; the Northwest Quarter of the Northwest Quarter and the Northwest Quarter of the Southwest Quarter of Section 28, Township 9 South, Range 1 W est of the Third Principal Meridian and the Northeast Quarter of the Northeast Quarter; the Southeast Quarter of the Southeast Quarter of Section 29, Township 9 South, Range 1 West of the Third Principal Meridian, all in Jackson County, Illinois. The Illinois counties located within a 50 mile radius of Campus Lake are shown in Figure 1-1. Campus Lake is located in EPA Region 5. The watershed of Campus Lake covers approximately 94 ha (232 acres) (Figure 1-2). The northern side of Campus Lake is classified as urban, with a mix of buildings, parking lots, grassed area and trees. This represents approximately one half of the watershed. Regions to the west of the lake are primarily grasses and trees, with the northwest corner of the watershed being primarily wooded. The area to the south of the lake is also heavily wooded. There are no permanent tributaries entering the lake. Based on the soil type descriptions given in the following section (predominantly clay type), exchange between groundwater and the lake is assumed to be negligible. Thus, the lake is fed primarily by rainwater falling directly on the lake and runoff from the watershed, particularly during storm events. When the lake level exceeds that of the spillway, water flows from the lake to an unnamed tributary, eventually reaching the Big Muddy River which is a subwatershed of the Mississippi River and is designated by the HUC 07140106 (HUC - Hydrologic Unit Code, a US-W ide classification system of all watersheds). During extreme high water levels, water may also occasionally leave the lake via the President’s pond (Figure 1-2). The maximum elevation range of the watershed is 14.6 m (48 feet) (103 to 148 m [337 to 485 feet] above sea level) in the northwest corner. The spillway sill for the lake is located 133 m (437 feet) above mean sea level. Campus Lake has a surface area of 16.2 ha (40 acres), a maximum depth of 5.2 m (17 feet) and a mean depth of 2.43 m (8 feet). The lake volume is 39.5 ×104 m (320 acre feet) and the mean retention time is 1.73 years. A bathymetric map of Campus Lake was developed during this study by Dr. Roy Frank and surveying students of the Civil Engineering Department during the course of this study. A modified version is shown in Figure 1-3.

2 Clinton Co. Marion Co.

57 Illinois 64

64 Washington Co.

2 1 Jefferson Co.

Randolph Co. Perry Co. Hamilton Co. Franklin Co. Jackson Co. 51 57 9 14 3 Carbondale Marion 13

2 1 Campus Lake Williamson Co. Saline Co. Johnson Co. Pope Co. Union Co.

146

Alexander Co. N Pulaski Co. 45 Massac Co.

0 50 MILES

0 100 KILOMETERS

Figure 1-1. Location of Campus Lake in Carbondale, Illinois. Counties of southern Illinois are indicated by dashed red lines ( ). Major highways are numbered; the watershed of the Big Muddy River is indicated in blue ( ), while the solid black circle ( ) marks a Radius of 50 miles from Campus Lake. Source: Modified from IDNR and ISGS Digital Raster Graphics (DRG) 1:100 000 topographic maps and statewide GIS data.

3 CHAUTAQUA RD.

F E

B 0 D 5 J 4 H I G C H A

K Campus Lake O L N

. M

T P

F 45 F 0

c 51

E. PLEASANT HILL RD. N

0 0.5 1.0 MILES

0 0.5 1.0 KILOMETERS

Figure 1-2. Location of Campus Lake on the portion of the Southern Illinois University Campus bounded by Chautaqua, McLafferty and E. PLeasant Hill Roads and Highway 51 in Jackson Co. IL. The Campus Lake watershed is indicated by the solid purple line ( ). Subwatersheds are marked in a similar manner and identified with a capital letter. The horticulture (H) and President’s (P) ponds are also shown. Contour interval = 10 feet. Source: Modified from IDNR and ISGS Digital Raster Graphics (DRG) 1:24 000 topographic maps.

4 Boat Dock

. Roy Frank,

1000 FEET

Spillway (336.6’ ASL)

250 METERS DAM A-A.

age is 336.6 feet above sea

Thompson Point and Greek

, and Tom Likes.

500

16.6

ared by SIUC Civil Engineering Survey

14.6

Thompson Point Dorms

Map prep Specialization. Field work and drawing by: Dr Ted Hartke, Nathan Dozier

Note: Depths were originally measured as elevations above mean sea level. Lake st level.

12.6

10.6

8.6

2.6

6.6 4.6 0.6

’s Pond is extension of Campus Lake and joins at matchline

Greek Row Dorms

’s

Bathymetric map of Campus Lake at Southern Illinois University Carbondale Campus, Jackson Co. IL.

To President Pond

Row dorms are student housing at SIUC. President

President Pond

Figure 1-3.

5 Water quality standards which apply to the lake include State of Illinois Rules and Regulations Title 35: Environmental Protection: Subtitle C: Water Pollution, Chapter 1: Pollution Control Board, Part 302, Subpart B: General Use Water Quality Standards. Designated uses as indicated in the IEPA 305B Reports are listed in Table 1-1.

Table 1-1. Designated uses for Campus Lake based on Illinois Environmental Protection Agency 305- b Report (IEPA 2002)

Use Description

F20 Full support: Aquatic life N42 Nonsupport: Primary contact (swimming) P1 Partial support: Overall use P20 Partial support: Aquatic life P44 Partial support: Secondary contact (recreation) X21 Use not assessed: Fish Consumption

6 2. GEOLOGICAL AND SOILS DESCRIPTION

2.1. GEOLOGICAL AND TOPOGRAPHICAL DESCRIPTION

Campus Lake is located approximately 16 km (10 miles) west of Crab Orchard Lake. In a 1993 engineering report prepared for the remedial investigation of the polychlorinated biphenyl (PCB) contaminated sediments and soils at the Crab Orchard Superfund site, the geology of this region was described as follows: “The Geology of the area was briefly described by O’Brien and Gere (1988). The bedrock which underlies the soil sequence consists of Pennsylvanian Age sandstones and shales known as the Carbondale Formation (American Association of Petroleum Geologists 1965 in O’Brien and Gere 1988). The upper portion of the bedrock sequence, penetrated by split spoon sampling, consists predominantly of sandstone. The area is situated near the southern limit of the Illinois basin structural feature. As a result, the bedrock in the area dips gently to the north and northeast.”

2.2. GROUNDWATER HYDROLOGY

The groundwater hydrology of Campus Lake and its watershed have not been thoroughly investigated. However, given the perched nature of the lake and its watershed (see elevations in Figure 1-2) and the impervious soil types in the watershed and surrounding vicinity (see Description of soils below), it is unlikely that groundwater plays a major role in hydrology of Campus Lake.

2.3. DESCRIPTION OF SOILS

An inventory of soil types found in the Campus Lake watershed is listed in Table 2.3-1 and shown in Figure 2.3-1 (US Department of Agriculture, 1979). The listing for soil type is an alpha numeric code (e.g., 214B2) in which the first number (214) indicates the soil name, the capital letter (B) provides the slope range and the third part (2) describes the degree of erosion. Descriptions of the soil types provided by the United States Department of Agriculture (1979) are given below. The order of the listing is that observed on the map starting at the far eastern end of the lake, where the spillway is located, and proceeding counter-clockwise around the lake. 533 - Urban land. This mapping unit consists primarily of the commercial areas of downtown Carbondale and Murphysboro and densely built-up sections of Southern Illinois

7 CHAUTAQUA RD.

164B 3 214B C 21 4 4 1 16 C 2 4B 2 2 1 4 533 C 2 214B H 801

2 214C B

6 1 Campus Lake 108 801 214B 214B 214C2 2 1 4 D 3

. D 164B R 214B 164B Y 2 T P 1

R 4 B E 108

c 51

E. PLEASANT HILL RD. N

0 0.5 1.0 MILES

0 0.5 1.0 KILOMETERS

Figure 2.3-1. Soils map of the Campus Lake watershed located on a portion of the Southern Illinois University Campus in Carbondale, Jackson Co. Il. bounded by Chautaqua, McLafferty, and E. Pleasant Hill Roads and State Hiway 51. The watershed is the region enclosed by the purple ( ) line. Soil type contours and descriptive number (see text) are in light brown ( ). Source: Base map modified from IDNR and ISGS Digital Raster Graphics (DRG) 1:24000 topographic maps; soil types modified from USDA 1979.

8 Table 2.3-1. Campus Lake watershed soil types.

Soil Type Name Slope (%)

164B Stoy Silt Loam 2-4

214B Homser Silt Loam 2-7

214C2 Homser Silt Loam 7-12

533 Urban Land -

801 Orthens Silt Loam -

University. The areas are rectangular in shape and range from about 20 to 81 ha (50 to 200 acres) in size. Typically, this unit consists of buildings, streets, sidewalks, and parking lots. Interspersed are some natural soil areas and disturbed soil areas that have been filled with bricks and cinders. Included in mapping are primarily Alvin, Camden, and St. Charles soils in the vicinity of Murphysboro, and Hosmer and Stoy soils in the Carbondale and Southern Illinois University area. Some areas of Orthents, silty are also included. For most uses, onsite investigation is necessary to determine suitability of the particular site.

214B - Hosmer silt loam, 2 to 7 percent slopes. This gently sloping, moderately well drained soil is on convex ridge tops, knolls, and side slopes along drainage ways. Individual areas of this soil are elongated or irregular in shape and range from 0.81 to about 404 ha (2 to about 1 000 acres) in size. Typically, the surface layer is brown silt loam about 9 inches thick. It ranges from 0.1 to 0.25 m (4 to 10 inches) in thickness over most of the area. The subsoil is about 1.04 m (41 inches) thick. The upper 0.36 m (14 inches) is strong brown light silty clay loam and heavy silt loam and mottled yellowish brown heavy silt loam. In the lower 0.7m (27 inches) the subsoil is a firm, compact zone; a thin layer of mottled, yellowish brown heavy silt loam, which has thick, pale brown coatings, overlies mottled yellowish brown and dark yellowish brown and pale brown, very firm silt loam. The substratum to a depth of about 1.7 m (67 inches) is mottled yellowish brown and pale brown, firm silt loam. In some places the upper part of the subsoil is thicker and the very firm, compact lower part is deeper and thinner. In other places the surface layer is dark yellowish brown. Included with this soil in mapping are a few areas of similar soils on short, steep slopes

9 and escarpments, a few small wet areas, and a few severely eroded areas. Also included are small areas of Alford and Stoy soils. Alford soils are on high knolls on ridges and Stoy soils are at the head of drainage ways and in nearly level areas on broad ridge tops. Inclusions make up about 5 percent of this unit. Water and air move through the upper part of the subsoil at a moderate rate and through the compact lower part at a very slow rate. Surface runoff from cultivated areas is medium. Reaction ranges from extremely acid to strongly acid in the subsoil and varies in the surface layer because of local liming practices. The surface layer is friable and easily tilled but tends to crust or puddle after hard rains. Root development is restricted below a depth of about 0.64 to 1.0 m (25 to 40 inches) by the very firm, compact lower part of the subsoil. Organic-matter content is low, and available water capacity is moderate. This soil is suited to building site development if the limitation imposed by the perched water table in the subsoil is overcome. Sewage lagoons function well, whereas septic tank adsorption fields do not function well because of reduced permeability. Proper design and installation of footings and footing tile will eliminate wetness and frost-action hazards. Capability subclass Iie; woodland suitability subclass 2o.

164B - Stoy silt loam, 2 to 4 percent slopes. This gently sloping, somewhat poorly drained soil is on undugently ridgetops, side slopes along drainageways, and foot slopes. Individual areas of this soil are irregular or elongated in shape and range from 0.81 to about 61 ha (2 to about 150 acres) in size. Typically, the surface layer is mixed dark grayish brown and brown silt loam about 0.2 m (8 inches) thick. It is underlain by a yellowish brown silt loam subsurface layer about 6 inches thick. The subsoil is about 1.07 m (42 inches) thick. The upper part is mixed yellowish brown, pale brown, and light brownish gray silt loam. The next layer is mottled yellowish brown and light brownish gray silty clay loam. The lower part is firm and slightly brittle, dark yellowish brown and light brownish gray silt loam. The substratum to a depth of about 1.62 m (64 inches) is mottled yellowish brown silt loam. In some places the firm and slightly brittle zone extends into the substratum. Included with this soil in mapping are a few small areas of short, steep slopes, a few depressions in wet areas, and a few severely eroded areas. Also included are a few areas of the poorly drained Weir soils on ridgetops, mainly at the head of drainageways; some areas of the better drained Hosmer soils along side slopes; and a few areas of more sloping Stoy soils along drainageways. Inclusions make up about 5 percent of this unit. Water and air move through this soil at a slow rate, and surface runoff from cultivated

10 areas is medium. Reaction in the subsoil ranges from extremely acid to strongly acid. The surface layer is friable and easy to till but tends to crust or puddle because of low organic-matter content and poor surface structure. Available water capacity is high. This soil is suited to trees, and a few areas remain in native hardwoods. Although growth rates are somewhat slow, there are no serious hazards to be concerned with after an adequate stand is established to limit erosion. This soil is not well suited to building site development or adsorption field waste disposal systems because of slow permeability and wetness. Sewage lagoons can be safely installed in the lesser sloping areas without much difficulty, although some reshaping of slopes is normally required. Surface drainage will eliminate much of the excess water, and footing drain tile should be installed to remove additional water from around foundations. Capability subclass IIe; woodland suitability subclass 3o.

214C2 - Hosmer silt loam, 7 to 12 percent slopes, eroded. This sloping, moderately well drained soil is on narrow ridgetops, knolls, and side slopes. Individual areas of this soil are irregular or elongated and range from 0.8 to about 20 ha (2 to about 50 acres) in size. Typically, the surface layer is dark yellowish brown silt loam about 0.15 m (6 inches) thick. It ranges from 0.1 to 0.2 m (4 to 8 inches) in thickness over most of the area. The subsoil is about 1.04 m (41 inches) thick. The upper 0.36 m (14 inches) is strong brown light silty clay loam over mottled yellowish brown heavy silt loam. In the lower 0.69 m (27 inches) the subsoil has a very firm and compact zone; a thin layer of mottled yellowish brown heavy silt loam, which has thick pale brown coatings, overlies mottled dark yellowish brown, very firm and compact silty clay loam and mottled dark yellowish brown, very firm and compact silt loam. The substratum to a depth of about 1.63 m (64 inches) is mottled yellowish brown, firm silt loam. In some places the upper part of the subsoil is thicker, and the very firm, compact lower part of the subsoil is deeper and thinner. In wooded areas the surface layer is dark grayish brown and is underlain by a yellowish brown silt loam subsurface layer. Included with this soil in mapping are a few small areas that are severely eroded. These areas are at the end of ridges and on side slopes. Also included are small areas of Stoy and Alford soils. Stoy soils are at the head of drainageways, and Alford soils are on higher knolls or ridgetops. Inclusions make up about 5 percent of this unit. Water and air move through the upper part of the subsoil at a moderate rate and through the very firm and compact lower part at a very slow rate. Surface runoff in cultivated areas is medium to rapid. Reaction ranges from extremely acid to strongly acid in the subsoil and varies in the surface layer because of local liming practices. The surface layer is friable and easily

11 tilled but tends to crust or puddle after hard rains, especially in areas where the plow layer contains subsoil material. Root development is restricted below a depth of 0.51 to 0.91 m (20 to 36 inches) by the very firm, compact zone. Organic-matter content is low, and available water capacity is moderate. This soil is well suited to trees, and many areas are in native hardwoods. Tree seeds and seedlings survive and grow well if competing vegetation is controlled or removed by site preparation or by spraying, cutting or girdling. Windthrow is a problem because of the restricted rooting depth and the perched water. Pine trees grow well and are adapted to this soil because of their tap root system. This soil is suitable for building site development if proper design and installation are used. Streets and roads are subject to frost action, which can be controlled by proper banking and ditching to remove excess water. Capability subclass IIIe; woodland suitability subclass 2o.

801 - Orthents, silty, sloping. These nearly level to moderately steep, somewhat poorly drained and moderately well drained soils are mostly in cut and fill areas of silty upland and terrace soils. Individual areas are rectangular or irregular in shape and range from about 2 to 809 ha (5 to 2000 acres) in size. Typically, these soils consist of mottled brown silt loam and silty clay loam to a depth of about 1.52 m (60 inches). Reaction is commonly strongly acid to slightly acid. Where terrace soils predominate, this mapping unit is more variable in texture, which ranges from silty clay to loamy fine sand and is similar to that of the adjoining soils. Included with these soils in mapping are a few areas of soils on levees and in borrow pits that consist of material similar to that of these Orthents. The levee areas have moderately steep side slopes, and the borrow pits have nearly vertical sidewalls and have flat bottoms, some of which are ponded for extended periods. Also included are a few areas of soils that have coarse fragments and other areas of soils that contain cinders, bricks, or organic debris. Inclusions make up 10 to 15 percent of this unit. Water and air move through these soils at a moderate to slow rate, and surface runoff is rapid to ponded. Reaction ranges from extremely acid to mildly alkaline. The surface is friable to very firm. Organic-matter content is very low, and available water capacity is moderate to high. Most areas of these soils have been or are being used for construction sites. These soils have poor to fair potential for cultivated crops, hay, and pasture, fair to good potential for trees, and poor to good potential for recreation, wildlife, and most engineering uses. These soils are suitable for building site development in places that have been

12 compacted to eliminate settling. Proper design and installation of footings and foundations is necessary to avoid damage from differential settling. Special onsite investigations are needed to determine the proper waste disposal system to install. Capability subclass IVe.

13 3. DESCRIPTION OF PUBLIC ACCESS

Carbondale and Campus Lake are readily accessible from the east and west by State Highway 13, and from the north or south by State Highway 51 (Figure 1-1). The Illinois Central Railroad (Amtrack) also runs north-south through the center of town with a station located on Illinois Avenue. The Saluki Bus Service is a local service which serves the University Campus and City of Carbondale. A bus stop is located near Campus Lake. The Lake is also easily accessible to students, other pedestrians who live close by and by bicycle from anywhere within Carbondale. A 3.5 km (2.2 mile) paved walking trail through the predominantly wooded lakeshore surrounds the entire lake. Fitness stations are also located along the trail. Because the lake is located on the grounds of SIUC, a public institution in the State of Illinois, the entire lake is open and accessible to the public. The SIUC Recreation Center oversees the Lake-on- the-Campus Boat Dock where small paddle boats and canoes are available for hire for a nominal fee (see Summary of Historical Lake Use below).

14 4. DESCRIPTION OF POPULATION SIZE AND ECONOMIC STRUCTURE

The following facts for Jackson County were obtained from the Regional Economic Information System, Bureau of Economic Analysis. Jackson is one of 102 counties in Illinois. It is not part of a metropolitan area and its 1990 population of 61 000 ranked 22nd in the state.

4.1. Per Capita Personal Income (PCPI)

The 1990 Per Capita Personal Income (PCPI) in Jackson County was $12 931, which ranked 97th in the state, and was 37% less than the state average ($20 433) and 31% less than the national average ($18 696). The average annual growth rate of PCPI over the past 10 years was 6.5%, which was the same as the state and national values (6.5%). The largest industries in 1990 were state and local government, which accounted for 41.7%, 21.0% and 11.3% of earnings, services, and retail trade, respectively.

4.2. Demographics of Region Surrounding Campus Lake

The demograpics of the region represented by the Illinois counties within a 80-km (50- mile) radius of Campus Lake are summarized in Tables 4.2-1 through 4.2-5. Table 4.2-1 provides 1990 estimates on a percentage basis of the population and age distribution of residents while population figures, broken down by age group, reported July 1, 1996 and July 1, 1997, respectively are presented in Tables 4.2-2 and 4.2-3. Further details for Jackson County residents in terms of selected social characteristics for 1990 are given in Table 4.2-5. Family and non-family income information for 1989 is presented as well. Overall median household income in Jackson County was $17 567, while median family income and non-family household incomes were $27 307 and $8 846, respectively. The differences are the result of the population structure in the Carbondale/Murphysboro area which includes a high percentage of university employees and students. Vehicle availability and a breakdown of households by types are also given. The students attending SIUC contribute a large proportion of the population (22 160 average for the years 1997-1999) to the Carbondale area. First- and second-year students stay in University housing, including Thompson Point and Greek Row residences located next to Campus Lake (see Figure 1-3). Approximately 1 530 students live in these residences, while another 3 500 students live in Campus Park, less than 2.4 km (1.5 miles) distant from Campus Lake.

15 Table 4.2-1. Estimates of population and age distribution of residents of counties in Illinois within an 80-km (50-mile) radius of Campus Lake, 1990. No. of Age classes (%) $5 < 18 $18<25 $25-45 $45<64 $65 $80 County Persons < 5 yrs. yrs. yrs. yrs. yrs. yrs. yrs.

Alexander 10 626 8.4 28.8 7.9 25.6 19.6 18.1 4.7 Franklin 40 319 6.1 24.0 8.6 27.1 20.1 20.2 4.9 Hamilton 8 499 5.9 24.0 7.0 26.2 21.0 21.7 5.9 Jackson 61 067 5.5 19.0 28.3 28.0 14.0 10.8 2.6 Jefferson 37 020 7.4 26.9 8.4 29.3 18.9 16.5 4.1 Johnson 11 347 4.8 19.8 10.1 34.1 20.6 15.4 3.6 Masaac 14 752 5.8 23.7 8.0 27.4 21.5 19.3 5.0 Perry 21 412 6.8 26.4 8.6 28.6 19.4 17.1 4.2 Pope 4 373 5.1 23.1 12.3 26.2 20.1 18.4 4.2 Pulaski 7 523 7.2 28.9 7.8 25.2 19.4 18.8 4.9 Randolph 34 583 6.1 24.3 9.8 32.3 18.3 15.3 4.0 St. Clair 262 852 8.0 28.5 9.9 31.0 18.0 12.7 2.9 Saline 26 551 6.1 24.1 8.1 26.6 20.8 20.4 5.4 Union 17 619 6.1 23.2 8.2 28.3 21.4 18.9 5.0 Washington 14 965 6.7 26.3 7.5 28.3 19.3 18.6 4.8 Williamson 57 733 6.4 24.0 9.0 29.8 20.3 16.9 4.0

Total 631 241 6.4 24.7 9.9 28.4 19.5 17.4 4.4

State of Illinois 11 430 602 7.4 25.8 10.6 32.3 18.7 12.6 2.9

Note: All values in age categories are percent of total.

16 Table 4.2-2. Estimates of population and age distribution of residents of counties in Illinois within an 80-km (50-mile) radius of Campus Lake, July 1, 1996. Age classes Total No. County < 5 yrs $5<18 yrs $18<24 yrs $25<45 yrs $45<65 yrs $16 yrs $21yrs $65 yrs $85 yrs of persons

Alexander 10 209 866 2 087 818 2 533 2 046 7 560 6 966 1 859 252 Franklin 40 972 2 433 7 518 2 999 10 766 8 805 32 305 29 593 8 441 1 047 Hamilton 8 583 491 1 578 519 2 191 1 892 6 750 6 256 1 912 268 Jackson 61 047 3 540 8 778 15 511 16 942 9 402 50 023 41 102 6 874 829 Jefferson 39 054 2 697 7 554 3 007 11 612 7 854 29 976 27 358 6 330 784 Johnson 12 898 588 1 914 1 014 4 762 2 643 10 733 9 961 1 977 227 Massac 15 315 857 2 827 1 052 4 050 3 512 12 086 11 118 3 017 406 Perry 21 449 1 417 4 257 1 653 5 980 4 442 16 441 15 001 3 700 475 Pope 4 710 226 856 553 1 192 1 022 3 832 3 334 861 109 Pulaski 7 316 512 1 625 494 1 764 1 484 5 380 4 913 1 407 198 Randolph 34 254 2 062 6 373 3 110 10 749 6 590 26 775 24 739 5 370 709 St. Clair 264 243 21 742 55 633 22 861 79 208 50 690 195 371 176 775 34 109 4 003 Saline 26 503 1 580 4 906 1 816 6 861 5 826 20 848 19 117 5 514 736 Union 18 066 1 072 3 163 1 249 4 914 4 169 14 351 13 247 3 499 418 Washington 15 201 993 3 045 967 4 151 3 142 11 605 10 712 2 903 397 Williamson 60 606 3 772 10 853 4 833 17 676 13 131 47 790 43 650 10 341 1 248

State of 11 845 316 912 768 2 240 199 1 099 007 3 734 887 2 372 707 9 031 394 8 211 490 1 485 748 172 793 Illinois

17 Table 4.2-3. Estimates of population and age distribution of residents of counties in Illinois within an 80-km (50-mile) radius of Campus Lake, July 1, 1997. Age classes Total No. of County <5 yrs $5<18yrs $18<25 yrs $25<45 yrs $45<65 yrs $16 yrs $21 yrs $65 yrs $85 yrs persons

Alexander 10 029 830 2 064 800 2 463 2 048 7 439 6 842 1 824 250 Franklin 40 679 2 372 7 486 2 967 10 568 8 932 32 116 29 376 8 354 1 072 Hamilton 8 621 483 1 588 512 2 174 1 946 6 790 6 288 1 918 276 Jackson 60 698 3 462 8 794 15 382 16 683 9 569 49 749 40 758 6 808 845 Jefferson 38 966 2 644 7 580 2 989 11 439 8 008 29 931 27 274 6 306 807 Johnson 13 074 587 1 958 1 020 4 765 2 745 10 879 10 083 1 999 235 Massac 15 420 845 2 861 1 062 4 030 3 600 12 181 11 186 3 022 414 Perry 21 368 1 391 4 260 1 646 5 882 4 517 16 390 14 928 3 672 483 Pope 4 681 222 852 549 1 172 1 035 3 812 3 313 851 106 Pulaski 7 209 522 1 611 480 1 715 1 490 5 304 4 841 1 391 201 Randolph 34 082 2 014 6 367 3 086 10 576 6 707 26 667 24 609 5 332 724 St. Clair 263 866 21 240 56 055 22 664 78 255 51 712 195 187 176 272 33 940 4 075 Saline 26 359 1 541 4 890 1 801 6 737 5 921 20 764 19 018 5 469 751 Union 18 037 1 053 3 163 1 243 4 847 4 248 14 348 13 227 3 483 429 Washington 15 325 984 3 086 971 4 121 3 240 11 708 10 791 2 923 416 Williamson 61 163 3 746 11 003 4 867 17 608 13 547 48 265 44 016 10 392 1 293

State of 11 895 849 903 568 2 270 655 1 094 701 3 713 201 2 432 421 9 068 279 8 231 351 1 481 303 176 859 Illinois

18 Table 4.2-4. Population estimates for towns in Jackson County (1990).

County / Town Population

Jackson County 61 067

Bradley 1 659 Carbondale 31 252 Degognia 174 De Soto 2 073 Elk 2 091 Fountain Bluff 304 Grand Tower 903 Kinkaid 365 Levan 596 Makanda 3 700 Murphysboro 11 316 Ora 365 Pomona 769 Sand Ridge 800 Somerset 4 021 Vergennes 679

Table 4.2-5. Selected social characteristics of the population in Jackson County for 1989-1990

No. of URBAN AND RURAL RESIDENCE persons Urban population 36 209.0 % of total population 59.3 Rural population 24 858.0 % of total population 40.7 Farm population 1 718.0 % of population 2.8 Total population 61 067.0

19 Table 4.2-5. Continued.

EDUCATIONAL ATTAINMENT No. of persons Persons $25 yrs 32 172 Less than 9th grade 3 283 9th to 12th grade, no diploma 3 548 High school graduate 7 617 % highschool grad or higher 78.8 Some college, no degree 5 935 Associate degree 2 293 Bachelor's degree 4 963 Graduate or professional degree 4 533 % bachelor's degree or higher 29.5

No. of Non-family Income (in 1989) No. of Families Households Households Total number 23 491 12 983 10508 Less than $ 5 000 3 765 914 2883 $ 5 000 to $ 9 999 3 938 1 177 2775 $ 10 000 to $ 14 999 2 781 1 328 1465 $ 15 000 to $ 24 999 4 281 2 506 1778 $ 25 000 to $ 34 999 3 031 2 159 853 $ 35 000 to $ 49 999 2 809 2293 487 $ 50 000 to $ 74 999 1 970 1 803 167 $ 75 000 to $ 99 999 531 488 30 $100 000 to $149 999 263 231 32 $150 000 or more 122 84 38 Median income ($) 17 567 27 307 8846

Note: Per capita income was $ 10 003.00

Vehicles available per Type of Housing Unit Occupied housing unit Total No. of vehicles 23 466 None 2 801 1 Person 9 067 2 Person 7 929 3 or more persons 3 669

20 Table 4.2-5. Continued.

HOUSEHOLDS BY TYPE Total No. of Households Total No. of Households 23 466.0 Family households 12 847.0 Married-couple families 10 194.0 Other family, male householder 557.0 Other family, female householder 2 096.0 Non-family households 10 619.0 % of total households 45.3 Householder living alone 7 519.0 Householder $65 yrs 2 194.0 Persons living in households 54 004.0 Persons per household 2.3

21 5. SUMMARY OF HISTORICAL LAKE USE

Campus lake (originally called Thompson Lake) was constructed in 1880 by damming three tributary streams to serve as a local ice supply. Later it was used for swimming and fishing by a private club. Southern Illinois University Carbondale entered into a lease agreement with Lavina Thompson April 8, 1930, and renewed the lease on May 15, 1935. The lease renewal also had the Thompson Lake Fishing Club as a party to the lease. The lake was purchased by SIU in the mid 1950’s for student recreation. In 1957 the lake was drained for dredging and to increase the height of the dam, effectively deepening the lake when it was refilled. Since that time, students at SIUC as well as residents of surrounding municipalities have enjoyed recreational opportunities at the lake. In addition to its recreational use, Campus Lake serves as an educational resource for several courses offered at the University.

5.1. ACTIVITIES AT CAMPUS LAKE

Campus Lake at SIUC provides outstanding recreational opportunities available to the campus and city population. It is a well-utilized asset that sets the SIUC campus apart from other campuses. A brief review of the current use and opportunities at Campus Lake is provided below.

5.2. LAKE-ON-CAMPUS BOAT DOCK

The boat dock is located on the east end of the near the College of Engineering (which is in the upper center of the photograph on the cover of this report). The dock is the busiest facility at Campus Lake and is open from mid-March through October with daily hours of operation hours from 12:00 to 18:00. While open, the facility is staffed by fully-certified lifeguards and a rescue motorboat is also on standby. A rental fleet of 16 canoes, 6 paddleboats, 4 rowboats, 4 Sunfish sailboats, 2 sailboards, 2 open top kayaks, and 1practice scull are available for use by students and the public. All boats and equipment are available for $0.50 per hour. The facility serviced and average of 3 900 individuals per season for the years 1994 through the end of the season in October 1999. This figure does not include spectators, fishing, special events and programming.

22 5.3. CAMPUS BEACH

Campus Beach offers lake-front recreational opportunities for a wide segment of the population in a secure and safe setting. The beach is shown in the lower right corner of the cover photo and is open from Memorial Day through Labor Day with daily operation hours of operation from 12:00 to 16:00. The facility provides sunbathing space, sand volleyball, and showers while the swimming area offers both a shallow wading section with zero-depth entry, and a deeper swimming section for lap swimming. The entire area is enclosed and has two floating docks for sunbathing, jumping/diving and is patrolled by certified lifeguards while open. The entry is free to holders of SIUC identification card and $0.50 for non-SIUC affiliated patrons. The estimated average number of patrons per season was 1 100 for the years 1994 through the end of the season in 1999. This figure does not include special events and programming.

5.4. CAMPUS LAKE TRAIL

The Campus Lake Trail is a 3.52 km (2.2 mile) handicap accessible paved foot path which loops around the entire lake. Only pedestrian traffic is permitted on the trail. In addition, several fitness stations (e.g., chin-up bars and sit-up stations) are also available at points along the trail which is a popular location for individuals to engage in aerobic activities or to seek relaxation. Unfortunately, patron use numbers are unavailable, but when weather permits, the trail is in near constant use. The busiest times of day are the noon hour and from about 16:30 to 18:00.

5.5. FISHING OPPORTUNITIES

Campus Lake is utilized by countless individuals who take advantage of fishing opportunities in an urban setting. Concrete piers, retaining walls and benches along the lakeshore provide ideal opportunities for a wide spectrum of the local population to enjoy fishing. It is not uncommon to see 5 to 10 individuals at any given time fishing at various locations around the lake. In addition, the lake also serves as a site for the Illinois Department of Natural Resources (IDNR) Urban Fishing Program which is discussed below.

5.6. CAMPUS LAKE RETREAT AND PICNIC AREAS

Five (5) retreat and picnic areas which can accommodate small to large groups are

23 located around Campus Lake. The areas are available for rental for large groups but the majority of use is by small, unregistered groups or individuals. The areas are rented approximately 20 times per year.

5.7. SPECIAL EVENTS

Campus Lake is the location of highly visible special events. The largest of these is the Annual Great Cardboard Boat Regatta which has brought national media to the campus and Campus Lake. An estimated 6 000 to 7 000 people attend this event at the end of April each year. Other major events include the Annual Doc Spackman Triathlon and numerous other campus functions. On average, the Boat Dock hosts some 140 special events each year while another 25 are held at the Campus Beach.

5.8. PROGRAMMING

In addition to the formal functions of the various facilities and independent use of the lake, the Campus Lake is a part of the programming offered by the Office of Intramural- Recreational Sports. Disabled student recreation uses the lake for programming such as disabled fishing and disabled boating. The aquatics department uses the lake for programs such as waterfront lifeguarding and sailing lessons. Intramural sports offers canoe races and sand volleyball leagues. Several sport slubs use Campus Lake for practice space and instructional events. Among these clubs are the Sailing Club, Windsurfing Club, Canoe and Kayak Club, Fishing Club, and the Outdoor Adventure Club.

Campus Lake is a very important part of SIUC. Often, visitors comment on the beauty and special nature of having a lake such as Campus Lake. Many cannot believe that a lake as large as Campus Lake is part of the campus itself. Many members of the campus community find refreshment and renewal in association with Campus Lake, a valuable and integral part of SIUC and the regional community as a whole.

24 6. POPULATION SEGMENTS ADVERSELY AFFECTED BY LAKE DEGRADATION

The population demographics of Jackson and surrounding counties suggest that degradation of the quality of Campus Lake waters would adversely affect a wide range and number of people. The greatest numbers of people affected would be the students at SIUC, which represent primarily an age group in the 18-30 year range and number 22 160 (average number of students at SIUC 1997-1999). Although, not all of the students would be directly affected by degradation of Campus Lake water quality, students living in residence halls on Campus Lake (Thompson Point and Greek Row = 1530) would be directly affected. As well, a large proportion of the student population participates in some event involving Campus Lake during their University career (classes, intramural activities, use of Campus Lake trail, fishing, picnicking/barbequing next to the lake, boating, swimming, other events). Given the open access and the wide range of activities pursued by the general public at Campus Lake, it’s degradation would be far reaching. For example, blue-green algal blooms in summer, one of the hottest time periods in southern Illinois, makes the lake unattractive for swimming. Thus, many school-aged children and their parents who may potentially use Campus Lake for water related activities are deterred. The majority of visits to Campus Beach (averaging 1 100 visitors annually between 1994-1999) result from such summer time use. Widespread algal blooms also cause the shallow bays to become anoxic (personal observations by authors) which can contribute to a ‘sewer’ like smell emanating from the lake when the wind blows towards campus. This causes people to avoid using the trail surrounding the lake. People fishing are also deterred by the smell and anoxic waters are deadly to fish, further decreasing the lake’s appeal. Furthermore, shoreline erosion in areas where the Urban Fishing Program is held decreases the overall aesthetic appeal of the lake. Because access to Campus Lake is unregulated, it is difficult to estimate the exact number or age groups of people adversely affected by lake degradation. However, the lake’s central, near-urban location and the varied uses it provides to a wide range of the community necessitate a management strategy to ensure its long-term health.

25 7. COMPARISON OF LAKE USES TO OTHER LAKES IN REGION

The Illinois counties within an 80-km (50-mile) radius of Campus Lake are indicated in Figure 1-1. Missouri was not included in the study area since the nearest access bridges from Missouri to Illinois, at Chester and Cape Girardeau are close to the 80-km (50-mile) distance. It is doubtful many southeast Missouri residents would choose to travel to Campus Lake given the inconvenience of crossing the Mississippi River. Illinois counties within an 80-km (50-mile) radius of Campus Lake and public access lakes 4 ha (10 acres) or greater within each county are listed in Table 7-1. The recreational activities offered at each lake are also indicated. This data was obtained mainly by phone calls to city officials at towns nearby the lakes. Several large public access lakes are near Carbondale including Crab Orchard Lake (about 16 km [10 miles] to the east); and Little Grassy and Devils Kitchen lakes (about 19.2 and 22.4 km [12 and 14 miles], respectively, toward the southeast). To the west is Kinkaid Lake, about 24 km (15 miles) from Carbondale, and Rend Lake is about 56km (35 miles) to the north. Little Grassy and Devils Kitchen lakes offer camping, swimming and fishing, while the other three larger lakes also allow larger boats for water-skiing and other activities. The lakes within 80 km (50 miles) of Campus Lake generally have overall use support ratings of fair similar to Campus Lake (IEPA 2002). However, Little Grassy, Devil’s Kitchen and Cedar lakes are among the three highest rated lakes in Illinois with an overall use support rating of good. This is due to their relatively undisturbed or non-agricultural or urbanized watersheds and overall depth. Similar to Crab Orchard and Kinkaid lakes, pollutants in Campus Lake include heavy metals and organics. Both a mercury and PCB consumption advisory are in effect for fish from Campus Lake. Although a number of large lakes in good condition are located relatively near Campus Lake, they are not accessible with public transport or without a personal vehicle. None are located close to a large urban population or within easy walking distance or bicycle ride similar to Campus Lake and offer the opportunity for the same wide range of activities.

26 Table 7-1. Public access lakes $ 4ha (10 acres) within an 80-km (50- mile) radius of Campus Lake Area Lake County Recreational Facilities (acres) Horseshoe Alexander 1 890.0 C,P,B,BR,F,PL,H Benton Franklin 67.6 B,BR,F,PL,W S Christopher New “ 43.2 - Hamilton “ 34.0 C,P,B,BR,F,PL C,P,HT,B,BR,BRT,F,S,PL,W S,V Rend “ 18 900.0 C,LC,FS,G,H,WST,HR Sesser “ 42.5 C,P,B,F,PL W. Frankfort New “ 214.0 P,B,BR,F,S,PL,LC,FS,W S W . Frankfort Old “ 146.0 C,P,B,BR,F,PL,FS,H McLeansboro New Hamilton 75.0 P,HT,B,BR,F,PL Carbondale City Jackson 135.6 P,B,BR,F,PL Cedar “ 1 800.0 HT,B,BR,F,S,PL,FS Elkville “ 58.5 B,BR,F,PL Kinkaid “ 3 475.0 C,P,B,BR,BRT,F,S,PL,W S Little Cedar “ 70.0 HT,B,BR,F,PL,BT,H Murphysboro “ 143.0 C,P,HT,B,BR,BRT,F,PL Jaycees Jefferson 105.0 - Miller “ 131.0 - Dutchman Johnson 118.0 B,BR,F,PL,H Willow Pond “ 16.0 C,P,HT,F,PL,H Mermet Massac 452.0 P,HT,B,BR,BRT,F,PLVS,H Boulder North Perry 17.0 C,P,HT,B,BR,F,PL,BT,H Boulder South “ 22.5 C,P,HT,B,BR,F,PL,BT,H Crystal “ 12.0 C,P,HT,B,BR,F,PL,BT,H Lost “ 15.0 C,P,HT,B,BR,F,PL,BT,H Pickneyville “ 165.0 P,B,BR,F,PL Wesslyn Cut “ 24.2 C,P,HT,B,BR,F,PL,BT,H Glendale Pope 79.0 C,P,B,BR,BRT,F,S,PL One Horse Gap “ 28.0 B,BR,F,PL Sugar Creek Lake “ 94.0 B,BR,F,PL Baldwin Randolph 1 967.0 P,HT,B,BR,F,PL,H Coulterville “ 23.6 C,P,B,BR,F Randolph “ 65.0 C,P,HT,B,BR,BRT,F,PL,FS

27 Table 7. Continued Area Lake County Recreational Facilities (acres) Sparta New “ 25.8 F,PL,H Sparta Old “ 26.3 C,P,F,PL,H Carrier Mills (PWS) Saline 13.6 - Eldorado “ 92.0 - Glen O. Jones Saline 105.0 C,P,HT,B,BR,F,PL,VC,FS,H Harrisburg Hold. “ 67.1 F,PL Harrisburg Res. “ 208.9 F,PL Dongola City Res. Union 70.0 P,B,F,PL Grassy “ 310.0 B,BR,F,PL Lyerla “ 260.0 B,BR,F,PL Ashley Reservoir Washington 18.0 B,F Nashville City “ 37.2 B,BR,F,PL Washington Co. “ 295.0 C,P,,HT,B,BR,BRT,F,PL,FS,H C,P,HT,B,BR,BRT,F,S,PL,VC,W Crab Orchard Williamson 6 965.0 S Lake of Egypt “ 2 300.0 C,P,B,BR,BRT,F,S,PL Devil’s Kitchen “ 810.0 C,P,HT,B,BR,BRT,F,S,PL,FS Herrin New (#1) “ 46.1 B,F,PL Herrin Old (#2) “ 51.3 C,P,B,BR,F,PL,H Johnson City “ 64.0 P,B,F,PL,H Little Grassy “ 1 000.0 C,P,B,BR,BRT,F,S,PL,FS Marion “ 220.0 B,BR,F,PL,H

Explanation for abbreviations of Recreational Facilities. C - Camping FS - Food Services P - Picnicking B - Boats allowed G - Golf PL - Pets on Leash BR - Boat Ramp H - Hunting S - Swimming BRT - Boat Rental HR - Horse Rental VC - Visitor Center BT - Bicycle Trail(s) HT - Hiking Trail(s) WS - Water skiing F - Fishing LC - Lodge / Cabins WS - Winter Sports

28 8. DESCRIPTION OF POINT SOURCE POLLUTION DISCHARGES

There are no National Pollutant Discharge Elimination System (NPDES) permits for point source discharges to Campus Lake and there are no known point source pollution loadings in the Campus Lake watershed.

29 9. LAND USES AND NON-POINT SOURCE POLLUTION LOADINGS

The north side of the lake borders an urban area of the SIUC campus, representing approximately 65% of the watershed. Forest and meadow areas comprise the south and west watershed areas of the lake (35% of the watershed). Urban storm water runoff draining student residential and other University building rooftops and sump seepage, parking lots, and sidewalks enters Campus Lake via 17 storm sewers primarily along the north shore of the lake. Runoff from the forest area is from direct overland flow and that which flows through natural channels. Approximately 27 discharge points exist around the lake. These discharge points are shown in Figure 9-1. Loading of suspended solids, phosphorus and nitrogen were measured directly for each sub-watershed for rain events exceeding 2.54 cm (1") total accumulation during the Phase I study (see Section 11 below). Thus, estimates of pollutant loadings from different land uses based on literature values were not completed for this section.

9.1. CURRENT AND PAST RESTORATION ACTIVITIES

Following the purchase of Campus Lake by Southern Illinois University in the mid 1950’s, considerable construction (expansion of SIUC campus) occurred in the north part of the lake watershed. The lake was drained and dredged from March 1957 to late October 1958 (Casper, 1993). A spill of PCB’s from a leaking transformer resulted in contamination of a northwest arm of the lake in the 1970’s. Dredging of sediments in the localized area of the spill was undertaken to remove the contamination. In recent years, some shoreline protection has been undertaken by promptly reseeding areas which were disturbed for the installation of recreational areas/facilities. The biological control of excessive weed growth was attempted through the introduction of grass carp in the mid 1960’s. This action is discussed further in the fisheries section of this report.

30 . The

Boat Dock

1000 FEET

Spillway (336.6’ ASL)

showing storm sewer

250 METERS DAM

500

16.6

, while hatched circles ( ) indicate free flow lake entry

14.6

Thompson Point Dorms

10’

13’

12 12.6

flow of the Horticulture Pond which drains into Campus Lake.

10.6

8.6

2.6

6.6 4.6 0.6

15’

15”

flow. Points 26 and 27 are located at out

s. Solid organge circles ( ) indicate a culvert type lake entry

Greek Row Dorms

Bathymetric map of Campus Lake at Southern Illinois University Carbondale Campus, Jackson Co. IL

discharge point spillway is an out

Figure 9.1-1.

31 32 10. BASELINE AND CURRENT LIMNOLOGICAL DATA

10.1. HISTORICAL AND CURRENT LAKE WATER QUALITY

10.1.a. Water transparency

Lake water transparency was measured with a standard 20 cm diameter Secchi disk lowered on the shady side of the boat. We compared the current data to historical data available for Campus Lake from the IEPA Volunteer Lake Monitoring Program (VLMP) through which Campus Lake has been monitored since 1981. Sites in the lake did not differ (ANOVA, P > 0.05), however, there was a pronounced seasonal trend (ANOVA P < 0.05, Figure 10.1.a-1A). Secchi depth was greatest in May, and then declined to a low in July and August, months when blue-green algal blooms dominate the lake and decrease its aesthetic appearance (Figure 10.1.a-1A). The mean Secchi depth for the Phase 1 study period was 1.64 m (64.7 inches). The seasonal trend observed during Phase 1 monitoring was similar to the long term trend recorded for Site 1 (Figure 10.1.a-1B) and is consistent with changes in chlorophyll pigments. Populations of algae interfere with light penetration and reduce the Secchi disk visibility at depth. Chlorophyll pigment concentrations were lowest in May and June and were highest in July and August (see below). Compared to other lakes in Illinois for which Secchi depths are recorded through the VLMP, the rank of Campus Lake varies from 28th to 91st (Table 10.1.a-1). The large inter-annual variation in Secchi depth suggests that Campus Lake productivity is influenced by large scale climatic factors as well as nutrient and sediment contributions from the catchment.

33 0 0 A

1 50

100 3

Site 1 150 4 Site 2 Site 3

5 1998 1997 0 0 B Secchi Depth (m) Secchi Depth (inches) 1 50

100 3

150 4

953521216 23 5051 49 46 17 5 5 JFMAMJJASOND Month (1981-2003)

Figure 10.1.a-1. Secchi depths for Campus Lake, Jackson Co., IL. between April 1997 and 1998 (A) and Long-term monthly averages (B) for years in which Secchi depths have been recorded for Campus Lake through the ILEPA Ambient or Volunteer Lake Monitoring programs. In A, sampling months are plotted to correspond to yearly plot in B. Numbers above x-axis in B indicate the number of months available to calculate the average. Error bars represent ±1 standard error (SE); symbols without error bars in A represent single measurements. (Data from EPA STORET, VLMP, and F. M. Wilhelm, SIUC Department of Zoology, unpublished data).

34 Table 10.1.a-1. Historic average Secchi depth measurements, average state-wide Secchi depths for lakes in the Illinois EPA Volunteer Lake Monitoring Program (VLMP) and rank of Campus Lake, Jackson Co., IL.

Average Secchi depth in Average state-wide State-wide rank Number of lakes Year Campus Lake Secchi depth of Campus Lake surveyed in VLMP m inchesa m inches 1997 1.50 59 1.32 52 51 162 1996 0.97 38 -- 75 157 1995 1.37 54 -- 46 130 1994 1.24 49 -- 52 129 1993 0.74 29 1.57 62 91 151 1992 1.14 45 1.24 49 57 134 1991 0.86 34 -- 65 142 1990 0.86 34 0.99 39 59 134 1989 1.30 51 1.07 42 36 139 1988 1.45 57 1.07 42 38 149 1987 0.91 36 1.60 63 61 134 1986 1.35 53 1.57 62 39 127 1985 0.88 34.8 1.16 45.6 62 120 1984 1.22 48 1.16 45.6 55 118 1983 1.03 40.5 -- 52 112 1982 0.94 37 -- 63 109 1981 1.17 46 1.01 39.9 28-29 72

Notes: a Average Secchi depth for VLMP is calculated for the period of monitoring (May to October, while the average Secchi depth for this diagnostic study was calculated for a 12 month period; – indicates no data available.

35 10.1.b. ph and Alkalinity

Campus Lake water was sightly basic with mean pH values of approximately 8.1. Among sites, pH was similar (ANOVA P > 0.05, site A = 8.07, B = 8.09 and C =8.14, See Appendix 3 for summary statistics) at the top. However, seasonal variation was apparent (ANOVA, P < 0.001), ranging from 7.6 in November and December and 8.1 in March and April to 8.3 in July and August (Figure 10.1.b-1). The pH at each site also decreased from top to bottom, a phenomenon not uncommon in lakes. This change was likely due to the influence of photosynthesis shifting the carbonic acid - CO2 equilibrium and was most pronounced during the summer (Figure 10.1.b-1). Values of pH greater than 8.0 in lakes usually indicate a photosynthetic demand for carbon dioxide (e.g., an algae bloom) that exceeds replenishment from plant and animal respiration, organic decomposition and diffusion from the atmosphere. These results are consistent with the high chlorophyll values in the surface waters of Campus Lake (see below) during the summer. The pH measured during the Phase I monitoring was similar to historic pH values for surface waters. The pH of Site 1 bottom water was somewhat lower than those recorded historically (Figure 10.1.b-1A). Worldwide, the pH of most natural waters ranges between 6.0 and 9.0 (Wetzel 2001). Given the type of soils in the drainage basin, the pH of Campus Lake is not expected to deviate from historic patterns and is ideal to support fish and other aquatic life. Alkalinity is generally considered to refer to the buffering capacity of water, especially the carbonate system. It is used interchangeably with acid neutralizing capacity (ANC) abd refers to the ability to neutralize strong inorganic acids. Alkalinity results from any dissolved species, usually weak acid anions, which accept protons. Thus, highly alkaline waters resist changes in pH when an acid is added. Expressing alkalinity as mg CaCO3 assumes that all alkalinity is contributed by calcium carbonate which may not always be the case (Wetzel 2001). In Campus Lake, historic alkalinity averages varied between 60 to 80 mg/L and were similar among sites as well as top and bottom samples (Figure 10.1.b-2). Seasonal changes were apparent, with the low alkalinity early in the year increasing to a maximum in late fall. This seasonal pattern probably results from the seasonal cycle related to primary production, the loss of calcium carbonate and its return at turnover (Cole 1994). During the Phase I period, alkalinity values appear higher than the historic average at Site 1 and 2. It must be remembered that the historic values are based on a large number of measurements, and the standard errors associated with the means indicate general high variability which may be related to seasonal differences in the water budget (i.e wet versus dry years) because Campus Lake is an endorheic lake. Given the nature of the Campus Lake drainage basin, exhaustion of

36 10 A

7 Top Bottom Phase I Top 6 Phase I Bottom 0 10 B

8 pH

6 0 10 C

6 6910677 7710 10 85 0 JFMAMJJASOND Month (1987-1998)

Figure 10.1.b-1. Historic and current pH for Sites 1 (A), 2 (B), and 3(C) in Campus Lake, Jackson Co., IL. Historic values were obtained from the Center for Environmental Health and Safety (SIUC). Numbers above the x-axis indicate the number of years for which monthly data were averaged; error bars represent ±1SE.

37 100 A 90

50 0 100 Top Bottom B

) Phase 1 Top

3 90 Phase 1 Bottom

60 Alkalinity (mg CaCO 50 0 100 C 90

50 913141111 81014 12 87 11 0 JFMAMJJASOND Month (1987-1998)

Figure 10.1.b-2. Historic and current alkalinity for Sites 1(A), 2(B) and 3 (C) in Campus Lake, Jackson Co., IL. Historic values were obtained from the Center for Environmental Health and Safety (SIUC). Numbers above x-axis indicate the number of monthly measurements averaged; error bars represent ±1SE.

38 alkalinity should not be a threat.

39 10.1.c. Conductivity

Specific conductance is a measure of the ability of water to conduct an electrical current and is often directly related to the amount of total dissolved solids present in the water (Cole 1994). During the Phase 1 monitoring, specific conductance was measured intermittently among months during winter through summer of 1997 and 1998 (Figure 10.1.c-1). Specific conductance was measured at the surface at three lake sites, and also at the bottom at site A. Historical data for specific conductance at Campus Lake is sparse, and represents surface measurements during two months (June and September) in a single year (1981). Seasonal values and patterns of specific conductance were similar among Sites 1, 2 and 3 during the Phase-1 monitoring (Figure 10.1.c-1). Conductance ranged from 132 to 237 :mhoscm-1 across seasons. Conductance was lowest during winter, moderate in summer, and peaked in spring and fall. Peaks in spring and fall probably reflect increases in turbidity associated with lake mixing during those seasons, especially since the lake is anoxic allowing internal loading of P and the solubilization of Fe, both of which would contribute to this increase in conductivity. Conductance at site A was higher at the bottom than at the surface during summer, again this is expected with anoxic bottom waters. Lack of suitable historic data precluded a detailed comparison to Phase 1 monitoring data. Conductance in June was slightly higher (approximately 10 :mhoscm-1) in the Phase 1 monitoring compared to historic data (Figure 10.1.c-1).

40 300 A

250

200

150 Top Bottom Phase 1 Top Phase 1 Bottom 100 0 )

-1 300 B

250

200

150

100 0 Specific conductance (µmhos·cm 300 C

250

200

150

100 1030 0 202 2 101 0 JFMAMJJASOND Month (1981-1998) Figure 10.1.c-1. Historic and current conductivity for Site 1 (A), 2 (B) and 3(C) in Campus Lake, Jackson Co., IL. Historic values were obtained from the EPA STORET database. Numbers above the x-axis indicate the number of monthly measurements averaged; error bars represent ±1SE.

41 10.1.d. Turbidity

Turbidity is a measure of the amount of suspended solids in water. High turbidity reduces water clarity and limits light penetration. Turbidity can be caused by colloidal clays and primary production. During the Phase 1 monitoring, turbidity was measured monthly (except March) in 1997 and 1998 (Figure 10.1.d-1). Turbidity was measured at the surface at three lake sites, and also at the bottom at Site 1. Historical data for turbidity at Campus Lake is sparse, and represents surface measurements during two months (June and September) in a single year (1981). Seasonal patterns of turbidity were similar among Sites 1, 2 and 3 (Figure 10.1.d-1) during the Phase 1 monitoring. Turbidity ranged from 0.9 to 12.6 formazin turbidity units (FTU) across seasons. Seasonal patterns in turbidity were similar to those for specific conductance and were significant (ANOVA P < 0.001, Figure 10.1.d-1). Turbidity was lowest during winter, moderate in summer, and peaked in spring and fall. Peaks in spring and fall probably reflect increases in suspended solids associated with lake mixing during those seasons. A single summer peak was observed at Site 2 in August, and may have been associated with increased primary production. There were no differences in turbidity between surface and bottom samples (ANOVA P = 0.75, Figure 10.1.d-1). Lack of suitable historic data precluded a detailed comparison to Phase-1 monitoring data. However, historic turbidity values closely paralleled those of the Phase-1 monitoring data. This may suggest that the distribution of particles in the water of Campus Lake has been consistent over time. However, this must be interpreted with caution, given the large variability observed in some months.

42 20 18 A 16 14 12 Top 10 Bottom Phase 1 Top 8 Phase 1 Bottom 6 4 2 0 25 B 20

10 Turbidity (FTU) 5

0 12 C 10

1030 0 202 2 101 0 JFMAMJJASOND Month (1981-1998) Figure 10.1.d.-1. Historic and current turbidity for Site 1 (A), 2 (B) and 3(C) in Campus Lake, Jackson Co., IL. Historic values were obtained from the EPA STORET database. Numbers above the x-axis indicate the number of monthly measurements averaged; error bars represent ±1SE.

43 10.1.e. Suspended Solids

In lakes suspended solids consist of organic and inorganic particles. Most often, soil particles washed in by storms or erosion of the shoreline contribute to the inorganic load, while algae and zooplankton compose the organic fraction. Generally, Secchi depth and suspended solids vary inversely, because the latter reflect and scatter incoming light preventing it from penetrating far into the water column. The total suspended solids (TSS) concentration combined with an analysis of volatile suspended solids (determined after combusting the sample in a muffle furnace which removes all organic material) can indicate the primary nature of the suspended solids. In Campus Lake, total suspended solids varied seasonally, with the lowest values (1 mg L-1) generally occurring in Winter (December and January) and early spring (April and May) (Figure 10.1.e-1). The highest total suspended solids concentration measured in Campus Lake was 15 mg L-1 in 1998 at Site 2. Although seasonal patterns were apparent, these did not differ significantly (ANOVA P = 0.225) given the high variability associated with the means. Similarly, there were no discernable differences between sites (ANOVA P = 0.397) or between top and bottom at Site 1. Totals suspended solids were higher at Sites 2 and 3 compared to Site 1 (Figure 10.1.e-1) and probably reflects the shallow depth of these sites and possible wind related resuspension of bottom sediments. The high variability associated with the means likely indicates the importance of storm events, both from an import of suspended material in runoff and wind related resuspension of bottom materials and possibly shoreline erosion. Due to the shallow nature of Campus Lake, strong summer storms which combine high rainfall and strong winds can break thermal stratification and mix the entire lake. This is likely the reason for the slightly higher means for total suspended solids at the bottom of Site 1 compared to the top (Figure 10.1.e-1). The frequency and magnitude of the summer storms is random and unpredictable. Potential measures to reduce the impact of sediment transported to the lake are discussed in the recommendations. Volatile suspended solids (VSS) analysis combined with a TSS analysis can indicate the if organic or inorganic constituents dominate the suspended solids. In Campus Lake, similar to the TSS analysis, there were no significant seasonal or site trends for VSS (ANOVA P = 0.33, P = 0.95, respectively). For Site 1 VSS ranged from a low of 1 mg/L in April 1997 to a high of 7.5 mg/L in August 1997 (Figure 10.1.e-2). Values for Sites 2 and 3 were similar (Figure 10.1.e-2). Relative to TSS, VSS ranged from 45.8 % to 87.5% (Table 10.1.e-1) indicating that in general, the suspended solids are of organic origin. This high level of organically based solids correlates with the high algal productivity and chlorophyl concentrations in the lake.

44 Table 10.1.e-1. Mean lake wide contribution of volatile suspended solids (VSS) to total suspended solids (TSS) for 1997 to 1998 in Campus Lake, Jackson, Co. IL. Lake wide average was derived by averaging surface values for Sites 1, 2 and 3.

VSS TSS VSS as % of TSS MEAN MEAN 2.50 4.00 62.50 4.67 9.33 50.00 7.00 1.83 4.00 45.83 3.50 3.92 89.36 2.83 5.42 52.31 5.33 8.50 62.75 5.67 8.50 66.67 4.00 6.33 63.16 5.25 7.50 70.00 3.33 6.00 55.56 3.50 4.00 87.50

45 16

14 A

4 Top Bottom 2 Phase 1 Top Phase 1 Bottom 0

) 16 -1 14 B

Total suspended solids (mg·L 0 16

14 C

0 1131 1 212 2 211 JFMAMJJASOND Month (1981-1998)

Figure 10.1.e-1. Historic and current total suspended solids for Site 1 (A), 2 (B) and 3(C) in Campus Lake, Jackson Co., IL. Historic values were obtained from the EPA STORET database. Numbers above the x-axis indicate the number of monthly measurements averaged; error bars represent ±1SE.

46 16

14 Top A Bottom 12 Phase 1 Top Phase 1 Bottom 10

0 ) 16 -1

14 B

Volatile suspended solids (mg·L suspended Volatile 0 16

14 C

0 1131 1 212 2 211 JFMAMJJASOND Month (1981-1998)

Figure 10.1.e-2. Historic and current volatile suspended solids for Site 1 (A), 2 (B) and 3(C) in Campus Lake, Jackson Co., IL. Historic values were obtained from the EPA STORET database. Numbers above the x-axis indicate the number of monthly measurements averaged; error bars represent ±1SE.

47 10.1.f. Nitrogen

Nitrogen is an essential element for life in freshwater. Although it is abundant on earth and in the atmosphere as N2 gas, relatively little of it is available to aquatic organisms. Nitrogen is an integral part of amino acids which are the building blocks of proteins. Nitrogen is also an important component of DNA and RNA and as such, growing plants and animals need a steady supply to fuel the formation of new cells and tissue. Interestingly, high concentrations of unionized ammonia (NH3) are toxic to many fish and other aquatic organisms. After plants and animals die, ammonia is released as the biomass decomposes. Under oxidized conditions, the ammonia is converted to nitrate (nitrification), while under anoxic conditions denitrification predominates and anaerobic bacteria reduce nitrate to N2 through nitrite (Wetzel 2001). Both can occur simultaneously in the same waterbody.

-2 - Plants readily take up inorganic nitrogen (Nitrate [ NO3 ] + Nitrite [NO2 ]and ammonium + -1 [NH4 ] and ammonia [NH3]), and low concentrations (>0.3 mgL ) can stimulate algal growth. If nitrogen supply is limited due to stratification and incorporation in to biomass, then blue-green algae which are capable of fixing atmospheric nitrogen are favored and can result in the formation of large algal blooms, some toxic (e.g., Microcystis). The Illinois General Water Quality Standards (IEPA 1999) for total ammonia are based on the un-ionized ammonia component because this is the from most toxic. The standards vary according to pH and water temperature, with the allowable concentration decreasing as temperature and pH increase. The allowable concentration varies from 1.5 t 15 mgL-1 and is more stringent in winter than in summer. The US EPA nitrate nitrogen standard of 10 mgL-1 applies only to public drinking water because of its potential physiological effects whereby the effectiveness of hemoglobin is reduced leading to methemoglobinemia in infants.

Nitrogen measurements undertaken at Campus Lake included NH3-N, NO2-N & NO3-N,

NH4-N and total Kjeldahl nitrogen (TKN). The TKN is a measure of all nitrogen, both organic and inorganic. Thus, some simple calculations are necessary to determine the inorganic and organic fractions of nitrogen in a sample. We used the following calculations to determine, inorganic, organic and total nitrogen for the Campus Lake samples: 1) TKN - as measured

2) NO2-N & NO3-N - as measured

3) NH3-N and NH4-N - as measured

48 Inorganic N = (NO2-N and NO3-N) + (NH3-N and NH4-N)

Organic N = TKN - (NO2-N & NO3-N) Total Nitrogen = Inorganic N + Organic N

Although organic nitrogen is not known to be taken up directly by plants, it can give an indication of the relative abundance of organic material in the water. Limited historical data was available for Campus Lake for comparison to the Phase 1 data collected. During 1997-98, organic nitrogen varied between 20 to > 95% of the total nitrogen concentration (Figure 10.1.f-1) with a mean of 76%. Little difference was seen among sites or among top and bottom samples at Site 1. The high percentage of organic nitrogen can be explained by the high phytoplankton and zooplankton biomass present in the lake. The measurements from this study did not differ from those in the early 1980's. In Campus Lake, nitrite and nitrate concentrations were similar at all three sites and between the top and bottom of the water column (Figure 10.1.f-2). Concentrations ranged from below the detection limit to 0.33 mgL-1 in December 1997. This high concentration occurred for a relatively short period of time and was probably due to the decomposition of macrophytes combined with the low productivity of algae in winter. Concentrations of ammonia (Figure 10.1.f-3) and ammonium (Figure 10.1.f-4) were similar among sites and followed a distinct seasonal pattern with low concentrations in early- to mid- summer and elevated concentrations in late-summer. This pattern may be due to the strong anoxic conditions in Campus Lake which limit nitrification. Inorganic nitrogen concentrations exceeded the 0.3 mgL-1 standard known to stimulate excessive plant growth (Sawyer 1952) on several occasions and the mean inorganic concentration for Campus Lake for the Phase 1 study period was 0.2 mgL-1, indicating the availability of nitrogen for plant growth. Concentration patterns of total Kjeldahl nitrogen (TKN) were opposite to those of nitrite/ nitrate and ammonia/ammonium and were highest in summer (Figure 10.1.f-5). Overall, concentrations appeared slightly higher in 1998 compared to 1997. Given the limited historic data available it is difficult to discern trends in the lake.

49 100 A 80

Top 20 Bottom

0 Jul 98 Jul 96 Jul 97 Apr 98 Oct 98 Oct 96 Apr 97 Oct 97 Jun 98 Jun 81 Jan 97 Jun 96 Jun 97 Mar 98 Feb 98 Nov 97 Nov Aug 98 Sep 98 Sep 81 Dec 97 Aug 96 Sep 96 Aug 97 Sep 97 May 98 100 May 96 May 97 B 80

20 Organic:total nitrogen (%) 0 Jul 98 Jul 96 Jul 97 Apr 98 Oct 98 Oct 96 Apr 97 Oct 97 Jun 81 Jan 97 Jun 98 Jun 96 Jun 97 Mar 98 Feb 98 Nov 97 Nov Sep 81 Dec 97 Aug 98 Sep 98 Aug 96 Sep 96 Aug 97 Sep 97 May 98 May 96 May 97 100

80 C

0 Jul 96 Jul 97 Jul 98 Oct 96 Apr 97 Oct 97 Apr 98 Oct 98 Jun 81 Jun 96 Jun 97 Jan 97 Jun 98 Mar 98 Feb 98 Nov 97 Nov Sep 81 Aug 96 Sep 96 Aug 97 Sep 97 Dec 97 Aug 98 Sep 98 May 96 May 97 May 98 Sampling time

Figure 10.1.f-1. Historic and current organic : total nitrogen ratio for Site 1 (A), 2 (B) and 3 (C) in Campus Lake, Jackson, Co., IL. Historic values were obtained from the EPA STORET database. See text for calculation of organic and total nitrogen.

50 0.5

Top A Bottom 0.4

0.3

0.2

0.1

) 0.0 -1 Jul 96 Jul 97 Jul 98 Oct 96 97 Apr Oct 97 98 Apr Oct 98 Jun 96 Jun 97 Jun 98 Jun Jun 81 Jun 97 Jan Mar 98 Feb 98 Feb Nov 97 Sep 81 Sep 96 Aug 96 Sep 97 Aug 97 Sep Dec 97 98 Aug 98 Sep 0.5 May 96 May 97 May 98 B

-N) (mg·L 0.4 -1 2

0.3

0.2 -N) + Nitrite (NO

-2 0.1 3

0.0 Jul 96 Jul Jul 97 Jul Jul 98 Jul Oct 96 Apr 97 Oct 97 Apr 98 Oct 98 Jun 81 Jun 96 Jun Jan 97 Jan Jun 97 Jun Jun 98 Jun Mar 98 Feb 98 Feb Nov 97 Aug 96 Aug 96 Sep Sep 81 Sep Aug 97 Aug 97 Sep Dec 97 Aug 98 Aug 98 Sep May 96 May 97 May 98

Nitrate (NO 0.5 C 0.4

0.3

0.2

0.1

0.0 Jul 96 Jul 97 Jul 98 Oct 96 Apr 97 Apr 98 Oct 97 Oct 98 Jun 81 Jun 96 Jun 97 Jan 97 Jun 98 Mar 98 Feb 98 Nov 97 Nov Sep 81 Aug 96 Sep 96 Aug 97 Sep 97 97 Dec Aug 98 Sep 98 May 96 May 97 May 98 Sampling time

Figure 10.1.f-2. Historic and current nitrite and nitrate for Site 1 (A), 2 (B) and 3 (C) in Campus Lake, Jackson, Co., IL. Historic values were obtained from the EPA STORET database. Error bars represent ± 1SE and are calculated for months with > 1 measurements.

51 0.06 Top A 0.05 Bottom

0.04

0.03

0.02

0.01

0.00 Jul 97 Jul 98 Jul 96 ) Oct 97 Oct 98 Oct 96 Apr 97 Apr 98 Jun 97 Jan 97 Jun 98 Jun 81 Jun 96 Mar 98 Feb 98 Nov 97 Nov Aug 97 Sep 97 Dec 97 Aug 98 Sep 98 Sep 81 Aug 96 Sep 96 May 97 May 98 May 96 -1 0.06 B 0.05 -N mg·L 3 0.04

0.03

0.02

0.01

0.00 Un-ionized ammonia(NH Jul 97 Jul 98 Jul 96 Oct 97 Oct 98 Oct 96 Apr 97 Apr 98 Jun 97 Jan 97 Jun 98 Jun 81 Jun 96 Mar 98 Feb 98 Nov 97 Nov Aug 97 Sep 97 Dec 97 Aug 98 Sep 98 Sep 81 Aug 96 Sep 96 May 97 May 98 May 96 0.06 C 0.05

0.04

0.03

0.02

0.01

0.00 Jul 97 Jul 96 Jul 98 Oct 97 Oct Oct 96 Oct Apr 97 Oct 98 Oct Apr 98 Jan 97 Jun 97 Jun 96 Jun 81 Jun 98 Mar 98 Feb 98 Nov 97 Nov Dec 97 Aug 97 Sep 97 Aug 96 Sep 96 Sep 81 Aug 98 Sep 98 May 97 May 96 May 98 Sampling time

Figure 10.1.f-3. Historic and current un-ionized ammonia (NH3-N) for Site 1 (A), 2 (B) and 3 (C) in Campus Lake, Jackson, Co., IL. Historic values were obtained from the EPA STORET database. Error bars represent ± 1SE and are calculated for months with > 1 measurements.

52 1.0

Top A Bottom 0.8

0.6

0.4

0.2

0.0 Jul 98 Jul Jul 97 Jul Jul 96 Jul Oct 98 Oct Apr 98 Apr Oct 97 Oct Oct 96 Oct 97 Apr Jun 98 Jun Jan 97 Jan Jun 97 Jun Jun 81 Jun 96 Jun Mar 98 Feb 98 Feb Nov 97 Nov Aug 98 Aug 98 Sep Aug 97 Aug 97 Sep 97 Dec Aug 96 Aug 96 Sep Sep 81 Sep May 98 May 97 1.0 May 96

) B -1 0.8

-N mg·L 0.6 4

0.4

0.2 Ammonium (NH 0.0 Jul 98 Jul Jul 97 Jul Jul 96 Jul Oct 98 Oct Oct 97 Oct 98 Apr Oct 96 Oct 97 Apr Jan 97 Jun 98 Jun 97 Jun 81 Jun 96 Mar 98 Feb 98 Nov 97 Nov Aug 98 Sep 98 Aug 97 Sep 97 Dec 97 Aug 96 Sep 96 Sep 81 May 98 May 97 May 96 1.0 C 0.8

0.6

0.4

0.2

0.0 Jul 98 Jul 97 Jul 96 Oct 98 Apr 98 Oct 97 Oct 96 Apr 97 Jan 97 Jan 98 Jun Jun 97 Jun Jun 81 Jun 96 Jun Mar 98 Feb 98 Feb Nov 97 Nov Aug 98 Aug 98 Sep Dec 97 Dec Aug 97 Aug 97 Sep Aug 96 Aug 96 Sep Sep 81 Sep May 98 May 97 May 96 Sampling time

Figure 10.1.f-4. Historic and current ammonium (NH4-N) for Site 1 (A), 2 (B) and 3 (C) in Campus Lake, Jackson, Co., IL. Historic values were obtained from the EPA STORET database. Error bars represent ± 1SE and are calculated for months with > 1 measurements.

53 2.0 Top A Bottom 1.5

1.0

0.5

0.0 ) Jul 96 Jul Jul 97 Jul Jul 98 Jul Oct 96 Oct 97 Apr Oct 97 Oct Apr 98 Apr Oct 98 Oct Jun 81 Jun Jun 96 Jun Jun 97 Jun Jan 97 Jan Jun 98 Jun Mar 98 Feb 98 Feb Nov 97 Nov Sep 81 Sep Aug 96 Aug 96 Sep Aug 97 Aug 97 Sep 97 Dec Aug 98 Aug 98 Sep May 96 May 97 May 98 -1 2.0 B

1.5

1.0

0.5

0.0 Total Kjeldahl Nitrogen(TKN mg·L Jul 96 Jul 97 Jul Jul 98 Jul Oct 96 Oct Apr 97 97 Oct Apr 98 98 Oct Jun 96 Jun 97 Jun Jun 81 Jun Jan 97 Jan 98 Jun Mar 98 Feb 98 Feb Nov 97 Aug 96 Sep 96 Aug 97 Sep 97 Sep 81 Dec 97 Aug 98 Sep 98 May 96 May 97 May 98 2.0 C

1.5

1.0

0.5

0.0 Jul 96 Jul 97 Jul 98 Oct 96 Apr 97 Oct 97 Apr 98 Oct 98 Jun 81 Jun Jun 96 Jun Jun 97 Jun 97 Jan Jun 98 Jun Mar 98 Feb 98 Feb Nov 97 Nov Sep 81 Sep Aug 96 Aug 96 Sep Aug 97 Aug 97 Sep 97 Dec Aug 98 Aug 98 Sep May 96 May 97 May 98 Sampling time

Figure 10.1.f-5. Historic and current total Kjeldahl nitrogen (TKN) for Site 1 (A), 2 (B) and 3 (C) in Campus Lake, Jackson, Co., IL. Historic values were obtained from the EPA STORET database. Error bars represent ± 1SE and are calculated for months with > 1 measurements.

54 10.1.g. Phosphorus

Phosphorus (P) is an important element in freshwaters, and is often the limiting nutrient (Schindler 1972). Phosphorus is needed by plants and animals for a variety of purposes, one of the most important being to provide energy for cellular processes from the chemical bonds of food stuffs through the phosphorylation of adenosine diphosphate (ADP) to adenosine triphosphate (ATP). Phosphorus is also an important component of both deoxyribonucleic and ribonucleic acids (DNA, RNA), thus new tissue growth requires the availability of adequate supplies of P (Elser and Urabe 1999). Total phosphorus (TP) is a measure of all forms of phosphorus in a sample of water and includes fractions which are not available to organisms. Dissolved phosphorus (DP) is a measure of the TP that is soluble and theoretically available for uptake by plants (See Hudson et al. 2000 for a discussion of limits and errors associated with DP measurements). Given the limits of DP measurements, relationships between algal growth, chlorophyll a and eutrophication are generally made with respect to TP (e.g. Carlson 1977). Because phosphorus is often the limiting nutrient in freshwaters, its addition can stimulate excessive algal growth leading to eutrophication. Thus, it is the primary focus of many lake restoration efforts. Sources of phosphorus to lakes include direct wet and dry deposition to the lake surface, runoff from the land surface (soil particles, sewage), decomposition of organic matter in the lake, and recycling from the lake sediments. Often phosphorus is transported into lakes tightly bound to soil (e.g., clay) or other particles but once it enters a lake, it’s fate is determined by the chemical and physical conditions of the lake. Under oxic, stratified conditions dissolved phosphorus (orthophosphate) is rapidly assimilated by algae thus reducing the lake- wide epilimnetic concentration and limiting algal production. In oxic hypolimnia, phosphorus generally remains bound to particles and precipitates to the sediments where it is unavailable to plants, although some uptake through roots of macrophytes may occur. In anoxic hypolimnia, the oxidized microzone at the sediment-water interface breaks down due to the reducing conditions from the lack of oxygen. This causes the reduction of chemical constituents such as iron, and leads to increasing concentrations of orthophosphate in the hypolimnion (Wetzel 2001). This soluble phosphorus may then become available to organisms in the epilimnion during the summer through epilimnetic entrainment associated with storm events (Wetzel 2001). Otherwise, it becomes available during fall turnover and is usually the stimulus for fall blooms of algae in north temperate lakes. Because the buildup of orthophosphate in the hypolimnion can fuel substantial epilimnetic algal growth, lake managers are interested in aeration options to maintain oxygen concentrations above 1 mgL-1 in the hypolimnion during restoration efforts.

55 For Illinois, general use water quality standards specify that TP concentrations should not exceed 0.05 mgL-1 in any reservoir or lake with a surface area greater than 8.1 ha (20 acres) or more (IEPA 1999). However, it is not uncommon for this concentration to be exceeded among the state’s many eutrophic lakes. In Campus Lake, TP concentrations ranged from a low of 0.015 mgL-1 to a high of 0.150 mgL-1 (Figure 10.1.g-1). No significant differences were found among sites (ANOVA P = 0.26), however, there was a significant (ANOVA P < 0.001) seasonal trend (Figure 10.1.g-1), with concentrations lowest in late winter and highest in summer and fall. Variability among bottom measurements was high, reflecting the anoxic/oxic conditions of Campus Lake. Because the lake stratifies in summer and the hyoplimnion becomes anoxic, significant internal loading can occur (See nutrient budget below). However, strong winds associated with summer storms can mix the entire lake at any time leading to large increases and variability in dissolved phosphorus measurements in the epilimnion (Figure 10.1.g-2). The high total phosphorus measurements in summer are associated with blooms of algae and zooplankton which contribute phosphorus from body tissues to the TP analysis. Overall the phosphorus concentration in Campus Lake is high and efforts should be undertaken to reduce its availability. Unloading of TP from the sediment may be possible through lake flow and water level management options.

56 0.25 A 0.20

0.15

0.10

0.05

0.00 0.25 Top

) Bottom B -1 Phase 1 Top 0.20 Phase 1 Bottom

0.15

0.10

0.05 Total phosphorus (mg·L

0.00 0.25 C 0.20

0.15

0.10

0.05

0.00 8811576 778 7 10 7 JFMAMJJASOND Month (1981-1998)

Figure 10.1.g-1. Historic and current concentrations of total phosphorus at Sites 1(A), 2 (B) and 3 (C) in Campus Lake, Jackson Co., IL. Historic values were obtained from the EPA STORET database. Error bars represent ±1SE and numbers above the x-axis indicate the number of months for which measurements were available.

57 0.020 A

0.015

0.010

0.005

0.000 0.020 ) Top -1 Bottom B Phase 1 Top 0.015 Phase 1 Bottom

0.010

0.005

Dissolved phosphorus (mg·L 0.000 0.020 C

0.015

0.010

0.005

0.000 003010 202 2 10 JFMAMJJASOND Month (1981-1998)

Figure 10.1.g-2. Historic and current concentrations of dissolved phosphorus at Sites 1(A), 2 (B) and 3 (C) in Campus Lake, Jackson Co., IL. Historic values were obtained from the EPA STORET database. Error bars represent ±1SE and numbers above the x-axis indicate the number of months for which measurements were available.

58 10.1.h. Chlorophyll

Chlorophyll is a plant pigment which occurs in chloroplasts and is responsible for harnessing sunlight. It occurs in all common algae and serves as an estimate of algal biomass in a water sample. Clear positive relationships between chlorophyll a and total phosphorus have been established for many freshwaters (Dillon and Rigler 1974) and serve as indicators of the degree of productivity or eutrophication (Carlson 1977; IEPA 1996). Chlorophyll pigments other and a exist and can be used to further characterize the algal community. Chlorophyll b is an auxiliary pigment present in green algae, while chlorophyll c is common in diatoms. Cyanobacteria only contain chlorophyll a, lacking b and c. Thus, during intense cyanobacteria blooms, one would expect to find primarily chlorophyll a, while spring samples when diatoms are abundant, should have high concentrations of chlorophyll a and c. It is important to note that chlorophyll concentrations for the same algal species and cell density can change depending on the amount of light the cells receive; increasing at low light intensity and decreasing at high light intensity. Thus, chlorophyll analysis should ideally be complemented by algal density counts to avoid possible errors associated with relying solely on chlorophyll concentration to estimate algal biomass. This is especially true for lakes with deep epilimnia or lakes that have high turbidity. In Campus Lake, chlorophyll a concentrations showed a distinct seasonal pattern ranging from a low of 10 :gL-1 in winter to a high of 125 :gL-1 in July (Figure 10.1.h-1). Maximum summer concentrations at Site 1 were slightly higher than at Sites 2 and 3, however, this difference as not significant (ANOVA P = 0.93) and concentrations among sites were similar. The summer high is consistent with summer productivity and algal growth seen in other lakes. The minimum chlorophyll concentration in May and early June is consistent with dense populations of zooplankton which graze the algae reducing their abundance. The clear water phase in May and June hint at interesting interactions between phytoplankton and zooplankton which warrant further investigation, as abundant zooplankton populations could be used to help reduce the density of algae.

59 160 Historic A 140 Phase 1 120

100

0 100 B

) 80 -1

Chlorophyll a (µg·L 20

0 100 C 80

0 124131 213 3 41 JFMAMJJASOND Month (1981-1998)

Figure 10.1.h-1. Historic and current concentrations of chlorophyll a at Sites 1 (A), 2 (B) and (C) in Campus Lake, Jackson Co., IL. Historic values were obtained from the EPA STORET database. Error bars represent ±1SE and numbers above the x-axis indicate the number of months for which data were available.

60 10.1.i. Dissolved Oxygen and Temperature

Dissolved oxygen and temperature are closely linked in aquatic ecosystems and are major factors contributing to the composition of the biotic community present in a particular water body. The dissolution of oxygen, a gas, in water adheres to conventional gas laws. Thus more gas can be dissolved in water at cold temperatures compared to warm temperatures. In addition, the solubility of oxygen in water also depends on atmospheric pressure or elevation of the lake, with higher solubility at low elevations or high atmospheric pressure compared to high elevations or low atmospheric pressure. Because most aquatic organisms require oxygen as a final electron acceptor in metabolic respiration, their presence in a water body is determined by a combination of minimum tolerable concentrations and the oxygen concentration present in the environment. It is not uncommon for shallow lakes and those with shallow bays and high algal biomass to exhibit large diurnal fluctuations in dissolved oxygen concentration. These fluctuations can range from super-saturation during the day, which may cause respiratory problems in fish, to anoxic conditions during the night, which can result in fish kills and the absence of other biota. Large fluctuations in dissolved oxygen and CO2 due to respiration can also significantly influence the carbonate/bicarbonate balance resulting in concurrent fluctuations of pH. The pH shift in lakes with high alkalinity (well buffered) will be less than in poorly buffered waters. Therefore, even if oxygen concentrations remain above critical levels, fluctuations of pH may limit the distribution of biota. The Illinois general use water quality standards indicate that dissolved oxygen concentrations should not fall below 5.0 mgL-1 and should be at least 6.0 mgL-1 during 16 hours of any 24-h period. In Campus Lake, oxygen concentrations varied temporally (season) and spatially (vertical) (Figure 10.1.i-1). The water was saturated during most of the winter and cold weather period. Because in most years Campus Lake is a warm monomictic lake (water generally remains at or above 4/C, and the lake is directly stratified in summer), circulation during the winter months is complete and little oxygen depletion occurs. However, in some years the lake does freeze over completely leading to rapid depletion of oxygen in bottom waters due to biological respiration and chemical reactions. The southerly geographic location of Campus Lake means that winter ice-cover rarely lasts more than 3 weeks at a time. After spring air temperature rises, and the lake stratifies, water below the thermocline is quickly depleted of oxygen and remains anoxic until fall turnover, or until a strong summer storm breaks stratification and mixes the lake. Although summer storms can mix the lake, stratification is usually re-established with the concomitant anoxic conditions in the hypolimnion. In the epilimnion, oxygen concentrations fluctuate daily, generally reaching super-saturation in

61 early afternoon on clear sunny days. No fish kills associated with the fluctuations have been observed, which suggests that nightly decreases remain above the minimum tolerance concentrations of the fish in Campus Lake. Installation of an aerator should provide the deepest part of the main basin with sufficient oxygen to avoid anoxic conditions, thus reducing the nutrients released from the sediments to the overlying water.

62 0.0

0.5 1

1 8 2

2 2

6 6

1 1.0

8 8 1

8 8 1 2 6 8 8 8 12 1 2 8 1.5

1 1 1

8 8

2 2 2 2 2

8 8 8

8 1

1 12 4 1 2.0 2

4 1

2 Depth (m)

4 4

2.5 8

1 3.0 6 0 0 0

12 4 3.5 4

AJAODF AJAODF AJAOD FAJAOD F AJAOD 1989 1990 1991 1992 1993

0.0 8

8 0.5

1.0 8

8 8

4 8

8 1.5 8

2 2 2 2

1 1 2.0 4

8 4

8 Depth (m) Depth

2.5

3.0 4

3.5 8 4

MAMJF JASONDJFMAMJJASOND J MAMJJAS 1997 1998 1999 Date Figure 10.1.i-1. Historic and current concentrations of dissolved oxygen in Campus Lake, Jackson Co., IL. Historic data was obtained from EPA STORET database, SIUC CEH&S, J. B. Stahl unpublished data)

63 Water temperature is closely related to the amount of incoming solar radiation and air temperature. As the air temperature warms in spring and solar radiation increases, the water is warmed rapidly. The non-linear relationship between water density and temperature causes the rapidly warming surface water to become less dense than the cooler water at the bottom of the lake. This differential heating results in stratification, or the layering of the water mass into distinct layers differing in temperature and density. The surface lay is the warmest and lightest and is called the epilimnion. The dense, cool bottom layer is called the hypolimnion, while the middle transition layer is called the metalimnion and contains the thermocline. The thermocline is defined as the point of most rapid temperature change with depth, which normally exceeds 1/C per meter. Typically, stratified deep north temperate lakes have surface water temperatures in the 15-20/C range and bottom temperatures less than 10/C (Wetzel 2001). However, stable stratification can also be reached with warmer overall lake temperatures and with a smaller temperature difference between the epi- and hypolimnion because the density of water decreases more rapidly per degree at warm temperatures (e.g. > 25/C) than at 15/C. This is seen in deep tropical lakes as well as shallow lakes in the US Midwest. Temperatures in Campus Lake remained near 4/C for most of the winter. In spring, Campus Lake warms rapidly and it is not uncommon for thermal stratification to be established in mid- to late-April, or early March (Figure 10.1.i-2). Due to spring storms which thoroughly mix the water column, the water mass warms up to approximately 12/C before the onset of stratification. As the summer progresses, bottom waters continually warm, reaching a maximum of approximately 25/C some years. Such warm bottom temperatures contribute to rapid microbial and chemical reactions which contribute to the rapid depletion of oxygen from the hypolimnion. In fall, storms combined with cool air temperatures rapidly cool the lake. The temperature regime in Campus Lake necessarily limits the fishery to warm water species.

64 0.0

3 7

0.5 3 2

3 1.0 0

2 3 3 1.5 7 0 0

3 30 0

2 2 1 1 1

8 2 5 8 5 2 5 7 1 5 4 1 4 8 2 2 8 7 8 5

4 4

6 9 9 6 9 2

1 1 2 1 1 1 1 1 2 1 1 2 2.0 2 1 1

2 2 2 2

7 7 1 30 Depth (m)

2 2.5

2 4

4 7

4 3.0 18 1

2 2

1 1

2 1 2 4 8

3.5 2 2 1 1 1 2

8 2 1 1 4.0 AMJF JASONDJFMAMJJASOND J MAMJJAO 1997 1998 1999 0.0

0.5 3

0 4

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3 2

0 7 1.5

2.0

1 1

2 1

6 9

1 8 5 2

2 1

9 6

1 2 1 1

1 Depth (m) Depth

8 8 7

1 2.5 2 1 8

2 3.0 7

2 4 12 2 4 3.5 15 21 21 18 4.0 MJ J ASOND J FMAMJ J ASOND J FMAMJ J ASOND J FMAMJ J 2000 2002 2002 2003 Date

Figure 10.1.i-2. Historic and current isopleths of water temperature in Campus Lake, Jackson Co., IL. Historic data were obtained from EPA STORET, the unpublished data of J. B. Stahl and F. M. Wilhelm from SIUC.

65 10.2. TROPHIC CONDITION

The trophic state of a lake can be easily summarized in an easy to understand index based on the amount of algal biomass in surface waters. Carlson’s (1977) trophic state index (TSI) ranging from 0 to 100 is commonly used to classify lakes according to trophic condition. It is based on three variables: Secchi depth (SD), chlorophyll a (Chl a) and total phosphorus (TP) which are all indicative of algal biomass in surface waters and thus trophic condition because lake ecosystem parameters are intimately linked to and controlled by algal primary producers. Comparing index numbers over time allows managers and user populations to easily examine whole-lake trends. Trophic state is assessed according to the following criteria:

Table 10.2-1. Relationship between Carlson’s (1977) trophic state index (TSI) and lake condition. Modified from Carlson (1977) Trophic State Surface total phosphorus Secchi depth Chlorophyll a TSI :gL-1 m :gL-1 Oligotrophic < 12 > 4 < 2.6 < 40 Mesotrophic 12 - 24 2 - 4 2.6 - 6.4 40 - 50 Eutrophic 24 - 96 0.5 - 2 6.4 - 56 50 - 70 Hypereutrophic > 96 < 0.5 > 56 > 70

It should be noted that TSI alone is not adequate to accurately assess the condition of some lakes. Lakes with high non-algal turbidity or high macrophyte density can be classified incorrectly. For example, macrophyte dominated lakes can have low concentrations of TP leading them to be classified as less eutrophic than is actually the case. Many lakes in Illinois are impacted by high sediment turbidity and macrophyte growth. Campus Lake is impacted by both factors, but the trophic state index is reliable given the high concentrations of TP, Chl a and low Secchi depth. For Campus Lake all three indexes indicate a eutrophic condition (Figure 10.2-1) ranging between 48 and 70. The secchi depth index has the longest record and shows a slight although non-significant (Regression P = 0.20) negative slope with time (Figure 10.2-1a). The large interannual variability is likely related to the shallow nature of Campus Lake, allowing for seasonal influences in regional climate to be noticed. It also illustrates the importance of a long term record to place the variable TSI values in context. The upward trend in the total phosphorus TSI (Figure 10.2-1c) may be indicative of the long term accumulation of phosphorus in the lake since it was dredged in 1957. This should receive further investigation and nutrient reduction to the lake must be considered in any restoration efforts.

66 70 A

55 TSI SD (Secchi depth) SD (Secchi TSI 50 65710911 10 6 12 111111 9 6 66 9 8 976 7 0 70 B ) a 65

55 TSI Chl a (Chlorophyll 50 2699 0 70 C 65

TSI TP (Total phosphorus) 50

2 9 1110 9 9 9 4 9 8 0 1975 1980 1985 1990 1995 2000 2005 Year

Figure 10.2-1. Historic and current values of Carlson’s trophic state index (TSI) for Secchi depth (A), chlorophyll a (B) and total phosphorus (C) in Campus Lake, Jackson Co., IL. Historic data were obtained from EPA STORET, IEPA VLMP, SIUC CEH&S and F. M. Wilhelm.

67 10.3. LIMITING ALGAL NUTRIENT

To estimate if either nitrogen or phosphorus limit algal growth, the ratio of total nitrogen (TN) to total phosphorus (TP) is compared because in natural populations of algae the tissue ratio of TN:TP is approximately 7:1 on a weight basis (Wetzel 2001). Therefore ratios of these nutrients close to 7:1 in water indicate that both nutrients are present in sufficient concentrations to sustain algal growth. However, ratios close to 10 to 12:1 would indicate phosphorus limitation, while a ratio less than 7:1 may indicate nitrogen limitation (Wetzel 2001). Although these are generalizations and can be applied to lakes in general, consideration must be given to situations in which both nutrients are available in such quantities that neither is limiting algal growth. Smith (1984) observed the dominance of cyanobacteria in lakes with TN:TP ratios 29 and suggested this is because light rather than nitrogen or phosphorus was the limiting factor. Cyanobacteria can regulate their buoyancy and therefore shade out other algae at the top of the water column. In Campus Lake, the Phase 1 TN:TP ratio exceeded 10:1 on most sampling dates (Table 10.3-1), suggesting phosphorus limitation based on the 7:1 standard. However, TP and DSP concentrations were consistently high and suggest that phosphorus is not limiting (See above). Thus, any restoration attempt in Campus Lake should target both nutrients.

Table 10.3-1. Ratios of total nitrogen to total phosphorus concentrations for 1997 to 1998 in Campus Lake, Jackson Co., IL Site Month 1 top 1 bottom 2 3 Jan 25:1 33:1 27:1 31:1 Feb 24:1 25:1 21:1 21:1 Mar Apr 28:1 18:1 20:1 22:1 May 21:1 13:1 19:1 20:1 Jun 120:1 14:1 12:1 14:1 Jul 21:1 9:1 18:1 18:1 Aug Sep 19:1 19:1 13:1 29:1 Oct 41:1 41:1 37:1 43:1 Nov Dec 25:1 25:1 24:1 12:1

68 10.4. SEDIMENT QUALITY AND SEDIMENTATION

10.4.a. Sediment Quality

The amount of sediment transported depends on factors such as soil type, land use and cover, land and channel slopes, watershed size, and the frequency and severity of floods. Transport rates can change as a result of changes in land use and cover and in response to erosion-control measures. Consequently, estimates of long-term sedimentation rates must be reassessed periodically (Weaver 1994), as evidenced by the great reduction in depth of the Horticulture pond from > 3.3 m (10') to less than 0.75 m (2') presently. Sediment accumulation can also be due to internal sources. Decomposing aquatic plants, algae, and animals are commonly the source of soft organic sediments (or “muck”) found at the bottom of lakes. Nutrients in decaying plants and animals do not disappear but can be recycled to the overlying lake water in large amounts. The decomposition of organic material can also contribute to low dissolved oxygen levels in the lake which is a large contributor to the release of nutrients, especially phosphorus, to overlying water (Nürnberg 1991; Wetzel 2001). Results of analyses of the sediment core samples taken from Campus Lake for the Phase I study are summarized in Table 10.4.a-1. Sampling dates, times and core locations of the original and supplementary cores are given in Appendix 1. One additional location (sample site 35) was taken at the west end of the lake at the entrance to the bay that receives the discharge from the horticulture pond. The sample site was approximately 30 m (98') northeast of site 31 (Figure A1.3-2). The classification of Illinois lake sediments according to Mitzelfelt (1996) is presented in table 10.4-2 for comparison. Results from Campus Lake show that most elements are in the normal range when compared to the data of Mitzelfelt. For those elements whose analyses were presented as a % composition and as their corresponding oxide in the Campus Lake samples, the Mitzelfelt values of element concentrations expressed in units of mg/kg were converted to % as oxide by multiplying by the appropriate gravimetric factor x 10 –4. For the fourteen samples analyzed, the elements exhibiting values above the normal range were the following: Potassium - To be rated “highly elevated”, a value should exceed 0.337% as the oxide. All Campus Lake samples gave values in the range of 1.80% to 2.11%, approximately six times the “highly elevated” value. Barium - All values are above the “highly elevated” value of 397 mgL-1. Chromium - All but one value (48 mgkg-1) equaled or exceeded the 49 mgkg-1 value to

69 Table 10.4.a-1. Current and historical sediment quality data for Campus Lake, Jackson Co., IL. Parameter Cores 6A 6B 11A 11B 23A 23B 23C 23D 33A 33B 33C 33D 35A 35B Total Carbon (%) 2.85 1.82 1.66 1.98 3.03 2.74 1.13 1.18 2.52 2.15 1.96 0.53 1.57 0.71 Inorganic Carbon (%) 0.04 0.03 0.02 0.02 0.02 0.02 0.01 0.02 0.02 0.02 0.01 0.02 0.01 0.02 Organic Carbon (%) 2.81 1.79 1.64 1.96 3.01 2.72 1.12 1.16 2.50 2.13 1.95 0.51 1.56 0.69

SiO2 69.4 72.8 72.4 67.0 70.0 71.9 78.8 81.6 71.9 70.6 70.3 81.2 77.2 79.1

Al2O3 11.9 11.5 11.5 14.0 11.4 11.1 9.3 7.8 11.4 12.1 12.3 8.6 9.5 9.5

Fe2O3 4.46 3.57 4.00 5.27 3.80 3.67 2.74 1.98 3.62 4.33 4.20 2.17 2.73 2.90 CaO 0.72 0.70 0.59 0.59 0.73 0.70 0.50 0.46 0.71 0.72 0.79 0.49 0.59 0.48 MgO 0.90 0.78 0.80 1.07 0.86 0.80 0.57 0.42 0.77 0.91 0.89 0.48 0.58 0.54

K2O 2.04 1.98 2.02 2.11 1.95 1.95 1.89 1.83 1.95 2.03 2.03 1.84 1.83 1.80

Na2O 0.92 1.00 0.93 0.75 0.89 0.94 0.94 0.98 0.97 0.93 0.90 1.01 0.98 0.93

TiO2 0.77 0.81 0.79 0.83 0.77 0.77 0.73 0.73 0.79 0.77 0.82 0.74 0.73 0.76

P2O5 0.14 0.09 0.22 0.23 0.12 0.12 0.09 0.07 0.10 0.13 0.13 0.06 0.07 0.07 MnO 0.14 0.06 0.08 0.11 0.08 0.07 0.06 0.05 0.07 0.12 0.09 0.06 0.06 0.11

SO3 0.16 0.17 0.15 0.14 0.32 0.16 0.13 0.11 0.15 0.14 0.18 0.12 0.14 0.12

Sr (ppm) 117 123 117 107 120 121 122 124 123 118 126 118 119 104 Ba (ppm) 550 461 598 634 509 501 563 589 495 543 524 534 478 539 Zr (ppm) 301 287 278 191 260 284 326 443 296 296 251 426 363 366

LOI(1000 /C %) 8.05 6.15 6.05 7.55 8.70 7.49 3.87 3.54 7.27 6.84 7.35 2.75 5.54 3.27

H2O (110 /C %) 2.74 2.51 2.68 3.28 2.81 2.77 1.82 1.1 2.78 2.93 0.90 1.15 0.76 1.87

V 90 83 88 112 82 80 67 52 80 91 92 66 66 68 Cr 77 58 64 85 61 63 49 46 68 68 75 53 53 52 Ni 33 27 28 35 29 28 25 27 27 30 33 24 24 24 Cu 63 55 49 85 52 52 34 22 60 67 71 43 43 24 Zn 100 74 74 101 123 107 43 17 79 98 88 54 54 24 Rb 93 84 89 111 86 84 75 66 82 89 92 71 71 72 Nb 16 18 18 22 16 15 16 15 15 16 17 15 15 16 Cl 133 119 112 144 129 113 48 15 120 152 104 67 67 45 Mo <5 <5 <5 <5 <5 <5 <5 <5 <5 <5 <5 <5 <5 <5 Cd <15 <15 <15 <15 <15 <15 <15 <15 <15 <15 <15 <15 <15 <15 Sn 8 5 <5 6 8 <5 <5 <5 7 <5 7 <5 <5 5 Pb 54 48 40 55 68 59 29 16 41 60 54 34 34 23 As <20 <20 <20 22 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20

70 Table 10.4.a-2. Classification of Illinois lake sediments. (Source Mitzelfelt 1996) Below Highly Parameter units Normal Elevated Normal elevated Nutrients Total Phosphorus mg/kg < 394 394 to < 1 115 1115 to < 2 179 $2 179 Total Kjeldahl mg/kg < 1 300 1300 to < 5357 5357 to < 11 700 $11 700 Nitrogen Metals Arsenic mg/kg < 4.1 4.1 to < 14 14 to < 95.5 $95.5 Barium mg/kg < 94 94 to < 271 271 to < 397 $397 Cadmium mg/kg n/a < 5 5 to < 14 $14 Chromium mg/kg < 13 13 to < 27 27 to < 49 $ 49 Copper mg/kg < 16.7 16.7 to < 100 100 to < 590 $ 590 Iron mg/kg < 16 000 16 000 to < 37 000 37 000 to < 56 000 $ 56 000 Lead mg/kg < 14 14 to < 59 59 to < 339 $ 339 Manganese mg/kg < 500 500 to < 1 700 1 700 to < 5 500 $ 5 500 Mercury mg/kg n/a < 0.15 0.15 to < 0.701 $ 0.701 Nickel mg/kg < 14.3 14.3 to < 31 31 to < 43 $43 Potassium mg/kg < 410 410 to < 2 100 2 100 to < 2 797 $ 2 797 Silver mg/kg n/a < 0.1 0.1 to < 1.0 $ 1.0 Zinc mg/kg < 59 59 to < 145 145 to < 1 100 $ 1 100 Organics Total PCBs :g/kg n/a < 10 10 to < 89 $ 89 Aldrin :g/kg n/a < 1.0 1.0 to < 1.2 $ 1.2 Dieldrin :g/kg n/a < 3.4 3.4 to < 15 $ 15 Total DDT :g/kg n/a < 10 10 to < 180 $ 180 Total Chlordane :g/kg n/a < 5.0 5.0 to < 12 $ 12 Endrin :g/kg n/a < 1.0 n/a $ 1.0 Methoxychlor :g/kg n/a < 5.0 n/a $ 5.0 "-HCH :g/kg n/a < 1.0 n/a $ 1.0 (-HCH (Lindane) :g/kg n/a < 1.0 n/a $ 1.0 Hexachlorobenzene :g/kg n/a < 1.0 n/a $ 1.0 Heptachlor :g/kg n/a < 1.0 n/a $ 1.0 Heptachlor epoxide :g/kg n/a < 1.0 1.0 to < 1.6 $ 1.6 be classified as “highly elevated”. Lead - Three values equaled or exceeded the normal high value of 59 mgkg-1. Arsenic - One value (22 mgkg-1) exceeded the normal high value of 14 mgkg-1; the remaining 13 values were reported as < 20 mgkg-1.

In the above list three elements, potassium, barium, and chromium are all rated “highly elevated”. However, comparing the Campus Lake data with that obtained from nearby Little

71 Grassy Lake (approximately 16 km [10 miles] southeast of Campus Lake), showed similar values for potassium and chromium, while no data was available for barium (Dreher et al. 1977). Concentration ranges observed were 9 960-17 430 mgkg-1 for potassium and 31-73 mgkg-1 for chromium. Sampling procedures were identical between the two studies and all analyses were completed at the Illinois State Geologic Survey (Dreher et al. 1977). Seven locations were sampled in Little Grassy Lake, with a total of 100 analyses performed for each constituent. Similar results were obtained for two other lakes reported in the same study, Lake DuQuoin (approximately 32 km [20 miles] north of Campus Lake) and Johnston City Lake (approximately 48 km [30 miles] northeast of Campus Lake). Thus the “highly elevated” values for potassium and chromium in Campus Lake appear characteristic of the region. Observations of the change in constituent concentration with respect to depth in the core indicate some trends (except for sample location 11, which is in one of the deepest region of the lake) for the following constituents: Organic Carbon concentrations are highest near the sediment/ water interface, where recent sediments are deposited and the deposits have not had as long a time for anaerobic decomposition as sediments deeper in the core. Phosphorus concentrations in the deepest portion of the cores were lower than those closer to the sediment-water interface (except for sample 35, which was taken from the bay receiving storm water discharge from the horticulture pond). The core sample at site 11 exhibited phosphorus concentrations about one third of the other sample sites, indicative of phosphorus loss to the overlying waters due to anoxic conditions in the deeper portion of the lake during summer stratification. LOI (Loss on Ignition) shows a general decrease with distance from the sediment- water interface, a trend consistent with that of organic carbon.

Most of the trace elements exhibit lower values in the core samples below the sediment depth. This could be indicative of contributions to the sediment from air borne sources from the industrial East St. Louis region, approximately 144 km [90 miles] northwest of Campus Lake. Sediment samples were also taken by IEPA personnel in August, 1997, and analyzed in their laboratory. These analyses included concentrations of priority organics (not included in analyses of our core samples), as well as nutrients and metals. These results, available from the STORET system and given in edited form in Appendix 2, include data from 1981. Both data sets include two sample locations; Site 1 is near the dam, and Site 3 is in the middle of the north arm of the lake. The 1981 data also includes an additional site, Site 2, which is in mid-lake. Inspection of these data indicates the following:

72 The August,1997 sampling at Site 1 showed elevated levels of Dieldrin (3.9 :gkg-1), arsenic (21 mgkg-1) and lead (65 mgkg-1). Highly elevated levels of Endrin (3.00 :gkg-1), Heptachlor (1.40 :gkg-1) and PCB’s (180 :gkg-1) were noted. The August, 1997 sampling at Site 3 showed elevated levels of Dieldrin (3.8 :gkg-1), arsenic (23 mgkg-1) and lead (66 mgkg-1) and highly elevated levels of Aldrin (3.5 :gkg-1), Methoxychlor (13 :gkg-1), and PCB’s (190 :gkg-1). For the constituents mentioned above, the 1981 sampling gave the following values: Site 1: Dieldrin 1.00 :gkg-1, arsenic 11-32 mgkg-1, lead 30-70 mgkg-1, PCB’s 10-38 :gkg-1. Endrin and Heptachlor were not reported. Site 3: Dieldrin 1.00 :gkg-1, arsenic 29-31 mgkg-1, lead 90-100 mgkg-1, PCB;s 33-45 :gkg-1. Methoxychlor was not reported. Site 2: Dieldrin 1.00 :gkg-1, arsenic 30-34 mgkg-1, lead 90 mgkg-1, PCB’s 55-62 :gkg-1. The August, 1997 sampling gave a value of 190 mgkg-1 for barium at site 1; it was not reported for sites 2 and 3, nor in the 1981 data. Chromium showed 25 mgkg-1 at site 1 on August, 1997 and 19-22 mgkg-1 from the 1981 data at that site. At site 2, the 1981 data showed 21-25 mgkg-1 chromium. Site 3 exhibited chromium concentrations of 20-25 mgkg-1 in 1981. The following additional observations may be made by inspection of the data presented. Chromium concentrations found in the IEPA sampling were generally less than half that found in the core sediment samples. The increase in PCB concentration between the 1981 and 1997 sampling is likely due to the transformer oil leak to the northern arm of the lake that occurred during that period. In spite of removal of sediment from that region of the lake following the leak, apparently some PCB containing sediments distributed to other regions of the lake. Although not concentrations to warrant further lake-wide remediation, a mercury and PCB consumption advisory are in effect for all fish taken from Campus Lake.

73 10.4.b. Shoreline erosion in and around Campus Lake

Shoreline erosion may increase turbidity and cause the basin to fill at an accelerated rate compared to natural lake succession. Such erosion not only contributes turbidity to the lake, but also decreases its esthetic appearance, both in terms of water clarity and the lake-land interface which most visitors encounter. Wave action induced by wind or boats (lone outboard powered life guard rescue boat on Campus Lake which is often driven at high speeds) as well as foot traffic next to the shoreline can cause shoreline erosion (Bickers and Hite 1994). On 25 and 30 June, and 1 July 1999, Campus Lake was surveyed for shoreline erosion. We used the methods described in Bickers and Hite (1994) to classify the erosion and located sites of erosion on a bathymetric map (Figure 10.4.b-1). Our observations are keyed to these sites. Sites 2 and 3 have the worst erosion. Heavy foot traffic is the principal cause of the erosion at those sites, although wave action contributes to the degradation of the shoreline. At the other sites foot traffic is the most common cause of erosion. We recommend the use of special coir rolls to control erosion from wave action, and sodding for erosion caused by foot traffic. Additional means might be necessary at sites 2 and 3. The degree of sediment erosion from the banks of Campus Lake are presented below in the sediment budget (Section 10.7).

74 Table 10.4.b-1. Areas of Shoreline erosion around Campus Lake, Jackson Co., IL. Site Description / Comment 1 Bank is eroded 1 to 1.5 feet for about 30 feet of shoreline. Pier A is now separated from the bank because of erosion (photo M4). Much of this erosion 2 comes from foot traffic on shore, although undercutting of the bank from wave action is evident toward the point (photo M5). In 1995 the pier base was still connected to the shore. There is much erosion from the point of land on the south shore at the entrance to the east arm of the lake to Pier B. Foot traffic is heavy here because this is where the children participating in the 3 Urban Fishing Program walk. This site has the worst erosion (photo M6). The net used to keep stocked fish in this arm of the lake is visible in this picture. Erosion is visible to a height of 3 feet and about 20 feet along the shore by Pier D. Foot traffic is 4 the principal cause of this erosion. In front (south) of Bowyer Hall there is slight undercutting from wave action, but aquatic 5 vegetation seems to have stabilized it. 6 This site also exhibits slight undercutting from wave action, but also seems to be stable now. 7 A cattail bed at this site, near Culvert 10, helps prevent erosion. 8 Another cattail bed by Culvert 15, helps stabilize the shoreline. An isolated spot of erosion along a 2 to 3 feet high bank occurs here. It is apparently caused by 9 foot traffic, (photo M12). 10 There is much erosion around a bench here from foot traffic (photo M13). 11 This is a narrow but rather high (up to 5 feet) area of erosion. This is an eroded foot path leading to a large fallen tree at the water’s edge (photo M16). 12 Evidently fishermen like this location. 13 This is a steep bank with a small bare area. The cause of the erosion is unclear. There is a concrete wall here that protects the point at the junction of the middle and west arms of 14 the lake. Behind the wall some collapse of the bank has occurred, apparently from seepage. This depression is filled with water and a lush growth of Elodea. Pier M (photo M20) illustrates a pier without erosion, the goal for all of the 21 concrete fishing 14A piers around Campus Lake. This site, just north of Pier R, shows slight undercutting from wave action, but the erosion appears 15 to have been stopped by vegetation. This high bank, between Pier U and the beach, shows no erosion (photo M27), because of 16 adequate cover of terrestrial vegetation. This site, across from the boat dock, shows some undercutting at the water line, probably from 17 wave action caused the life guard rescue motor boat.

75 Boat Dock

1000 FEET

Spillway (336.6’ ASL)

250 METERS

3 DAM

age is 336.6 feet above sea

500

16.6

14.6

Thompson Point Dorms

12.6

Note: Depths were originally measured as elevations above mean sea level. Lake st level.

7 2.6

N 0.6

10.6

8.6

6.6 4.6

Greek Row Dorms

’s

14A

Map showing sites (circled numbers) of shoreline erosion along the shores of Campus Lake, Jackson Co., IL. Survey was

’s

To President Pond

completed on 25 and 30 June and 1 July 1999.

President Pond

Figure 10.4.b-1.

76 10.5. HYDROLOGIC BUDGET

The hydrologic budget for Campus Lake was estimated using a mass balance approach. Precipitation to the watershed and lake surface, runoff from the land and water leaving the lake via the spillway were calculated for the 1997 study year. The Campus Lake watershed map indicating sub-watersheds is shown in Figure 1-2. Sub-watersheds were determined by inspection of topographic maps and by direct observation during late winter when leaves did not obstruct line of sight. Watershed area was calculated using a mass per unit area approach. First the map was photocopied onto heavy stock paper and then each sub-watershed was cut out and weighed. By evaluation of the mass per unit area of the paper, the area of each watershed was calculated. Sub-watershed areas and annual rainfall flow volume to the lake are listed in Table 10.5-1 while major discharge points of each watershed to the lake are summarized in Table 10.5-2. A discharge coefficient of 18% was used for the land surface.

Table 10.5-1. Sub-watershed rainfall flow in volume to Campus Lake, Jackson Co., IL. Sub-watershed Area Area Rainfall flow volume Sub-watershed ha acresPercent (%) ×103 m3 × 105 ft3 A 4.52 11.16 4.8 8.77 3.099 B 7.34 18.14 7.8 14.26 5.037 C 6.34 15.72 6.8 12.36 4.365 D 2.71 6.70 2.9 5.27 1.861 E 10.10 24.85 10.7 19.54 6.901 F 10.60 26.17 11.3 20.58 7.267 G 5.66 13.99 6.0 11.00 3.885 H 1.08 2.68 1.2 2.11 0.744 I 3.26 8.07 3.5 6.34 2.241 J 21.55 53.24 23.0 41.87 14.785 K 4.13 10.20 4.4 8.02 2.833 L 5.94 14.69 6.3 11.55 4.079 M 8.13 20.09 8.7 15.80 5.579 N 1.08 2.68 1.2 2.11 0.744 O 1.37 3.39 1.5 2.66 0.941 Total 93.81 231.80 100.0 182.28 64.370

77 Table 10.5-2. Sub-watersheds and their associated discharge points for Campus Lake, Jackson Co., IL. Watershed Discharge points A 1, 2, 25 B3, 4 C 5, 6, 7, 8, 9, 10, 10’, 11, 12 D --- E 13, 13', 14 F 15, 15', 15", 16 G17 H --- I 18, 19 J 20, 26, 27 K 21, 22 L23 M24 N --- O ---

Other data used for calculating the hydrologic budget are also listed below: Watersheds map scale: 1.85 in:1000 ft - therefore 1 in2 : 6.53 acre. 1 acre = 43560 ft2 ; 1ft3 = 28.32 Liter; Paper density: 0.1403 gin-2; 1 acre = 0.404685642 ha; 1 m3 = 35.314 ft3; 1 m2 = 10.76 ft2 Annual rainfall: 42.5 inches = 3.5417 ft. = 1.079 m Annual free water surface evaporation: 32 inches = 2.6667 ft. = 0.8182 m Lake area = 39.31 acre = 1 712 343.6 ft2 = 1.712×106 ft2 = 15.9 ha Lake surface evaporation volume = 2.6667 x 1 712 343.6 = 4.57×106 ft3 = 129.41×103 m3 (1) Lake rainfall volume = 3.5417 x 1 712 343.6 = 6.06×106 ft3 = 171.60×103 m3 (2) Watershed flow in volume = 3.5417 x (231.8 x 43 560) x 18% =6.437×106 ft3 = 182.28×103 m3 (3) Spillway flow out volume = (2) + (3) - (1) = 7.935×106 ft3 = 2.25×105m3

An annual flow over the spillway at Campus Lake was calculated by difference to be 2.25×105m3 (7.935x106 ft3). The calculation presented previously was based on annual rainfall, the area of the lake, the area of the watershed, an average land surface discharge coefficient of 18%, and an annual evaporation loss. Actual flow over the spillway at different depth of water was not available at the time the data was analyzed, hence the spillway flow was of necessity a difference calculation.

78 Recently (1998), flow measurements were obtained (with a newly purchased flowmeter) at different depths of flow over the spillway, allowing a calibration curve to be constructed. Flow readings were taken at six different locations across the spillway. The gauge readings at the spillway were then converted to flow rates. Based on the gauge readings taken at the spillway throughout the study, the total annual measured flow was 2.45×105m3 (8.64x106 ft3). This value is only 8.9% higher than that obtained by the difference calculation, which is reasonable for this type of study. The average flow rates based on average gauge readings at the spillway are presented in Table 10.5-3 for the winter, spring, summer and fall periods.

Table 10.5-3. Spillway gauge heights and seasonal flow volumes. Spillway flow volume Avg. gauge Season height Flow rate Flow rate Flow rate (month of year) per day per season cm inches ×10-3m3 ft3/s m3 ft3 ×103m3 ×103ft3 Winter 0.185 0.073 0.40 0.014 3.44 1216.5 3.15 111.16 (12, 1, 2) Spring 2.390 0.943 30.50 1.077 2 634.30 93 026.9 24.04 848.87 (3, 4, 5) Summer 0.071 0.028 0.077 0.003 6.66 235.2 0.61 21.44 (6, 7, 8) Fall 0.056 0.022 0.053 0.002 4.59 162.3 0.42 14.82 (9, 10, 11)

total per year 244.55 8 636.13

79 10.6. PHOSPHORUS AND NITROGEN BUDGETS

Nutrient inputs to Campus Lake may come from several sources. These sources and their relative importance to the nutrient budgets for nitrogen and phosphorus in Campus Lake are listed below.

10.6.a. Direct wet and dry deposition to the lake

Particulate and gaseous matter present in the air passing over the lake contribute nitrogen and phosphorus compounds to the lake. Some of this material may fall on or be absorbed directly from the air to the lake (dry deposition); other is carried to the lake by rainfall (wet deposition). Wet deposition rates for nitrogen are available from the National Atmospheric Deposition Program (NADP) (NRSP-3) / National Trend Network (2003) on the internet, where data is summarized from many sampling sites throughout the country. Generally, dry deposition rates are not available, nor is phosphorus deposition data available from that source. The USEPA CASTnet Annual Report (2000), accessible through the National Atmospheric Deposition Program website, does report wet and dry deposition of nitrogen compounds. It states that there were no trends in nitrogen deposition over the past 11 years and that, on a national basis, approximately 70% of nitrogen deposition was from wet deposition. The site near Champaign Illinois (BVL130) indicated a lower % wet deposition, and data reported by Quon (1977) suggested only 23% of the nitrogen deposition occurred by wet deposition. A value of 60% wet nitrogen deposition was used to estimate the total (wet + dry) nitrogen deposition in the calculations for Campus Lake. A monitoring location for the NADP had been active near Southern Illinois University at Carbondale (Monitoring Location IL 35) from 1979 to 1993. The data used for this report was

-1 -1 the 1993 annual wet deposition data for NH4 (3.26 kgha ) and NO3 (15.05 kgha ). Conversion of these values to equivalent N and summing them gives a total annual wet deposition of nitrogen of 5.69 kgha-1. Assuming this represents 60% of the total nitrogen deposition, a total annual (wet + dry) nitrogen deposition rate of 9.48 kgha-1 is estimated, or a total of 153.5 kg of nitrogen to the 16.19 ha area of Campus Lake. As mentioned above, there is no data for phosphorus deposition rates in the NADP data base. A rough estimate of phosphorus deposition rates at Campus Lake may be made by multiplying the annual wet total N deposition rate by the ratio of total P/wet total N derived from the previously mentioned report by Quon (1977):

80 5.69 kg wet total Nha-1 x (0.54 kg total Pha-1/ 8.9 kg wet total Nha-1) = 0.1626 kg total Pha-1.

Thus for the 16.19 ha area of Campus Lake the annual wet and dry deposition of phosphorus is estimated to be 2.63 kg.

10.6.b. Runoff entering the lake from the shoreline and storm drains during storms

A major input of nutrients to Campus Lake is from the 27 storm sewers that enter the lake, primarily on the north and west shorelines. The calculated estimates of nutrient inputs from each of the sub watersheds assumes that the nutrient concentrations that were present in the storm sewers from a given sub watershed are representative of any runoff that occurs directly to the lake from that watershed; values are given in Table 10.6.b-1 and an estimate of the annual discharge amount of each nutrient is given in Table 10.6.b-2.

Table 10.6.b-1. Mean of storm water runoff parameter for each watershed Concentration of constituents TSS1 VS2 Turbidity TP3 TKN4 NO -N5 NH -N6 Watershed x 3 mgL-1 mgL-1 NTU mgL-1 mgL-1 mgL-1 mgL-1 A 12.0 4.7 5.3 0.115 0.610 0.170 0.140 B 28.5 14.5 13.0 0.096 0.489 0.087 0.155 C 10.5 3.2 5.1 0.056 0.461 0.232 0.149 E 39.8 15.8 10.7 0.148 0.671 0.315 0.168 F 50.0 12.2 19.9 0.240 0.834 0.204 0.235 G 26.0 6.0 17.0 0.200 0.700 0.200 0.200 I 69.3 11.5 8.1 0.150 0.630 0.110 0.158 J 33.5 10.6 9.8 0.189 0.900 0.313 0.153 K 53.6 14.3 10.6 0.220 2.230 0.173 0.170 L 78.0 20.5 15.0 0.290 1.310 0.340 0.200 M 32.0 10.0 9.0 0.148 0.900 0.070 0.200 Note: 1TSS - total suspended solids; 2VS - voltatile solids; 3TP - total phsphorus; 4TKN - total 5 6 Kjeldahl nitrogen; NOx-N - nitrite and nitrate ammonia; and NH3-N - ammonia

81 Table 10.6.b-2. Annual discharge amount for each sub watershed from Campus Lake, Jackson Co., IL for the period 1997-1998. Mass of constituents Rainfall Sub- TSS1 VS2 TP3 TKN4 NO -N5 NH -N6 flow vol. x 3 watershed kg kg kg kg kg kg ×106L I 6.35 439.8 73.0 0.95 4.00 0.70 1.00 K 8.02 430.0 114.3 1.77 17.89 1.39 1.36 A 8.78 105.3 41.0 1.01 3.35 1.49 1.23 G 11.00 286.0 66.0 2.20 7.70 2.20 2.20 L 11.55 901.0 236.8 3.35 15.10 3.93 2.31 C 12.36 129.8 39.4 0.69 5.70 2.87 1.84 B 14.27 406.6 206.8 1.37 6.98 1.24 2.21 M 15.80 506.0 158.0 2.34 14.20 1.11 3.16 E 19.54 777.7 309.3 2.89 13.11 6.16 3.28 F 20.58 1029.0 250.0 4.94 17.16 4.20 4.84 J 41.87 1404.0 444.0 7.91 37.68 13.11 6.41 Total 170.10 6415.0 1939.0 29.42 144.90 38.40 29.84

Note: This table is sorted by rainfall flow in volume; Annual discharge amount = Annual rainfall flow in volume x Average concentration of each parameter; 1TSS - total suspended 2 3 4 5 solids; VS - voltatile solids; TP - total phsphorus; TKN - total Kjeldahl nitrogen; NOx-N 6 - nitrite and nitrate ammonia; and NH3-N - ammonia

Inspection of the table indicates that in general, watersheds E, F and J discharge large amounts of constituents to Campus Lake. The calculated annual loss of each constituent over the spillway for each season is given in Table 10.6.b-3. The lower row of Table 10.6.b-3 repeats the data presented previously and is the calculated input of the nutrients based on calculated flows from each drainage basin and average concentration values from the storm event discharges to each drainage basin. Comparison of the last two rows of Table 10.6.b-3 is of interest. The annual nitrate loss over the spillway was 8.8 kg compared to 38.4 kg input from storm event discharges. Although part of this loss may be attributed to denitrification in the lake bottom during the summer months, it is likely most of the nitrogen lost was converted to algal cells, rooted aquatic vegetation, fish and other organisms and accumulated in the lake sediments. In contrast to nitrate, that exhibited a lower discharge quantity than the input, ammonia nitrogen leaving the lake over the spillway increased to 48.9 kgyr-1 compared to the input of 29.84 kgyr-1. This increase may be attributed primarily to decomposition of decaying plant matter on the lake

82 bottom. A total of 29.42 kgyr-1 of phosphorus entered the lake, compared to 7.83 kgyr-1 leaving over the spillway. This loss primarily represents uptake by algae and other plants, as well as precipitation as insoluble phosphates. The total suspended solids in the exiting flow was 2 935 kgyr-1, compared to an input of 6 415 kg.

Table 10.6.b-3. Nutrient outflow over spillway for winter, spring, summer and fall in Campus Lake, Jackson Co., IL. Concentration and mass of constituents 1 2 3 4 5 6 Season TSS VS TP TKN NOx-N NH3-N (month of year) mgL-1 mgL-1 mgL-1 mgL-1 mgL-1 mgL-1 Winter 37.7 14.2 0.1 4.8 0.1 0.6 (12, 1, 2) Spring 2884.9 1081.8 7.7 363.5 8.7 48.1 (3, 4, 5) Summer 7.3 2.7 0.02 0.9 0.02 0.12 (6, 7, 8) Fall 5.0 1.9 0.01 0.6 0.02 0.08 (9, 10, 11) Total (kg/year) 2 934.9 1 100.6 7.83 369.8 8.8 48.9 Total (kg/year)7 6 415.0 1 939.0 29.42 144.9 38.4 29.8

Note: 1TSS - total suspended solids; 2VS - voltatile solids; 3TP - total phsphorus; 4TKN - total 5 6 7 Kjeldahl nitrogen; NOx-N - nitrite and nitrate ammonia; NH3-N - ammonia; from storm events (from Table 4.1.1)

10.6.c. Waterfowl

As discussed previously, waterfowl are estimated to contribute approximately 6.1 kg of phosphorus to Campus Lake annually.

10.6.d. Groundwater flow to the lake

As previously discussed, the impervious clay soil forming the lake bottom was assumed to provide minimal groundwater flow to or from the lake, and thus nutrient inputs or outputs from groundwater are assumed negligible in the overall nutrient balance.

10.6.e. Macrophytes

Macrophytes remove nutrients from the bottom soil and water column during growth,

83 and release them during decomposition. Annual phosphorus contribution from macrophytes to Campus Lake has been estimated by Gaskill (2003) to be 60 kg. Removal of macrophytes would certainly reduce the nutrient content in Campus Lake, but for the study period no harvesting occurred. They are therefore neglected as an independent nutrient source in the nutrient budget; their effect is recognized in the nutrient contribution of the bottom sediments.

10.6.f. Leaves and other shoreline vegetation that falls into the lake

Most of the shoreline of Campus Lake is wooded. The leaves and other shoreline vegetation that find their way to the lake contribute to the organic content of the bottom sediments. The phosphorus input to the lake from leaves has been estimated at 7.6 kgyr-1 (Gaskill 2003) but, as in the case with macrophytes, their effect on the lake water is recognized in contributions of nitrogen and phosphorus from the lake sediments.

10.6.g. Bottom sediments

The organically rich sediments in the bottom of the lake may contribute and/or remove nutrients from the water column, depending largely on the oxidation state of that environment. As long as the oxygen concentration at the sediment surface remain above about 1 mgL-1, release of nutrients is minimal. Under anoxic conditions, however, nutrient release can be significant. Calculation of nutrient release of phosphorus and nitrogen from the bottom sediments of Campus Lake was determined separately for the oxic and anoxic zones of the lake. During the summer stratification period, the area under the thermocline, which occurs at approximately 2.6 meters, is estimated to be 72 491 m-2 of the total 161 000 m2 area of the lake. We calculated the average length of time of stratification is approximately 90 days, and that temperatures are warm enough to promote biological activity in spring and fall for an additional 150 days. Daily phosphorus release rates of 12 mgm-2 under anoxic conditions and 0.3 mgm-2 under oxic conditions (Nürnberg 1984) were used in the calculation. Nitrogen release rate was taken as five times that of phosphorus (based on the study by Hudson 2001 for Maple Lake). Multiplying the phosphorus release rates by the applicable lake areas and number of days gave an annual input of 93.8 kg of phosphorus and 469.2 kg of nitrogen released from the sediments of Campus Lake. The phosphorus and nitrogen budgets for Campus Lake are summarized in Table 10.6-6.

84 Table 10.6.g-1. Nutrient budget for total phosphorus and nitrogen for Campus Lake, Jackson Co., IL. Phosphorus Nitrogen Input source kgyr-1 %kgyr-1 % Direct Wet and Dry deposition 2.63 2.0 153.5 22.2 Groundwater 0.0 0.0 0.0 0.0 Runoff from shoreline and storm 29.4 22.3 68.2 9.9 drains Waterfowl 6.1 4.6 ------Bottom sediments 93.8 71.1 469.2 67.9

Total input 131.9 100.0 690.9 100.0 Outflow over dam 29.4 57.7 Net loading 102.5 633.2

85 10.7. SEDIMENT BUDGET

Since the dredging of Campus Lake was completed in 1958 until the current sediment study was performed in 1998, sediment has accumulated in the lake bottom. Over this 40-year period, an estimated 10 761 m3 (379 999 ft3) of sediment has accumulated. This estimate is based on an average sediment depth of 6.73 cm (2.65 inches) and lake area of 1.62 × 104 m2 (1.74 × 106 ft 2). The average annual sediment depth increase of 0.17 cm (0.066 inches) corresponds to an annual sediment load of 272.6 m3 (9 625 ft 3). The major sources of sediment in the lake occur from the storm water inflows, bank erosion, direct deposition (wet and dry) from the air, and leaves and other plant material falling into the lake. Based on the difference between the measured input of total solids from the storm events, and loss of total solids over the spillway, approximately 2.2 m3 (77 ft 3) of solids (assuming a density of 1.6 gcm3) are retained in the lake. Atmospheric contribution of solids is estimated at 0.17 m3 (6 ft3). The atmospheric contribution of solids was based on the reported deposition rate of wet nitrogen of 5.69 kgha-1yr-1 multiplied by the ratio of total solids/ wet nitrogen (27.5) calculated from data given by Quon (1977). Neglecting the volume increase in the sediment by leaf and other plant residues, the difference between the total sediment volume of 272.6 m3 (9 625 ft3) and the sum of the storm water solids contribution and direct deposition from the air provides an estimate of the sediment load by bank erosion:

272.6 m3 (9 625 ft3) - [2.2 m3 (77 ft 3) + 1.58 m3 (56)ft3] = 268.8 m3 (9 492 ft3)

This should be regarded as a maximum estimate, since leaf and plant residues were neglected in the calculation. Assuming an average shoreline bank height of 0.61 m (2 ft), the estimated annual shoreline loss for Campus Lake would be 0.08 myr-1 (0.27ftyr-1), or 3.26 m (10.7 ft) over the past 40 years. That this degree of erosion has indeed occurred over the years was evident by the existence of a lighted pole just west of the beach at Campus Lake. In 1997, it stood about 6.1 m (20 ft) into the lake from the existing shoreline, indicating the prior shoreline location; the pole has subsequently been removed.

86 10.8. STORM WATER RUNOFF ANALYSIS

A first step in the restoration and maintenance of the physical, chemical, and biological properties of Campus Lake is to thoroughly comprehend the present water quality. However, since present water quality is the result of various hydrologic inputs, including storm water runoff. Because Campus Lake is only recharged by surface runoff or direct deposition to the lake, it is important to assess the importance of surface inputs to the lake in terms of water and associated constituents. Campus Lake discharge points were shown in Figure 9.1-1. Twenty nine sampling locations around the lake were selected and the spillway is labeled as Site 0. Chemical parameters such as nitrogen, phosphorus, solids, and turbidity were analyzed for each site. There was no statistical evidence that site affected the concentration of nitrate & nitrite nitrogen, ammonia nitrogen, total suspended solids, volatile suspended solids and turbidity. Only total phosphorous and Kjeldahl nitrogen concentrations were site dependent. The top fifteen sites with the highest concentration of each parameter are listed in descending order in Table 10.8-2. Weight factors corresponding to each rank are listed in Table 10.8-3 to evaluate which discharge point(s) are important pollution sources. Total weight for each site is equal to S (weight). The result of the total weight calculation of sites found to be significant are shown in Table 10.8-4 (tabular values indicate rank). The higher the total weight value, the greater the mass of constituents the site contributes to the lake. From Table 10.8-4 we find that the top thirteen discharge points with high total weight values are located to the north and west of Campus Lake. These significant discharge points are marked in Figure 9.1-1. The culvert at site 23 with a total weight value of 91 contributed the highest concentration of constituents to the lake. The culvert at site 14 ranked weight order 2, while the culvert at site 26 ranked weight order 3 and is where the Horticulture Pond discharges. Duckweed growing in this pond, as well that growing in the President’s pond has the potential to remove nutrients, if harvested. However due to the shallow nature of both of these ponds and the high Duckweed cover, they are likely anoxic, and thus contribute constituents due to internal loading. The Horticulture Pond should be deepened to encourage deposition of material and kept oxic to discourage the internal loading of nutrients such as nitrogen and phosphorus. The culvert at site 13 ranked weight order 9. Site 13 collects the runoff from several large parking lots. Several times during runoff event sampling oil was seen in the discharge from this culvert. More attention should be given to mitigating/reducing inputs from this site. A

87 Table 10.8-1. Mean concentrations of constituents in storm water runoff entering Campus Lake, Jackson Co., IL. form each of 27 storm drains located around the lake. - Mean NOx -N NH3-N TP TSS VSS TKN Turbidity mgL-1 mgL-1 mgL-1 mgL-1 mgL-1 mgL-1 NTU Site 0-27 0.21 0.17 0.146 35.7 10.4 0.77 10.0 Site 0 0.04 0.20 0.032 12.0 4.5 1.51 6.4 Site 1 0.30 0.20 0.050 8.0 2.0 0.40 5.0 Site 2 0.20 0.13 0.096 9.0 3.0 0.30 5.0 Site 3 0.07 0.11 0.091 33.0 17.0 0.38 16.1 Site 4 0.10 0.20 0.100 24.0 12.0 0.60 10.0 Site 5 0.20 0.20 0.048 3.0 2.0 0.35 4.1 Site 6 0.11 0.09 0.112 34.0 5.0 0.69 5.6 Site 7 0.20 0.18 0.090 5.0 2.0 0.40 5.0 Site 8 0.20 0.10 0.040 5.0 2.0 0.40 5.3 Site 9 0.30 0.23 0.040 10.3 3.5 0.42 5.2 Site 10 0.05 0.11 0.030 8.0 4.0 0.39 4.0 Site 11 0.49 0.13 0.010 10.0 3.0 0.60 6.0 Site 12 0.31 0.16 0.080 8.8 4.0 0.45 5.7 Site 13 0.38 0.14 0.154 39.6 17.0 0.77 10.7 Site 13’ 0.17 0.17 0.090 43.8 17.0 0.44 10.3 Site 14 0.40 0.20 0.200 36.0 13.5 0.80 11.0 Site 15 0.20 0.30 0.300 32.0 11.5 0.90 16.0 Site 16 0.21 0.17 0.175 67.8 12.8 0.77 23.7 Site 17 0.20 0.20 0.200 26.0 6.0 0.70 17.0 Site 18 0.06 0.12 0.102 9.0 5.0 0.57 7.2 Site 19 0.17 0.20 0.200 129.5 18.0 0.70 9.0 Site 20 0.10 0.10 0.200 60.0 14.0 0.80 10.0 Site 21 0.18 0.19 0.200 40.5 9.0 0.90 9.1 Site 22 0.17 0.15 0.244 66.8 19.5 1.33 12.1 Site 23 0.34 0.20 0.290 78.0 20.5 1.31 15.0 Site 24 0.07 0.20 0.148 32.0 10.0 0.90 9.0 Site 25 0.02 0.10 0.200 19.0 9.0 1.13 6.0 Site 26 0.20 0.20 0.200 35.0 15.0 0.93 11.0 Site 27 0.64 0.16 0.166 5.6 2.8 0.97 8.2

88 Table 10.8-2. Ranking of the 15 sites which contribute the highest concentration of each constituent to Campus Lake. Site numbers are given first followed by the mean for the site in brackets. NO -N NH -N TP TSS VSS TKN Turbidity Rank x 3 mgL-1 mgL-1 mgL-1 mgL-1 mgL-1 mgL-1 NTU 1 27 (0.64) 15 (0.30) 15 (0.300) 19 (129.5) 23 (20.5) 0 (1.51) 16 (23.7) 2 11 (0.49) 9 (0.23) 23 (0.290) 23 (78.0) 22 (19.5) 22 (1.33) 17 (17.0) 3 14 (0.40) 14 (0.20) 22 (0.244) 16 (67.8) 19 (18.0) 23 (1.31) 3 (16.1) 4 13 (0.38) 23 (0.20) 14 (0.200) 22 (66.8) 13' (17.0) 25 (1.13) 15 (16.0) 5 23 (0.34) 1 (0.20) 17 (0.200) 20 (60.0) 13 (17.0) 27 (0.97) 23 (15.0) 6 12 (0.31) 5 (0.20) 26 (0.200) 13' (43.8) 3 (17.0) 26 (0.93) 22 (12.1) 7 1 (0.30) 17 (0.20) 19 (0.200) 21 (40.5) 26 (15.0) 15 (0.90) 26 (11.0) 8 9 (0.30) 26 (0.20) 21 (0.200) 13 (39.6) 20 (14.0) 24 (0.90) 14 (11.0) 9 16 (0.21) 19 (0.20) 20 (0.200) 14 (36.0) 14 (13.5) 21 (0.90) 13 (10.7) 10 2 (0.20) 4 (0.20) 25 (0.200) 26 (35.0) 16 (12.8) 20 (0.80) 13' (10.3) 11 5 (0.20) 24 (0.20) 16 (0.175) 6 (34.0) 4 (12.0) 14 (0.80) 20 (10.0) 12 7 (0.20) 0 (0.20) 27 (0.166) 3 (33.0) 15 (11.5) 13 (0.77) 4 (10.0) 13 8 (0.20) 21 (0.19) 13 (0.154) 15 (32.0) 24 (10.0) 16 (0.77) 21 (9.1) 14 15 (0.20) 7 (0.18) 24 (0.148) 24 (32.0) 21 (9.0) 17 (0.70) 24 (9.0) 15 17 (0.20*1) 16 (0.17) 6 (0.112) 17 (26.0) 25 (9.0) 19 (0.70) 19 (9.0) Note: *1 - same mean value 0.20mgL-1: site 17, 26.

Table 10.8-3. Weight factor form for calculating the importance of storm drain contribution to the mass of constituents entering Campus Lake, Jackson Co., IL. Rank123456789101112131415 Weight 15 14 13 12 11 10 9 8 7 6 5 4 3 2 1

89 Table 10.8-4. Storm discharge point ranking based on weights.

– Site NOx -N NH3-N TP TSS VSS TKN Turb Total Weight mgL-1 mgL-1 mgL-1 mgL-1 mgL-1 mgL-1 NTU Weight Order Site 235322135911 Site 1433499107672 Site 26103410767653 Site 15 10 1 1 13 12 7 4 64 4 Site 22 3 4 2 2 6 63 5 Site 19 3 4 1 3 15 14 56 6 Site 16 9 15 11 3 10 13 1 50 7 Site 17 10 3 4 15 14 2 48 8 Site 134 1384129469 Site 20 4 5 810114210 Site 21 13 4 7 14 7 13 38 11 Site 24 3 14 13 13 7 14 32 12 Site 27 1 12 5 30 13 Site 3 12 4 3 29 14 Site 0 3 1 28 15 Site 13’ 6 4 10 28 15 Site 25 4 14 4 26 17 Site 9 7 2 23 18 Site 4 3 11 11 23 18 Site 1 7 3 22 20 Site 5 10 3 19 21 Site 11 2 14 22 Site 12 6 10 23 Site 7 10 14 8 24 Site 2 10 6 25 Site 6 15 11 6 25 Site 8 10 6 25 Note: Blank means the parameter concentration for this site ranked greater than fifteen. storm water management wetland could be established on the north side of Douglas Drive to accomplish this. The culvert at site 15 ranked weight order 4. It had the highest nutrient (ammonia nitrogen and total phosphorus) concentrations to the lake. The culvert at site 27 had the highest concentrations of nitrate + nitrite nitrogen to the lake.

90 11. BIOLOGICAL RESOURCES AND ECOLOGICAL RELATIONSHIPS

11.1. PHYTOPLANKTON (1997 Data provided under contract by Dr. L. M. O’Flaherty to IEPA in Sprngfield, IL)

Campus Lake was sampled at one site (Site 1) on 18 April, 17 June, 16 July, 25 August and 7 October, 1997. No records exist on phytoplankton sampling from this lake in previous years. Samples were analyzed using the sweep method. Phytoplankton reached their peak density on 25 August (19 940.54mL-1) (Table 11.1-1; 11.1-2; Figure 11.1-1a). Most (89.1%) of this total density was due to the presence of a large number (17 767.194mL-1) of blue-greens (Phylum Cyanophyta). Members of the Phylum Bacillariophyta (diatoms) reached their peak density (599.704mL-1) on 17 June (Table 11.1-2; Figure 11.1-1b). No diatoms were in the sample taken on 18 April. Diatoms characteristically appear when water temperatures and competition with other algae are low. Two of the taxa (Asterionella formosa and Melosira italica var. tenuissima) that appeared in the sample on 17 June are typical of eutrophic, temperate lakes and are often present during winter and early spring (Table 11.1-2 and Table A3.1-1 Appendix 3). Cyclotella meneghiniana is another taxon characteristic of eutrophic lakes and one that typically appears early in spring. It did not appear in the samples from Campus Lake until 16 July. Nitzschia spp. seen in samples during the year may have developed on the bottom of tributaries entering the lake or in shallow zones on the margin of the lake. Green algae (Phylum Chlorophyta)reached their peak density on 25 August (1 755.958mL-1) (Table 11.1-2; Figure 11.1-1c). Taxa representing this group were all typical of euthrophic lakes (Table A3.1-1 Appendix 3). Taxa found in densities greater than 100mL-1 on 25 August included Ankistrodesmus falcatus var. acicularis (at 267.858mL-1), Dictyosphaerium pulchellum (744.050/mL), Scenedesmus abundans (178.572mL-1) and Teraedron minimum (119.048mL-1). The only member of the Phylum Chrysophyta seen in 1997 was Dinobryon sociale at 25.298mL-1 on 17 June (Table 11.1-1; 11.1-2). As in the case of the diatoms, this alga usually appears earlier in the year when temperatures are low and competition with other algae is not as great. Cryptomonads (Phylum Cryptophyta) reached their maximum density in the lake on 17 June (729.169mL-1) and formed their second highest density on 7 October (Table 11.1-1; 11.1- 2; Figure 11.1-1d). These algae were present throughout the year in Campus Lake, but characteristically form their peak density in early spring (April-June) or in the fall when

91 temperatures are lower than they are in mid-summer months. Blue-greens (Phylum Cyanophyta) were the dominant members of the phytoplankton on every date in 1997 (Table 11.1-1; 11.1-2; Figure 11.1-1e). They reached their highest density on 25 August (17 767.914mL-1) easily forming the majority of the total phytoplankton density. Two eutrophic indicator species occurred in the lake in 1997. Aphanizomenon flos-aquae reached bloom status (1 Million or more individualsmL-1) on 16 July (1 369 052mL-1) and on 25 August (2 321 436mL-1) (Table 11.1-2; Figure 11.1-1f). Microcystis aeruginosa was present on 16 July and in countable numbers on 25 August (89.286mL-1). Two innocuous blue-greens, Anacystis montana and Gomphosphaeria lacustris, were in countable numbers on all dates during the year. Raphidopsis curvata appeared at a low density (14.881mL-1) on 25 August. This blue-green is indicative of waters that are warm and shallow. Schizothrix calcicola was at high density on 25 August (7 485.143mL-1). This filamentous blue-green often develops on the bottom in shallow areas, forms gas bubbles under its mat and floats to become suspended in the water column Euglenoids (Phylum Euglenophyta) were at their highest density on 25 August (193.453mL-1) (Table 11.1-1; 11.1-2; Figure 11.1-1g). Trachelomonas volvocina (at 133.929mL-1) was the dominant euglenoid on 25 August and 16 July (104.167mL-1). It is typical of eutrophic lakes and is found in shallow ponds as well. Ophiocytim capitatum var. longispinum (Xanthophyta or Tribophyta) was in the sample from 7 October in a substantial density (1 398.814mL-1). This yellow-green alga has been reported from a wide range of lakes and permanent or semi-permanent pools and is considered to be a euplankter. Summary Based on the phytoplankton data collected and the types of algae present in the samples, Campus Lake was eutrophic in 1997. Support for this conclusion comes from the presence of a wide variety of eutrophic indicator taxa representing each of the major phyla. The presence of blooms of Aphanizomenon was a strong indicator of eutrophic conditions. Many of the organisms found on different dates during the course of the study are tolerant of high concentrations of organic materials (Euglena acutissima, Nitzschia palea, Trachelomonas volvocina). A major portion of the lake must be shallow with light penetrations to the bottom which led to the development of Schizothrix calicola in large density along with high numbers of Gomphosphaeria lacustris and the presence of Raphidiopsis curvata.

92 Table 11.1-1. Summary of number of algae from Campus Lake, Jackson Co., IL at Site 1 in 1997. Division 18 Apr 17 Jun 16 Jul 25 Aug 7 Oct Bacillariophyta 0 599.7 44.64 74.4 14.88 Chlorophyta 133.93 119.05 758.93 1 755.96 491.07 Chrysophyta 0 25.3 0 0 0 Cryptophyta 133.93 729.17 327.38 133.93 639.88 Cyanophyta 461.31 892.86 2 678.58 17 767.91 1 130.96 Euglenophyta 14.88 59.52 119.05 193.45 14.88 Pyrrhophyta 0 59.52 0 14.88 0 Xanthophyta 00001 398.81 Total 744.05 2 485.13 3 958.58 19 940.54 3 690.49 Aphanizomenon 0 0 1 369.05 2321.44 0 Microcystis 0 0 0 89.29 0

Table 11.1-2. Summary of numbers and biovolumes of organisms for Campus Lake, Jackson Co., IL Site 1 in 1997. Top numbers in each cell are densities (No.mL-1) and bottom numbers are biovolumes in :m3. Phylum 18 Apr 17 Jun 16 Jul 25 Aug 7 Oct 599.704 44.643 74.405 14.881 Bacillariophyta 0 2 755 492.6 8 875.0 14 462.9 2 958.3 133.929 119.048 758.931 1 755.958 491.073 Chlorophyta 46 409.4 185 165.7 1 061 868.0 4 184 921.1 429 245.2 25.298 Chrysophyta 0 000 184 463.2 133.929 729.169 327.382 133.929 639.883 Cryptophyta 122 723.6 1 377 688.9 391 543.0 260 051.4 1 158 545.4 461.311 892.860 2 678.580 17 767.914 1 130.956 Cyanophyta 234 218.0 469 916.7 4 508 389.3 10 635 353.8 1 464 838.0 14.881 59.524 119.048 193.453 14.881 Euglenophyta 10 946.5 251 980.0 295 765.8 711 782.0 10 946.5 59.524 14.881 Pyrrhophyta 0 0 0 9 250 868.8 2 312 717.2 1 398.814 Xanthophyta 0000 1 373 215.7 744.050 2 485.127 3 928.584 19 940.540 3 690.488 Total 414 297.5 14 475 575.1 6 266 441.1 18 119 288.4 4 439 749.1 Arthropoda 00000 14.881 Gastrotrichia 0 000 4 628 249.9 29.762 14.881 29.762 14.881 Protozoa 0 455 813.9 12 1744.4 1 804 749.7 121 744.4 Rotatoria00000 44.643 14.881 29.762 14.881 Total 0 5 084 063.8 121 744.4 1 804 749.7 121 744.4

93 25000 700

AB600 20000 500

15000 400

10000 300 200 5000 100

0 0 2000 800 1800 CD 1600 600 1400 1200 1000 400 800 600

-1 200 400 200 0 0 20000 25000 18000 EF

Number ·ml 16000 20000 14000 12000 15000 10000 8000 10000 6000 4000 5000 2000 0 0 Jan Feb Mar Sep Dec Nov 250 May 7-Oct 16-Jul 18-Apr 17-Jun G 25-Aug 200

150

100

0 Jan Feb Mar Dec Sep Nov May 7-Oct 16-Jul 18-Apr 17-Jun 25-Aug Date

Figure 11.1-1. Density of various algal species in Campus Lake during 1997. A - total algae; B - Bacillariophyta; C - Chlorophyta; D - Cryptophyta; E - Cyanophyta; F - Aphanizomenon; G - Euglenophyta.

94 11.2. BACTERIAL DENSITIES

Fecal coliform bacterial densities were measured at two different depths at three locations on Campus Lake from January 1987 to April 1997; a total of 638 samples were collected and analyzed during the ten-year period. Fecal coliform bacteria colonize the intestinal tract of all mammals and birds. The presence of fecal coliform may indicate the presence of other pathogenic microorganisms, and is used to help determine the suitability of the water for recreational use (Pepper et al. 1996). The peak densities of fecal coliform bacteria (measured as colony forming units, CFU) generally occurred in April at the surface of the water, and in August for the deeper sample (Figure 11.2-1). Samples described as colony forming units too numerous to count (TNTC) were reported seven times during the study, in August and September 1988 and in May 1996. High densities of bacteria at the surface in the spring are probably the result of temporary more abundant migratory waterfowl, while elevated densities deeper in the water column of the lake in late summer may be produced by the increase of the resident waterfowl population due to recruitment of young and their growth to adulthood (see section 11.5 Waterfowl). Bacterial densities very rarely (2.4%, n=15) exceeded the limit of 235 CFU generally recommended for recreational use. Thus, Campus Lake is suited for primary and secondary contact purposes such as swimming and recreation.

95 250 A 200

150

100

0 250 Top B Bottom 200

150

100

50 Fecal coliforms (CFU/100 ml) Fecal coliforms (CFU/100 0 250 C 200

150

100

0 67688 756 7 6 74 JFMAMJJASOND Month (1987-1997) Figure 11.2-1. Densities of fecal coliform bacteria for Site 1 (A), 2 (B) and 3 (C) in Campus Lake, Jackson Co., IL. Points represent the monthly average for the period 1987-1997 while error bars represent ±1(SE).

96 11.3. ZOOPLANKTON AND BENTHIC MACROINVERTEBRATES

11.3.a. Zooplankton

The zooplankton in Campus Lake is composed of three principal groups, the Cladocera, the Copepoda, and the Rotifera. These animals can affect water clarity by grazing on phytoplankton. Grazing efficiency increases with size, so large species clear the water better than small species. Two common genera of cladocerans illustrate this: Daphnia species are larger than Bosmina species, and even among the various species of Daphnia grazing efficiency correlates with size (See Figure 6.34 in Lampert and Sommer 1997). Thus the minimum food concentration that is able to support growth in the large species D. magna is about half that of Ceriodaphnia reticulata (a species in the family Daphniidae). Rotifers, because of their small size, seldom have much impact on phytoplankton populations and water clarity. They are likely to become abundant only if cladocerans and/or copepods are sparse. The size of species present depends in turn on selective predation on the zooplankton. Fish are usually the most important predators, and fish prefer large-bodied species. In ponds without fish, dense populations of large cladocerans develop and keep the water clear, even in the presence of high nutrient concentrations and rapid phytoplankton growth (Hrbáek et al. 1961). In spring it is typical for dense populations of zooplankton to develop, causing a spring clear water phase. Later, phytoplankton populations increase because species of algae develop which are not vulnerable to grazing and because predation by fish reduces zooplankton abundance (see Figure 20.6B in Dodson and Frey 1991). We consider the populations of the following taxa: the principal genera of Cladocera--- Daphnia, Ceriodaphnia, and Bosmina, the adult and copepodid stages of cyclopoid Copepoda and of calanoid Copepoda, the nauplii (larval stage of both groups of copepods), and the Rotifera. For each taxon the mean value of all three sites combined is calculated and graphed, and the value for each station tabulated to assess variation among sites. This approach is based on the premise that combining data from the three sites will give the best estimate of the entire population in the lake on each date. The only species of Daphnia identified was D. ambigua and of Ceriodaphnia was C. reticulata. Note that these are two of the three smallest species of Daphniidae (cf. Figure 6.34, Lampert and Sommer 1997). This suggests moderately heavy predation on the Cladocera, as would be expected by the presence of large pelagic bluegill. Daphnia The peak population of Daphnia occurred on 22 May 97 (Figure 11.3.a-1a). The

97 200 100 A Daphnia B Ceriodaphnia 80 150

60 100

40 50 20

0 0 300 300 C D 250 1480 848 Bosmina 250 Cyclopoids

200 200

150 150

100 100 ) -1 50 50

0 0 50 800 E F Calanoids 700 Nauplii 40 600 Individuals (No. · L 30 500 400 20 300 200 10 100 0 0 JFMAMJJASONDJFMAMJJASO 2000 G 1997 1998 Rotifers 1500

1000

500

0 JFMAMJJASONDJFMAMJJASO 1997 1998

Figure 11.3.a-1. Density of zooplankton taxa in Campus Lake, Jackson Co., IL for the period May 1997 to October 1998. Points represent the average for the three sampling stations. Error bars represent ±1(SE).

98 population was consistently lower for the 1998 sampling period, 23 May 98 - 16 Jul 98, than the comparable sampling period in 1997, with the highest density in 1997 over two times greater than the corresponding time period in 1998. The second highest density on 25 Oct 97, was over 9 times higher than on the final sampling date of 17 Oct 98. Although Station 2 had the highest population of Daphnia over the entire sampling period, Stations 1 and 3 did not have appreciably lower totals. Daphnia were found on 23 of the 33 sampling dates at all 3 stations. Ceriodaphnia The peak population of Ceriodaphnia occurred on 22 May 97 (Figure 11.3.a-1b). The second highest density, on 12 Sep 98, was less than half that of the highest. Short periods are evident when animals were not detected at any station. Station 2 had the highest population density for the entire sampling period. Ceriodaphnia were found at all 3 stations on 19 of the 33 sampling dates. Animals were reported on 25 of the 33 sampling dates at Station 1, compared with 22 and 20 days at Stations 2 and 3, respectively. Three out of four times when animals were counted at only one station, they were found at Station 1. The greatest difference between comparable sampling periods in 1997 and 1998 occurred during the months of August and September when, in 1997, both August and early September samples yielded no animal counts while Ceriodaphnia were evident at all three stations during corresponding periods in 1998, which includes the second highest density on 12 Sep 98. Bosmina The highest density of Bosmina occurred on 24 Sep 97, while the following sampling date, 8 Oct 97, reflected the second highest mean, but in numbers nearly half those of 24 Sep (Figure 11.3.a-1c). The only other sampling date with a substantial population was the final sampling date, but that was only one fifth the density of 24 Sep 97. The highest population density also occurred at Station 1 on 24 Sep 97. This number is 24 times greater than the total found at Station 3 for that date. Bosmina were found at all three stations for the first 18 sampling periods of the study. Subsequently, animals were only found on 5 and 6 of the 15 remaining sampling dates at Stations 3 and 2, respectively. No animals were found at any station on three sampling dates in the summer of 1998. Population densities at Stations 1 and 2 were eight or more times greater than at Station 3. Adult and Copepodid Cyclopoid Copepoda The peak population of cyclopoid Copepoda was reported on 7 Feb 9; it was only slightly more than on 18 Jun 97 (Figure 11.3.a-1d). In both instances, population densities showed a marked increase on the two sampling dates previous to these two high counts. Means for comparative sampling periods are lower in 1998 than 1997. Station 1 had the population over the entire study. On 18 Jun 97, the date of the second highest mean, the greatest one day total

99 was reported at Station 1, over six times greater than the two other stations. Cyclopoid Copepoda were found at every station on all sampling dates, except at Station 2 on 2 Jul 98. Adult and Copepodid Calanoid Copepoda The peak population of calanoid Copepoda occurred on 17 Oct 98, the final sampling date of the study (Figure 11.3.a-1e). The second highest density appeared three weeks earlier on the penultimate sampling date. Animals were found at all three stations only 4 times during the first year of the study in comparison with 7 sampling dates out of the final 11 sampling dates. This shows a marked contrast between comparable sampling dates in 1997 and 1998, when the former revealed no Copepoda on four of the first five sampling dates; animals were also only found at one of three stations on three of the first eight sampling dates. This trend of higher density for 1998 contrasts with the higher density in 1997 for cyclopoid Copepoda. Station 3 had the highest population. The greatest daily population at a single station, Station 1, also coincided with the peak populaton sampling date. Nauplii Nauplii of cyclopoid and calanoid Copepoda were present at all three stations on every sampling date throughout the entire sampling period (Figure 11.3.a-1f). The peak population occurred on 18 Jun 97 while the previous sampling date, 6 Jun 97, was second overall. Comparing the peak population on 18 Jun 97 with 21 Jun 98, the 1997 mean was over 4 times greater than in 1998. The density on 6 Jun 97 was over six times greater than approximately a year later, on 4 Jun 98. Station 1 had the highest population for the entire sampling period. The lowest density at a single station was reported at Station 2 on 6 Jun 97, compared with the second greatest density at the same station the following sample date. The lowest daily density occurred on 21 Mar 98 when all three stations had relatively low numbers of animals. Rotifera The peak population of Rotifera occurred on 18 Jun 97 (Figure 11.3.a-1g). This high came approximately one month after the lowest density of the year. In 1998 the minimum was also in late May. Rotifers can be outcompeted by cladocerans, and the minimum values are probably related to an abundant population of cladocerans. Later, when fish predation controls the larger zooplankton more effectively the rotifers can become more abundant. About two dozen species of rotifers were identified. Keratella, Polyarthra, Kellicottia and several species of Brachionus were nearly always present. These are common forms and suggest that the water quality is good. Overall, the zooplankton community is Campus Lake is characterized by small-bodied species which do reach prolific densities, but can not consume phytoplankton as efficiently as large-bodied species. The small body size likely results from intense predation by planktivorous

100 fish (see fish section below). Thus to achieve a longer lasting clear-water phase and use zooplankton to reduce algal abundance, the recruitment and retention of large-bodied species should be encouraged through management options of the fish community.

11.3.b. PROFUNDAL BENTHOS

In Campus Lake the benthos in the profundal (deep-water) zone consists mostly of three families of insects: Chaoboridae (phantom midges, Chaoborus), Chironomidae (true midges), and Ceratopogonidae (biting midges). Various other organisms may occur, though only oligochaetes of the family Tubificidae are at times abundant. Fish feed on these organisms, and as with the zooplankton they select the larger bodied individuals. Many species of profundal benthos are more resistant to oxygen depletion than fish, and so can use the profundal zone as a refuge from predation when the overlying water becomes depleted in oxygen. Nevertheless, the midges are vulnerable to predation in the pupal stage as they rise to the surface to emerge. One sample was taken from each station on each date with an Ekman dredge covering 225 cm2. The sediment was strained through a No. 40 brass sieve (425 :m apertures). In the laboratory the animals were picked out while they were still living. The number of benthic organisms per m-2 collected on 32 dates at each of the three stations during 17 months of sampling is shown in Table 11.3.b-1 to 11.3.b-3. Total numbers varied from 222 to 49 595 individuals m-2 (5 to 1 117 per Ekman sample). Both the minimum and the maximum density occurred at Station 3. Chaoborus predominated, and the maximum consisted exclusively of them. The absence of larvae in September and October is a result of metamorphosis of the larvae and subsequent emergence of adults. Chironomids were the second most abundant group, reaching a maximum of 11 056 per m-2 (at Station 1, 23 May 1998), but usually with fewer than 1 776 larvae per m-2. Chironomids will be discussed in more detail below. The third most abundant group of insects was the Ceratopogonidae. Their maximum was 2 398 per m-2 at Station 2 on 20 April 1998, but usually each sample had fewer than 20 larvae. Even this number is rather high compared to most lakes. The taxonomy of this family is not well worked out, so nothing more will be said about these biting midges. Seven other taxa were collected. The combined number was usually less than 20 per Ekman. These miscellaneous taxa will be discussed below. The family Chironomidae is the most widely distributed family of aquatic insects, occurring in every continent (including Antarctica) and in virtually every aquatic habitat (as well

101 as some terrestrial ones)(Coffman and Ferrington 1996). Relatively few species live in the profundal zone. In stratified eutrophic lakes, with oxygen depletion in summer, species of Chironomus are characteristic, whereas in oligotrophic lakes with little or no oxygen depletion

Table 11.3.b-1. Population density of principal benthic groups at sampling Site 1 in Campus Lake, Jackson Co., IL for the period May 1997 to October 1998. Date Site 1 Chaoborus Chironomidae Ceratopogonidae Other Total Depth (m) Nom-2 Nom-2 Nom-2 Nom-2 Nom-2 22-May-97 2.90 78.43 627.45 901.96 470.59 2078.43 06-Jun-97 3.53 745.10 313.73 235.29 392.16 1686.27 18-Jun-97 3.05 274.51 313.73 235.29 0.00 823.53 01-Jul-97 3.20 666.67 313.73 313.73 78.43 1372.55 17-Jul-97 2.92 1058.82 196.08 627.45 0.00 1882.35 31-Jul-97 3.15 8078.43 117.65 78.43 0.00 8274.51 14-Aug-97 2.59 1960.78 470.59 156.86 78.43 2666.67 27-Aug-97 3.08 8980.39 156.86 39.22 0.00 9176.47 10-Sep-97 3.24 9411.76 196.08 39.22 9647.06 24-Sep-97 2.70 13921.57 862.75 156.86 39.22 14980.39 08-Oct-97 2.78 1058.82 0.00 39.22 1098.04 25-Oct-97 2.80 3176.47 313.73 627.45 392.16 4509.80 08-Nov-97 2.73 1254.90 1058.82 745.10 1254.90 4313.73 22-Nov-97 2.71 8784.31 431.37 901.96 235.29 10352.94 06-Dec-97 3.10 7372.55 196.08 470.59 352.94 8392.16 17-Jan-98 2.72 1960.78 274.51 627.45 352.94 3215.69 07-Feb-98 2.60 901.96 1372.55 274.51 666.67 3215.69 21-Mar-98 2.70 352.94 156.86 784.31 509.80 1803.92 04-Apr-98 3.03 5254.90 666.67 0.00 0.00 5921.57 20-Apr-98 2.61 1764.71 4823.53 0.00 862.75 7450.98 04-May-98 2.83 549.02 352.94 313.73 0.00 1215.69 23-May-98 2.44 627.45 9764.71 313.73 274.51 10980.39 04-Jun-98 2.68 1098.04 823.53 0.00 274.51 2196.08 21-Jun-98 2.68 2117.65 4039.22 784.31 0.00 6941.18 02-Jul-98 2.75 2901.96 3098.04 0.00 0.00 6000.00 16-Jul-98 2.49 7176.47 2078.43 78.43 39.22 9372.55 31-Jul-98 2.69 11803.92 1058.82 39.22 0.00 12901.96 13-Aug-98 2.68 9019.61 39.22 78.43 0.00 9137.25 26-Aug-98 2.90 3294.12 0.00 39.22 0.00 3333.33 12-Sep-98 2.47 6352.94 78.43 196.08 313.73 6941.18 26-Sep-98 2.58 2666.67 0.00 196.08 39.22 2901.96 17-Oct-98 2.56 1843.14 39.22 78.43 6705.88 8666.67

102 Table 11.3.b-2. Population density of principal benthic groups at sampling Site 2 in Campus Lake, Jackson Co., IL for the period May 1997 to October 1998. Date Site 2 Chaoborus Chironomidae Ceratopogonidae Other Total Depth (m) Nom-2 Nom-2 Nom-2 Nom-2 Nom-2 22-May-97 2.40 4117.65 745.10 4862.75 06-Jun-97 2.61 823.53 2980.39 0.00 39.22 3843.14 18-Jun-97 2.72 1647.06 3058.82 392.16 196.08 5294.12 01-Jul-97 2.77 1607.84 1411.76 392.16 117.65 3529.41 17-Jul-97 2.63 823.53 4235.29 745.10 588.24 6392.16 31-Jul-97 2.56 1098.04 2156.86 352.94 117.65 3725.49 14-Aug-97 2.43 39.22 705.88 705.88 0.00 1450.98 27-Aug-97 2.53 2666.67 509.80 1137.25 0.00 4313.73 10-Sep-97 2.44 10588.24 352.94 1098.04 0.00 12039.22 24-Sep-97 2.52 352.94 0.00 0.00 352.94 08-Oct-97 2.44 431.37 0.00 156.86 588.24 25-Oct-97 2.38 431.37 235.29 2078.43 0.00 2745.10 08-Nov-97 2.80 1568.63 352.94 705.88 0.00 2627.45 22-Nov-97 2.48 2745.10 117.65 862.75 627.45 4352.94 06-Dec-97 2.53 2156.86 117.65 1019.61 666.67 3960.78 17-Jan-98 2.64 2588.24 392.16 862.75 431.37 4274.51 07-Feb-98 2.70 666.67 0.00 588.24 274.51 1529.41 21-Mar-98 2.71 1647.06 980.39 901.96 627.45 4156.86 04-Apr-98 2.80 9098.04 1215.69 352.94 0.00 10666.67 20-Apr-98 2.68 1568.63 3568.63 2117.65 2078.43 9333.33 04-May-98 2.59 745.10 392.16 0.00 5921.57 7058.82 23-May-98 2.51 2078.43 705.88 509.80 39.22 3333.33 04-Jun-98 2.44 784.31 2470.59 0.00 0.00 3254.90 21-Jun-98 2.43 1803.92 156.86 39.22 117.65 2117.65 02-Jul-98 2.59 5372.55 156.86 274.51 39.22 5843.14 16-Jul-98 2.7 9607.84 313.73 117.65 0.00 10039.22 31-Jul-98 2.53 6000.00 78.43 196.08 0.00 6274.51 13-Aug-98 2.69 7764.71 39.22 78.43 78.43 7960.78 26-Aug-98 2.62 6901.96 0.00 0.00 0.00 6901.96 12-Sep-98 2.42 9843.14 0.00 117.65 196.08 10156.86 26-Sep-98 2.5 4156.86 274.51 235.29 39.22 4705.88 17-Oct-98 2.5 823.53 117.65 196.08 5294.12 6431.37

103 Table 11.3.b-3. Population density of principal benthic groups at sampling Site 3 in Campus Lake, Jackson Co., IL for the period May 1997 to October 1998. Date Site 3 Chaoborus Chironomidae Ceratopogonidae Other Total Depth (m) Nom-2 Nom-2 Nom-2 Nom-2 Nom-2 22-May-97 3.90 4000.00 549.02 0.00 0.00 4549.02 06-Jun-97 4.56 3803.92 39.22 0.00 0.00 3843.14 18-Jun-97 4.33 2078.43 78.43 117.65 78.43 2352.94 01-Jul-97 4.44 2196.08 0.00 0.00 0.00 2196.08 17-Jul-97 4.45 1843.14 39.22 0.00 0.00 1882.35 31-Jul-97 4.38 549.02 0.00 39.22 0.00 588.24 14-Aug-97 4.29 4313.73 0.00 0.00 117.65 4431.37 27-Aug-97 4.32 10941.18 0.00 0.00 0.00 10941.18 10-Sep-97 4.20 14196.08 0.00 39.22 117.65 14352.94 24-Sep-97 4.15 0.00 39.22 0.00 156.86 196.08 08-Oct-97 4.05 0.00 0.00 0.00 392.16 392.16 25-Oct-97 4.16 23058.82 392.16 0.00 196.08 23647.06 08-Nov-97 4.20 10352.94 588.24 0.00 196.08 11137.25 22-Nov-97 4.40 12588.24 1098.04 0.00 39.22 13725.49 06-Dec-97 4.12 30627.45 235.29 274.51 39.22 31176.47 17-Jan-98 4.52 19411.76 235.29 78.43 0.00 19725.49 07-Feb-98 4.45 43607.84 156.86 0.00 39.22 43803.92 21-Mar-98 4.52 23960.78 588.24 0.00 156.86 24705.88 04-Apr-98 4.23 14431.37 274.51 235.29 0.00 14941.18 20-Apr-98 4.34 23686.27 196.08 196.08 235.29 24313.73 04-May-98 4.23 20000.00 235.29 78.43 78.43 20392.16 23-May-98 4.20 9568.63 156.86 39.22 0.00 9764.71 04-Jun-98 4.29 2392.16 78.43 0.00 0.00 2470.59 21-Jun-98 4.69 3137.25 156.86 117.65 0.00 3411.76 02-Jul-98 4.27 4509.80 78.43 78.43 0.00 4666.67 16-Jul-98 4.5 4705.88 0.00 39.22 0.00 4745.10 31-Jul-98 4.36 7137.25 39.22 0.00 0.00 7176.47 13-Aug-98 4.24 6901.96 0.00 0.00 0.00 6901.96 26-Aug-98 4.25 2235.29 0.00 0.00 0.00 2235.29 12-Sep-98 4.38 6745.10 0.00 0.00 0.00 6745.10 26-Sep-98 4.08 17882.35 0.00 39.22 156.86 18078.43 17-Oct-98 4.05 22862.75 0.00 39.22 156.86 23058.82

species of Tanytarsus are typically predominant. The use of chironomids in characterizing lakes was summarized by Saether (1979). He identified 15 chironomid communities, ranging from the ultraoligotrophic alpha community to the highly eutrophic omicron community. In the latter no chironomids survive, but the phantom midge, Chaoborus, may be abundant. Saether found very good correlation between these communities and the total phosphorus and chlorophyll a concentrations. Because the chironomids have a life cycle of a few months to a

104 year, they integrate short-term changes in nutrient concentrations and food supply, and thus their identification provides a valuable complement to chemical analysis of lake water in evaluating the trophic status of lakes. At Station 1 the most abundant chironomid species was Einfeldia natchitocheae (Sublette). This finding is of great interest because this is the first time that an abundant population of this species has been found and quantitatively sampled. The species was described from a lake in Louisiana (Sublette 1964); since then it has been found in a few other states (J. E. Sublette, personal communication), but this is the first record from Illinois. In the spring of 1998 this species was especially abundant: it reached its maximum of 248 larvae on 23 May. The absence of this species two weeks earlier is baffling, as two weeks before that the population was high. Larvae of Chironomus plumosus, f. semireductus and Procladius were frequently present, but usually there were fewer than five per sample. The Chironomus larvae are large, however, so their biomass and value as fish food are high. A few other genera occurred, mostly on 20 April 1998. These were probably dislocated from the littoral zone by water movement associated with spring turnover. Station 2, in the middle arm of the lake, had comparable depths to Station 1 and also had Einfeldia natchitoches as the most abundant chironomid species. However, in contrast to Station 1 this species was most abundant in the spring of 1997. Cladopelma was notably abundant at Station 2 in the spring of 1998. Chironomus plumosus, f. semireductus and Procladius were frequently present at this station also, and in rather large numbers on 31 Jul 1997 and 4 Apr 1998. Cryptochironomus occurred in low numbers but rather frequently, on six dates. Station 3, in the central basin of the lake, was about 2 meters deeper than the other stations and was therefore subjected to more intense and longer-lasting oxygen depletion. This was reflected in the chironomid fauna in which Chironomus plumosus f. semireductus and Procladius were almost the only species present. The abundance of Chironomus in October and November probably resulted from rapid growth of the larvae after the autumn turnover began. Just a few Cladopelma and Einfeldia natchitocheae were collected from this station. Of the benthic animals other than the three families of midges only oligochaetes of the family Tubificidae were abundant at any time. High abundance was sporadic; over 100 per Ekman were collected on 4 May 1998 at Station 2, and at Stations 1 and 2 on 17 Oct 1998. Tubificids are known to aggregate intensely at times, so the high numbers probably result from this behavior and do not have any particular significance. A few specimens of the large tubificid, Branchiura sowerbyi, also were obtained. This originally tropical species has become

105 widespread in warm temperature reservoirs (Brinkhurst and Gelder 1991). Perhaps the most surprising finding was that of the rhabdocoel flatworms in the genus Phaenocora. These flatworms were consistently quite abundant at Station 2 from November through March. A few were collected from Station 1 and even one specimen from Station 3. This genus is known to have species adapted to cope with anaerobic conditions (Kolasa 1991). We were able to recover specimens of Phaenocora only because the benthic samples were sorted while the animals were still alive; they would be very difficult to detect in preserved samples. In summary, the profundal benthos of Campus Lake indicates a eutrophic lake, but one in which the seasonal thermal stratification of the water plays the principal role in determining the conditions of the habitat. The proportionately small volume of the tropholytic zone, in which decomposition predominates, ensures that seasonal oxygen depletion will be severe. The abundance of Chaoborus larvae correlates with this oxygen depletion. The occurrence of Einfeldia natchitocheae in the upper profundal (represented by Stations 1 and 2) offers an intriguing possibility of using this species as an indicator of a distinctive habitat. Variations in abundance of the principal species of insects from one year to the next probably results primarily from variations in regional weather patterns rather than lake degradation. The midge adults only live for a few days, and successful mating is more likely in calm weather.

106 Table 11.3.b-4. Population density of other benthic taxa at Site 1, 2 and 3 in Campus Lake, Jackson Co., IL for the period May 1997 to October 1998. Numbers are individuals per square meter, and columns are in the order of Site 1 to 3 under each taxon heading. Date Taxa Naididae Tubificidae Branchiura Hirudinea Mermithidae Phoenocora Sphaeriidae 22-May-97 0.00 0.00 0.00 488.89 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 44.44 0.00 0.00 06-Jun-97 0.00 0.00 0.00 311.11 44.44 0.00 0.00 0.00 0.00 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 88.89 0.00 0.00 18-Jun-97 0.00 0.00 0.00 0.00 222.22 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 44.44 01-Jul-97 0.00 0.00 0.00 44.44 0.00 0.00 0.00 0.00 0.00 44.44 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 88.89 0.00 17-Jul-97 0.00 0.00 0.00 0.00 666.67 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 31-Jul-97 0.00 0.00 0.00 0.00 0.00 0.00 0.00 44.44 0.00 0.00 88.89 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 14-Aug-97 0.00 0.00 0.00 88.89 0.00 133.33 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 27-Aug-97 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 10-Sep-97 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 44.44 0.00 133.33 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 24-Sep-97 0.00 0.00 0.00 0.00 0.00 177.78 0.00 0.00 0.00 0.00 0.00 0.00 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 08-Oct-97 0.00 0.00 0.00 44.44 88.89 444.44 0.00 44.44 0.00 0.00 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 25-Oct-97 0.00 0.00 0.00 355.56 0.00 222.22 44.44 0.00 0.00 0.00 0.00 0.00 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 08-Nov-97 0.00 0.00 0.00 1333.33 0.00 177.78 44.44 0.00 0.00 0.00 0.00 44.44 0.00 0.00 0.00 44.44 0.00 0.00 0.00 0.00 0.00 22-Nov-97 0.00 0.00 0.00 222.22 177.78 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 44.44 533.33 0.00 0.00 0.00 0.00 06-Dec-97 0.00 0.00 0.00 400.00 533.33 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 222.22 0.00 0.00 0.00 0.00 17-Jan-98 0.00 0.00 0.00 400.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 488.89 0.00 0.00 0.00 0.00 07-Feb-98 0.00 0.00 0.00 666.67 222.22 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 88.89 88.89 44.44 0.00 0.00 0.00 21-Mar-98 0.00 0.00 0.00 444.44 666.67 133.33 0.00 0.00 44.44 0.00 0.00 0.00 0.00 0.00 0.00 133.33 44.44 0.00 0.00 0.00 0.00 04-Apr-98 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 20-Apr-98 311.11 133.33 0.00 666.67 2222.22 266.67 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 04-May-98 0.00 133.33 0.00 0.00 4844.44 88.89 0.00 88.89 0.00 0.00 177.78 0.00 0.00 0.00 0.00 0.00 1377.78 0.00 0.00 88.89 0.00 23-May-98 0.00 0.00 0.00 311.11 0.00 0.00 0.00 0.00 0.00 0.00 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 04-Jun-98 0.00 0.00 0.00 311.11 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 21-Jun-98 0.00 0.00 0.00 0.00 88.89 0.00 0.00 0.00 0.00 0.00 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 02-Jul-98 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 44.44 0.00 16-Jul-98 0.00 0.00 0.00 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 31-Jul-98 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 13-Aug-98 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 88.89 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 26-Aug-98 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 12-Sep-98 0.00 0.00 0.00 355.56 133.33 0.00 0.00 44.44 0.00 0.00 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 0.00 26-Sep-98 0.00 0.00 0.00 0.00 0.00 177.78 0.00 0.00 0.00 0.00 0.00 0.00 44.44 44.44 0.00 0.00 0.00 0.00 0.00 0.00 0.00 17-Oct-98 311.11 0.00 0.00 6488.89 6000.00 177.78 88.89 0.00 0.00 133.33 0.00 0.00 133.33 0.00 0.00 311.11 0.00 0.00 133.33 0.00 0.00

107 11.4. FISHERIES POPULATION

Campus Lake has a fish community consisting primarily of bluegill (Lepomis macrochirus), redear sunfish (L. microlophus) and largemouth bass (Micropterus salmoides) (Dudash and Heidinger 1996). Although canoes and paddle boats are available for rental at the boat dock, most fishing is conducted from the banks and from small cement piers around the lake. The anglers include SIUC students (many of whom come from the Chicago area, other regions of the state, as well as some out of state and out of country students) and residents of Carbondale and nearby towns.

11.4.a. Urban Fishing Program

Since 1996, Campus Lake has been one of three locations in Region V of the Illinois Urban Fishing Program. The other locations are at Centralia and Mt. Vernon (Illinois Department of Natural Resources 1999). In addition to stocking fish in the lakes, fishing gear is loaned free of charge to anyone interested in fishing, and fishing clinics are held at the lake. The put-and take stocking programs provide fishing experiences to many Illinois residents, primarily children. At Campus Lake, a northern bay of the lake is separated from the rest of the lake by netting and the fishing clinics are held at the boat dock and the point on the eastern side of the net.

11.4.b. Stocking History

Under the Urban Fishing Program, stocking of channel catfish (Ictalurus punctatus) has occurred six times each year since 1996. Stocking occurs during the first and third weeks of June, July and August. Each stocking consists of 300 kg of fish in the 0.5-1.5 kg range (Martin 1999). On 10 November 1982, 300 pure grass carp (Ctenopharyngodon idella) were stocked for the purpose of biological weed control. This stocking plan was based on prior studies (Monaghan 1983; Young 1981). Prior to introduction of the grass carp, 35% of the lake’s surface area was covered with vegetation during the summer, preventing effective management of the bass/bluegill community. In 1983, vegetative cover was reduced to about 1%. In November 1979, 300 hybrid grass carp and 300 bighead carp (Aristichthys nobiliis) were stocked in Campus Lake at the rate of 19 fish/ha. Significant decreases in the total density (approximately 50% each year) of the macrophytes was observed in 1980 and 1981. It was

108 suggested that some of this decrease resulted from environmental factors other than the grass carp, and that the hybrid species was not nearly as effective in reducing the macrophyte population than was the regular grass carp (Young 1981). In a 1984 study designed to determine the most economical size of channel catfish to stock in a lake having a bass/bluegill fish population, Dudash and Heidinger (1996) stocked 1 500 channel catfish, 300 in each of five size ranges from 76 to 203 mm. Throughout the study grass carp reduced aquatic vegetation to less than 1.0% of the surface area, and secchi disk readings ranged from 51 to 125 cm.

11.4.c. Fish Community Study

The condition of the sport fish community is one measure of the general health of a lake. Sport fish species tend to be relatively high in the foodweb and, therefore, their growth rate integrates the effects that pollution has on lower organisms on which these fish rely. In Campus Lake the sport fish community consists primarily of bluegill, largemouth bass, and channel catfish. A few redear sunfish and crappie (Pomoxis spp.) are also found in the lake. Gizzard shad (Dorosoma cepedianum) are not present. Since bluegill and largemouth bass are the most common sport fishes in the lake, they were used as index species to determine if the fish community was in balance. Fish were collected by 68 minutes of electrofishing from 6:00 pm to 9:00 pm on May 13, 1997. Three phase AC 4 000 watt generation was used with a balanced six dropper electrode array (Novotny and Priegel 1974) to sample four different areas of the lake. A total of 137 largemouth bass and 39 bluegill were collected. Each fish was measured to the nearest millimeter (total length) and weighed to the nearest gram. Surface temperature was 23.8ºC and the electrofishing unit drew approximately 11 amps on each of the three lines. Two measures that fishery biologists often use to determine the desirability of fish populations are relative weight and proportional stock density (Anderson and Neumann 1996). Relative weight is an index of plumpness of fish. A fish that weighs more than another individual of the same length will have a higher relative weight. The relative weight of a fish is calculated by dividing the actual weight of a fish by a standard weight. Length-specific standard weight equations have been developed for many species from weight-length regressions for many populations of that species. For a general largemouth bass and bluegill community relative weight values s that fall between 95-105 are considered desirable. Proportional stock density (PSD) and relative stock-density (RSD) are numerical descriptors of length-frequency data (Anderson and Neumann 1996). Proportional stock

109 density (Anderson 1976) is calculated as

Stock length for largemouth bass is 20 cm and quality is 30 cm. For bluegill stock length is 8 cm and quality length is 15 cm. Note, quality length does not refer to anglers perceptions of quality. Proportional stock density values range from 0-100. A balanced largemouth bass population tends to have values from 40 to 70 and balanced bluegill populations range from 20 to 40. Under the large sunfish management option the goal is to produce large bluegill by having many small largemouth bass in the lake to crop off bluegill recruitment. Under this option the acceptable PSD values for bluegill range up to 60. The relative stock density of preferred-length fish (RSD-P ;Wege and Anderson 1978) is the percentage of stock length fish that are preferred length. RSD-P is calculated as:

where preferred length is 38 cm for largemouth bass and 20 cm for bluegill. The mean relative weight of largemouth bass from the electrofishing sample was 86 (Figure 11.4.c-1A). Mean relative weight of bluegill was 95 (Figure 11.4.c-1B). Largemouth bass PSD was 19 and the PSD of bluegill was 52 (Figure 11.4.c-2). RSD-P for largemouth bass was 1.9 and the RSD-P for bluegill was 23. The catch per unit effort of electrofishing was 156 bass per hour and 44 bluegill per hour. Although the largemouth bass and especially the bluegill in Campus Lake are providing a considerable amount of sport fishing, their population structures could be improved. There appear to be too many 30 cm and smaller largemouth bass in the population. The bluegill have a relatively high PSD as would be expected under the large sunfish management option. Twenty three percent of the bluegill are larger than 20 cm in total length.

110 120 A 110

100

60 N = 137, Mean = 86 0 0 5 10 15 20 25 Total Length (inches) 140 B

Relative weight Relative 130

120

110

100

70 N = 39, Mean = 95 0 012345678910 Total length (inches)

Figure 11.4.c-1. Relative weight of largemouth bass (A) and bluegill (B) collected by electrofishing at night on May 13, 1997 from Campus Lake, Jackson, Co., IL.

111 90

60 Balance range for each species 50

30 Campus Lake bluegill = 52 largemouth bass = 19 20 Largemouth bass PSD 10

0 01020304050607080 Bluegill PSD

Figure 11.4.c-2. Proportional stock densities of largemouth bass and bluegill based on May 13, 1997 electrofishing samples in Campus Lake, Jackson Co., IL.

112 11.5. WATERFOWL

A census of the waterfowl was conducted early in the morning every two weeks (monthly in winter) along with our sampling of zooplankton and benthos. Mallard ducks were the dominant species, although five domestic geese were present, and in November and December grebes and coots were abundant (Figure 11.5-1). As many as 152 mallard ducks were observed (6 Dec 1997), but the mean for the 32 dates was 64. Census data such as these are inherently variable since ducks can fly to or from the lake, but we feel the mean value is representative given there is a resident duck population on Campus Lake. Manny et al. (1994) discuss nutrient contributions of ducks and geese to lakes. They calculated that each duck adds 0.22 g of phosphorus per day, while each goose adds 0.49 g. With mean numbers of 64 for ducks and 5 for geese, that amounts to 14.14 + 2.45 = 16.59 g P day-1, or 6 055 g P per year. This is significant, about 20 percent of the phosphorus input from the watershed. The importance of fecal input by ducks is illustrated by the photo of the dock at Campus Lake that shows one night’s accumulation (Figure 11.5-2). Each morning the dock is hosed to wash the night’s accumulation of feces into the lake. We recommend that the feces be scooped up morning and disposed of away from the lake.

113 200 180 160 140 120 100 80 60 40 Total number of waterfowl 20 0 Jul 97 Jul 98 Apr 97 Apr Oct 97 Oct Apr 98 Apr Oct 98 Oct Jan 97 Jan Jun 97 Jun Jan 98 Jan Jun 98 Jun Mar 97 Mar 98 Feb 97 Feb 98 Nov 97 Nov Nov 98 Nov Dec 97 Dec 98 Aug 97 Aug 98 Sep 97 Sep 98 May 97 May 98 Date (1997-1998)

Figure 11.5-1. Total number of waterfowl on Campus Lake, Jackson, Co. IL. on each date of observation from May 1997 to October 1998. Mean number of waterfowl was 64 for the study period.

114 Figure 11.5-2. One night’s accumulation of duck and goose droppings on the boat dock at Campus Lake, Jackson, Co., IL.

115 11.6. AQUATIC VEGETATION

Before 1979 macrophytes were so abundant in Campus Lake that fishing was severely hindered. Hybrid grass carp were introduced in November 1979 and their effect on macrophyte abundance assessed by two graduate students (Young 1981; Monaghan 1983). Since then macrophytes have not been excessively abundant. It is important to have some macrophytes in the lake, because many species of fish spawn in plant beds, young fish use them for shelter, and many invertebrates and algae live on the surface. Five species of submersed and floating-leaved macrophytes were collected: Elodea canadensis (waterweed), Ceratophyllum demersum (coontail), Potamogeton nodosus (pondweed), Ludwigia peploides, better known as Jussiaea diffusa (Water primrose), and Najas guadalupensis (common water nymph or bushy pondweed). A sixth species,Polygonum sp. (smartweed) was collected in four of the shoreline quadrats, but that is an emergent species and not likely to interfere with fishing. A few beds of Typha latifolia (common cattail) occurred around the lake, but these were not sampled, nor was the Nelumbo lutea (yellow water lotus) that grows at several places along the shoreline. The creeping primrose, which has floating, emergent, and submersed leaves, was dominant; it composed over half the total dry weight. Elodea was second most abundant with about one-fourth of the total dry weight. Wet weights and dry weights of each species at each station and overall are given in Table 11.6-1. From the transect measurements we estimate that 16% (28 262 m2) of the lake surface has macrophytes growing on and under it. From this survey it seems that the macrophyte abundance is about right for the overall health and usefulness of this ecosystem.

116 Table 11.6-1. Summary of dry weights and percentages from the Campus Lake macrophyte survey in 1997. Mass is per 0.25m2 quadrat (see Appendix 1 for sampling methodology and location of sample sites). Najas Elodea Ludwigia Sample Ceratophyllum guadulapensis Potamogeton Percent canadensis L.C. peploides Polygonum spp. Other TOTAL Number demersum L. (Spreng.) nodosus Poir. age Rich (HBK.) Raven Magnus (creeping (coontail) (waterweed) (naiad) (smartweed) (pondweed) primrose willow) Mass %tage Mass %tage Mass %tage Mass %tage Mass %tage Mass %tage Mass %tage Mass %tage 1A 0.00 1.40 0.02 38.60 0.58 0.00 17.90 0.27 0.00 8.40 0.13 66.30 2.56 1B 0.00 25.10 48.83 21.10 41.05 5.20 10.12 0.00 0.00 0.00 51.40 1.98 2A 0.00 24.00 79.21 0.00 6.30 20.79 0.00 0.00 0.00 30.30 1.17 2B 0.00 8.40 63.64 0.00 4.80 36.36 0.00 0.00 0.00 13.20 0.51 3A 0.00 16.40 94.25 1.00 5.75 0.00 0.00 0.00 0.00 17.40 0.67 3B 0.20 0.63 30.60 96.53 0.50 1.58 0.40 1.26 0.00 0.00 0.00 31.70 1.22 4A 0.00 0.00 454.20 100.00 0.00 0.00 0.00 0.00 454.20 17.50 4B 0.00 0.20 0.06 363.20 99.94 0.00 0.00 0.00 0.00 363.40 14.00 5A 0.00 0.00 153.30 100.00 0.00 0.00 0.00 0.00 153.30 5.91 5B 0.00 3.80 2.45 151.10 97.55 0.00 0.00 0.00 0.00 154.90 5.97 6A 0.00 57.40 99.83 0.00 0.10 0.17 0.00 0.00 0.00 57.50 2.22 6B 0.00 12.10 93.80 0.00 0.80 6.20 0.00 0.00 0.00 12.90 0.50 7A 0.00 0.30 8.11 0.20 5.41 3.20 86.49 0.00 0.00 0.00 3.70 0.14 7B 0.00 0.90 10.71 0.00 7.50 89.29 0.00 0.00 0.00 8.40 0.32 8A 0.00 12.10 79.61 0.60 3.95 2.50 16.45 0.00 0.00 0.00 15.20 0.59 8B 0.00 7.70 57.89 0.10 0.75 5.50 41.35 0.00 0.00 0.00 13.30 0.51 9A 0.40 0.30 23.20 17.62 108.00 82.00 0.10 0.08 0.00 0.00 0.00 131.70 5.08 9B 0.00 4.10 8.25 36.00 72.43 9.60 19.32 0.00 0.00 0.00 49.70 1.92 10A 0.00 0.40 0.22 0.00 0.00 184.80 99.78 0.00 0.00 185.20 7.14 10B 0.00 0.10 0.74 0.00 13.50 99.26 0.00 0.00 0.00 13.60 0.52

117 Table 11.6-1. Continued. Najas Elodea Ludwigia Sample Ceratophyllum guadulapensis Potamogeton Percent canadensis L.C. peploides (HBK.) Polygonum spp. Other TOTAL Number demersum L. (Spreng.) nodosus Poir. age Rich Raven Magnus (creeping (coontail) (waterweed) (naiad) (smartweed) (pondweed) primrose willow) Mass %tage Mass %tage Mass %tage Mass %tage Mass %tage Mass %tage Mass %tage Mass %tage 11A 2.80 9.46 25.00 84.46 0.00 0.50 1.69 1.30 4.39 0.00 0.00 29.60 1.14 11B 0.30 0.67 42.90 96.19 0.00 0.10 0.22 1.30 2.91 0.00 0.00 44.60 1.72 12A 0.40 0.74 5.00 9.21 48.90 90.06 0.00 0.00 0.00 0.00 54.30 2.09 12B 0.00 38.70 42.11 53.20 57.89 0.00 0.00 0.00 0.00 91.90 3.54 13A 0.00 0.10 100.00 0.00 0.00 0.00 0.00 0.00 0.10 0.00 13B 0.00 0.00 0.00 6.80 100.00 0.00 0.00 0.00 6.80 0.26 14A 0.00 17.40 33.40 5.00 9.60 0.00 24.90 47.79 0.00 4.80 9.21 52.10 2.01 14B 0.00 58.10 88.70 4.60 7.02 2.80 4.27 0.00 0.00 0.00 65.50 2.52 15A 0.50 4.72 0.60 5.66 0.00 0.00 0.00 0.00 9.50 89.62 10.60 0.41 15B 0.10 0.24 4.70 11.44 36.30 88.32 0.00 0.00 0.00 0.00 41.10 1.58 16A 0.00 48.40 83.59 0.00 0.00 3.00 5.18 0.00 6.50 11.23 57.90 2.23 16B 0.10 0.12 76.10 92.69 5.90 7.19 0.00 0.00 0.00 0.00 82.10 3.16 17A 0.80 0.80 88.60 88.07 5.60 5.57 0.00 0.00 5.60 5.57 0.00 100.60 3.88 17B 0.00 0.40 6.15 0.00 6.10 93.85 0.00 0.00 0.00 6.50 0.25 18A 0.30 0.94 30.40 95.00 0.00 0.50 1.56 0.00 0.00 0.80 2.50 32.00 1.23 18B 0.10 1.02 4.10 41.84 0.00 5.60 57.14 0.00 0.00 0.00 9.80 0.38 19A 0.10 0.27 35.30 96.98 0.00 1.00 2.75 0.00 0.00 0.00 36.40 1.40 19B 0.70 18.42 2.60 68.42 0.00 0.50 13.16 0.00 0.00 0.00 3.80 0.15 20A 0.30 0.90 33.00 98.80 0.00 0.10 0.30 0.00 0.00 0.00 33.40 1.29 20B 0.00 5.80 69.05 0.00 2.60 30.95 0.00 0.00 0.00 8.40 0.32 Total 7.10 0.27 745.40 28.73 1487.40 57.32 86.10 3.32 233.20 8.99 5.60 0.22 30.00 1.16 2594.80 100.00

118 Part B

Restoration of Campus Lake at Southern Illinois University Carbondale: A Feasibility Study

Prepared by

Frank Wilhelm, Co-Principal Investigator Department of Zoology

Robert Neumann, Co-Principal Investigator Fisheries and Illinois Aquaculture Center

Ami Ruffing, Project Director Center for Environmental Health and Safety Southern Illinois University Carbondale, Illinois 62901

Submitted to

Illinois Environmental Protection Agency 1021 North Grand Avenue East P.O. Box 19276 Springfield, Illinois 62794-9276

October 31, 2003

119 1. INTRODUCTION

Campus Lake, a 16-hectare impoundment located on the campus of Southern Illinois University Carbondale (SIUC), was constructed in the 1880’s. The lake is a regional asset and provides multiple benefits including fishing, swimming, boating, wildlife watching, and hiking. Historically, the lake also served as an ice-supply. Campus Lake is also part of the Illinois Department of Natural Resources’ (ILDNR) Urban Fishing Program. The lake is an important educational resource for several university courses including fisheries management, limnology, biology, and surveying, among others. In the Phase-I diagnostic study, several factors were identified that are impairing the quality of Campus Lake. These include excess nutrient inputs, poor zooplankton community, erosion, unbalanced fish populations and lack of regular fish monitoring, and lack of handicap-access. This feasibility study was undertaken to develop a restoration plan to enhance the many benefits Campus Lake provides.

2. FACTORS IMPAIRING THE QUALITY OF CAMPUS LAKE

2.1. EXCESSIVE NUTRIENT INPUTS/ALGAE BLOOMS, BLUE GREENS

Nutrient inputs to Campus Lake were monitored during the 1997-1998 Phase I diagnostic study. Surface runoff and direct rainfall are the only sources of water to Campus Lake. Twenty-seven inflows were identified for storm events exceeding 2.54 cm. Runoff from the urbanized north half of the watershed (SIUC Campus) enters the lake via a number of storm drains. Of these, the drains to the lake south of the communications parking lot and from the horticulture pond contributed the majority of total suspended solids and nutrients (nitrogen [N] and phosphorus [P]) and are targeted for improvement. The predominance of blue-green algae in the phytoplankton community on all dates when samples were analyzed for algal composition suggests an overabundance of P. However, the epilimnetic TN:TP ratio was >10 (annual mean = 25.1) on all sampling dates, suggesting P limitation (Wetzel 2001). Smith (1984) observed dominance of blue-green algae in lakes at TN:TP ratios 29 and concluded that they predominate in lakes with high TN:TP ratios if concentrations of N and P are non-limiting. In such cases, phytoplankton would be limited by light availability, conditions which would favor buoyant blue-green algae. In Campus Lake, concentrations of both N (0.51 - 1.53 mg/L) and P (16 - 70 ug/L) were consistently high, suggesting that neither nutrient is limiting and both should be reduced to improve the water quality. Abatement strategies are planned to address both

120 nutrients.

2.2. POOR ZOOPLANKTON COMMUNITY

Zooplankton are a key component of a healthy lake ecosystem. Because they feed (graze) on algae, zooplankton can directly influence algal biomass and hence water clarity (Wetzel 2001). In general, algal biomass is inversely related to zooplankton size because large zooplankton can graze a wide range of phytoplankton sizes including large cells (Burns 1968, Reynolds 1984). Large zooplankton are also more efficient than small zooplankton at filtering water (Gliwicz 1990). Furthermore, large-bodied zooplankton have a lower size-specific metabolic rate than small-bodied species (Peters 1983). As a result, larger species can grow and reproduce better than small-bodied species at low food concentrations. To effectively control phytoplankton during the summer, large-bodied zooplankton must reach and maintain a high density early in spring and throughout the growing season (Gliwicz 1990). The Phase-I diagnostic study for Campus Lake indicated that the zooplankton community was primarily composed of small-bodied species, such as Ceriodaphnia, which are ineffective at reducing algal abundance during the summer. In numerous biomanipulation studies and experiments algal biomass, including filamentous blue-green species, was low when the density of large Daphnia was high (de Bernardi and Giussani 1978, Anderson et al. 1978, Lynch and Shapiro 1981). Thus, a high abundance of large-bodied zooplankton, especially Daphnia, is key to increased water clarity. One method to ensure a high abundance of large-bodied zooplankton is to reduce the density of planktivorous fish (Carpenter et al. 1985) which was considered as an alternative in the Campus Lake implementation plan described below.

2.3. BANK EROSION

Campus Lake is a site for the ILDNR Urban Fishing Program. Each spring the ILDNR sets a net to cordon off the north arm closest to the campus boat dock. This enclosed area is then stocked with fish for children to catch. As a result, the shoreline where the fishing occurs receives much foot traffic which has led to erosion along the bank, destabilizing its face and top. Currently wave action continues to undercut the face of the bank, especially in summer when the lake level is below pool elevation, while surface runoff erodes exposed soil around trees and roots. Combined, these erosional processes threaten the future survival of several mature pine trees along the water’s edge which are key features of the point, adjacent picnic area, and Frisbee golf course. Although the erosion is not thought to contribute significantly to lake

121 turbidity (see Phase I), it does degrade the quality of the lake as a whole because it impairs the water/land interface experienced by lake users. Moreover, sedimentation in littoral regions along the perimeter of the eroded shoreline may degrade fish spawning habitat.

2.4. UNBALANCED FISH POPULATIONS AND LACK OF LONG-TERM MONITORING

In May 1997, a fisheries survey was conducted using 3-phase alternating current boat electrofishing to determine fish community structure and population characteristics. The fish community consisted primarily of bluegill Lepomis macrochirus and largemouth bass Micropterus salmoides. Redear sunfish L. microlophus and crappie Pomoxis spp. were also sampled but were less common. Channel catfish Ictalurus punctatus have been stocked every year since 1996 as part of the Illinois Urban Fishing Program. Approximately 300 kg of channel catfish (individuals weighing approximately 0.5-1.5 kg) are stocked six times each year.

The results of the Phase-I fisheries survey indicated that the fish community was not balanced. A balanced fish community is one in which recruitment of predators and prey is consistent and adequate, growth rates of predators and prey are moderate to fast, and mortality is not excessive. Under balanced conditions, annual yields of harvestable-size fish are sustainable (Flickinger et al. 1999). Balanced fish populations are also characterized as having a variety of sizes available to anglers. In Campus Lake there is an overabundance of small (< 300 mm) largemouth bass and lack of large largemouth bass. This condition is common in small impoundments when recruitment and natural mortality are excessive. Overpopulation of small largemouth bass leads to slow growth rates, poor body condition, and undesirable size structure. Unbalanced fish populations could also be contributing to the low abundance of large zooplankton. Large zooplankton serve as effective grazers on phytoplankton and help to maintain desirable water quality.

Long-term monitoring of fish populations is necessary for effective fisheries management. Observation of trends in fish populations can be coupled with pro-active management strategies to maintain a quality fishery. Long-term monitoring is needed to understand the impacts of fish and lake management activities on the structure and dynamics of fish populations.

122 2.5. INADEQUATE RECREATIONAL ACCESS FOR THE DISABLED

Campus Lake is an important resource for a variety of recreational activities including hiking, boating, swimming, wildlife watching, and fishing. Southern Illinois University Carbondale maintains a boat dock and offers boat rentals. The dock is often crowded, and fishing is not allowed. The pathway around the lake is wheel-chair accessible, but there are several concrete piers along the perimeter of the lake that are degraded and inaccessible due to bank erosion. There are currently no fishing access areas that meet the Americans with Disabilities Act Guidelines for Buildings and Facilities (United States Access Board 2003).

3. OBJECTIVES OF THE CAMPUS LAKE IMPROVEMENT PLAN

The objectives for improving the quality of Campus Lake are outlined below. These objectives address the enhancement of water quality through watershed-level and in-lake approaches. We believe that addressing these objectives will substantially improve the quality of Campus Lake, and considerably enhance the many benefits the lake provides to the region.

1. Improve water quality for multiple lake uses

2. Reduce shoreline erosion

3. Maintain high-quality fishing opportunities

4. Improve recreational access

5. Enhance public knowledge about the Campus Lake ecosystem and improvement efforts

123 4. Alternatives for Addressing Factors Impairing Campus Lake

4.1. IMPROVE WATER QUALITY OF CAMPUS LAKE

4.1.a. Watershed-level approaches

Implementing watershed-level nutrient reductions is an integral part of sound lake restorations. Reducing nutrient inputs before they reach the lake is often more efficient than attempting to manage them once in the lake. The Phase-I study identified two sub-catchments, which contribute 44% and 40% of the total P and N budgets, respectively. By implementing in- watershed management actions, we estimate the input from these sources can be reduced by a minimum of 24% for each nutrient, assuming an efficiency of 70% for the horticulture pond and 30% for the constructed wetland north of Douglas Drive. Generally, the efficiency of constructed wetlands ranges between 30 to 50% (Luederitz et al. 2001, Healy and Cawley 2002). Our planned management action for the horticulture pond and outflow to Campus Lake involves multiple approaches including deepening of the pond, aeration, and the construction of a series of stepped constructed wetlands to allow additional settling of sediment and extraction of nutrients by plants. This multiple approach for the horticulture pond should result in high efficiency removal of sediment and associated nutrients.

i. Renovation of the horticulture pond area to reduce sediment and nutrient loading to Campus Lake. – The 0.8-hectare horticulture pond is located within the Campus Lake watershed approximately 200 m from the Campus Lake shoreline. The horticulture pond has accumulated excessive sediment over the past 30 years, and now has an average depth of approximately 0.75 m. The horticulture pond has excessive macrophyte growth and coontail and duckweed cover 100% of the pond’s surface area from spring through fall. The dense macrophyte coverage prevents substantial wind/water interaction resulting in a stagnant pond. It has a large surface area of anoxic sediments in contact with the water, which causes internal loading of P and contributes about 27% of the total P to Campus Lake. We considered two alternatives for this pond: dredging and alum treatment. The limitations of alum treatment are addressed in a later section; we feel that it is a short-term, unreliable solution to reduce excess P loading. We propose to dredge this pond to a mean depth of 1.5 m and maximum depth of 3 m. Further description of the dredging projects follows in “Proposed Implementation Strategies.”

124 Discharge from the horticulture pond flows through a culvert under a paved road and then through a severely-eroded, narrow-cut ditch before it enters Campus Lake. During storm events the velocity of the outflow is excessive, contributing to erosion and sedimentation in Campus Lake. Two alternatives to repairing the ditch and reducing the velocity of the water were considered: installation of rock check dams, and installation of pocket urban stormwater wetlands. Both of these structures are described in the Natural Resources Conservation Service document “Illinois Urban Manual” (2002). Rock check dams are, in general, considered to be temporary structures designed to trap sediment and reduce flow velocities, but are usually not considered as permanent installations. On the other hand, constructed wetlands serve to reduce flow velocity, trap sediment, and maximize nutrient removal through interaction of emergent and riparian wetland plants. We propose to install a series of five stepped sediment basins between the discharge point of the horticulture pond and Campus Lake to reduce erosion, sediment, and nutrient export to Campus Lake.

ii. Construction of a stormwater wetland. – Two discharge culverts entering Campus Lake along Douglas Drive were identified in Phase I as contributing the most ammonia N and total P concentrations of all the stormwater points discharging into Campus Lake. Immediately to the north of the culverts and road is a 0.75-hectare sparsely-wooded area. Two alternatives were considered to address the problem of nutrient loading at this site: filter strips and urban stormwater wetlands, as defined by the Natural Resources Conservation Service “Illinois Urban Manual” (2002). Filter strips are an area of vegetation designed to remove sediment and nutrients before runoff enters a body of water. Urban stormwater wetlands are more extensive constructs of shallow pools that utilize emergent and riparian plants to remove nutrients and reduce sediment input from stormwater events. Of the two alternatives, stormwater wetlands were considered more effective in reducing nutrient input and have the added benefit of creating wetland habitat. Filter strips are more useful in areas which experience sheet runoff. The location of the 0.75-hectare plot through which the inflow now occurs affords an opportunity to construct a stormwater wetland. iii. Storm-drain catchments. – At present, most of the storm drains flowing into Campus Lake include a poured-concrete catchment basin of approximately 1 m3. Ideally, they should be larger to increase their efficiency. However, increasing their size is currently

125 unrealistic because of prohibitive costs associated with removal and replacement of sidewalks and roads. Due to university budget and personnel constraints, current practices are unlikely to change in the immediate future. iv. Waterfowl management. – Campus Lake is home to a substantial number of resident waterfowl, which may be impacting the water quality of Campus Lake. Because waterfowl watching and feeding are popular activities, we do not propose any waterfowl reduction plans at this time. However, options for managing waterfowl will be considered over the next several years.

4.1.b. In-lake approaches i. Lake aeration. – The lack of oxygen in the hypolimnion can make large volumes of water unsuitable as habitat for aerobic organisms and shift chemical equilibria to favor reduced chemical species. Under anoxic conditions, iron-bound P is released leading to internal loading which can be a significant source of P in the nutrient budget of a water body (Nürnberg 1991, Wetzel 2001). Lake aeration is a pneumatic/mechanical/chemical process used to increase the dissolved oxygen concentration of water (Cooke et al. 1993) and has been used widely in the remediation of water bodies. Benefits include raising the oxygen content of the water without destratifying the water body, providing greater habitat for fish species, and reducing internal loading of P, if controlled by the iron complex. Lake aeration can be used to destratify the water mass to mix it entirely and increase the oxygen concentration through diffusion at the air/water surface and to aerate without destratification. The latter is generally employed in deep lakes that provide cold-water habitat for fish species which would be lost if the temperature increased above the species’ tolerance threshold. Given the shallow nature of Campus Lake, its high temperature (water temperature during July and August is 24-28/C), and the ability of occasional strong storm events to mix the water column during summer, it is not considered necessary to retain a stratified water column.

Reducing the anoxia in Campus Lake would provide the benefits outlined above, the most important of which would be to avoid the internal loading of P from the sediments. Aerating the water column, but keeping the bottom waters below 3 mgL-1, would provide the additional benefit of a deep water oxygen refuge for large zooplankton (Shapiro 1990, Wright and Shapiro 1990). For example, Wright and Shapiro (1990)

126 found that the mid-summer loss of large-bodied Daphnia was correlated with the decline in refuge thickness (0 to 3 mgL-1 range ) in three lakes. Thus, aerating Campus Lake would be consistent with the Phase II implementation objectives.

Aeration devices and processes range from the injection of molecular oxygen and air into the water via diffusers, coarse bubble diffusers, soaker hoses, airlift systems, or diffusing jets (Johnson 1984, Prepas et al. 1990, Cook et al. 1993, DeMoyer et al. 2001). Pastorok et al. (1981) review aeration techniques and methods. Destratification and mixing of the entire water mass can be achieved through large airlift systems in which air is pumped to the bottom of the lake and released as bubbles. As the bubbles rise to the surface, they entrain water and establish vertical mixing of the entire water mass (DeMoyer et al. 2001, Beduhn 1995). Oxygen diffusion across the bubbles and the air-water interface at the lake surface increase the oxygen content of the water. Large diameter (2-5 m) propellers have also been used to physically mix water in lakes. Again, the principle of increasing the oxygen concentration is the same as outlined above. DeMoyer et al. (2001) recently studied the efficiency of three types of diffusers (coarse bubble, membrane diffuser and soaker hose), concluding that membrane diffusers delivered good oxygen transfer due to the small bubbles generated and also provided high capacity airflow. Consultations with R. Burke (Aquatic Biologists Inc., Fond du Lac, Wisconsin) regarding aeration devices appropriate for Campus Lake indicated that a diffuser system connected by sinking hose to shore-stationed piston pumps would provide sufficient aeration to mix the entire water column and supply oxygen at a rate to prevent anoxic conditions in the bottom waters. Shore based air pumps which deliver air to a diffuser bed are also among the most inexpensive types of aerators to install and maintain (R. Burke, personal communication).

Thomas et al. (1995) did not report any negative effects of aeration on the abundance of large zooplankton (Cladocerans and Copepods) in Newman Lake, Washington. However, the density of soft-bodied rotifers decreased after aeration, likely due to a water movement disturbance effect. Because rotifers do not graze on large filamentous blue-green algae, any decline in their density in Campus Lake should not detract from the benefits of aeration. Field and Prepas (1997) also reported higher abundances of crustacean zooplankton in the basin of Amisk Lake in which they injected liquid oxygen into the hypolimnion. The localized nature of the proposed diffusers should not negatively influence the density of large crustacean zooplankton in Campus

127 Lake. ii. Biomanipulation. – Fish play an important role in ecosystem balance, as they have direct effects on their prey, which indirectly affects the biological, physical, and chemical components of lake ecosystems (Hayes et al. 1999). Desirable zooplankton size structure and abundance have been associated with balanced fish populations. For example, Mills and Schiavone (1982) showed that in New York lakes, zooplankton size structure was low (zooplankton dominated by individuals < 1 mm) in a small lake containing high-density fish populations, while zooplankton size structure (zooplankton dominated by individuals > 1 mm) was high in a lake with a more balanced fish community. Large Daphnia abundance served as an index to fishing quality in Michigan trout lakes (Galbraith 1975).

The Phase-I diagnostic study indicated that excess nutrient inputs, bank erosion, and lack of large herbivorous zooplankton were contributing factors leading to poor water quality in Campus Lake. Large Daphnia species were absent in zooplankton samples and only D. ambigua and Ceriodaphnia reticulata, two of the three smallest species of Daphnia, were collected. These smaller species are less efficient at controlling algae than larger species (Reynolds 1994), which may lead to reduced grazing on algae, increased turbidity, and frequent algal blooms.

Fish may be indirectly affecting the water quality in Campus Lake through reduction of large herbivorous zooplankton, although the magnitude of their impacts relative to other biological and physical processes affecting water quality is unclear. Manipulation of fish populations has led to direct improvements in size structure and abundance of zooplankton, leading to improved water quality in a variety of systems (Drenner and Hambright 1999). In Campus Lake, pathways of fish predation on zooplankton are numerous and complex as zooplankton is a primary food source for a variety of species and life stages of fish. Zooplankton is an important food source for both young and adult bluegill (Baumann and Kitchell 1974; Mittelbach 1981; Harris et al. 1999), and planktivory by bluegill has been shown to be a function of season (Gerking 1962; Keast and Welsh 1968; Keast 1978), fish size (Engel 1988), and habitat (Baumann and Kitchell 1974). Age-0 largemouth bass are also zooplanktivorous, and shift to piscivory as they grow (Heidinger 1975).

128 The use of biomanipulation alone as a lake management tool to restructure the zooplankton community and improve water quality in Campus Lake is uncertain. Direct reduction in nutrient inputs, in combination with restoring balance in the fish populations, may hold the most promise for improving the quality of Campus Lake for maximum benefits. Restructuring the fish community alone may show no direct improvements in water quality if other factors control zooplankton size structure and abundance. For example, during the Phase-I study, large quantities of filamentous blue-green algae were observed in Campus Lake during summer coincident with reduced Daphnia abundance. Large cladocerans are at a disadvantage relative to small bodied Daphnia during blooms of filamentous blue-green algae because the algae clog the filtering apparatus leading to excessive filter clearing and rejection of food particles (see Gliwicz 1990, Gliwicz and Lampert 1990). This inefficient feeding reduces growth and reproductive rates, resulting in summer declines of large zooplankton, regardless of the structure of the fish community. However, Gliwicz (1990) indicates that filamentous blue-green algae in eutrophic lakes can be suppressed by ensuring a high density of large Daphnia at the onset of the growing season. In numerous biomanipulation studies and experiments, algal biomass, including filamentous blue-green species, was low when the density of Daphnia was high (de Bernardi and Giussani 1978, Anderson et al. 1978, Lynch and Shapiro 1981). iii. Chemical treatment. – Alum treatment (aluminum sulfate) has been used to reduce the P content in a number of lakes (Welch et al. 1988). Generally, such treatments have been successful in reducing the P content of the water. However, in some cases, alum treatment has failed. These failures have been attributed to storm events which disturbed newly settled flocs, concentrating them in small parts of the lake, thus rendering the application ineffective. Alum treatment is not permanent and requires re- application after a number of years. This is especially true if it is the only treatment undertaken. Alum treatment can be effective if combined with other management actions in the watershed. Alum involves the direct application of aluminum which is toxic and has complex reactions, not all of which are completely understood (Rosseland et al. 1990, Cooke et al. 1993). Because most of Campus Lake is relatively shallow and wind storms can cause significant mixing of the entire water column, coupled with the cost for treating the whole lake, the application of alum to Campus Lake or the horticulture pond is not recommended.

129 4.2. REDUCE SHORELINE EROSION

4.2.a. Vegetation establishment

One point on the lake (near the Engineering Building) is badly eroded, due primarily to heavy foot traffic and wave action. This area is the site of the ILDNR “Urban Fishing Program” and the “Saluki Kids Academy” for low-income children from grades 4 through 6. As discussed in Phase I, these programs establish opportunities for urban youth to participate in a fishing program. A large cove adjacent to the eroded point is separated from the main lake using a block net and is stocked with fish to provide angling opportunities. One unfortunate result of the program is erosion from heavy foot traffic. To reduce the erosion, we considered the consequences of eliminating or moving the fishing programs, or establishing better access through an extension of the present footpath and associated vegetative plantings. Eliminating the fishing programs is not a viable alternative. These programs provide educational and recreational opportunities for disadvantaged children and other youth. A better alternative is to improve the area with an extension of the asphalt footpath, in conjunction with vegetative plantings and riprap, to reduce erosion at the point.

4.2.b. Physical structures

We considered three physical structures for stabilizing the bank in this area described above: riprap, bulkhead, and gabions. Riprap is the least expensive option and requires the least maintenance. Bulkhead and gabion structures are more complex and expensive, more difficult to maintain, and less useful for the intended application; this area is heavily used by children and youth for fishing. Gabions are rectangular, rock-filled wire baskets that are most commonly used on stream banks to protect the edge from erosion and to divert flow away from eroding channel sections. Bulkheads are usually made of reinforced concrete and are similar to retaining walls. Both bulkheads and gabions would reduce the attraction and usefulness of the area. We propose to install riprap along approximately 90 m of shoreline, according to the specifications of the Natural Resource Conservation Service’s “Illinois Urban Manual” Code 61 for riprap.

4.3. MAINTAIN HIGH-QUALITY FISHING OPPORTUNITIES

Creating balanced fish populations can be accomplished using several techniques. In

130 small impoundments with simple fish communities, such as in Campus Lake, balanced fish populations can be achieved through predator management. Manipulating predator populations (e.g., largemouth bass) will have direct effects on prey fishes (e.g., bluegill). For example, in Campus Lake, the largemouth bass population was overpopulated and dominated by small individuals. Reducing the number of small largemouth bass will help improve size structure and achieve balance.

4.3.a. Manual predator reduction

Reducing the density of small largemouth bass can be achieved through manual removal using traditional sampling gears (e.g., electrofishing). The advantage to using this technique is that the number and biomass removed are known and can be controlled to achieve the desired result. Eder (1984) found that a removal of 19 largemouth bass/hectare/year that were shorter than 300 mm successfully increased bass population size structure in a Missouri impoundment. Manual removal of 21-48% of largemouth bass 200-300 mm long resulted in population balance and increased growth and body condition of largemouth bass in a South Dakota impoundment (Neumann et al. 1994). Although manual removal has proved successful, a disadvantage to this technique is that long-term maintenance of the fish population is required to sustain quality. In the South Dakota impoundment studied by Neumann et al. (1994), discontinued manual removal of largemouth bass resulted in the population reverting back to a high density population of slow growing fish (D. Willis, personal communication, South Dakota State University).

4.3.b. Harvest regulations

Harvest regulations (e.g., length and creel limits) are used to maintain desirable fish population size structure and abundance. Slot length limits, designed to protect fish within a specified length range, have been applied to high-density, slow-growing largemouth bass populations to increase size structure (Noble and Jones 1999). Slot length limits are designed to allow harvest of small fish, protect fish within a slot range, and increase the abundance of larger fish, thereby retaining or creating a balanced population (Anderson 1976).

An advantage of harvest regulations over manual removal is reduced effort on the part of the biologist. However, a disadvantage to slot-length limit regulations is that anglers need to be relied upon to remove suitable numbers of largemouth bass, but not overharvest the fishery.

131 Thus, angler compliance with the regulation, and long-term monitoring of fish populations are necessary. Therefore, the success of a slot-length limit will depend on the willingness of anglers to harvest fish shorter than the protected slot. The number of small largemouth bass to be harvested depends on the density of small fish remaining in the system, and only surplus bass should be removed to prevent overharvest.

4.3.c. Chemical controls

The use of fish toxicants (e.g., rotenone) can be used to poison fish and renovate existing fish communities. However, the use of piscicides should be restricted to applications when other management options are not expected to produce adequate results. In Campus Lake, management techniques, other than renovation, are expected to result in desired outcomes.

4.3.d. Long-term fish population monitoring

By developing a long-term monitoring program, fisheries management can be conducted on a proactive basis. Because fish populations are dynamic, characteristics of fish populations are expected to fluctuate in response to environmental conditions. Southern Illinois University Carbondale is home to the Fisheries and Illinois Aquaculture Center, and faculty and students in the Center are well suited to conduct long-term fish population monitoring. There are several courses offered that utilize Campus Lake as a teaching resource. Long-term standardized monitoring of Campus Lake can be made a part of student class exercises on an annual basis, thus providing excellent educational opportunities while providing data to guide the management of the fish populations.

4.4. IMPROVE RECREATIONAL ACCESS

4.4.a. Renovate existing facilities

Development of handicap-access fishing piers requires several considerations. The facility should meet the Americans with Disabilities Act Guidelines for Buildings and Facilities (United States Access Board 2003). The pier should be wheel-chair accessible (including pathways and gangways), and allow ample space for fishing positions and to maneuver around

132 other users. Just as importantly, the pier should be positioned at a location along the shoreline that will provide high-quality fishing. The pier should be in a location to avoid crowded conditions away from other recreational users (i.e., boaters and swimmers) as well as be situated where fishing can occur in suitable water depths.

The existing boat dock is the only access point that can be potentially renovated to serve as a handicap-access fishing pier. However, the boat dock is often crowded and fishing is prohibited, as it is the location of boat rentals and frequent foot and boat traffic. The boat dock is also situated in shallow water near the back of a cove, which would not provide the best habitat for fishing.

4.4.b. Develop new access point

A new permanent handicap-accessible fishing pier could be constructed which would provide higher-quality fishing opportunities compared to the existing boat dock. This pier would be designed specifically for wheel-chair access, and include fishing stations (4-6 stations) suitable for anglers who are seated. This pier would make an ideal fishing location for all anglers, regardless of their physical status. An ideal location for the pier would be at the point being targeted for bank stabilization. The use of riprap to control erosion, along with wheel- chair accessible pathways and vegetative plantings, will redirect and reduce the impact of foot traffic in this area. The point area also has suitable depths for high-quality fishing, and would be located within the zone of the lake which receives channel catfish stocking as part of the Illinois Urban Fishing Program.

4.5. ENHANCE PUBLIC KNOWLEDGE ABOUT CAMPUS LAKE ECOSYSTEM AND IMPROVEMENT EFFORTS

Public education is important to the support and success of on-going lake management activities. The popular pathway around the perimeter of Campus Lake provides an excellent opportunity for public education about the Campus Lake ecosystem and lake management topics in general. One practical way to enhance public education is to install a series of well- designed interpretive displays at various stations along the pathway. These displays, with illustrations, maps and easy-to-read text, can be used to explain the benefits of the lake

133 improvement activities, discuss general information about biological, chemical, and physical processes in Campus Lake and its watershed, and promote the Illinois Environmental Protection Agency’s Clean Lakes Program.

5. PROPOSED IMPLEMENTATION STRATEGIES

5.1. EROSION CONTROL AND BANK STABILIZATION

We propose to install approximately 90 m of riprap along the bank on the eroded point to stabilize the bank. This installation will be done according to NRCS Illinois Urban Manual 61, Loose Rock Riprap. Bio-rolls planted with appropriate vegetation will be installed adjacent to the riprap areas and at other areas where shoreline erosion needs to be controlled. We will also extend the asphalt footpath into and around this area along the top of the bank next to the riprap, and combine this work with vegetative planting to redirect and reduce foot traffic. These activities will complement the installation of the handicap-accessible fishing pier discussed below.

5.2. RENOVATION OF THE HORTICULTURE POND

We propose to deepen the horticulture pond by draining the pond and dredging it. Currently the average depth is 0.75 m. We would remove approximately 6 200 m3 of accumulated sediment from this 0.75-hectare pond, resulting in an average depth of 1.5 m and a maximum depth of 3 m. The removal of sediment will reduce the surface area of anoxic sediment in contact with the water, and thus reduce internal loading of P to overlying water that drains into Campus Lake. Dredging the pond will also reduce the abundance of submerged macrophytes. At present, the macrophytes choke the pond and prevent wind/water interactions, resulting in a stagnant pond and a high abundance of duckweed. Preventing the growth of duckweed and limiting macrophyte growth will also avoid the release of nutrients stored in plant tissue when the plants decay each fall. Dredged material will be removed by a track hoe, loaded into trucks, and transported approximately 1.2 km to an area currently used for storage of mulch piles and yard waste. The dredged material will be bermed and seeded with a mixture of annual and perennial grasses to stabilize the surface and prevent erosion. We plan to use the dredged material in other construction projects on campus. We also propose to install an aeration system to mix the entire pond and keep the water well-oxygenated, thus reducing

134 internal loading of nutrients, primarily P. The aeration system maintenance will be minimal, involving yearly inspection and maintenance of the pump. Specifications for the size and design of the aeration system were provided to us by the manufacturer (R. Burke, Aquatic Biologists, Inc.), and consist of a ¼ HP vane pump with two diffusers and a cabinet with a fan.

5.3. CONSTRUCTION OF SEDIMENT BASINS

We propose to install a series of five small sediment catchment basins between the outflow of the horticulture pond and Campus Lake. The sediment basins will be designed to reduce sediment input into Campus Lake from the horticulture pond, to reduce erosion of the outlet from the horticulture pond, and to reduce outfall velocity from concentrated stormwater flows. The series of basins will be placed in the existing outfall V-cut channel which conveys flow from the horticulture pond to Campus Lake. The first basin will be placed approximately 8 m from the outfall of the horticulture pond, and the remaining four basins will be placed at approximately 30 m intervals. These basins will be designed and constructed according to criteria published by the NRCS “Illinois Urban Manual” Code 800, “Urban Stormwater Wetlands”, Design #4, “Pocket Wetlands.” Basins will be approximately 6 m wide and 6.5 m long. Design criteria states that these pools should be cleaned out every 10 years. These sediment basins will be seeded with a mixture of arrowhead, pickerel weed, water plantain, sedges, grasses, rush, and iris, available commercially from Aquatic Biologists, Inc.

5.4. CONSTRUCTION OF STORMWATER WETLAND

A stormwater wetland will be constructed at the north side of Douglas Drive to intercept overland flow of runoff that originates on rooftops and parking lots, flowing into Campus Lake from two major discharge points. Wetland construction will create growing conditions for emergent plants to utilize dissolved nutrients, and will slow runoff velocities thus reducing sediment load in the lake. This larger basin will also be constructed according to the NRCS “Urban Manual” Code 800 Design #4, “Pocket Wetland.” This basin will be 30 m long and vary from 9 to 15 m wide, providing a surface area to watershed ratio of approximately 1%. A diverse wetland plant community will be established by planting a seed mix of arrowhead, pickerel weed, water plantain, sedges, grasses, rush, and iris, available commercially from Aquatic Biologists, Inc. Volunteer students from campus environmental organizations will provide labor for the plantings. Design criteria states that this wetland should also be cleaned out every 10 years.

135 5.5. LAKE AERATION

We propose to install an aeration system in Campus Lake to prevent anoxic conditions in the hypolimnion. Lake aeration equipment and installation services will be provided by Aquatic Biologists, Inc. Four rocking piston pumps connected by hoses to four MIX Air TB-16 diffusers will be placed in the deep basin of Campus Lake. The aerator system will “turn over” the lake volume approximately every 3 to 4 days (personal communication, R. Burke, Aquatic Biologists, Inc.). The effectiveness of the diffusers will be assessed through the regular monitoring program for water quality parameters and zooplankton. Maintenance for the system should be minimal, and consist largely of yearly inspections of the pump and aeration lines.

5.6. ZOOPLANKTON MONITORING

Pelagic zooplankton will be collected once a month for the duration of the study from the deepest site in Campus Lake. Only one site will be sampled for two reasons. First, results of the Phase I study showed that there were no differences among the three sites sampled in Campus Lake with regard to chemical parameters such as Chlorophyll a, suggesting that the lake can be adequately characterized from a representative site. Secondly, the identification, enumeration and size measurement of the zooplankton will be labor intensive and time consuming and one site will more than adequately occupy a graduate student.

A Wisconsin-style plankton net (deBernardi 1984) with 64 :m-mesh and 20 cm diameter mouth will be hauled vertically from just above the lake bottom to the surface to collect triplicate samples of pelagic zooplankton. Contents of the net will be preserved in 4% buffered formalin. Zooplankton will be identified to lowest possible taxonomic level with the aid of an inverted compound microscope. Subsamples of zooplankton will be used to estimate density of all identifiable plankton and the size distribution of the dominant taxon present on each sampling date. This will allow us to examine the impact of Phase II implementations on the size distribution of zooplankton in Campus Lake. The gut contents of the dominant zooplankton taxon may also be examined (depending on ability to identify algal species from the food tract of zooplankton) to estimate the grazing pressure on the different algal species. Past studies have used a variety of techniques ranging from direct observation of algal parts to pigment analysis (e.g., Dini et al. 1995, Vinebrooke and Leavitt 1999). If the algal species can be identified from gut contents, additional zooplankton samples will be collected and preserved with Lugol’s iodine (APHA 1995). This will allow us to track the balance between Daphnia density, algal biomass

136 and the structure of the fish community. Results will be analyzed using standard statistical tests.

5.7. LONG-TERM FISH POPULATION MONITORING

We will conduct fish population monitoring during the spring and fall of each year during the Phase-2 implementation. Results of the fisheries surveys will provide data to guide management actions to sustain a quality fishery and also to determine the impacts of lake management strategies on fish populations. Annual surveys will include species composition, fish population size structure, abundance, growth rates, and body condition. Fishes will be sampled using nighttime boat electrofishing with pulsed direct current and with modified fyke nets. All fish will be identified to species and measured to the nearest mm. A sample of five fish of each species per cm length group will be weighed to the nearest g, and sacrificed for determination of age and growth. Catch-per-unit-effort will be used as an index to relative abundance, and will be calculated as the number captured per hour of electrofishing or the number captured per night for modified fyke nets. Length-frequency histograms will be constructed, and size structure will be indexed using PSD [PSD = (number of fish $ quality length/number of fish $ stock length)x100] and relative stock density of preferred-length fish [RSD-P = number of fish $ preferred length/number of fish $ stock length)x100]. Fish will be aged using otoliths, and back-calculated length at age will be determined using the Fraser-Lee method. Age structures will be determined using age-length keys. Body condition will be quantified using the Wr index. Relative weight is calculated as: Wr=(W/Ws)*100; where, W is the measured weight of a fish and Ws is the standard weight calculated from a species-specific Ws equation.

5.8. INSTALL HANDICAP ACCESSIBLE FISHING PIER

A handicap-accessible fishing pier will be constructed during the second year of the implementation. The fishing pier will be designed to have 4-6 fishing stations, and will be constructed to meet ADA specifications.

5.9. WATER QUALITY MONITORING

Water quality will be monitored as specified in Appendix B of the Illinois Clean Lakes Program Application Guide. Samples will be taken once per month between September and

137 April and twice per month between May and August. Analyses will be completed at the EPA water analysis laboratory in Springfield, Illinois.

5.10. ENHANCE PUBLIC EDUCATION

A series of interpretive signs will be installed at 7 to 8 stations along the pathway that circles Campus Lake. These signs will serve the purpose of educating the public about lake ecosystems and lake management activities. Signs will focus on content areas such as the function of watersheds, soil erosion, constructed wetlands, lake aeration, eutrophication, lake ecosystems, etc. Appropriate credits to the IL EPA will be provided on each sign. Signs will consist of aluminum post and frame with high-quality text and graphics on durable outdoor pressure laminate suitable for long-term outdoor use. Cost estimates for sign frames and pressure-laminate printing were obtained from BEST-EX, Inc. of Baraboo, Wisconsin and Envirosigns of North Canton, Ohio.

138 6. PHASE-II WATER QUALITY MONITORING

Water-quality parameters will be monitored in accordance with ILEPA specifications set out in Appendix B of the Illinois Clean Lakes Program Financial Assistance Application Package. Briefly, water samples for the analysis of water chemistry parameters and analysis of phytoplankton will be collected as detailed below. Analysis of chemical parameters and phytoplankton specified in Appendix B will be provided by the ILEPA water analysis laboratory in Springfield, Illinois. Sampling will be undertaken at the deepest site in Campus Lake, as it was found to adequately characterize the water column during the Phase I study. The surface area of aquatic macrophytes between the 0 and 10-m depth contour will be measured.

Table 6.1. Detailed Phase II water quality monitoring program for Campus Lake. Parameter Sampling frequency Depth of sample Total Phosphorus M, 2M T, B Dissolved Phosphorus M, 2M T, B Ammonia-N M, 2M T, B Nitrite+Nitrate- Nitrogen M, 2M T, B Kjeldahl-Nitrogen M, 2M T, B Total suspended solids M, 2M T, B Volatile suspended solids M, 2M T, B Turbidity M, 2M T, B pH M, 2M T, B Alkalinity M, 2M T, B Conductivity M, 2M T, B, T-B 1m Chlorophyll a, b, c M, 2M Integrated 2 X SD Phytoplankton M, 2M Integrated 2 X SD Transparency – Secchi disc M, 2M 1 Dissolved oxygen – M, 2M T-B 1m temperature profiles Zooplankton See above Littoral Fish See above T-B vertical hauls M Monthly samples (September to April) 2M - Two samples per month (May – August) T - Top of water column (1 foot below surface) B - Bottom of water column (1 foot above sediment) T-B 1m – Top to bottom profile (at specified meter interval) SD Secchi depth

139 7. PROPOSED PHASE-II BUDGET (Year 1: May 2004-April 2005)

Budget for Year 1 (May 2004-April 2005) Category Salary Per. Mo. ILEPA Per. Mo. SIU A. Professional Staff Neumann 7 500.0 0 0.5 3 750 Wilhelm 4 989.0 0 0.5 2 495 Ruffing 4 100.0 0 0.5 2 050 Engineering Services 5 055.0 0 0.5 2 528 Subtotal 0 2 10 823 B. Other Personnel Graduate Research Assistantship 2 364.0 6 14 184 0 Graduate Research Assistantship 2 364.0 6 14 184 0 Undergraduate hourly 3 000 0 Subtotal 31 368 0 C. Subtotal Personnel 31 368 10 823 D. Fringe Benefits for Professional Staff 1. Retirement @ 12.37 0 1 339 2. Medical & Life @ $1133/Person Month 0 2 266 Subtotal 0 3 605 E. Subtotal Personnel and Benefits 31 368 14 428 F. Equipment Electrofishing unit 3 800 0 D.O. meter 1 500 Boat motor 500 5 000 Plankton nets 500 Computer 2 000 Horticulture pond aerator 1 625 Spectrophotometer 1 500 3 000 Subtotal 11 425 8 000 G. Travel Field travel 500 Subtotal 500 0 H. Commodities Boat gas and maintenance 800 0 Misc. field and lab supplies 1 000 Office supplies/postage 460 Trolling motor batteries 200 Subtotal 2 460 0 I. Contractual Horticulture Pond aerator installation 2 300 3 000 Horticulture Pond Excavation 40 000 20 000 Sludge analysis (Horticulture Pond) 650 Subtotal 42 950 23 000 J. Direct Costs 88 703 45 428 K. Indirect Costs (20% of MTDC) 15 456 Unrecovered ILEPA indirects (12%) 9 273 SIU contribution indirects match (32%) 11 977 Tuition waiver (2 MS students) 5 200 L. Total Project Costs 104 159 71 878

140 PROPOSED PHASE-II BUDGET (Year 2: May 2005-April 2006)

Budget for Year 2 (May 2005-April 2006) Category Salary Per. Mo. ILEPA Per. Mo. SIU A. Professional Staff Neumann 7 500.0 0 1 7 500 Wilhelm 4 989.0 0 1 4 989 Ruffing 4 100.0 0 1 4 100 Engineering Services 5 055.0 0 1 5 055 Subtotal 0 0 4 21 644 B. Other Personnel Graduate Research Assistantship 2460.0 6 14 760 0 Graduate Research Assistantship 2460.0 6 14 760 0 Undergraduate hourly 3 120 Subtotal 32 640 0 C. Subtotal Personnel 32 640 21 644 D. Fringe Benefits for Professional Staff 1. Retirement @ 12.37 0 2 677 2. Medical & Life @ $1133/Person Month 0 4 532 Subtotal 0 7 209 E. Subtotal Personnel and Benefits 32 640 28 853 F. Equipment Aerator (Campus Lake) 6 300 Subtotal 6 300 0 G. Travel Field travel 500 Travel to meetings (Wilhelm) 1 000 Travel to meetings (Neumann) 1 000 0 Subtotal 2 500 0 H. Commodities Boat gas and maintenance 800 0 Misc. field and lab supplies 1 000 Plants for constructed wetland 2 500 Herbicides 250 Materials for interpretive display 2 400 Publications 800 Office supplies/postage 460 Subtotal 8 210 0 I. Contractual Campus Lake Aerator Installation 800 5 000 Student Labor (plantings) 1 000 Labor for sign installations (PP) 1 200 Riprap labor and materials 5 000 5 000 C.L. point erosion control (plantings, fill) 12 500 12 500 Earthwork for basins, wetland 5 000 5 000 Handicap fishing pier and path 20 000 12 500 Subtotal 43 300 42 200 J. Direct Costs 92 950 71 053 K. Indirect Costs (20% of MTDC) 17 330 Unrecovered ILEPA indirects (12%) 10 398 SIU contribution indirects match (32%) 22 737 Tuition waiver (2 MS students) 5 200 L. Total Project Costs 110 280 109 388

141 PROPOSED PHASE-II BUDGET (Year 3: May 2006-April 2007)

Budget for Year 3 (May 2006-April 2007) Category Salary Per. Mo. ILEPA Per. Mo. SIU A. Professional Staff Neumann 7 500.0 0 0.5 3 750 Wilhelm 4 989.0 0 0.5 2 495 Ruffing 4 100.0 0 0.5 2 050 Engineering Services 5 055.0 0 0.5 2 528 Subtotal 0 0 2 10 823 B. Other Personnel Graduate Research Assistantship 1 280.0 3 3 840 9 11 520 Graduate Research Assistantship 1 280.0 3 3 840 9 11 520 Undergraduate hourly 3 400 Subtotal 11 080 23 040 C. Subtotal Personnel 11 080 33 863 D. Fringe Benefits for Professional Staff 1. Retirement @ 12.37 0 1 339 2. Medical & Life @ $1133/Person Month 0 2 266 Subtotal 0 3 605 E. Subtotal Personnel and Benefits 11 080 37 468 F. Equipment Subtotal 0 0 G. Travel Field travel 500 Travel to meetings (Wilhelm) 1 000 Travel to meetings (Neumann) 1 000 0 Subtotal 2 500 0 H. Commodities Boat gas and maintenance 800 0 Misc. field and lab supplies 1 000 Publications 1 000 Vegetation, erosion maintenance 3 000 Office supplies/postage 460 Subtotal 6 260 0 I. Contractual Subtotal 0 0 J. Direct Costs 19 840 37 468 K. Indirect Costs (20% of MTDC) 3 968 Unrecovered ILEPA indirects (12%) 2 381 SIU contribution indirects match (32%) 11 990 Tuition waiver (2 MS students) 5 200 L. Total Project Costs 23 808 57 039

142 PROPOSED PHASE-II BUDGET (Total Project: May 2004-April 2007)

Total Project Budget (May 2004-April 2007) Category Salary Per. Mo. ILEPA Per. Mo. SIU A. Professional Staff Neumann 7 500.0 0 2 15 000 Wilhelm 4 989.0 0 2 9 978 Ruffing 4 100.0 0 2 8 200 Engineering Services 5 055.0 0 2 10 110 Subtotal 0 0 8 43 288 B. Other Personnel Graduate Research Assistantship 32 784 11 520 Graduate Research Assistantship 32 784 11 520 Undergraduate hourly 9 520 0 Subtotal 75 088 23 040 C. Subtotal Personnel 75 088 66 328 D. Fringe Benefits for Professional Staff 1. Retirement @ 12.37 0 5 355 2. Medical & Life @ $1133/Person Month 0 9 064 Subtotal 0 14 419 E. Subtotal Personnel and Benefits 75 088 80 747 F. Equipment Electrofishing unit 3 800 0 D.O. meter 1 500 Boat motor 500 5 000 Plankton nets 500 Computer 2 000 Horticulture pond aerator 1 625 Spectrophotometer 1 500 3 000 Campus Lake aerator 6 300 Subtotal 17 725 8 000 G. Travel Field travel 1 500 Travel to meetings (Wilhelm) 2 000 Travel to meetings (Neumann) 2 000 0 Subtotal 5 500 0 H. Commodities Boat gas and maintenance 2 400 Misc. field and lab supplies 3 000 Office supplies/postage 1 380 Trolling motor batteries 200 Plants for constructed wetland 2 500 Herbicides 250 Materials for interpretive display 2 400 Publications 1 800 Vegetation, erosion maintenance 3 000 Subtotal 16 930 0 I. Contractual Horticulture Pond aerator installation 2 300 3 000 Hortuculture Pond Excavation 40 000 20 000 Sludge analysis (Hort. Pond) 650 Campus Lake aerator installation 800 5 000 Student Labor (plantings) 1 000 Labor for sign installations 1 200 Riprap labor and materials 5 000 5 000 C.L. point erosion control (plantings, fill, biorolls) 12 500 12 500 Earthwork for basins/wetland 5 000 5 000 Handicap fishing pier and path 20 000 12 500

143 Subtotal 86 250 65 200 J. Direct Costs 201 493 153 947

K. Indirect Costs (20% of MTDC) 36 754 Unrecovered ILEPA indirects (12%) 22 052 SIU contribution indirects match (32%) 46 703 Tuition waiver (2 MS students) 15 600 L. Total Project Costs 238 247 238 302 Total project cost 476 549

144 7.1 EXPLANATION OF BUDGET

Professional staff

A portion of faculty and staff time and engineering services will be dedicated to this project and will be provided by SIUC as match.

Other personnel

We are requesting funds to support two graduate assistantships (M.S. level). These students will be assisting in the collection and analysis of data related to limnological and fisheries aspects of this project. Funding for an undergraduate student worker is also requested. These students will receive career-oriented education and training directly related to lake management. Nine months of a graduate research assistantship will be provided as match by the Department of Zoology. Tuition will be provided as match by SIUC.

Equipment

Funding is requested to purchase necessary equipment items including an electrofishing unit, dissolved oxygen meter, plankton nets, computer, lake aerators, and a spectrophotometer. These items will complement a variety of equipment items owned by SIUC to be used on the project. A boat motor and most costs for the spectrophotometer are being provided by SIUC.

Travel

A modest amount of field travel is being requested for project vehicle rental, maintenance, and fuel. Additional funds are requested to support investigator and student travel to regional or national lake management conferences to present findings.

Commodities

These funds are requested to support boat maintenance and boat fuel, miscellaneous field and laboratory supplies, office supplies and postage, trolling motor batteries, plants

145 for stormwater wetland and erosion control, herbicides, materials for interpretive display, and publications. Vegetation and erosion control maintenance will be matched by SIUC.

Contractual

Contractual services include installation of aerators in the horticultural pond and Campus Lake by Aquatic Biologists, Inc. Horticulture pond excavation, sludge analysis, riprap material and installation, sediment basin and stormwater wetland construction, other erosion control measures, and construction of a handicap-access fishing pier will be undertaken by the SIUC Physical Plant Engineering Services. Substantial match for these activities will be provided by SIUC.

Indirect costs

Southern Illinois University will reduce the indirect cost rate for this project from 32% to 20%, and will contribute the remaining 12%. Indirect costs associated with direct costs provided by SIUC will be contributed.

8. SOURCES OF MATCHING FUNDS

Southern Illinois University Carbondale will provide matching funds through contributions of salary, matching labor, supplies, tuition waivers, one 9-month graduate student assistantship, costs of some equipment, and provision of volunteer labor for some portions of the projects. Additional match from SIUC was provided by the Office of Research and Development Administration and the Fisheries and Illinois Aquaculture Center.

9. RELATIONSHIP TO OTHER POLLUTION CONTROL PROGRAMS

There are no point-source discharges into Campus Lake, so there is no requirement for a National Pollution Discharge Elimination System (NPDES) permit. The dredging of the horticulture pond will require an Army Corps of Engineers Section 404 permit, and the application will be jointly reviewed by the ILEPA and the ILDNR Office of Water Resources. Areas adjacent to Campus Lake are included in the Spill Prevention Control and

146 Countermeasures Plan (SPCC) at present.

10. PUBLIC INPUT/PARTICIPATION SUMMARY

From the beginning of the Phase I application process, various campus constituencies have been consulted regarding their views of the needs and uses of the campus community in regard to Campus Lake. Some of these groups include the departments of Zoology, Fisheries and Illinois Aquaculture Center, Plant Biology, Microbiology, Civil Engineering, and Mechanical Engineering and Energy Processes, and Chemistry; the Student Recreation Center; Plant and Service Operations; the Center for Environmental Health and Safety; the Office of Intramural and Recreational Sports; the Aquatics Department; and various student organizations, including the Sailing Club, the Windsurfing Club, the Canoe and Kayak Club, the Fishing Club, and the Outdoor Adventure Club.

As part of the Phase-I study, SIUC sponsored a full-day program entitled “Discover Campus Lake” in October 1998. This informational gathering open to the public was co- sponsored by the ILEPA and the Greater Egypt Regional Planning and Development Commission. The program included a Campus Lake study overview, presentations, as well as social activities.

In October 2003, a public meeting was held in the Carbondale Civic Center. A press release announcing the meeting was issued by SIUC to regional media outlets. The purpose of this meeting was to provide the public with an overview of proposed lake restoration activities and to receive feedback. Positive feedback was received. A copy of the public presentation is attached.

11. OPERATION AND MAINTENANCE PLAN

Of all available alternatives, we selected those which were considered effective but entailed the least amount of ongoing, expensive maintenance. At the completion of Phase II, the two aeration systems will be inspected regularly and repaired as needed. The constructed wetland areas will be regularly monitored for sedimentation and stability; none of these areas should require sediment removal for about ten years. The handicap-accessible fishing pier, associated pathways, vegetated areas, and the interpretive kiosks will be inspected regularly

147 and repaired as needed.

12. ENVIRONMENTAL EVALUATION

Will the project displace people?

No. The restoration activities will be confined to the lake and adjacent watershed areas. Improvement of access will lead to more uses of the lake.

Will the project deface any existing residences or residential areas?

No. There are no residences other than the Thompson Point dormitories owned by Southern Illinois University (SIU).

Will the project likely lead to changes in the established land use patterns or an increase in development pressure?

There will be no changes in land-use patterns except for improved access. Because the project is located completely on SIU property, no changes in development are anticipated.

Will the project affect agricultural land?

No agricultural land will be affected.

Will the proposed project result in significant adverse effects on parkland, public lands, or scenic lands?

Only positive impacts are expected.

Will the project adversely affect land or structures of historic, architectural, archaeological, or cultural value?

No, the State Historical Society has not been contacted regarding this project. Its effects

148 on land use overall are negligible. No adverse effects are anticipated for any land of historic, archeological or cultural value. No structures will be affected by the project.

Will the project lead to a significant long-range increase in energy demand?

No, the project calls only for the installation of two relatively small pumps, anticipated to use less than 5.3 amps per pump.

Will the project adversely affect short- and long-term ambient air quality or noise levels?

No, the project will not result in long-term adverse changes in ambient air quality. Some very short-term increase in noise levels may be experienced during the four to five days anticipated for the dredging of Horticulture Pond, due to heavy equipment moving, but there are no residences or office buildings within about 300 m of the pond. No long- term noise level increases are anticipated.

If the project involves the use of in-lake chemical treatment, will it cause short- or long- term adverse impacts?

No use of chemicals is planned.

Is the proposed project in a floodplain?

No.

If the project involves physically modifying the lakeshore or its bed or its watershed, what steps will be taken to minimize and immediate and long-term adverse effects of such activities? Where will any dredged material be deposited, and what measures will be employed to minimize any significant adverse impacts of deposition?

The project involves dredging approximately 6,000 cubic meters of material from the horticulture pond. This material will be transported by truck less than 1.2 km to an area used at present for mulch piles and yard waste from the University. The material will be bermed and seeded with a mixture of annual and perennial grasses to minimize erosion

149 of the stockpile. We anticipate using this material as fill for various University construction projects in the future

Will the project have significant impacts on fish and wildlife, or on wetlands or any other wildlife habitat, especially those of endangered species?

The proposed project is expected to have positive impacts on aquatic resources. No adverse impacts on wildlife are expected. Habitat is expected to be enhanced by the creation of a small vegetated wetland.

Describe feasible alternatives?

Alternatives to separate components of the project were discussed in detail earlier in the feasibility study. To recap, we considered chemical treatment of the lake with alum, and rejected this as a short-term, possibly ineffective treatment compared to aeration. We considered construction of gabions, bulkheads, and larger concrete sediment basins, and deemed them to be too expensive and not suitable for intended uses, as well as requiring expensive maintenance.

Are there other measures not previously discussed which are necessary to mitigate adverse impacts resulting from the project?

There are no other measures necessary to mitigate adverse environmental impacts from this project. We expect only environmentally favorable, useful and aesthetically pleasing results from the project.

150 13. CAMPUS LAKE PHASE II IMPLEMENTATION SCHEDULE

2004 2005 2006 2007 Task M JJASOND JFMAMJJASOND JFMAMJJASOND JFMA Horticulture pond dredging x x x Horticulture pond aerator installation x x Construction of hort. pond sediment basins x x x x x x Construction of stormwater wetland x x x x x x Riprap installation at Campus Lake point x x x x x x Installation of path at Campus Lake point x x x x x x Grading and vegetation establishment x x x x x x Inspection of erosion control measures x x x x x Installation of Campus Lake aerator x x x Construction of handicap-access pier x x x Annual fisheries surveys x x x x x x Installation of interpretive displays x x x Water quality monitoring x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x Zooplankton monitoring x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x x Maintenance as needed x x x x x x x x x x x Preparation of Phase-II final report xxx xxxx

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157 APPENDICES

158 APPENDIX 1.

SAMPLING PROGRAM / PROCEDURES

159 A1. BATHYMETRIC MAP A bathymetric survey of Campus Lake was conducted by the Civil Engineering Survey Class under the direction of Dr. Roy Frank of the Civil Engineering Department, during May and June, 1997. From this survey the bathymetric map used throughout this report was produced.

A 1.1. GENERAL ON-LAKE SAMPLING PROCEDURES Sampling of water for chemical analysis and zooplankton abundance was performed twice monthly from April 1997 through October 1997, and monthly over the winter period, November 1997 through March 1998. This sampling was performed primarily by personnel from the SIUC Center for Environmental Health and Safety (CEH&S) and represented an extension of the regularly scheduled monthly sampling program in place under the IEPA Voluntary Lake Sampling Program (VLMP) which was begun in 1989. Sampling for water chemistry was also undertaken by the IEPA Marion office under the auspices of the Ambient Lake Monitoring Program (ALMP) for the period of April 1997 through October 1998. Water samples were analyzed at the IEPA Laboratory in Springfield for the parameters listed in Table A1.1, except for secchi depth, temperature and dissolved oxygen which were recorded at the time the samples were taken from the lake. General sampling procedures followed at each site are summarized below. Data from the analyses were entered in and are available from the USEPA STORET database at http://www. epa.gov/storet/. The general sampling procedures to collect water samples are outlined below. For detailed methods see the IEPA VLMP and water sample collection manuals. (1) Bottles for water samples were prepared by putting lake name, site and date on each bottle. For each site a separate bottle was taken to store the chlorophyll sample. (2) Sites were located using a depth finder and shore triangulation in conjunction with a detailed map of the lake. (3) Once at the site, the anchor was lowered slowly to avoid disturbing the bottom and then the boat was allowed to drift away from the anchor. (4) The Secchi depth was measured and recorded on a data sheet. (5) An integrated chlorophyll sample was collected by lowering the chlorophyll bottles to twice the Secchi depth. (6) A water sample for analysis was collected from approximately 0.3 m, [1 foot] below the lake surface. (7) A deep water sample for analysis was collected from 0.6 m [2 feet] above the bottom using a Kemmerer sampler. All depths and locations were recorded on the data sheet. (8) After calibration of the dissolved oxygen meter, dissolved oxygen and temperature profiles

160 were recorded at 0.3 m [1 foot] intervals from the surface to the lake bottom, with the last sample taken 0.6 m [2 feet] above the bottom. (9) These procedures were repeated at the other two sites in the lake. (10) On return to the laboratory, samples for chlorophyll analysis were filtered in semi-darkness through a glass fiber filter. The quantity filtered was dependent on the Secchi depth on each sampling date. All volumes filtered were recorded on the data sheets and filter wrappings. Samples and filters were stored in a refrigerator until shipment to the IEPA Laboratory in Springfield which occurred within 24 h of sampling.

Table A 1.1. Parameters analyzed for water samples collected from Campus Lake, Jackson County, IL. Constituent Unit Total Suspended Solids mg/L Volatile Suspended Solids mg/L Total Phosphorus mg/L Dissolved Phosphorus mg/L Nitrate + Nitrite Nitrogen mg/L Ammonia Nitrogen mg/L Total Kjeldahl Nitrogen mg/L Phenolphthalein Alkalinity mg/L Total Alkalinity mg/L Chlorophyll-A corr :g/L Chlorophyll-A unco :g/L Chlorophyll-B :g/L Chlorophyll-C :g/L Pheophytin-A :g/L Chemical Oxygen Demand mg/L Dissolved Oxygen mg/L Temperature /C Turbidity NTU* Secchi Disk Transparency inch pH Conductivity :mho/cm

*NTU: nephelometric turbidity units

161 A 1.2. STORM EVENT SAMPLING

A subset of the parameters analyzed for the lake water samples was also analyzed for water samples collected from runoff generated by storms (Table A1.2.). This sampling and analyses were completed to calculate the water and nutrient budget for the lake. Storm water runoff was initially collected after precipitation events of 0.5 inch. This was later modified to storm events exceeding 1.0 inch which produced sufficient measureable runoff. Eight storm events on the following dates: 5/3/97, 5/31/97, 6/14/97, 6/17/97, 8/19/97, 10/24/97, 2/17/98, 3/20/98 were sampled during the study. For each storm, 27 discharge points around the lake were sampled (Figure 9.1-1). However, some discharge points on the north side of the lake that were minor runoff inputs (e.g. low flow and concentrations) compared to other nearby runoff channels were omitted in later storm sampling to reduce cost associated with sample analysis. Water samples of sufficient quantity to meet the requirements for laboratory analyses were obtained where storm drains or intermittent stream channel in the forest entered the lake. All runoff samples were kept cold with ice and transported to the IEPA office in Marion within 24 hours of being collected from where they were transported to the IEPA laboratory in Springfield, IL, for analysis.

Table A 1.2. Parameters and constituents analyzed for storm water runoff entering Campus Lake. Constituent Unit Total Suspended Solids mg/L Volatile Suspended Solids mg/L Total Phosphorus mg/L Nitrate + Nitrite Nitrogen mg/L Ammonia Nitrogen mg/L Total Kjeldahl Nitrogen mg/L Turbidity NTU* *NTU: nephelometric turbidity units

162 A 1.3. SEDIMENT CORE SAMPLE COLLECTION AND ANALYSIS

Sediment core samples were taken to determine sediment depth and characteristics in all regions of the lake. A core sampler, constructed by Gerald Fink of the Mechanical Engineering and Energy Processes Department, SIUC, was used to obtain samples. It was made from 304 stainless steel tubing according to the configuration and dimensions given in Figure A 1.3-1 which is similar to the sampler used by Dreher et al. 1977. The 34 sample locations in Campus Lake are shown in Figure A 1.3-2.

Hammer 15.3 2.8 1.3 5.2 5.9

94.2 83.5 92.2

Figure A 1.3-1. Sediment Core Sampler Configuration and Dimensions

Thirty-three sediment core samples were taken from the bottom of Campus Lake in July 1998. Sites, 6, 11, 23, 33 were re-sampled in duplicate in December 1998 to obtain sediment samples for analysis (see below). Additional duplicate samples (#35) for analysis were taken at the deepest location in June 1999. Samples were obtained with the corer, and extruded. For each sample the total sediment depth retained in the corer was recorded. Additionally, the sediment accumulation since the lake was dredged in 1957 was measured. The black sediment accumulated during filling was visually distinguished from the clay hardpan of the lake basin. This depth was recorded as sediment thickness (Table A1.3-1). For the cores to be analyzed for metals and sediment quality, each was sectioned into 5.1 cm (2") sections starting at the top until four sections were obtained (A, B, C, D) or until the surficial sediment core was consumed. Sections, were kept cold until shipping to the Illinois State Geological Survey (IGSS) Analysis Laboratory in Champaign, IL. Analysis at the IGSS followed standardized methods (see Dreher et al. 1977). Quality control data from X-ray fluorescence spectrometry analysis for major and minor elements as well as trace elements is included in Appendix 2.

163 Boat Dock

1000 FEET

Spillway (336.6’ ASL)

250 METERS 6 DAM

age is 336.6 feet above sea

500

16.6

14.6

Thompson Point Dorms

12.6

Note: Depths were originally measured as elevations above mean sea level. Lake st level.

13 2.6

N 0.6

20 10.6 8.6

6.6 22 4.6

Greek Row Dorms

’s

Map showing locations in Campus Lake, Jackson Co., IL. where sediment samples were collected for analysis (circled numbers).

’s

To President Pond

Contour intervals indicated by other numbers.

President Pond

Figure A1.3-2.

164 Table A1.3-1. Depth and location of Sediment cores from Campus Lake, Jackson Co., IL. Sediment Core length Water Distance A Distance B Site thickness (cm) depth (m) (m) (m) (cm) 1 6.35 17.78 2.13 15 --- 2 6.35 12.70 3.05 ------3 3.81 10.16 2.74 ------4 5.08 12.70 3.35 28 74 5 8.89 21.59 4.23 56 49 6 7.62 --- 3.96 79 27 7 5.08 10.16 2.44 18 54 8 8.89 12.70 3.35 39 32 9 2.54 ---- 3.05 49 21 10 6.98 12.24 4.57 42 128 11 8.30 13.97 4.57 82 88 12 6.35 16.51 4.23 106 64 13 3.81 10.16 3.35 44 140 14 2.54 12.06 3.96 97 89 15 6.35 12.24 3.66 136 44 16 5.72 11.43 3.05 27 91 17 3.18 11.43 3.35 58 57 18 3.08 11.43 1.83 101 17 19 6.35 13.97 2.44 29 83 20 8.89 19.05 2.74 57 56 21 6.35 12.70 2.74 86 27 22 7.62 19.05 1.83 20 49 23 15.24 24.13 2.13 35 32 24 6.35 15.24 1.83 49 17 25 4.44 22.86 2.44 31 85 26 2.54 17.15 2.74 56 64 27 7.62 15.24 1.83 90 31 28 3.81 12.70 3.05 24 66 29 7.62 15.24 3.66 42 48 30 3.81 13.97 2.13 67 20 31 7.62 19.05 2.13 20 59 32 5.08 13.79 2.44 36 43 33 22.86 26.67 2.74 58 22 35 Note: Distance A: the distance from the sampling location to the north, northeast or northwest of the lake shore. Distance B: the distance from the sampling location to the south, southeast or southwest of the lake shore.

165 A 1.4. ZOOPLANKTON AND BENTHOS COLLECTIONS

Water for the analysis of zooplankton was collected with a tube sampler. The bottom of the tube was lowered to precisely 0.5 m above the bottom. The depth was measured with a weighted tape. Once in the water, the top of the tube was plugged and the tube raised and allowed to empty into buckets in the bottom of the boat. Ten liters were strained through a plankton bucket with 61:m apertures. The zooplankton was fixed with a squirt of 95% ethanol and preserved in 5% formalin. One sample was taken from each station on each date with an Ekman dredge covering 225 cm2. The sediment was strained through a No. 40 brass sieve (425 :m apertures) and animals were picked out while they were still living. To count zooplankton, standard zooplankton enumeration techniques (see APHA 1998) and a dissecting and inverted microscope were employed.

A 1.5. MACROPHYTE SAMPLING

Quantitative estimates of distribution of the principal species of macrophytes were obtained using methods similar to those of Young (1981) and Morgan (1993), however, this study is not strictly comparable to those of Young (1981) and Monaghan (1983) because we sampled on 23 July 1997 whereas they sampled in the month of October during their respectve studies. Two 0.25 m2 quadrats at each of 20 locations were taken around the shore (Figure 11.6-1). The first quadrat had one edge at the shoreline and the second quadrat was 1 m from the lakeward edge of the first. The depth of water was measured in the center of the second quadrat. The width of the macrophyte beds was measured at each location. In the laboratory the species of macrophytes were separated and weighed separately, first as wet weight (after squeezing out excess water by hand), and then as dry weight (after air drying for several weeks).

A 1.6. PHYTOPLANKTON ENUMERATION METHODS (L. M. O'Flaherty)

Each sample was preserved by adding sufficient formalin to give a final concentration of 4% formalin by volume. Counts were made using a sedgwick-rafter (s-r) cell and performing a "strip count" (APHA, 1985). In preparing each s-r cell for counting, the sample bottle was inverted 7 times and a 1-mL aliquot of mixed sample removed using a pipette (hensen-stempel). Each s-r cell was allowed to lay undisturbed on the microscope stage for 20 min. A total of 4

166 strips were examined for each sample. Individuals of species normally occurring as single cells were counted as "one". Taxa occurring as coenobia, colonies, chains or filaments were counted as "one" in the strips when 10 or more cells were present. Individuals touching the top of the whipple field were counted while those touching the bottom were ignored. The No.mL-1 was C x 14.881 (APHA 1985). This means that if one individual was present in one of the four strip counts, it was present in a density of 14.881 mL-1 or 14 881 L-1. After completion of the s-r counts, 300 mL of sample were passed through a continuous flow centrifuge (Forest Mechanical Specialties) to prepare a 10-mL concentrate. A slide was prepared from this concentrate and the identification of algae seen in the s-r cells confirmed. Additional taxa seen in the aliquot from the concentrate were identified and included in the list of taxa for that lake. Efforts were made to identify organisms to the lowest possible taxon (genus, species or variety), but if this was not possible, the organism was listed as "Unknown. . ." or as sp. such as Trachelomonas sp. A portion of the concentrated sub-sample was placed in the Algal Section of the R M. Myers Herbarium (MWI), Western lllinois University, Macomb, IL. A letter sent from Dr. O’Flaherty to the IEPA and tables detailing species occurrence, size, volume, density and total biovolume on each sampling date are included in Appendix 3.

167 A 1.7. STATISTICAL METHODS

Data collected were compiled on a computer spreadsheet and analyzed with RS/Explore statistical software (BBN, 1988). Basic descriptive statistics (mean, median, standard deviation, minimum, maximum, and number of cases), correlation matrices, factor analysis, principal components analysis and analysis of variance (ANOVA) were computed to analyze trends in parameters spatially and temporally. Box plots were also constructed with RS/Explore to indicate the range among parameters at each site. The upper and lower lines of the box indicate the range of concentrations between the 25th quartile (Q1) and 75th quartile (Q3) for that site, and the median is represented by the center line within the box. Inter-quartile range (IQR) values show the data clustered around the median value within the range from Q1 to Q3. The whisker lines extend to the limits of the data set for each site. Outliers are plotted as points and are defined as concentrations more than 1.5 times above or below the IQR. One way analysis of variance (Zar 1996) was used to examine temporal (seasonal) and spatial (site) trends among the parameters. Site was used as the independent variable, while parameters measured were classified as the dependent or response values. The null hypothesis tested was that the response values belonged to the same populations. The F ratio indicates if variance among response values is greater among than within sites. The lower the P value (significance level), the less likely it is that the result would be obtained by chance. Hence, P values less than 0.05 indicate greater likelihood that there is an inherent relationship between the predictor variable and the response variables. For spatial (site trend) analysis of water samples, site (top and bottom of each site, inflow and outflow) was the predictor variable and measurements of chemical parameters were the response variables. For temporal (seasonal trend) analysis of water samples, month (in two month increments Jan\Feb, Mar\Apr, May\Jun, Jul\Aug, Sep\Oct, Nov\Dec ) was the predictor variable and measurements of chemical parameters were the response variables. To analyze storm water runoff the land use trend was studied, with site (27 total sampling locations) as the predictor variable and measurements of chemical parameters as the response variables.

168 APPENDIX 2.

SEDIMENT ANALYSIS QUALITY ASSURANCES

169 170 171 Table A2-3. Historic sediment quality parameters for Campus Lake, Jackson Co., IL. Data were obtained from the EPA STORET database. Date SITE 1 Value 26-Aug-97 NITROGEN KJELDAHL TOTAL BOTTOM DEP DRY WT MG/KG " 4200.00 12-Jun-81 NITROGEN KJELDAHL TOTAL BOTTOM DEP DRY WT MG/KG " 2640.00 12-Jun-81 NITROGEN KJELDAHL TOTAL BOTTOM DEP DRY WT MG/KG " 2630.00 18-May-81 NITROGEN KJELDAHL TOTAL BOTTOM DEP DRY WT MG/KG " 1790.00 18-May-81 NITROGEN KJELDAHL TOTAL BOTTOM DEP DRY WT MG/KG " 1320.00 26-Aug-97 PHOSPHORUS TOTAL BOTTOM DEPOSIT (MG/KG-P DRY WGT) 969.00 12-Jun-81 PHOSPHORUS TOTAL BOTTOM DEPOSIT (MG/KG-P DRY WGT) 508.00 12-Jun-81 PHOSPHORUS TOTAL BOTTOM DEPOSIT (MG/KG-P DRY WGT) 519.00 18-May-81 PHOSPHORUS TOTAL BOTTOM DEPOSIT (MG/KG-P DRY WGT) 561.00 18-May-81 PHOSPHORUS TOTAL BOTTOM DEPOSIT (MG/KG-P DRY WGT) 530.00 26-Aug-97 POTASSIUM IN BOTTOM DEPOSITS (MG/KG AS K DRY WGT) " 1200.00 26-Aug-97 ARSENIC IN BOTTOM DEPOSITS (MG/KG AS AS DRY WGT) " 21.00 12-Jun-81 ARSENIC IN BOTTOM DEPOSITS (MG/KG AS AS DRY WGT) " 32.00 12-Jun-81 ARSENIC IN BOTTOM DEPOSITS (MG/KG AS AS DRY WGT) " 32.00 18-May-81 ARSENIC IN BOTTOM DEPOSITS (MG/KG AS AS DRY WGT) " 11.00 18-May-81 ARSENIC IN BOTTOM DEPOSITS (MG/KG AS AS DRY WGT) " 12.00 26-Aug-97 BARIUM IN BOTTOM DEPOSITS (MG/KG AS BA DRY WGT) " 190.00 26-Aug-97 CADMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 1.00 12-Jun-81 CADMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 1.00 12-Jun-81 CADMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 1.50 18-May-81 CADMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 0.50 18-May-81 CADMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 0.50 26-Aug-97 CHROMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WT) 25.00 12-Jun-81 CHROMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WT) 21.00 12-Jun-81 CHROMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WT) 21.00 18-May-81 CHROMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WT) 22.00 18-May-81 CHROMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WT) 19.00 26-Aug-97 COPPER IN BOTTOM DEPOSITS (MG/KG AS CU DRY WGT) " 63.00 12-Jun-81 COPPER IN BOTTOM DEPOSITS (MG/KG AS CU DRY WGT) " 64.00 12-Jun-81 COPPER IN BOTTOM DEPOSITS (MG/KG AS CU DRY WGT) " 67.00 18-May-81 COPPER IN BOTTOM DEPOSITS (MG/KG AS CU DRY WGT) " 21.00 18-May-81 COPPER IN BOTTOM DEPOSITS (MG/KG AS CU DRY WGT) " 21.00 26-Aug-97 LEAD IN BOTTOM DEPOSITS (MG/KG AS PB DRY WGT) " 65.00 12-Jun-81 LEAD IN BOTTOM DEPOSITS (MG/KG AS PB DRY WGT) " 70.00 12-Jun-81 LEAD IN BOTTOM DEPOSITS (MG/KG AS PB DRY WGT) " 70.00 18-May-81 LEAD IN BOTTOM DEPOSITS (MG/KG AS PB DRY WGT) " 44.00 18-May-81 LEAD IN BOTTOM DEPOSITS (MG/KG AS PB DRY WGT) " 30.00 26-Aug-97 MANGANESE IN BOTTOM DEPOSITS (MG/KG AS MN DRY WGT)" 1300.00 12-Jun-81 MANGANESE IN BOTTOM DEPOSITS (MG/KG AS MN DRY WGT)" 1100.00 12-Jun-81 MANGANESE IN BOTTOM DEPOSITS (MG/KG AS MN DRY WGT)" 1200.00 18-May-81 MANGANESE IN BOTTOM DEPOSITS (MG/KG AS MN DRY WGT)" 1900.00 18-May-81 MANGANESE IN BOTTOM DEPOSITS (MG/KG AS MN DRY WGT)" 1300.00 26-Aug-97 NICKEL TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 21.00 26-Aug-97 SILVER IN BOTTOM DEPOSITS (MG/KG AS AG DRY WGT) " 1.00 26-Aug-97 ZINC IN BOTTOM DEPOSITS (MG/KG AS ZN DRY WGT) " 140.00 12-Jun-81 ZINC IN BOTTOM DEPOSITS (MG/KG AS ZN DRY WGT) " 110.00 12-Jun-81 ZINC IN BOTTOM DEPOSITS (MG/KG AS ZN DRY WGT) " 120.00 18-May-81 ZINC IN BOTTOM DEPOSITS (MG/KG AS ZN DRY WGT) " 100.00 18-May-81 ZINC IN BOTTOM DEPOSITS (MG/KG AS ZN DRY WGT) " 140.00 26-Aug-97 IRON IN BOTTOM DEPOSITS (MG/KG AS FE DRY WGT) " 29000.00 12-Jun-81 IRON IN BOTTOM DEPOSITS (MG/KG AS FE DRY WGT) " 28000.00 12-Jun-81 IRON IN BOTTOM DEPOSITS (MG/KG AS FE DRY WGT) " 29000.00 18-May-81 IRON IN BOTTOM DEPOSITS (MG/KG AS FE DRY WGT) " 33000.00 18-May-81 IRON IN BOTTOM DEPOSITS (MG/KG AS FE DRY WGT) " 29000.00 26-Aug-97 METOLACHLOR (DUAL) IN BOTTOM SEDIMENT DRYWT UG/KG " 25.00 26-Aug-97 CHLORDANE-CIS ISOMER BOTTOM DEPOS (UG/KG DRY SOL " 3.60 26-Aug-97 CHLORDANE-TRANS ISOMER BOTTOM DEPOS(UG/KG DRY SL) 2.00 26-Aug-97 BHC-ALPHA ISOMER BOTTOM DEPOS (UG/KG DRY SOL) 1.00 26-Aug-97 P P' DDT IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) 1.00 26-Aug-97 P P' DDT IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) 1.00 26-Aug-97 P P' DDT IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) 5.30 26-Aug-97 ALDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 1.00 26-Aug-97 GAMMA-BHC(LINDANE) SEDIMENTS DRY WGT UG/KG 1.00 12-Jun-81 CHLORDANE(TECH MIX&METABS) SEDIMENTS DRY WGT UG/KG 5.00 12-Jun-81 CHLORDANE(TECH MIX&METABS) SEDIMENTS DRY WGT UG/KG 5.00 18-May-81 CHLORDANE(TECH MIX&METABS) SEDIMENTS DRY WGT UG/KG 5.00 18-May-81 CHLORDANE(TECH MIX&METABS) SEDIMENTS DRY WGT UG/KG 5.00

172 12-Jun-81 DDT IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 10.00 12-Jun-81 DDT IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 10.00 18-May-81 DDT IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 10.00 18-May-81 DDT IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 10.00 26-Aug-97 DIELDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOL.) " 3.90 12-Jun-81 DIELDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOL.) " 1.00 12-Jun-81 DIELDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOL.) " 1.00 18-May-81 DIELDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOL.) " 1.00 18-May-81 DIELDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOL.) " 1.00 26-Aug-97 ENDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 3.00 26-Aug-97 HEPTACHLOR IN BOT. DEP. (UG/KILOGRAM DRY SOLIDS) " 1.40 26-Aug-97 HEPTACHLOR EPOXIDE IN BOT. DEP. (UG/KG DRY SOL.) " 1.00 12-Jun-81 HEPTACHLOR EPOXIDE IN BOT. DEP. (UG/KG DRY SOL.) " 1.00 12-Jun-81 HEPTACHLOR EPOXIDE IN BOT. DEP. (UG/KG DRY SOL.) " 1.00 18-May-81 HEPTACHLOR EPOXIDE IN BOT. DEP. (UG/KG DRY SOL.) " 1.00 18-May-81 HEPTACHLOR EPOXIDE IN BOT. DEP. (UG/KG DRY SOL.) " 1.00 26-Aug-97 METHOXYCHLOR IN BOTTOM DEPOSITS (UG/KG DRY SOL.) " 5.00 26-Aug-97 PCBS IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) " 180.00 12-Jun-81 PCBS IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) " 38.00 12-Jun-81 PCBS IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) " 28.00 18-May-81 PCBS IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) " 10.00 18-May-81 PCBS IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) " 10.00 26-Aug-97 ATRAZINE IN BOTTOM DEPOS (UG/KG DRY SOLIDS) " 50.00 26-Aug-97 HEXACHLOROBENZENE IN BOT DEPOS (UG/KG DRY SOLIDS) " 5.00 26-Aug-97 CARBON TOTAL ORGANIC (uv OXID.) DRY WT SEDIMENT% 0.66 26-Aug-97 CAPTAN DRY WEIGHT SEDIMENT UG/KG 10.00 26-Aug-97 SOLIDS TOTAL PERCENT OF WET SAMPLE 15.40 26-Aug-97 SOLIDS VOLATILE PERCENT OF TOTAL SOLIDS 11.50 26-Aug-97 MERCURY TOT. IN BOT. DEPOS. (MG/KG AS HG DRY WGT) 0.100 12-Jun-81 MERCURY TOT. IN BOT. DEPOS. (MG/KG AS HG DRY WGT) 0.090 12-Jun-81 MERCURY TOT. IN BOT. DEPOS. (MG/KG AS HG DRY WGT) 0.070 18-May-81 MERCURY TOT. IN BOT. DEPOS. (MG/KG AS HG DRY WGT) 0.060 18-May-81 MERCURY TOT. IN BOT. DEPOS. (MG/KG AS HG DRY WGT) 0.110 26-Aug-97 ALACHLOR (LASSO) BOTTOM DEPOSITS DRY WGT UG/KG 10.00 26-Aug-97 METRIBUZIN (SENCOR) SEDIMENT DRY WEIGHT UG/KG 10.00 26-Aug-97 TREFLAN(TRIFLURALIN) IN SEDIMENT DRY WEIGHT UG/KG" 10.00 26-Aug-97 PENOXALIN IN SEDIMENT (PROWL) DRY WEIGHT UG/KG" 10.00 26-Aug-97 BLADEX (CYANAZINE) IN SEDIMENT DRY WEIGHT MG/KG " 25.00

173 Table A2-4. Historic sediment quality parameters for Campus Lake, Jackson Co., IL. Data were obtained from the EPA STORET database. Date SITE 2 Value 12-Jun-81 NITROGEN KJELDAHL TOTAL BOTTOM DEP DRY WT MG/KG " 3340.00 12-Jun-81 NITROGEN KJELDAHL TOTAL BOTTOM DEP DRY WT MG/KG " 3320.00 12-Jun-81 PHOSPHORUS TOTAL BOTTOM DEPOSIT (MG/KG-P DRY WGT) 512.00 12-Jun-81 PHOSPHORUS TOTAL BOTTOM DEPOSIT (MG/KG-P DRY WGT) 593.00 12-Jun-81 ARSENIC IN BOTTOM DEPOSITS (MG/KG AS AS DRY WGT) " 34.00 12-Jun-81 ARSENIC IN BOTTOM DEPOSITS (MG/KG AS AS DRY WGT) " 30.00 12-Jun-81 CADMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 1.50 12-Jun-81 CADMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 1.50 12-Jun-81 CHROMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WT) 21.00 12-Jun-81 CHROMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WT) 25.00 12-Jun-81 COPPER IN BOTTOM DEPOSITS (MG/KG AS CU DRY WGT) " 89.00 12-Jun-81 COPPER IN BOTTOM DEPOSITS (MG/KG AS CU DRY WGT) " 88.00 12-Jun-81 LEAD IN BOTTOM DEPOSITS (MG/KG AS PB DRY WGT) " 90.00 12-Jun-81 LEAD IN BOTTOM DEPOSITS (MG/KG AS PB DRY WGT) " 90.00 12-Jun-81 MANGANESE IN BOTTOM DEPOSITS (MG/KG AS MN DRY WGT)" 1200.00 12-Jun-81 MANGANESE IN BOTTOM DEPOSITS (MG/KG AS MN DRY WGT)" 1200.00 12-Jun-81 ZINC IN BOTTOM DEPOSITS (MG/KG AS ZN DRY WGT) " 150.00 12-Jun-81 ZINC IN BOTTOM DEPOSITS (MG/KG AS ZN DRY WGT) " 130.00 12-Jun-81 IRON IN BOTTOM DEPOSITS (MG/KG AS FE DRY WGT) " 34000.00 12-Jun-81 IRON IN BOTTOM DEPOSITS (MG/KG AS FE DRY WGT) " 29000.00 12-Jun-81 CHLORDANE(TECH MIX&METABS) SEDIMENTS DRY WGT UG/KG 5.00 12-Jun-81 CHLORDANE(TECH MIX&METABS) SEDIMENTS DRY WGT UG/KG 5.00 12-Jun-81 DDT IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 10.00 12-Jun-81 DDT IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 10.00 12-Jun-81 DIELDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOL.) " 1.00 12-Jun-81 DIELDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOL.) " 1.00 12-Jun-81 HEPTACHLOR EPOXIDE IN BOT. DEP. (UG/KG DRY SOL.) " 1.00 12-Jun-81 HEPTACHLOR EPOXIDE IN BOT. DEP. (UG/KG DRY SOL.) " 1.00 12-Jun-81 PCBS IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) " 55.00 12-Jun-81 PCBS IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) " 62.00 12-Jun-81 MERCURY TOT. IN BOT. DEPOS. (MG/KG AS HG DRY WGT) 0.040 12-Jun-81 MERCURY TOT. IN BOT. DEPOS. (MG/KG AS HG DRY WGT) 0.140

174 Table A2-5. Historic sediment quality parameters for Campus Lake, Jackson Co., IL. Data were obtained from the EPA STORET database. Date SITE 3 Value 26-Aug-97 NITROGEN KJELDAHL TOTAL BOTTOM DEP DRY WT MG/KG " 4900.00 12-Jun-81 NITROGEN KJELDAHL TOTAL BOTTOM DEP DRY WT MG/KG " 3130.00 12-Jun-81 NITROGEN KJELDAHL TOTAL BOTTOM DEP DRY WT MG/KG " 2940.00 26-Aug-97 PHOSPHORUS TOTAL BOTTOM DEPOSIT (MG/KG-P DRY WGT) 619.00 12-Jun-81 PHOSPHORUS TOTAL BOTTOM DEPOSIT (MG/KG-P DRY WGT) 512.00 12-Jun-81 PHOSPHORUS TOTAL BOTTOM DEPOSIT (MG/KG-P DRY WGT) 494.00 26-Aug-97 POTASSIUM IN BOTTOM DEPOSITS (MG/KG AS K DRY WGT) " 1300.00 26-Aug-97 ARSENIC IN BOTTOM DEPOSITS (MG/KG AS AS DRY WGT) " 23.00 12-Jun-81 ARSENIC IN BOTTOM DEPOSITS (MG/KG AS AS DRY WGT) " 31.00 12-Jun-81 ARSENIC IN BOTTOM DEPOSITS (MG/KG AS AS DRY WGT) " 29.00 26-Aug-97 BARIUM IN BOTTOM DEPOSITS (MG/KG AS BA DRY WGT) " 190.00 26-Aug-97 CADMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 1.00 12-Jun-81 CADMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 1.50 12-Jun-81 CADMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 1.50 26-Aug-97 CHROMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WT) 24.00 12-Jun-81 CHROMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WT) 20.00 12-Jun-81 CHROMIUM TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WT) 25.00 26-Aug-97 COPPER IN BOTTOM DEPOSITS (MG/KG AS CU DRY WGT) " 62.00 12-Jun-81 COPPER IN BOTTOM DEPOSITS (MG/KG AS CU DRY WGT) " 73.00 12-Jun-81 COPPER IN BOTTOM DEPOSITS (MG/KG AS CU DRY WGT) " 70.00 26-Aug-97 LEAD IN BOTTOM DEPOSITS (MG/KG AS PB DRY WGT) " 66.00 12-Jun-81 LEAD IN BOTTOM DEPOSITS (MG/KG AS PB DRY WGT) " 100.00 12-Jun-81 LEAD IN BOTTOM DEPOSITS (MG/KG AS PB DRY WGT) " 90.00 26-Aug-97 MANGANESE IN BOTTOM DEPOSITS (MG/KG AS MN DRY WGT)" 1300.00 12-Jun-81 MANGANESE IN BOTTOM DEPOSITS (MG/KG AS MN DRY WGT)" 1100.00 12-Jun-81 MANGANESE IN BOTTOM DEPOSITS (MG/KG AS MN DRY WGT)" 1200.00 26-Aug-97 NICKEL TOTAL IN BOTTOM DEPOSITS (MG/KG DRY WGT) 21.00 26-Aug-97 SILVER IN BOTTOM DEPOSITS (MG/KG AS AG DRY WGT) " 1.00 26-Aug-97 ZINC IN BOTTOM DEPOSITS (MG/KG AS ZN DRY WGT) " 140.00 12-Jun-81 ZINC IN BOTTOM DEPOSITS (MG/KG AS ZN DRY WGT) " 140.00 12-Jun-81 ZINC IN BOTTOM DEPOSITS (MG/KG AS ZN DRY WGT) " 130.00 26-Aug-97 IRON IN BOTTOM DEPOSITS (MG/KG AS FE DRY WGT) " 29000.00 12-Jun-81 IRON IN BOTTOM DEPOSITS (MG/KG AS FE DRY WGT) " 31000.00 12-Jun-81 IRON IN BOTTOM DEPOSITS (MG/KG AS FE DRY WGT) " 28000.00 26-Aug-97 METOLACHLOR (DUAL) IN BOTTOM SEDIMENT DRYWT UG/KG " 25.00 26-Aug-97 CHLORDANE-CIS ISOMER BOTTOM DEPOS (UG/KG DRY SOL " 2.00 26-Aug-97 CHLORDANE-TRANS ISOMER BOTTOM DEPOS(UG/KG DRY SL) 2.90 26-Aug-97 BHC-ALPHA ISOMER BOTTOM DEPOS (UG/KG DRY SOL) 1.00 26-Aug-97 P P' DDT IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) 1.00 26-Aug-97 P P' DDT IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) 1.00 26-Aug-97 P P' DDT IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) 8.50 26-Aug-97 ALDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 3.50 26-Aug-97 GAMMA-BHC(LINDANE) SEDIMENTS DRY WGT UG/KG 1.00 12-Jun-81 CHLORDANE(TECH MIX&METABS) SEDIMENTS DRY WGT UG/KG 5.00 12-Jun-81 CHLORDANE(TECH MIX&METABS) SEDIMENTS DRY WGT UG/KG 5.00 12-Jun-81 DDT IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 10.00 12-Jun-81 DDT IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 10.00 26-Aug-97 DIELDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOL.) " 3.60 12-Jun-81 DIELDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOL.) " 1.00 12-Jun-81 DIELDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOL.) " 1.00 26-Aug-97 ENDRIN IN BOTTOM DEPOS. (UG/KILOGRAM DRY SOLIDS) " 1.00 26-Aug-97 HEPTACHLOR IN BOT. DEP. (UG/KILOGRAM DRY SOLIDS) " 1.00 26-Aug-97 HEPTACHLOR EPOXIDE IN BOT. DEP. (UG/KG DRY SOL.) " 1.00 12-Jun-81 HEPTACHLOR EPOXIDE IN BOT. DEP. (UG/KG DRY SOL.) " 1.00 12-Jun-81 HEPTACHLOR EPOXIDE IN BOT. DEP. (UG/KG DRY SOL.) " 1.00 26-Aug-97 METHOXYCHLOR IN BOTTOM DEPOSITS (UG/KG DRY SOL.) " 13.00 26-Aug-97 PCBS IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) " 190.00 12-Jun-81 PCBS IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) " 45.00 12-Jun-81 PCBS IN BOTTOM DEPOSITS (UG/KG DRY SOLIDS) " 33.00 26-Aug-97 ATRAZINE IN BOTTOM DEPOS (UG/KG DRY SOLIDS) " 50.00 26-Aug-97 HEXACHLOROBENZENE IN BOT DEPOS (UG/KG DRY SOLIDS) " 5.00 26-Aug-97 CARBON TOTAL ORGANIC (uv OXID.) DRY WT SEDIMENT% 0.54 26-Aug-97 CAPTAN DRY WEIGHT SEDIMENT UG/KG 10.00 26-Aug-97 SOLIDS TOTAL PERCENT OF WET SAMPLE 11.50

175 26-Aug-97 SOLIDS VOLATILE PERCENT OF TOTAL SOLIDS 13.00 26-Aug-97 MERCURY TOT. IN BOT. DEPOS. (MG/KG AS HG DRY WGT) 0.100 12-Jun-81 MERCURY TOT. IN BOT. DEPOS. (MG/KG AS HG DRY WGT) 0.070 12-Jun-81 MERCURY TOT. IN BOT. DEPOS. (MG/KG AS HG DRY WGT) 0.150 26-Aug-97 ALACHLOR (LASSO) BOTTOM DEPOSITS DRY WGT UG/KG 10.00 26-Aug-97 METRIBUZIN (SENCOR) SEDIMENT DRY WEIGHT UG/KG 10.00 26-Aug-97 TREFLAN(TRIFLURALIN) IN SEDIMENT DRY WEIGHT UG/KG" 10.00 26-Aug-97 PENOXALIN IN SEDIMENT (PROWL) DRY WEIGHT UG/KG" 13.00 26-Aug-97 BLADEX (CYANAZINE) IN SEDIMENT DRY WEIGHT MG/KG " 25.00

176 APPENDIX 3.

PHYTOPLANKTON REFERENCES AND TABLES

177 178 A3.1 LIST OF REFERENCES ON ALGAE General references used for techniques: American Public Health Association (APHA). 1985. Standard methods for the examination of water and wastewater. 16th Edition. American Public Health Association, Washington, D.C. 1268 pp. Brower, J. E., J. R Zar and C. N. von Ende. 1990. Field and laboratory methods for general ecology. 3rd Edition. Wm C. Brown Publishers, Dubuque, IA 237 pp. Weber, C. I. 1973. Biological field and laboratory methods for measuring the quality of surface waters and effluents. U. S. Environmental Protection Agency, Cincinnati, OR.

Other references used in identification: Boyer, C. S. 1927. Synopsis of North American Diatomaceae. Proc. Acad. Natur. Sci Phila. Vol 78(1) Supplement: 1-228; Vol 79(2) Supplement:229-583. Boyer, C. S. 1973. The Diatomaceae of Philadelphia and vicmity. H. Tripp, Lafargeville, NY. 143pp. Britton, M. E. 1944. A catalog of Illinois algae. Northwestern University, Evanston, ll 177 pp. Cleve, P. T. 1965. Synopsis of the naviculoid diatoms. Asher and Co., Amsterdam, The Netherlands. 219 pp. Cleve-Euler, A. 1968. Die Diatomeen von Schweden und Finland. Kungl. Svenska Velenskapsokademiens Handlingar Fjarde Serien. 2(1): 1-163; 3(3): 1-153; 4(1):1-158; 4(5):1-253; 5(4):1-232. Dillard, G. E. and R. H Mohlenbrock. 1962. The Desmidiaceae of Madison Pond, Williamson County, Illinois. Amer. MidI. Natur. 67:204-207. Dillard, G. E. and D. R. Tindall. 1973. Notes on the algal flora of Illinois III. Additions to the Chlorophyceae. Ohio J. Sci 73:229-233. Dillard, G. E., K L. Weik and R. H Mohlenbrock. 1963. Notes on the algal flora of Illinois. Amer. Midl. Natur. 69: 127-135.

Dodd, J. J. 1987. Diatoms. Southern IL. Univ. Press, Carbondale. 477 pp. Drouet, F. 1968. Revision of the classification of the Oscillatoriaceae. Monograph 15. Acad. Natur. Sci, Philadelphia. 370 pp. Drouet, F. 1973. Revision of the N ostocaceae with cylindrical trichomes. Hafner Press, NY. 292 pp. Drouet, F. 1978. Revision of the Nostocaceae with constricted trichomes. Beih. Nova Hedw. 57: 1-258. Drouet, F. 1981. Revision of the Stigonemataceae with a Summary of the classification of the blue-green algae. Beih. Nova Hedw. 66:1-221 Drouet, F. and W. A Daily. 1956. Revision of the coccoid Myxophyceae. Butler Univ. Bot. Studies 12:1-218. Eddy, S. 1930. The fresh-water armored or thecate dinoflagellates. Trans. Amer. Microscop. Soc. 49:277-320. Eddy, S. 1931. The plankton of the Sangamon River in the summer of 1929. Illinois Natur. Hist. Surv. Bull 19:469-486. Geitler, L. 1932. Cyanophyceae. Pages 1-1156 in L. Rabenhorst, ed. Kryptogamen-Flora von Deutschland, Osterreich und der Schweiz. Band 14. Akademische Verlagsgesellschaft, Leipzig, Germany. Grady, M. M. 1974. New algal records for Lake County, Illinois. Trans. Illinois Acad. Sci. 67:318-332. Grubaugh, J. W., J. A Engman, L. M. O'Flaherty and R. V. Anderson. 1988. New algal records for Hancock and Henderson counties from Pool19, Upper Mississippi River. Trans. Illinois Acad. Sci. 81:287-292. Hustedt, F. 1930. Bacillariophyta (Diatomeae). Pages 1-466 in A Pascher, ed. Die

179 Susswasserllora Mitteleuropas. Heft 10. Gustav Fisher Verlag, Jena. Hutchinson, G. E. 1967. A treatise on limnology. Vol II. Wiley and Sons, New York. 1115 pp. Hutchinson, G. E. 1975. A treatise on limnology. Vol ill. Wiley and Sons, New York. 660 pp. Illinois EPA Staff. 1978. Assessment and classification of Illinois lakes. Illinois EPA, Springfield. Vol 1, 173 pp. Vol II, 358 pp. Kim, J. H and L. M. O'Flaherty. 1997. Phytoplankton communities m fertilized fish ponds: Effects of different nutrient loadings. Algae (Korean J. Phycol) 12:215-228. Kofoid, C. A. 1908. Plankton studies V. The plankton of the llIinois River, 1894-1899. Part II, Constituent organisms and their seasonal distribution. Bull 1l1 State Lab. Nat. Hist. 6:95- 635. Komarek, J. and B. Fott. 1983. Chlorophyceae (Grunalgen) Ordung: Chlorococcales. Pages 1- 1044 in G. Huber-Pestalozzi, ed. Das Phytoplankton des Susswassers. Systematik und Biologie. Die Binnengewasser. Vol 16, Part 7, No.1. E. Schweizerbart'sche Verlaagbuchhandlung, Stuttgart, Germany. Lipsey, L. L., Jr. 1975. Notes on the diatom flora of Kane County, Illinois. I. The Fox River at Elgin. Trans. Illinois State Acad. Sci. 68:339-346. Lipsey, L. L., Jr. 1976. Notes on the diatom flora of Lake and McHenry counties, Illinois. Trans. Illinois State Acad. Sci 69:283-291. Lipsey, L. L. Jr. and R. V. Anderson. 1988. Notes on the algal flora of Cass, Morgan and Pike counties (Illinois), including the boundary waters of the Mississippi River. Trans. Illinois Acad. Sci 81:45-60. Patrick, R. and C. W. Reimer. 1966. The diatoms of the United States. Vol 1. Acad. Natur. Sci, Philadelphia. 233 pp. Patrick, R. and C. W. Reimer. 1975. The diatoms of the United States. Vol 2, Part 1. Acad. Natur. Sci, Philadelphia. 233 pp. Prescott, G. W. 1951. Algae of the western Great Lakes area. Cranbrook Inst. Sci Bull. 31:1-946. Prescott, G. W. 1978. How to know the freshwater algae. 3rd Ed. Brown Co., Dubuque, IA 293 pp. Round, F. E. 1981. The ecology of algae. Cambridge Univ. Press, New York. 653 pp. Smith, G. M. 1920. Phytoplankton of the inland lakes of Wisconsin. Part I. Wisconsin Geol. Natur. Hist. Surv., Madison. 243 pp. Smith, G. M. 1924. Phytoplankton of the inland lakes of Wisconsin. Part II. Desmidiaceae. Wisconsin Geol. Natur. Hist. Surv., Madison. 227 pp. Smith, G. M. 1950. The fresh-water algae of the United States. McGraw-Hill Co., New York. 719 pp. Starmach, K. 1985. Chrysophyceae und Haptophyceae. VoL 1 in H Ettl, T. Gerloff: H Heying and D. Mollenhauer, eds. Susswasser von Mitteleuropa. Gustav Fischer Verlag, Stuttgart, Germany. Tiffany, L. H and M. E. Britton. 1952. The algae ofll1inois. Univ. Chicago Press, Chicago. 407 pp. Vaultonburg, D. L. and C. L. Pederson. 1994. Spatial and temporal variation in diatom community structure in two east-centralll1inois streams. Trans. ll1inois State Acad. Sci 87:9-27. Wetzel, R. G. and G. E. Likens. 1979. Limnological analysis. W. B. Saunders Co., Philadelphia. 357 pp.

180 Table A3.2-1. List of taxa found at Site 1 in Campus Lake-SIUC (RNZH) during 1997.

Taxa Date Found BACILLARIOPHYTA Asterionella A. formosa Hass. 6-17(C) Cvclotella C. meneqhiniana Kuetz. 7-16, 8-25, 10-7 (All C) Melosira M. italica (Ehr.) Kuetz. var. tenuissima (Grun.) Muell. 6-17(C) Nitzschia N. acicularis (Kuetz.) Wm. Sm. 6-17 (C) N. linearis (Ag.) Wm. Sm. 8-25 (C) N. galea (Kuetz.) Wm. Sm. 8-25 (C)

CHLOROPHYTA Ankistrodesmus A. falcatus (Corda) Ralfs var. acicularis (A. Br.) G. S. West 4-18, 8-25, 10-7 (All C) Carteria C. multifilis (Fres.) Dill. 6-17, 7-16, 8-25, 10-7 (All C) C. sp. (No.1) 7-16, 8-25 (Both C) Chloroqonium C. elonqatum (Dang.) 4-18, 6-17(P), 7-16, 8-25, 10-7(P) Franze var. elonqatum (All C except as noted.) Chodatella C. citriformis Snow 7-16(C) Closterium C. acutum (Lyngb.) Breb. 7-16, 8-25, 10-7 (All C) C. qracile Breb. var. elonqatum W. & G. S. West 8-25, 10-7 (Both C) Coelastrum C. carnbricum Arch. 7-16(C) C. microporum Naeg. 7-16, 8-25, 10-7 (All C) Cosmarium C. sp. (10.0 x 10.0 :m) 7-16, 8-25 (Both C) C. sp. (10.5 x 10.5 :m) 7-16(C) Crucigenia C. rectangylaris (A. Br.) Gray 7-16, 8-25 (Both C) Dictyosphaerium D. pulchellum Fres. 4-18, 6-17, 8-25 (All C) Elakatothrix E. viridis (Snow) Printz 7-16(P), 8-25(C) Euastrum E. sp. 7-16(C)

181 Taxa Date and Site Found Golenkinia G. radiata Chod. 7-16, 8-25 (Both C) Oocystis O. borgei Snow 4-18, 6-17, 7-16, 10-7 (All C) Pandorina P. morum Bory 7-16, 8-25 (Both C) Pediastrum P. boryanum (Turp.) Meneg. 6-17(C) Phacotus P. lenticularis (Ehr.) Stein 6-17, 7-16, 8-25, 10-7 (All C) Scenedesmus S. abundans (Kirch.) Chod. 6-17, 7-16, 8-25, 10-7 (All C) Schroederia S. setigera (Schroed.) 4-18, 6-17(P), 7-16, 8-25, 10-7 Lemm. (All C except as noted.) Staurastrum S. sp. (35.0 x 75.0 :m) 6-17(C) S. sp. (45.0 :m arm to arm) 7-16(C), 10-7(P) Tetraedron T. minimum (A. Br.) Hansg. 7-16, 8-25, 10-7 (All C) T. trigonum (Naeg.) Hansg. var. gracile (Rein.) deToni 8-25(C) Treubaria T. crassispina G. M. Sm. 7-16(C)

CHRYSOPHYTA Dinobryon D. sociale Ehr. 6-17(C)

CRYPTOPHYTA Cryptomonas C. erosa Ehr. 4-18, 6-17, 7-16, 8-25, 10-7 (All C) C. sp. (No.1) 4-18, 6-17, 7-16, 8-25, 10-7 (All C)

CYANOPHYTA Anabaena A. sp. (5.0 x 50.0 :m) 7-16, 8-25 (Both C) A. sp. (7.5 x 75.0 :m) 7-16, 8-25 (Both C) A. sp. (10.0 x 100.0 :m) 7-16(C) A. sp. (10.0 x 100.0 :m) 7-16, 8-25, 10-7 (All C) Anacystis A. montana (Lightf.) Dr. & Daily 4-18, 6-17, 7-16, 8-25, 10-7 (All C)

182 Taxa Date and Site Found

Aphanizomenon A. flos-aguae Born. et Flah. 6-17, 7-16, 8-25 (All C) Gomphosphaeria G. lacustris Chod. 4-18, 6-17, 7-16, 8-25, 10-7 (All C) Merismopedia M. guadruplicata Trev. 7-16, 8-25 (Both C) Microcystis M. aeruginosa Kuetz. 7-16, 8-25 (Both C) Oscillatoria O. lutea 6-17, 7-16 (Both C) Raphidiopsis R. curvata Fritsch & Rich 8-25(C) Schizothrix S. calcicola Gom. 4-18, 6-17, 8-25 (All C)

EUGLENOPHYTA Euglena E. acutissima Lemm. 6-17(C) E. viridis Ehr. 8-25(C) E. sp. (10.0 x 20.0 :m) 6-17(P) E. sp. (12.5 x 85.0 :m) 8-25(C) E. sp. (15.0 x 30.0 :m) 8-25(C) Phacus P. acuminatus Stokes 6-17(P) Trachelomnonas T. hispida (Perty) Stein 4-18(P), 6-17, 7-16, 8-25 (All C except as noted.) T. volvocina Ehr. 4-18, 6-17, 7-16, 8-25, 10-7 (All C) T. sp. (cyl.-srnooth) (15.0 x 17.5 :m) 8-25(C)

PYRRHOPHYTA Ceratium C. hirundinella (0. F. Muell.) Duj. 6-17, 8-25 (Both C)

XANTHOPHYTA Ophiocytium O. capitatum Wolle var. longispinum Moeb. 10-7(C)

GASTROTRICHA Unknown Gastrotrich 6-17(C)

PROTOZOA-Sub-Phylum Ciliophora-Class Ciliata- Unknown Ciliate (25.0 :m) 8-25(C) Unknown Ciliate (35.0 :m) 6-17(C) Unknown Ciliate (60.0 :m) 8-25(C)

183 Taxa Date and Site Found

Order Oligotrichida-Farnily Halteriidae Halteria H. sp. (25.0 :m) 6-17, 7-16, 10-7 (All C)

Sub-Phylum Mastigophora-Class Zoomastigophora- Order Protomastigida-Family Bodonidae Bodo B. edax 4-18(P)

ROTATORIA-Class Monogonata- Order Ploima-Family Brachionidae Brachionus B. sp. (25.0 x 80.0 :m) 6-17(P) B. sp. (65.0 x 80.0 :m) 8-25(P) Order Ploima-Family Trichocercidae Trichocerca T. sp. (15.0 x 133.0 :m) 7-16(C)

184 Table A3.1-2. Size, volume, density and total biovolume of individual organisms found in Campus Lake in 1997.

LAKE Campus (SIUC) DATE 4-18-97 SITE: RNZH-1

TAXA SIZE (:m) UNIT VOL. (:m3) No. /mL VOLUME BACILLARIOPHYTA-None CHLOROPHYTA Ankistrodesmus A. falcatus var. acicularis 1.25 x 18.0 22.1 14.881 328.9 Chlorogonium C. elonqatum var. elongatum 5.0 x 20.0 392.7 29.762 11687.5 Dictyosphaerium D. pulchellum 20.0 (col.-diam.) 4188.8 Present Oocystis O. borgei 12.5 (diam.) 1022.7 14.881 15218.8 Schroederia S. setigera 2.5 x 52.5 257.7 74.405 19174.2 CHRYSOPHYTA-None

CRYPTOPHYTA Crygtomonas C. erosa 12.5 x 20.0 2454.4 44.643 109571.8 C. sp. (No.1) 5.0 x 7.5 147.3 89.286 13151.8

CYANOPHYTA Anacystis A. montana 10.0 (col.-diam.) 523.6 297.620 155833.8 Gomphosphaeria G. lacustris 10.0 (col.-diam.) 523.6 148.810 77916.9 Schizothrix S. calcicola 2.0 x 10.0 31.4 14.881 467.3

EUGLENOPHYTA Trachelomonas T. volvocina 11.2 (diam.) 735.6 14.881 10946.5

PYRRHOPHYTA-None

XANTHOPHYTA-None

ANIMAL MATERIAL-None

185 DATE 6-17-97 SITE: RNZH-1 TAXA SIZE (:m) UNIT VOL. (:m3) No. /mL VOLUME BACILLARIOPHYTA Asterionella A. formosa 110.0 x 0.5 47517.0 569.942 2708194.8 Melosira M. italica var. tenuissima 5.0 x 14.0 2748.9 14.881 40906.4 Nitzschia N. acicularis 2.5 x 87.5 429.5 14.881 6391.4

CHLOROPHYTA Carteria C. multifilis 7.5 (diam.) 220.9 14.881 3287.2 Dictyosphaerium D. pulchellum 20.0 (col.-diam.) 4188.8 14.881 62333.5 Oocystis O. borgei 12.5 (diam.) 1022.7 14.881 15218.8 Pediastrum P. boryanum 55.0 x 2.0 4751.7 14.881 70710.0 Phacotus P. lenticularis 7.5 x 12.5 552.2 29.762 16434.6 Scenedesmus S. abundans 7.5 x 15.0 577.3 29.762 17181.6 Staurastrum S. sp. 35.0 x 75.0 928.1 Present

CHRYSOPHYTA Dinobryon D. sociale 35.0 x 100.0 7291.7 25.298 184463.2

CRYPTOPHYTA Cryptomonas C. erosa 12.5 x 20.0 2454.4 550.597 1351385.2 Cryptomonas C. sp. (No.1) 5.0 x 7.5 147.3 178.572 26303.7

CYANOPHYTA Anacystis A. montana 10.0 (col.-diam.) 523.6 386.906 202584.0 Aphanizomenon A. flos-aquae 5.0 x 50.0 981.7 Present Gomphosphaeria G. lacustris 10.0 (col.-diam.) 523.6 476.192 249334.1 Oscillatoria O. lutea 5.0 x 60.0 1178.1 14.881 17531.3 Schizothrix S. calcicola 2.0 x 10.0 31.4 14.881 467.3

186 DATE 6-17-97 SITE: RNZH-1 TAXA SIZE (:m) UNIT VOL. (:m3) No. /mL VOLUME

EUGLENOPHYTA Euglena E. acutissima 7.5 x 117.5 5191.0 Present Trachelomonas T. hispida 25.0 x 30.0 14726.2 14.881 219140.6 T. volvocina 11.2 (diam.) 735.6 44.643 32839.4

PYRRHOPHYTA Ceratium C. hirundinella 50.0 x 237.5 155414.1 59.524 9250868.8

XANTHOPHYTA-None ANIMAL MATERIAL GASTROTRICHA Unknown Gastrotrich 60.0 x 110.0 311017.4 14.881 4628249.9

PROTOZOA-Sub-Phylum Ciliophora-Class Ciliata Unknown Ciliate 35.0 (diam.) 22449.4 14.881 334069

Order Oligotrichida-Family Halteriidae Halteria H. sp. 25.0 (diam.) 8181.2 14.881 121744.4

DATE 7-16-97 SITE: RNZH-1 TAXA SIZE (:m) UNIT VOL. (:m3) No. /mL VOLUME BAC I LLARIOPHYTA Cyclotella C. meneghiniana 11.2 (diam.) 198.8 44.643 8875.0

CHLOROPHYTA Carteria C. multifilis 7.5 (diam.) 220.9 29.762 6574.4 C. sp. 15.0 x 20.0 3534.3 14.881 52593.9 Chloroqonium C. elongatum var. elongatum 5.0 x 20.0 392.7 14.881 5843.8 Chodatella C. citriformis 12.5 x 20.0 2454.4 14.881 36523.9 Closterium C. acutum 2.5 x 62.5 306.8 29.762 9131.0 Coelastrum C. cambricum 15.0 (col.-diam.) 1767.2 14.881 26297.7 C. microporum 20.0 (col.-diam.) 4188.8 14.881 62333.5 Cosmarium C. sp. 10.0 x 10.0 785.4 267.858 210375.7

187 DATE 7-16-97 SITE: RNZH-1 TAXA SIZE (:m) UNIT VOL. (:m3) No. /mL VOLUME Cosmarium (cont’d) C. sp. 10.5 x 10.5 909.2 44.643 40589.4 Crucigenia C. rectangularis 8.0 x 8.0 x 1.0 64.0 29.762 1904.8 Euastrum E. sp. 10.0 x 15.0 150.0 14.881 2232.2 Golenkinia G. radiata 15.0 (diam.) 1767.2 14.881 26297.7 Oocystis O. borgei 12.5 (diam.) 1022.7 44.643 45656.4 Pandorina P. morum 32.5 x 92.5 10210.2 29.762 303876.0 Phacotus P. lenticularis 7.5 x 12.5 552.2 74.405 41086.4 Scenedesmus S. abundans 7.5 x 15.0 577.3 14.881 8590.8 Schroederia S. setigera 2.5 x 52.5 257.7 14.881 3834.8 Staurastrum S. sp. 15.0 x 30.0 5301.4 29.762 157780.3 Tetraedron T. minimum 7.5 421.8 29.762 12553.6 Treubaria T. crassisoina 10.0 523.6 14.881 7791.7

CHRYSOPHYTA-None

CRYPTOPHYTA Crygtomonas C. erosa 12.5 x 20.0 2454.4 148.810 365239.3 C. sp. (No.1) 5.0 x 7.5 147.3 178.572 26303.7

CYANOPHYTA Anabaena A. sp. 5.0 x 50.0 981.7 119.048 116869.4 A. sp. 7.5 x 75.0 3313.4 312.501 1035440.8 A. sp. 10.0 x 100.0 7854.0 14.881 116875.4 A. sp. 10.0 x 100.0 7854.0 193.453 1519379.8 Anacystis A. montana 10.0 (col.-diam.) 523.6 342.263 179208.9 Aphanizomenon A. flos-aquae 5.0 x 50.0 981.7 1369.052 1343998.3 Gomphosphaeria G. lacustris 10.0 (col.-diam.) 523.6 297.620 155833.8 Merismopedia M. guadruplicata 25.0 x 25.0 x 2.5 1562.5 14.881 23251.6 Microcvstis M. aeruginosa 40.0 (col.-diam.) 33510.4 Present Oscillatoria O. lutea 5.0 x 60.0 1178.1 14.881 17531.3

188 DATE 7-16-97 SITE: RNZH-1 TAXA SIZE (:m) UNIT VOL. (:m3) No. /mL VOLUME

EUGLENOPHYTA Trachelomonas T. hispida 25.0 x 30.0 14726.2 14.881 219140.6 T. volvocina 11.2 (diam.) 735.6 104.167 76625.2

PYRRHOPHYTA-None XANTHOPHYTA-None ANIMAL MATERIAL PROTOZOA-Sub-Phylum Ciliophora-Class Ciliata Order Oligotrichida-Family Halteriidae Halteria H. sp. 25.0 (diam.) 8181.2 14.881 121744.4

ROTATORIA-Class Monogonata-Order ploima-Family Trichocercidae Trichocerca T. sp. 15.0 x 133.0 23503.0 Present

DATE 8-25-97 SITE: RNZH-1 TAXA SIZE (:m) UNIT VOL. (:m3) No. /mL VOLUME BACILLARIOPHYTA Cyclotella C. meneghiniana 11.2 (diam.) 198.8 59.524 11833.4 Nitzschia N. linearis 5.0 x 70.0 1374.4 Present N. palea 3.0 x 25.0 176.7 14.881 2629.5

CHLOROPHYTA Ankistrodesmus A. falcatus var. acicularis 1.25 x 18.0 22.1 267.858 5919.7 Carteria C. multifilis 7.5 (diam.) 220.9 29.762 6574.4 C. sp. 15.0 x 20.0 3534.3 59.524 210375.7 Chlorogonium C. elongatum var. elongatum 5.0 x 20.0 392.7 44.643 17531.3 Closterium C. acutum 2.5 x 62.5 306.8 14.881 4565.5 C. gracile var. elongatum 5.0 x 250.0 4908.7 44.643 219139.1 Coelastrum C. microporum 20.0 (col.-diam.) 4188.8 44.643 187000.6 Cosmarium C. sp. 10.0 x 10.0 785.4 29.762 23375.1

189 DATE 8-25-97 SITE: RNZH-1 TAXA SIZE (:m) UNIT VOL. (:m3) No. /mL VOLUME Crucigenia C. rectanqularis 8.0 x 8.0 x 1.0 64.0 14.881 952.4 Dictyosphaerium D. pulchellum 20.0 (col.-diam.) 4188.8 744.050 3116676.6 Elakatothrix E. viridis 2.5 x 15.0 73.6 14.881 1095.2 Golenkinia G. radiata 15.0 (diam.) 1767.2 29.762 52595.4 Pandorina P. morum 32.5 x 92.5 10210.2 14.881 151938.0 Phacotus P. lenticularis 7.5 x 12.5 552.2 29.762 16434.6 Scenedesmus S. abundans 7.5 x 15.0 577.3 178.572 103089.6 Schroederia S. setigera 2.5 x 52.5 257.7 59.524 15339.3 Tetraedron T. minimum 7.5 421.8 119.048 50214.4 T. trigonum var. gracile 20.0 x 20.0 141.4 14.881 2104.2

CHRYSOPHYTA-None

CRYPTOPHYTA Crptomonas T. erosa 12.5 x 20.0 2454.4 104.167 255667.5 T. sp. (No.1) 5.0 x 7.5 147.3 29.762 4383.9

CYANOPHYTA Anabaena A. sp. 5.0 x 50.0 981.7 14.881 14608.7 A. sp. 7.5 x 75.0 3313.4 252.977 838214.0 A. sp. 10.0 x 100.0 7854.0 29.762 233750.7 Anacystis A. montana 10.0 (col.-diam.) 523.6 193.453 101292.0 Aphanizomenon A. flos-aquae 5.0 x 50.0 981.7 2321.436 2278953.7 Gomphosphaeria G. lacustris 10.0 (col.-diam.) 523.6 7291.690 3817928.8 Merismopedia M. guadruplicata 25.0 x 25.0 x 2.5 1562.5 74.405 116257.8 Microcystis M. aeruginosa 40.0 (col.-diam.) 33510.4 89.286 2992009.5 Raphidiopsis R. curvata 5.0 x 25.0 490.9 14.881 7305.1 I Schizothrix S. calcicola 2.0 x 10.0 31.4 7485.143 235033.5

190 DATE 8-25-97 SITE: RNZH-1 TAXA SIZE (:m) UNIT VOL. (:m3) No. /mL VOLUME EUGLENOPHYTA Euglena E. viridis 22.5 x 45.5 18091.1 14.881 269213.6 E. sp. 15.0 x 30.0 5301.4 14.881 78890.1 E. sp. 12.5 x 85.0 10431.1 Present Trachelomonas T. hispida 25.0 x 30.0 14726.2 14.881 219140.6 T. volvocina 11.2 (diam.) 735.6 133.929 98518.2 T. sp. 15.0 x 17.5 3092.5 14.881 46019.5

PYRRHOPHYTA Ceratium C. hirundinella 50.0 x 237.5 155414.1 14.881 2312717.2

XANTHOPHYTA-None

ANIMAL MATERIAL PROTOZOA-Sub-Phylum Ciliophora-Class Ciliata Unknown Ciliate 25.0 8181.2 14.881 121744.4 Unknown Ciliate 60.0 113097.6 14.881 1683005.3

DATE 10-7-97 SITE: RNZH-1 TAXA SIZE (:m) UNIT VOL. (:m3) No. /mL VOLUME BACILLARIOPHYTA Cyclotella C. meneghiniana 11.2 (diam.) 198.8 14.881 2958.3 CHLOROPHYTA Ankistrodesmus A. falcatus var. acicularis 1.25 x 18.0 22.1 29.762 657.7 Carteria C. multifilis 7.5 (diam.) 220.9 14.881 3287.2 Closterium C. acutum 2.5 x 62.5 306.8 14.881 4565.5 C. gracile var. elongatum 5.0 x 250.0 4908.7 29.762 146092.7 Coelastrum C. microporum 20.0 (col.-diam.) 4188.8 29.762 124887.1 Oocystis O. borgei 12.5 (diam.) 1022.7 29.762 30437.6 Phacotus P. lenticularis 7.5 x 12.5 552.2 14.881 8217.3 Scenedesmus S. abundans 7.5 x 15.0 577.3 14.881 8590.8 Schroederia S. setiqera 2.5 x 52.5 257.7 178.572 46018.0

191 DATE 10-7-97 SITE: RNZH-1 TAXA SIZE (:m) UNIT VOL. (:m3) No. /mL VOLUME Tetraedron T. minimum 7.5 421.8 133.929 56491.3

CHRYSOPHYTA-None

CRYPTOPHYTA Crptomonas C. erosa 12.5 x 20.0 2454.4 461.311 1132241.7 Cryptomonas C. sp. (No.1) 5.0 x 7.5 147.3 178.572 26303.7

CYANOPHYTA Anabaena A. sp. 10.0 x 100.0 7854.0 119.048 935003.0 Anacystis A. montana 10.0 (col.-diam.) 523.6 476.192 249334.1 Gomohosphaeria G. lacustris 10.0 (col.-diam.) 523.6 535.716 280500.9

EUGLENOPHYTA Trachelomonas T. volvocina 11.2 (diam.) 735.6 14.881 10946.5

PYRRHOPHYTA-None XANTHOPHYTA Ophiocytium O. capitatum var. lonqispinum 5.0 x 50.0 981.7 1398.814 1373215.7 ANIMAL MATERIAL PROTOZOA-Sub-Phylum Ciliophora-Class Ciliata Order Oligotrichida-Family Halteriidae Halteria H. sp. 25.0 (diam.) 8181.2 14.881 121744.4

192 APPENDIX 4.

DETAILED ZOOPLANKTON AND BENTHOS COUNT DATA

193 A4-1. DETAILED ZOOPLANKTON AND BENTHOS COUNT DATA

This appendix contains tables detailing the count data for each zooplankton taxon monitored at the three sampling sites in Campus Lake between 1997 and 1998 as part of the Phase I monitoring program. See Appendix 1 for general collection methods. Data are summarized in section 11.4. of the main body of the report.

194 Table A4.1-1. Summary of taxa means and total number of organisms one each sampling date for three stations in Campus Lake, Jackson Co., IL spanning the period May 1997 - October 1998. Date Taxa Total Daphnia Cerodaphnia Bosmina Cyclopoids Calanoids Nauplii Rotifers Mean Mean Mean Mean Mean Mean Mean 16-May-97 12.2 31.1 27.8 32.2 0.0 42.2 50.0 195.6 22-May-97 70.0 190.0 23.3 83.3 3.3 116.7 51.1 537.8 06-Jun-97 42.2 19.1 7.1 185.1 0.0 656.0 212.4 1122.0 18-Jun-97 21.1 2.2 64.5 258.9 0.0 762.2 1965.5 3074.4 01-Jul-97 23.3 21.1 18.9 30.0 0.0 262.2 306.7 662.2 17-Jul-97 43.3 63.3 21.2 65.5 5.5 263.3 170.0 632.3 31-Jul-97 15.6 26.7 22.2 88.9 3.3 253.3 164.4 574.5 14-Aug-97 2.2 7.8 33.3 5.6 158.9 735.5 943.3 27-Aug-97 0.0 16.7 40.0 2.2 146.7 403.4 608.9 10-Sep-97 7.8 16.6 51.1 16.7 217.8 438.9 748.8 24-Sep-97 17.2 5.0 1480.0 26.7 1.9 87.2 683.6 2301.6 08-Oct-97 30.0 14.4 848.9 22.2 3.3 70.0 997.8 1986.7 25-Oct-97 62.2 20.0 32.2 17.8 15.6 67.8 886.7 1102.3 08-Nov-97 46.7 10.0 41.1 30.0 12.2 132.2 762.2 1034.4 22-Nov-97 38.9 11.1 14.4 22.2 10.0 183.3 1151.1 1431.0 06-Dec-97 5.6 1.1 17.8 18.9 0.0 261.1 1304.4 1609.0 17-Jan-98 4.4 1.1 11.1 178.9 2.2 122.2 756.7 1076.7 07-Feb-98 14.4 22.2 272.2 7.8 54.5 412.2 783.4 21-Mar-98 0.0 4.4 50.6 2.5 33.3 272.5 363.3 04-Apr-98 11.1 1.1 13.3 18.9 3.3 91.1 763.3 902.2 20-Apr-98 5.5 4.4 34.5 10.0 96.7 176.6 327.7 04-May-98 23.3 4.5 15.5 20.0 90.0 321.1 474.4 23-May-98 34.4 36.7 1.1 7.8 16.7 105.6 85.6 287.8 04-Jun-98 7.8 14.5 0.0 17.8 5.5 107.8 227.8 381.1 21-Jun-98 10.0 37.8 1.1 26.7 5.5 173.3 332.2 586.6 02-Jul-98 8.9 10.0 2.2 17.8 3.3 114.4 366.7 523.3 16-Jul-98 2.2 53.3 3.3 31.1 6.7 128.9 863.3 1088.9 31-Jul-98 1.1 24.5 0.0 30.0 8.9 205.6 223.3 493.4 13-Aug-98 17.8 16.7 1.1 22.2 318.9 203.3 580.0 26-Aug-98 2.2 7.8 0.0 22.2 5.5 232.2 800.0 1070.0 12-Sep-98 1.1 87.8 5.6 86.7 14.4 251.1 233.3 680.0 26-Sep-98 8.9 66.7 7.8 122.2 40.0 400.0 675.6 1321.1 17-Oct-98 6.7 2.2 293.3 130.0 45.6 187.8 405.6 1071.1 TOTALS 598.2 775.2 3036.2 2091.1 282.5 6845.6 17402.9 31031.7

195 Table A4.1-2. Summary of Daphnia counts and station means from Campus Lake, Jackson Co., IL for the period May 1997 - October 1998. Date Station Mean SE 1.0 2.0 3.0 16-May-97 13.3 3.3 20.0 12.2 4.85 22-May-97 36.7 96.7 76.7 70.0 17.64 06-Jun-97 100.0 10.0 16.7 42.2 28.95 18-Jun-97 33.3 10.0 20.0 21.1 6.75 01-Jul-97 30.0 13.3 26.7 23.3 5.11 17-Jul-97 50.0 30.0 50.0 43.3 6.67 31-Jul-97 20.0 20.0 6.7 15.6 4.43 14-Aug-97 0.0 3.3 3.3 2.2 1.10 27-Aug-97 0.0 0.0 0.0 0.0 0.00 10-Sep-97 0.0 20.0 3.3 7.8 6.19 24-Sep-97 5.0 43.3 3.3 17.2 13.06 08-Oct-97 23.3 60.0 6.7 30.0 15.75 25-Oct-97 30.0 56.7 100.0 62.2 20.40 08-Nov-97 3.3 96.7 40.0 46.7 27.17 22-Nov-97 30.0 23.3 63.3 38.9 12.37 06-Dec-97 10.0 6.7 0.0 5.6 2.94 17-Jan-98 3.3 3.3 6.7 4.4 1.13 07-Feb-98 10.0 20.0 13.3 14.4 2.94 21-Mar-98 0.0 0.0 0.0 0.0 0.00 04-Apr-98 3.3 6.7 23.3 11.1 6.18 20-Apr-98 10.0 3.3 3.3 5.5 2.23 04-May-98 50.0 6.7 13.3 23.3 13.47 23-May-98 40.0 30.0 33.3 34.4 2.94 04-Jun-98 6.7 13.3 3.3 7.8 2.94 21-Jun-98 13.3 10.0 6.7 10.0 1.91 02-Jul-98 16.7 6.7 3.3 8.9 4.02 16-Jul-98 6.7 0.0 0.0 2.2 2.23 31-Jul-98 0.0 3.3 0.0 1.1 1.10 13-Aug-98 26.7 20.0 6.7 17.8 5.88 26-Aug-98 6.7 0.0 0.0 2.2 2.22 12-Sep-98 0.0 3.3 0.0 1.1 1.11 26-Sep-98 0.0 6.7 20.0 8.9 5.88 17-Oct-98 6.7 3.3 10.0 6.7 1.92 TOTALS 584.9 629.9 579.9 598.2 15.92

196 Table A4.1-3. Summary of Ceriodaphnia counts and station means from Campus Lake, Jackson Co., IL for the period May 1997 - October 1998. Date STATION Average SE 1.0 2.0 3.0 16-May-97 3.3 53.3 36.7 31.1 14.70 22-May-97 83.3 276.7 210.0 190.0 56.72 06-Jun-97 24.0 10.0 23.3 19.1 4.55 18-Jun-97 3.3 3.3 0.0 2.2 1.10 01-Jul-97 33.3 6.7 23.3 21.1 7.76 17-Jul-97 90.0 30.0 70.0 63.3 17.64 31-Jul-97 26.7 36.7 16.7 26.7 5.77 14-Aug-97 27-Aug-97 10-Sep-97 24-Sep-97 15.0 0.0 0.0 5.0 5.00 08-Oct-97 30.0 10.0 3.3 14.4 8.02 25-Oct-97 40.0 6.7 13.3 20.0 10.18 08-Nov-97 6.7 10.0 13.3 10.0 1.91 22-Nov-97 20.0 10.0 3.3 11.1 4.85 06-Dec-97 3.3 0.0 0.0 1.1 1.10 17-Jan-98 3.3 0.0 0.0 1.1 1.10 07-Feb-98 21-Mar-98 04-Apr-98 0.0 0.0 3.3 1.1 1.10 20-Apr-98 04-May-98 23-May-98 46.7 60.0 3.3 36.7 17.12 04-Jun-98 16.7 20.0 6.7 14.5 4.00 21-Jun-98 60.0 43.3 10.0 37.8 14.70 02-Jul-98 6.7 23.3 0.0 10.0 6.93 16-Jul-98 120.0 20.0 20.0 53.3 33.33 31-Jul-98 10.0 26.7 36.7 24.5 7.79 13-Aug-98 3.3 30.0 16.7 16.7 7.70 26-Aug-98 10.0 6.7 6.7 7.8 1.11 12-Sep-98 46.7 210.0 6.7 87.8 62.19 26-Sep-98 63.3 123.3 13.3 66.7 31.80 17-Oct-98 3.3 3.3 0.0 2.2 1.11 TOTALS 769.0 1020.0 536.5 775.2 139.61

197 Table A4.1-4. Summary of Bosmina counts and station means from Campus Lake, Jackson Co., IL for the period May 1997 - October 1998. Date Station Average SE 123 16-May-97 50.0 16.7 16.7 27.8 11.10 22-May-97 30.0 30.0 10.0 23.3 6.67 06-Jun-97 8.0 6.7 6.7 7.1 0.43 18-Jun-97 146.7 30.0 16.7 64.5 41.30 01-Jul-97 16.7 16.7 23.3 18.9 2.20 17-Jul-97 43.7 16.7 3.3 21.2 11.88 31-Jul-97 40.0 16.7 10.0 22.2 9.09 14-Aug-97 6.7 3.3 13.3 7.8 2.94 27-Aug-97 10.0 30.0 10.0 16.7 6.67 10-Sep-97 3.3 23.3 23.3 16.6 6.67 24-Sep-97 2816.7 1506.7 116.7 1480.0 779.54 08-Oct-97 766.7 1710.0 70.0 848.9 475.21 25-Oct-97 86.7 6.7 3.3 32.2 27.25 08-Nov-97 63.3 30.0 30.0 41.1 11.10 22-Nov-97 10.0 23.3 10.0 14.4 4.43 06-Dec-97 36.7 6.7 10.0 17.8 9.50 17-Jan-98 13.3 6.7 13.3 11.1 2.20 07-Feb-98 26.7 23.3 16.7 22.2 2.94 21-Mar-98 0.0 10.0 3.3 4.4 2.94 04-Apr-98 16.7 0.0 23.3 13.3 6.93 20-Apr-98 3.3 10.0 0.0 4.4 2.94 04-May-98 6.7 0.0 6.7 4.5 2.23 23-May-98 3.3 0.0 0.0 1.1 1.10 04-Jun-98 0.0 0.0 0.0 0.0 0.00 21-Jun-98 3.3 0.0 0.0 1.1 1.10 02-Jul-98 3.3 3.3 0.0 2.2 1.10 16-Jul-98 10.0 0.0 0.0 3.3 3.33 31-Jul-98 0.0 0.0 0.0 0.0 0.00 13-Aug-98 3.3 0.0 0.0 1.1 1.11 26-Aug-98 0.0 0.0 0.0 0.0 0.00 12-Sep-98 6.7 6.7 3.3 5.6 1.11 26-Sep-98 13.3 10.0 0.0 7.8 4.01 17-Oct-98 440.0 383.3 56.7 293.3 119.46 TOTALS 4685.1 3926.8 496.6 3036.2 1288.52

198 Table A4.1-5. Summary of adult and copepodid Copepoda counts and station means from Campus Lake, Jackson Co., IL for the period May 1997 - October 1998. Date STATION Mean SE 123 16-May-97 23.3 16.7 56.7 32.2 12.38 22-May-97 43.3 93.3 113.3 83.3 20.82 06-Jun-97 252.0 46.6 256.7 185.1 69.26 18-Jun-97 590.0 96.7 90.0 258.9 165.56 01-Jul-97 23.3 3.3 63.3 30.0 17.64 17-Jul-97 106.6 30.0 60.0 65.5 22.28 31-Jul-97 80.0 93.3 93.3 88.9 4.43 14-Aug-97 33.4 3.3 63.3 33.3 17.32 27-Aug-97 73.3 10.0 36.6 40.0 18.35 10-Sep-97 3.3 116.7 33.3 51.1 33.92 24-Sep-97 30.0 13.3 36.7 26.7 6.96 08-Oct-97 6.7 20.0 40.0 22.2 9.68 25-Oct-97 6.7 20.0 26.7 17.8 5.88 08-Nov-97 3.3 73.3 13.3 30.0 21.86 22-Nov-97 13.3 20.0 33.3 22.2 5.88 06-Dec-97 6.7 23.4 26.7 18.9 6.19 17-Jan-98 216.7 173.3 146.7 178.9 20.40 07-Feb-98 323.3 416.7 76.7 272.2 101.42 21-Mar-98 75.0 30.0 46.7 50.6 13.13 04-Apr-98 16.7 16.7 23.3 18.9 2.20 20-Apr-98 36.7 20.0 46.7 34.5 7.79 04-May-98 10.0 26.6 10.0 15.5 5.53 23-May-98 3.3 3.3 16.7 7.8 4.47 04-Jun-98 20.0 10.0 23.3 17.8 4.00 21-Jun-98 40.0 10.0 30.0 26.7 8.82 02-Jul-98 40.0 0.0 13.3 17.8 11.76 16-Jul-98 50.0 40.0 3.3 31.1 14.20 31-Jul-98 60.0 20.0 10.0 30.0 15.28 13-Aug-98 20.0 20.0 26.6 22.2 2.20 26-Aug-98 36.7 10.0 20.0 22.2 7.79 12-Sep-98 110.0 110.0 40.0 86.7 23.33 26-Sep-98 103.3 90.0 173.3 122.2 25.84 17-Oct-98 60.0 63.3 266.7 130.0 68.36 TOTALS 2516.9 1739.9 2016.6 2091.1 227.38

199 Table A4.1-6. Summary of adult and calanoid Copepoda counts and station means from Campus Lake, Jackson Co., IL for the period May 1997 - October 1998. Date STATION Mean SE 1.0 2.0 3.0 16-May-97 0.0 0.0 0.0 0.0 0.00 22-May-97 0.0 10.0 0.0 3.3 3.33 06-Jun-97 0.0 0.0 0.0 0.0 0.00 18-Jun-97 0.0 0.0 0.0 0.0 0.00 01-Jul-97 0.0 0.0 0.0 0.0 0.00 17-Jul-97 6.6 3.3 6.7 5.5 1.12 31-Jul-97 10.0 0.0 0.0 3.3 3.33 14-Aug-97 0.0 16.7 0.0 5.6 5.57 27-Aug-97 0.0 3.3 3.3 2.2 1.10 10-Sep-97 0.0 46.7 3.3 16.7 15.05 24-Sep-97 2.5 3.3 0.0 1.9 0.99 08-Oct-97 6.7 3.3 0.0 3.3 1.93 25-Oct-97 40.0 0.0 6.7 15.6 12.37 08-Nov-97 13.3 3.3 20.0 12.2 4.85 22-Nov-97 10.0 3.3 16.7 10.0 3.87 06-Dec-97 0.0 0.0 0.0 0.0 0.00 17-Jan-98 0.0 6.7 0.0 2.2 2.23 07-Feb-98 3.3 20.0 0.0 7.8 6.19 21-Mar-98 7.5 0.0 0.0 2.5 2.50 04-Apr-98 0.0 0.0 10.0 3.3 3.33 20-Apr-98 16.7 10.0 3.3 10.0 3.87 04-May-98 40.0 13.3 6.7 20.0 10.18 23-May-98 16.7 20.0 13.3 16.7 1.93 04-Jun-98 3.3 10.0 3.3 5.5 2.23 21-Jun-98 13.3 0.0 3.3 5.5 4.00 02-Jul-98 3.3 3.3 3.3 3.3 0.00 16-Jul-98 13.3 6.7 0.0 6.7 3.84 31-Jul-98 6.7 6.7 13.3 8.9 2.20 13-Aug-98 26-Aug-98 13.3 3.3 0.0 5.5 4.00 12-Sep-98 30.0 13.3 0.0 14.4 8.68 26-Sep-98 26.6 70.0 23.4 40.0 15.03 17-Oct-98 70.0 23.3 43.4 45.6 13.52 TOTALS 354.2 299.9 193.3 282.5 47.26

200 Table A4.1-7. Summary of cyclopoid and calanoid nauplii counts and station means from Campus Lake, Jackson Co., IL for the period May 1997 - October 1998. Date STATION Mean SE 1.0 2.0 3.0 16-May-97 36.7 36.7 53.3 42.2 5.53 22-May-97 100.0 56.7 193.3 116.7 40.30 06-Jun-97 1326.0 12.0 630.0 656.0 379.54 18-Jun-97 903.3 806.7 576.7 762.2 96.87 01-Jul-97 106.7 193.3 486.7 262.2 114.98 17-Jul-97 286.7 203.3 300.0 263.3 30.26 31-Jul-97 200.0 273.3 286.7 253.3 26.95 14-Aug-97 83.3 220.0 173.3 158.9 40.12 27-Aug-97 196.7 106.7 136.7 146.7 26.46 10-Sep-97 200.0 300.0 153.3 217.8 43.27 24-Sep-97 95.0 93.3 73.3 87.2 6.97 08-Oct-97 53.3 116.7 40.0 70.0 23.66 25-Oct-97 30.0 73.3 100.0 67.8 20.40 08-Nov-97 143.3 110.0 143.3 132.2 11.10 22-Nov-97 203.3 196.7 150.0 183.3 16.78 06-Dec-97 150.0 346.7 286.7 261.1 58.20 17-Jan-98 136.7 143.3 86.7 122.2 17.87 07-Feb-98 36.7 90.0 36.7 54.5 17.77 21-Mar-98 30.0 40.0 30.0 33.3 3.33 04-Apr-98 90.0 86.7 96.7 91.1 2.94 20-Apr-98 83.3 110.0 96.7 96.7 7.71 04-May-98 80.0 86.7 103.3 90.0 6.93 23-May-98 56.7 43.3 216.7 105.6 55.70 04-Jun-98 80.0 110.0 133.3 107.8 15.43 21-Jun-98 216.7 120.0 183.3 173.3 28.36 02-Jul-98 160.0 110.0 73.3 114.4 25.13 16-Jul-98 160.0 176.7 50.0 128.9 39.74 31-Jul-98 300.0 266.7 50.0 205.6 78.38 13-Aug-98 390.0 260.0 306.7 318.9 38.02 26-Aug-98 143.3 276.7 276.7 232.2 44.44 12-Sep-98 256.7 233.3 263.3 251.1 9.09 26-Sep-98 240.0 93.3 866.7 400.0 237.14 17-Oct-98 233.3 126.7 203.3 187.8 31.76 TOTALS 7733.3 5526.7 7276.7 6845.6 672.49

201 Table A4.1-8. Summary of rotifer counts and station means from Campus Lake, Jackson Co., IL for the period May 1997 - October 1998. Date STATION Mean SE 1.0 2.0 3.0 16-May-97 43.3 56.7 50.0 50.0 3.87 22-May-97 66.7 40.0 46.7 51.1 8.02 06-Jun-97 324.0 23.3 290.0 212.4 95.07 18-Jun-97 2010.0 2853.3 1033.3 1965.5 525.86 01-Jul-97 213.3 236.7 470.0 306.7 81.95 17-Jul-97 173.3 136.7 200.0 170.0 18.35 31-Jul-97 100.0 153.3 240.0 164.4 40.80 14-Aug-97 530.0 1243.3 433.3 735.5 255.41 27-Aug-97 476.7 496.7 236.7 403.4 83.53 10-Sep-97 506.7 476.7 333.3 438.9 53.51 24-Sep-97 547.5 543.3 960.0 683.6 138.21 08-Oct-97 490.0 1420.0 1083.3 997.8 271.85 25-Oct-97 693.3 806.7 1160.0 886.7 140.53 08-Nov-97 526.7 1123.3 636.7 762.2 183.30 22-Nov-97 1406.7 863.3 1183.3 1151.1 157.69 06-Dec-97 873.3 1570.0 1470.0 1304.4 217.49 17-Jan-98 810.0 643.3 816.7 756.7 56.72 07-Feb-98 370.0 450.0 416.7 412.2 23.20 21-Mar-98 237.5 283.3 296.7 272.5 17.92 04-Apr-98 706.7 960.0 623.3 763.3 101.24 20-Apr-98 113.3 163.3 253.3 176.6 40.96 04-May-98 346.7 293.3 323.3 321.1 15.45 23-May-98 56.7 106.7 93.3 85.6 14.94 04-Jun-98 356.7 173.3 153.3 227.8 64.72 21-Jun-98 373.3 346.7 276.7 332.2 28.81 02-Jul-98 623.3 286.7 190.0 366.7 131.32 16-Jul-98 1173.3 860.0 556.7 863.3 178.00 31-Jul-98 320.0 200.0 150.0 223.3 50.44 13-Aug-98 236.7 180.0 193.3 203.3 17.11 26-Aug-98 983.3 943.3 473.3 800.0 163.74 12-Sep-98 203.3 123.3 373.3 233.3 73.71 26-Sep-98 786.7 743.3 496.7 675.6 90.31 17-Oct-98 343.3 360.0 513.3 405.6 54.10 TOTALS 17022.3 19159.9 16026.6 17402.9 924.31

202 Table A4.1-9. Dates on which Rotifer species occurred in samples taken from Campus Lake, Jackson Co., IL. TAXA 01-Jul-97 17-Jul-97 31-Jul-97 02-Jul-98 16-Jul-98 31-Jul-98 08-Oct-97 25-Oct-97 17-Oct-98 04-Apr-98 20-Apr-98 06-Jun-97 18-Jun-97 17-Jan-98 04-Jun-98 21-Jun-98 07-Feb-98 21-Mar-98 14-Aug-97 27-Aug-97 10-Sep-97 24-Sep-97 08-Nov-97 22-Nov-97 06-Dec-97 13-Aug-98 26-Aug-98 12-Sep-98 26-Sep-98 16-May-97 22-May-97 04-May-98 23-May-98 Asplanchna X X XX XXXXXXXXXX XXXX Asplanchnopus X Brachionus angularis X XXXXX XX XX XXXXXXX Brachionus calyciflorus* XX X XXX X?X? X X Brachionus forbicula X Brachionus havanaensis XXXXXXXX X XXXXXX Brachionus pterodinoides XX Brachionus quadridentata X Brachionus rubens XXXXXX XXX X XX XXXXX? X?XXX XX Brachionus sp. A X Brachionus sp. B XX Brachionus sp. XX XXXX XX XX XXXXXX Conochilus XXXXXXXX XX X XXX XXXXXX Cephalodella XXXXX Filinia XXXXXX XXX Kellicottia spp. XXXX XXXXXXXXXXXX XXXXXX XXXX Keratella XXXXXXXXXXXXXXXXXXXXXXXXXXXXXXXXX Lecane sp. X Platyias patulus X XXX X Polyarthra XXXXXXXXXXXXXXXXX X XXXXXXX XXXX Trichocerca X XXXXXXXXXXX XXXXXXXXX

203