Prepared in cooperation with the Lake Maxinkuckee Environmental Council and the 

Marshall County Soil and Water Conservation District

Occurrence and Trends of Selected Nutrients, Other 

Chemical Constituents, Diatoms, and Cyanobacteria in 

Bottom Sediment, Lake Maxinkuckee, Northern Indiana

Scientific Investigations Report 2014–5199

U.S. Department of the Interior

U.S. Geological Survey
Front cover. Lake Maxinkuckee at sunset [photograph by Chi-sen (Jason) Chan, Culver Military Academy].

Back cover. Lake Maxinkuckee (photograph by Eric Looper, U.S. Geological Survey).
Occurrence and Trends of Selected 

Nutrients, Other Chemical Constituents, 

Diatoms, and Cyanobacteria in Bottom 

Sediment, Lake Maxinkuckee, Northern 

Indiana

By Kyle E. Juracek

Prepared in cooperation with the Lake Maxinkuckee Environmental Council and 

the Marshall County Soil and Water Conservation District

Scientific Investigations Report 2014–5199

U.S. Department of the Interior

U.S. Geological Survey
U.S. Department of the Interior

SALLY JEWELL, Secretary

U.S. Geological Survey

Suzette M. Kimball, Acting Director

U.S. Geological Survey, Reston, Virginia: 2015

For more information on the USGS—the Federal source for science about the Earth, its natural and living 

resources, natural hazards, and the environment, visit http://www.usgs.gov or call 1–888–ASK–USGS.

For an overview of USGS information products, including maps, imagery, and publications, 

visit http://www.usgs.gov/pubprod

To order this and other USGS information products, visit http://store.usgs.gov

Any use of trade, firm, or product names is for descriptive purposes only and does not imply endorsement by the 

U.S. Government.

Although this information product, for the most part, is in the public domain, it also may contain copyrighted materials 

as noted in the text. Permission to reproduce copyrighted items must be secured from the copyright owner.

Suggested citation:

Juracek, K.E., 2015, Occurrence and trends of selected nutrients, other chemical constituents, diatoms, and cyanobacteria in bottom sediment, Lake Maxinkuckee, northern Indiana: U.S. Geological Survey Scientific Investigations 

Report 2014–5199, 61 p., http://dx.doi.org/10.3133/sir20145199.

ISSN 2328-0328 (online)
iii

Acknowledgment

This study was made possible, in part, by support from the Lake Maxinkuckee Environmental 

Council and the Marshall County Soil and Water Conservation District. 
iv

Contents

Abstract...........................................................................................................................................................1

Introduction.....................................................................................................................................................1

Purpose and Scope ..............................................................................................................................3

Description of Lake Maxinkuckee and its Basin .............................................................................3

Methods...........................................................................................................................................................3

Sediment-Core Collection and Processing ......................................................................................3

Chemical Analyses ...............................................................................................................................5

Age Dating and Sedimentation Rate .................................................................................................6

Biological Analyses..............................................................................................................................7

Particle-size Analysis...........................................................................................................................7

Trend Analysis .......................................................................................................................................7

Sediment-Quality Guidelines........................................................................................................................7

Background Information for Selected Chemical Constituents, Diatoms, and Cyanobacteria..........8

Nutrients and Total Organic Carbon ..................................................................................................8

Trace Elements......................................................................................................................................9

Diatoms...................................................................................................................................................9

Cyanobacteria .......................................................................................................................................9

Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in 

Bottom Sediment..............................................................................................................................9

Nutrients and Total Organic Carbon ..................................................................................................9

Trace Elements....................................................................................................................................13

Diatoms.................................................................................................................................................24

Cyanobacteria .....................................................................................................................................29

Summary and Conclusions.........................................................................................................................33

References Cited..........................................................................................................................................33

Appendix........................................................................................................................................................39

Figures

1. Map showing location of Lake Maxinkuckee and land use (2011) in the Lake

Maxinkuckee Basin, northern Indiana......................................................................................2

2. Map showing location of bottom-sediment coring sites in Lake Maxinkuckee,

northern Indiana ...........................................................................................................................4

3. Graphs showing variation in total nitrogen concentrations with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013....................10

4. Graphs showing variation in total phosphorus and manganese concentrations 

with depth of bottom-sediment samples in box cores collected from coring 

sites LM–1, LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern 

Indiana, May 2013.......................................................................................................................11

5. Graph showing corn and soybean acres planted in Marshall County, Indiana,

1996–2012 .....................................................................................................................................12
v

6. Graphs showing variation in total organic carbon concentrations with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013. ..................12

7. Graphs showing variation in arsenic concentrations with depth of bottom-sediment

samples in box cores collected from coring sites LM–1, LM–2, LM–3, LM–4, and

LM–5 in Lake Maxinkuckee, northern Indiana, May 2013 ...................................................14

8. Graphs showing variation in cadmium concentrations with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013....................15

9. Graphs showing variation in chromium concentrations with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013....................16

10. Graphs showing variation in copper concentrations with depth of bottom-sediment

samples in box cores collected from coring sites LM–1, LM–2, LM–3, LM–4, and

LM–5 in Lake Maxinkuckee, northern Indiana, May 2013 ...................................................17

11. Graphs showing variation in lead concentrations with depth of bottom-sediment

samples in box cores collected from coring sites LM–1, LM–2, LM–3, LM–4, and

LM–5 in Lake Maxinkuckee, northern Indiana, May 2013 ...................................................18

12. Graphs showing variation in mercury concentrations with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013....................19

13. Graphs showing variation in nickel concentrations with depth of bottom-sediment

samples in box cores collected from coring sites LM–1, LM–2, LM–3, LM–4, and

LM–5 in Lake Maxinkuckee, northern Indiana, May 2013 ...................................................20

14. Graphs showing variation in selenium concentrations with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013....................21

15. Graphs showing variation in silver concentrations with depth of bottom-sediment

samples in box cores collected from coring sites LM–1, LM–2, LM–3, LM–4, and

LM–5 in Lake Maxinkuckee, northern Indiana, May 2013 ...................................................22

16. Graphs showing variation in zinc concentrations with depth of bottom-sediment

samples in box cores collected from coring sites LM–1, LM–2, LM–3, LM–4, and

LM–5 in Lake Maxinkuckee, northern Indiana, May 2013 ...................................................23

17. Graphs showing variation in occurrence of Achnanthidium minutissimum with

depth of bottom-sediment samples in box cores collected from coring sites LM–1,

LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013........25

18. Graphs showing variation in occurrence of Amphora ovalis with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013....................26

19. Graphs showing variation in occurrence of Asterionella formosa with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013....................27

20. Graphs showing variation in occurrence of Aulacoseira ambigua with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013....................28

21. Graphs showing variation in occurrence of Cyclotella bodanica with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013....................29
vi

22. Graphs showing variation in occurrence of Cyclotella ocellata with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013....................30

23. Graphs showing variation in occurrence of Cyclotella pseudostelligera with depth

of bottom-sediment samples in box cores collected from coring sites LM–1 and

LM–4 in Lake Maxinkuckee, northern Indiana, May 2013 ...................................................31

24. Graphs showing variation in occurrence of Fragilaria crotonensis with depth of

bottom-sediment samples in box cores collected from coring sites LM–1, LM–2,

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013....................31

25. Graphs showing variation in occurrence of Anabaena, Aphanizomenon, and

Gloeotrichia echinulata akinetes with depth of bottom-sediment samples in box

cores collected from coring sites LM–1, LM–2, LM–3, LM–4, and LM–5 in Lake

Maxinkuckee, northern Indiana, May 2013 ............................................................................32

Tables

1. Chemical analyses for bottom-sediment samples collected from Lake Maxinkuckee, 

northern Indiana, 2013 .................................................................................................................5

2. Sediment-quality guidelines for selected trace elements and associated 

bioaccumulation index.................................................................................................................8

3. National baseline concentrations for selected trace elements in sediment ...................13

4. Relative abundance of the most frequently encountered diatom species in bottomsediment samples collected from Lake Maxinkuckee, northern Indiana, May 2013 ......24

Appendix Tables

1–1. Latitude and longitude coordinates and water depth for bottom-sediment coring 

sites at Lake Maxinkuckee, northern Indiana, May 2013.....................................................40

1–2. Vertical profiles of water-quality parameters measured at bottom-sediment coring 

sites LM–1 through LM–5, Lake Maxinkuckee, northern Indiana, May 14, 2013 .............40

1–3. Activity of cesium-137, lead-210, and radium-226 in bottom-sediment samples 

collected from Lake Maxinkuckee, northern Indiana, May 2013........................................42

1–4. Percentage of sand, silt, and clay in bottom-sediment samples collected from 

Lake Maxinkuckee, northern Indiana, May 2013...................................................................44

1–5. Concentrations of nutrients, carbon, and trace elements for bottom-sediment 

samples collected from coring site LM–1 in Lake Maxinkuckee, northern Indiana, 

May 2013 ......................................................................................................................................45

1–6. Concentrations of nutrients, carbon, and trace elements for bottom-sediment 

samples collected from coring site LM–1G in Lake Maxinkuckee, northern 

Indiana, May 2013.......................................................................................................................46
vii

1–7. Concentrations of nutrients, carbon, and trace elements for bottom-sediment 

samples collected from coring site LM–2 in Lake Maxinkuckee, northern Indiana, 

May 2013 ......................................................................................................................................47

1–8. Concentrations of nutrients, carbon, and trace elements for bottom-sediment 

samples collected from coring site LM–2G in Lake Maxinkuckee, northern Indiana, 

May 2013 ......................................................................................................................................48

1–9. Concentrations of nutrients, carbon, and trace elements for bottom-sediment 

samples collected from coring site LM–3 in Lake Maxinkuckee, northern Indiana, 

May 2013 ......................................................................................................................................49

1–10. Concentrations of nutrients, carbon, and trace elements for bottom-sediment

samples collected from coring site LM–3G in Lake Maxinkuckee, northern Indiana,

May 2013 ......................................................................................................................................50

1–11. Concentrations of nutrients, carbon, and trace elements for bottom-sediment

samples collected from coring site LM–4 in Lake Maxinkuckee, northern Indiana,

May 2013 ......................................................................................................................................51

1–12. Concentrations of nutrients, carbon, and trace elements for bottom-sediment

samples collected from coring site LM–5 in Lake Maxinkuckee, northern Indiana,

May 2013 ......................................................................................................................................52

1–13. Concentrations of nutrients, carbon, and trace elements for bottom-sediment

samples collected from coring site LM–6G in Lake Maxinkuckee, northern Indiana,

May 2013 ......................................................................................................................................53

1–14. Abundant diatom species in bottom-sediment samples collected from coring 

site LM–1 in Lake Maxinkuckee, northern Indiana, May 2013............................................54

1–15. Abundant diatom species in bottom-sediment samples collected from coring 

site LM–1G in Lake Maxinkuckee, northern Indiana, May 2013 .........................................54

1–16. Abundant diatom species in bottom-sediment samples collected from coring 

site LM–2 in Lake Maxinkuckee, northern Indiana, May 2013. ..........................................55

1–17. Abundant diatom species in bottom-sediment samples collected from coring 

site LM–2G in Lake Maxinkuckee, northern Indiana, May 2013 .........................................55

1–18. Abundant diatom species in bottom-sediment samples collected from coring 

site LM–3 in Lake Maxinkuckee, northern Indiana, May 2013............................................56

1–19. Abundant diatom species in bottom-sediment samples collected from coring

site LM–3G in Lake Maxinkuckee, northern Indiana, May 2013 .........................................56

1–20. Abundant diatom species in bottom-sediment samples collected from coring 

site LM–4 in Lake Maxinkuckee, northern Indiana, May 2013............................................57

1–21. Abundant diatom species in bottom-sediment samples collected from coring 

site LM–5 in Lake Maxinkuckee, northern Indiana, May 2013............................................57

1–22. Abundant diatom species in bottom-sediment samples collected from coring

site LM–6G in Lake Maxinkuckee, northern Indiana, May 2013 .........................................58

1–23. Rare diatom species in bottom-sediment samples collected from 

Lake Maxinkuckee, northern Indiana, May 2013...................................................................59

1–24. Cyanobacterial akinetes in bottom-sediment samples collected from 

Lake Maxinkuckee, northern Indiana, May 2013. .................................................................60
viii

Conversion Factors

Multiply By To obtain

Length

centimeter (cm) 0.3937 inch (in.)

foot (ft) 0.3048 meter (m)

inch (in.) 2.54 centimeter (cm)

mile (mi) 1.609 kilometer (km)

Area

acre 4,047 square meter (m2)

acre 0.4047 hectare (ha)

acre 0.004047 square kilometer (km2)

square mile (mi2) 259.0 hectare (ha)

square mile (mi2) 2.590 square kilometer (km2) 

Mass

milligram per kilogram (mg/kg) 1.0 part per million (ppm)

percent concentration 10,000 milligram per kilogram (mg/kg)

Temperature in degrees Celsius (°C) may be converted to degrees Fahrenheit (°F) as follows:

°F=(1.8×°C)+32

Temperature in degrees Fahrenheit (°F) may be converted to degrees Celsius (°C) as follows:

°C=(°F-32)/1.8

Horizontal coordinate information is referenced to the North American Datum of 1983 (NAD 83).
Occurrence and Trends of Selected Nutrients, Other 

Chemical Constituents, Diatoms, and Cyanobacteria in 

Bottom Sediment, Lake Maxinkuckee, Northern Indiana

By Kyle E. Juracek

Abstract

Bottom-sediment cores collected in 2013 were used to 

investigate the recent and predevelopment (pre-1863) occurrence of selected nutrients (total nitrogen and total phosphorus), carbon, 39 trace elements, diatoms, cyanobacterial 

akinetes, and 3 radionuclides in the bottom sediment of Lake 

Maxinkuckee, a kettle lake in northern Indiana. Total nitrogen 

concentrations in the recent sediment (since about 1970) were 

variable with no consistent trend indicated. Total phosphorus 

concentrations in the recent sediment generally were uniform 

from about 1970 to about 2000 and indicated consistent inputs 

to the lake during that time. Subsequently, the history of total 

phosphorus deposition apparently was obscured by postdepositional upward diffusion. 

Trace-element concentrations in the bottom sediment 

of Lake Maxinkuckee generally were not cause for concern. 

Elevated concentrations of cadmium, copper, lead, mercury, 

and zinc in the recent sediment, compared to the predevelopment sediment, indicated likely human-related contamination; 

however, the trace-element concentrations were less than 

probable-effects guidelines (available for nine trace elements), 

which represent the concentrations above which toxic aquatic 

biological effects usually or frequently occur. Arsenic concentrations typically exceeded the threshold-effects guideline, which represents the concentration above which toxic 

aquatic biological effects occasionally occur, in the recent and 

predevelopment sediment. The arsenic likely originated from 

natural sources. Lead concentrations historically exceeded the 

threshold-effects guideline, but since had decreased below it 

in the recent sediment at most coring sites. The decreasing 

trend likely was indicative of the effect of the phase out of 

leaded gasoline. 

Biological indicators in the bottom sediment provided 

evidence for an improving, or at least not worsening, lake 

trophic condition. The occurrence of multiple diatom species, 

none of which were overwhelmingly dominant, was indicative 

of a minimally contaminated lake ecosystem. The combined 

evidence of several diatom species in the recent sediment 

indicated that the lake had not become more productive in 

recent decades. The combined evidence provided by akinetes 

for three cyanobacterial genera in the recent and predevelopment sediment indicated similar nutrient conditions in the 

lake during the past 40 years and possibly back to at least the 

mid-1800s. 

Introduction

Lake Maxinkuckee is a kettle lake located in Marshall 

County, northern Indiana (fig. 1). The lake is valued for the 

recreational and educational opportunities it provides and is of 

central importance to the economic well-being of the town of 

Culver (JF New & Associates, 2006), which is located along 

the northwest shore (fig. 1). Effective management to preserve 

and protect the lake requires an understanding of past and 

present lake conditions. Such an understanding is attainable, 

in part, through an analysis of the sediment deposited on the 

lakebed. Information obtained from an analysis of bottomsediment cores can be used to assess current and historical 

water-quality and sediment-quality conditions, assess habitat quality, help identify constituents of concern in the lake, 

understand the trophic history of the lake, establish a baseline 

of lake and basin conditions, and assess the effects of human 

activity on the condition of the lake. 

A 2-year study by the U.S. Geological Survey (USGS), 

in cooperation with the Lake Maxinkuckee Environmental 

Council and the Marshall County Soil and Water Conservation 

District, was begun in 2013 to investigate the past and present 

condition of Lake Maxinkuckee through an analysis of the 

lakebed sediment. Specific objectives of the study were to: 

1. Determine the occurrence and temporal trends of selected 

chemical constituents in the bottom sediment; 

2. Assess the quality of the bottom sediment with respect to 

available sediment-quality guidelines; and

3. Determine the occurrence, relative abundance, and trends 

of diatoms and cyanobacterial akinetes in the bottom sediment as an indication of the trophic history of the lake. 
2 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Figure 1. Location of Lake Maxinkuckee and land use (2011) in the Lake Maxinkuckee Basin, northern Indiana.

ILLINOIS

INDIANA

MICHIGAN

South Bend

Chicago

Aurora

Gary

Plymouth

Rochester

Winamac

Lake

Michigan

0 25 50 MILES

0 25 50 KILOMETERS

Map area

Lake

Maxinkuckee

Base modified from U.S. Geological Survey digital data, 2011 

86°26’ 86°24’ 86°22’ 86°20’

41°14’

41°12’

41°10’

Culver

Culver

Academies

MARSHALL COUNTY

FULTON COUNTY

Clifton Ditch

Wolf Creek

0 0.5 1 1.5 MILES

0 0.5 1 1.5 KILOMETERS

Basin boundary

Water

Wetlands

Forest

Grassland

Cropland

Developed

EXPLANATION

Land-cover category

Curtiss Ditch Curtiss Ditch

Cowan DitchCowan Ditch

Kline DitchKline Ditch

Thompson DitchThompson Ditch

Wilson DitchWilson Ditch

Wagoner Ditch

Land-cover data from U.S. Geological Survey National

Land Cover dataset, 30-meter resolution, 2011

Wilson Ditch Wilson Ditch
Methods 3

Purpose and Scope

The purpose of this report is to present the results of the 

USGS study to assess the condition of Lake Maxinkuckee by 

an analysis of bottom-sediment cores that were collected at six 

sites in 2013. A total of nine cores were analyzed for several 

chemical and biological constituents. Locally, the information 

provided in this report will help improve the understanding 

of current and historical lake conditions and allow for better informed decisions regarding the future management of 

the lake and its basin. Nationally, the methods and results 

presented in this report provide guidance and perspective for 

future studies concerned with the issues of sediment quality, contaminant loading, and trophic status as related to the 

environmental condition of lakes and their ability to meet the 

needs of wildlife and humans. 

Description of Lake Maxinkuckee and its Basin

Lake Maxinkuckee (fig. 1) is a kettle lake that was 

created about 15,000 years ago when the glaciers of the last 

Ice Age retreated (Schneider, 1966; Schneider and Johnson, 1966). A kettle lake is formed when an ice block from 

a retreating glacier is left behind and melts resulting in a 

depression on the land surface that fills with water (Wetzel, 

2001). Lake Maxinkuckee has a surface area of 1,854 acres 

and measures 2.6 miles (mi) in length and 1.6 mi in width. 

Water depth in the lake averages 24 feet (ft) with a maximum 

depth of 88 ft. Primary tributaries to the lake are Curtiss Ditch, 

Kline Ditch, and Wilson Ditch (fig. 1). Underground springs 

also feed into the lake (JF New & Associates, 2006). Based 

on multiple water-quality criteria (for example, transparency, 

nutrient content, and chlorophyll-a content), the lake has 

been classified as mesotrophic (JF New & Associates, 2006). 

A mesotrophic lake is characterized by moderate productivity with moderate nutrient concentrations (Wetzel, 2001). 

Crisman (1986), based on an analysis of algal data (collected 

periodically from 1899 to 1978), concluded that the lake was 

moderately productive and the summer algal community was 

dominated by cyanobacteria since at least 1899. More recently, 

using multiple water-quality criteria, the lake was classified as 

oligotrophic (Indiana Department of Environmental Management, 2012). An oligotrophic lake is characterized by low 

productivity with low nutrient concentrations (Wetzel, 2001). 

The Lake Maxinkuckee Basin is an area of about 13.5 mi2

located in southwest Marshall County and northwest Fulton 

County, Indiana (fig. 1). Physiographically, the basin is located 

along the western edge of the Maxinkuckee Moraine, which 

was formed by the advance and subsequent stagnation of the 

Saginaw Lobe during the latter part of the Wisconsin Age glaciation (Schneider and Johnson, 1966). Topographically, the 

land surface in the Maxinkuckee Moraine is a diverse terrain 

of moderate relief with kames, moraines, outwash plains, and 

kettles (Wayne, 1966; Gray, 2000). Slopes range from nearly 

level to strongly sloping. In general, soils in the basin are 

sandy at the surface and well drained (Smallwood, 1980; Furr, 

1987). Bedrock in the basin is shale of Devonian and Mississippian age (Gutschick, 1966). 

The climate, as characterized using the Koppen climate 

classification system (Peel and others, 2007), is moist with 

warm to hot summers and cold winters. Mean annual precipitation at Plymouth, Indiana, located about 10 mi northeast of 

Lake Maxinkuckee (fig. 1), is about 40 inches (in.; period of 

record 1981–2010; National Climatic Data Center, 2013). 

Land use (2011) in the basin is diverse (fig. 1). Agricultural land use (cropland and grassland) accounts for about 

43 percent of the basin. Wetlands and open water (including Lake Maxinkuckee) cover about 26 percent of the basin. 

Developed land, which includes the town of Culver, the Culver Academies, and residences along the lakeshore, accounts 

for about 15 percent of the basin. Most of the developed land 

is low-intensity residential land use and urban parkland. About 

16 percent of the basin is forested (Jin and others, 2013). To 

reduce sediment and nutrient inputs to the lake, constructed 

wetlands were completed on Wilson Ditch in 1987, Curtiss Ditch in 1990, and Kline Ditch in 1992 (fig. 1) (Kathy 

Clark, Lake Maxinkuckee Environmental Council, written 

commun., 2013). 

Wastewater treatment in the basin differs by location. For 

the town of Culver, including the Culver Academies (fig. 1), 

wastewater is collected, treated, and discharged downstream 

from Lake Maxinkuckee. Along the east side of the lake, 

wastewater is collected and treated in a wetland. Throughout 

the remainder of the basin, wastewater is treated using septic 

systems (JF New & Associates, 2006). In 2011, most of the 

residences along the lakeshore that previously used septic systems were converted to Culver’s wastewater treatment system 

(Kathy Clark, Lake Maxinkuckee Environmental Council, oral 

commun., 2014). 

Methods

The objectives of this study were accomplished by the 

analysis of bottom-sediment cores collected at six sites in the 

lake. A description of the core collection and processing and 

the chemical, biological, and physical analyses completed is 

provided in the following sections. 

Sediment-Core Collection and Processing

In May 2013, bottom-sediment cores were collected 

at six sites (fig. 2) within Lake Maxinkuckee. The coring 

sites were selected to provide representative information on 

conditions throughout the lake and to provide an indication of 

spatial variability. The specific objectives of the coring were 

to collect undisturbed cores of the most recently deposited 

sediment and to collect deeper cores to provide an indication 

of conditions before substantial human activity in the area. 

These respective objectives were accomplished using a box 
4 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

corer and a gravity corer. At sites LM–1, LM–2, and LM–3, a 

box core and a gravity core were collected. At sites LM–4 and 

LM–5, a box core was collected. A gravity core was collected 

at site LM–6, which was located in the deepest part of the 

lake. The latitude and longitude for each site, obtained using 

global positioning system (GPS) technology, are provided in 

table 1–1 in the appendix at the back of this report. All cores 

were collected from a pontoon boat. 

The box corer, which has a steel jaw activated by a 

spring-loaded pin, was slowly lowered by rope to the lakebed 

at each site. After the corer settled into the bottom sediment, 

a tug of the rope released the pin causing the steel jaw to shut 

and capture the core. The inside dimensions of the square 

transparent acrylic liner used to hold the sample were 14 centimeters (cm) long by 14 cm wide by 50 cm deep. 

The gravity corer was lowered by cable to a depth of 

about 5 ft above the lakebed and then released to penetrate 

into the bottom sediment. The liner used for the gravity cores 

was cellulose acetate butyrate transparent tubing with an 

inside diameter of about 6.7 cm. 

When using a gravity corer, a phenomenon referred to as 

“core shortening” may occur that results in a recovered sediment core the length of which is less than the actual thickness 

of sediment penetrated (Emery and Hulsemann, 1964). Core 

shortening is caused by friction of the sediment against the 

inner wall of the core liner as the corer penetrates the sediment 

(Emery and Hulsemann, 1964; Hongve and Erlandsen, 1979; 

Blomqvist, 1985; Blomqvist and Bostrom, 1987). In “normal” 

lake-bottom sediment, which is characterized by uniform 

texture with decreasing water content at depth, core shortening 

results in a core that provides a thinned but complete representation of all of the sediment layers that were penetrated 

(Emery and Hulsemann, 1964; Hongve and Erlandsen, 1979). 

In this study, a comparison of the length of core recovered by 

gravity coring to the thickness of sediment penetrated indicated that core recovery ranged from 31 to 52 percent with an 

average of 38 percent. The thickness of sediment penetrated 

was computed as the total depth of corer penetration (as measured from the water surface) minus the water depth. 

Following collection, the cores were processed to obtain 

samples for specific depth intervals. The box cores were processed immediately after collection at the lake. For each box 

core, the sediment was sampled into plastic jars for successive 

2-centimeter (cm) intervals throughout the entire length of the 

core (that is, 0–2 cm, 2–4 cm, and so on). The 2-cm samples 

were transported to the USGS laboratory in Lawrence, Kansas, 

LM–1

LM–2

LM–3

LM–4

LM–5

LM–6

Lake

Maxinkuckee

Base from U.S. Department of Agriculture, Farm Service 

Agency-Aerial Photography Field Office, National Agriculture 

Inventory Program, 2012, 1:12,000

Culver

Culver

Academies

86°26’ 86°25’ 86°24’ 86°23’

41°13’

41°12’

41°11’

0 0.5 1 MILE

0 0.5 1 KILOMETER

EXPLANATION

Bottom-sediment coring sites

Predevelopment sediment (more than 150 years old)

Recent and predevelopment sediment

Recent sediment (less than 60 years old)

Figure 2. Location of bottomsediment coring sites in Lake 

Maxinkuckee, northern Indiana.
Methods 5

where they were refrigerated (at 5 degrees Celsius [°C]) until 

final processing. 

The gravity cores were transported to the USGS laboratory in Lawrence, Kansas, where they were stored vertically 

and refrigerated (at 5 °C) until processed (within 1 week of 

collection). The core liners were cut lengthwise in two places 

180 degrees apart. The cuts were completed with a 4-in. 

hand-held circular saw with the blade set at a depth to minimize penetration of the sediment in the cores. The cores were 

split in half by pulling a tightly held nylon string through the 

length of the cores and allowing the halves to separate. Once 

split, the relatively undisturbed inner parts of the cores were 

exposed for examination and sampling. To provide sufficient 

sample material for all of the planned analyses, the sediment 

was sampled into plastic jars for successive 10-cm intervals 

throughout the entire length of each core. All samples were 

refrigerated (at 5 °C) until final processing. 

Final processing involved two steps. First, each sample 

was homogenized using a clean plastic spatula. Second, 

each sample was subdivided into six subsamples for subsequent shipment to different laboratories for chemical, biological, and physical analyses (see details provided in the 

following sections). 

At coring sites LM–1 to LM–5, water-quality data were 

collected for the water column using a 7-parameter YSI 

6600V2 water-quality monitor (YSI, 2013). The properties 

measured were pH, temperature, specific conductance, dissolved oxygen, turbidity, chlorophyll (total), and cyanobacteria. These data are provided (see table 1–2 in the appendix) but 

not discussed. 

Chemical Analyses

The bottom-sediment samples were analyzed for nutrients 

(total nitrogen and total phosphorus), inorganic and total carbon, 39 trace elements, and 3 radionuclides. A complete list of 

the chemical constituents for which analyses were completed 

is provided in table 1. With the exception of total nitrogen, 

51 samples were analyzed for the various constituents. For 

total nitrogen, 45 samples were analyzed. Analyses of the 

samples for total phosphorus, inorganic and total carbon, and 

39 trace elements were performed at USGS laboratories in 

Denver, Colorado, using the methods described by Taggart 

(2002). Analyses for total nitrogen (that is, the sum of total 

Kjeldahl nitrogen and nitrate plus nitrite) were performed at 

TestAmerica Laboratories, Inc. in Denver, Colorado, using 

the methods described by the U.S. Environmental Protection 

Agency (1983). Radionuclide analyses were performed at a 

USGS laboratory in St. Petersburg, Florida, using the methods 

described by Marot and Smith (2012). 

Quality control (QC) for the various chemical constituents was provided by additional analyses. For phosphorus 

and most of the trace elements, QC included the analysis 

of 11 reference samples and 2 duplicate analyses of core 

samples. For phosphorus, analysis of the reference samples 

Table 1. Chemical analyses for bottom-sediment samples 

collected from Lake Maxinkuckee, northern Indiana, 2013.

[Number in parentheses is the method reporting limit for each constituent. 

mg/kg, milligrams per kilogram; %, percent dry weight; dpm/g, disintegrations per minute per gram]

Nutrients

Nitrogen, total Kjeldahl 

(25 mg/kg)

Phosphorus, total (5 mg/kg)

Nitrogen, nitrate plus nitrite 

(0.3 mg/kg)

Carbon

Carbon, total (0.05%) Carbon, inorganic (0.01%)

Trace elements

Aluminum (50 mg/kg) Mercury (0.01 mg/kg)

Antimony (0.04 mg/kg) Molybdenum (0.05 mg/kg)

Arsenic (1 mg/kg) Nickel (0.3 mg/kg)

Barium (0.25 mg/kg) Niobium (0.1 mg/kg)

Beryllium (0.03 mg/kg) Potassium (15 mg/kg)

Bismuth (0.06 mg/kg) Rubidium (0.014 mg/kg)

Cadmium (0.007 mg/kg) Scandium (0.04 mg/kg)

Calcium (100 mg/kg) Selenium (0.1 mg/kg)

Cerium (0.1 mg/kg) Silver (0.01 mg/kg)

Cesium (0.003 mg/kg) Sodium (25 mg/kg)

Chromium (0.5 mg/kg) Strontium (0.8 mg/kg)

Cobalt (0.03 mg/kg) Sulfur (0.05%)

Copper (2 mg/kg) Thallium (0.08 mg/kg)

Gallium (0.015 mg/kg) Thorium (0.1 mg/kg)

Iron (50 mg/kg) Titanium (40 mg/kg)

Lanthanum (0.05 mg/kg) Uranium (0.02 mg/kg)

Lead (0.4 mg/kg) Vanadium (0.15 mg/kg)

Lithium (0.3 mg/kg) Yttrium (0.05 mg/kg)

Magnesium (6 mg/kg) Zinc (3 mg/kg)

Manganese (0.7 mg/kg)

Radionuclides

Cesium-137 (0.05 dpm/g) Radium-226 (0.05 dpm/g)

Lead-210 (0.05 dpm/g)

indicated that the measured concentrations were, on average, 

within 9 percent of the most probable value (MPV). Measured 

concentrations in the reference samples for arsenic, cadmium, 

chromium, copper, lead, nickel, and zinc were, on average, 

within about 10 percent (or less) of the MPV. However, for 

silver, measured concentrations were, on average, within 

104 percent of the MPV and indicated the difficulty in detecting concentrations near the method reporting limit. Measured 

concentrations in four reference samples for mercury and 

selenium were, on average, within 13 percent and 4 percent 

of the MPV, respectively. The duplicate analyses (core LM–2, 
6 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

interval 24–26 cm; core LM–4, interval 20–22 cm) typically 

were within 10 percent of the original analyses. 

Quality control for nitrogen was provided by the analysis 

of reference samples and blank samples. For Kjeldahl nitrogen and nitrate plus nitrite, three reference samples and three 

blank samples were analyzed. Measured concentrations in the 

reference samples for Kjeldahl nitrogen and nitrate plus nitrite 

were, respectively, within 3 percent and 9 percent of the MPV. 

With one exception, measured concentrations in the blank 

samples were less than the method reporting limits. For the 

one exception, a low concentration of nitrate plus nitrite was 

measured (0.41 milligram per kilogram [mg/kg]). 

Quality control for the radionuclides was provided by 

the duplicate analysis of three samples (core LM–1, interval 

8–10 cm; core LM–4, interval 8–10 cm; core LM–5, interval 

0–2 cm). On average, the duplicate results for cesium-137 

(137Cs), lead-210 (210Pb), and radium-226 (226Ra) were within 

9 percent, 2 percent, and 3 percent of the original results, 

respectively. Results for the duplicate analyses are provided in 

table 1–3 in the appendix. 

Age Dating and Sedimentation Rate

Age dating of the bottom-sediment samples from all 

six coring sites (fig. 2) was accomplished by determining the 

activity of 137Cs, 210Pb, and 226Ra. 137Cs is a radionuclide that is 

a byproduct of aboveground nuclear weapons testing. Measurable activity of 137Cs first appeared in the atmosphere about 

1952, peaked during 1963–64, and has since declined (Ritchie 

and McHenry, 1990). Measurable activity in soils began about 

1954 (Wise, 1980). 137Cs is an effective marker for age dating 

bottom sediment in lakes and reservoirs that existed before 

1963–64 (Van Metre and others, 1997). The activity of 137Cs 

in a sediment core also can be used to demonstrate that the 

sediment is relatively undisturbed if the 1963–64 peak is welldefined and a generally uniform, exponential decrease in 137Cs 

activity follows the peak. 

Lead-210 is a radionuclide that occurs naturally in the 

uranium-238 decay series. As 226Ra in soils decays to radon222 (222Rn), some of the 222Rn escapes to the atmosphere 

where it quickly decays through two short-lived radionuclides 

to 210Pb. The fallout of 210Pb from the atmospheric 222Rn results 

in more 210Pb in surface soil than can be accounted for by the 

in situ decay of 226Ra in the soil. As surface sediments in a lake 

are gradually buried and isolated from additional fallout, the 

“unsupported” 210Pb decays with a half-life of 22.3 years. The 

relation between unsupported 210Pb and 226Ra in the lakebed 

sediment can be used to estimate the time since the sediment 

was deposited and buried (Appleby and Oldfield, 1992). Using 

this relation, lakebed sediments can be dated as far back as 

150 years (Olsson, 1986; Appleby, 2001; Smol, 2008). When 

the activity of 210Pb and 226Ra in a lakebed sediment sample is 

equal (allowing for analytical variability), it may be concluded 

that all of the unsupported 210Pb has decayed, and the sediment 

is older than 150 years. In this study, a constant initial activity 

of unsupported 210Pb for each interval of the sediment core was 

assumed to be equal to the activity of the most recently deposited interval (Appleby and Oldfield, 1983, 1992). The age of 

each interval was estimated using the following equation:

t = (1/k)ln(Co/Cx), (1)

where

t is the age of the interval (in years), 

k is the 210Pb radioactive decay constant 

(0.03114), 

Co is the initial unsupported 210Pb activity, and 

Cx is the unsupported 210Pb activity for the 

interval being dated (Appleby and 

Oldfield, 1978). 

In this study, ages were estimated primarily using 210Pb 

because (1) with the exception of coring site LM–3, the 137Cs 

peak was not measured in the sediment cores, and (2) 137Cs 

activity profiles for natural lakes with low sedimentation rates 

may be misleading or unusable (Van Metre and others, 2004). 

The 137Cs, 210Pb, and 226Ra activity profiles for all six coring 

sites are provided in table 1–3 in the appendix. 

Lead-210 dates assigned to individual core intervals 

were approximate. The uncertainty associated with the dates 

increases as the years before present increase. In general, the 

estimated dates were in agreement with ages inferred based 

on the total lead concentration profile for each core. In this 

report, “recent” sediment was defined as sediment for which 

137Cs activity was detected. The recent sediment was less than 

60 years old. “Predevelopment” sediment was defined as 

sediment for which 137Cs activity was not detected, and 210Pb 

and 226Ra activity were in secular equilibrium (that is, all of 

the unsupported 210Pb had decayed). Predevelopment sediment 

generally was older than 150 years (that is, pre-1863). 

Some of the predevelopment sediment samples analyzed 

may be considerably older than 150 years. For example, 

assuming a constant sedimentation rate (estimated from the 

box cores) and accounting for core shortening, sediment 

samples analyzed from the 50–60 cm depth for the gravity 

cores collected at sites LM–1 and LM–3 (fig. 2) may be more 

than 200 years old. Further, sediment samples analyzed from 

the 70–80 cm depth for the same gravity cores may be more 

than 300 years old. 

Mean annual sedimentation rate was estimated for each 

box core as the total thickness of the deposited sediment 

divided by the number of years of deposition. Respectively, 

for coring sites LM–1, LM–2, LM–3, and LM–4 (fig. 2), the 

mean annual sedimentation rates were about 0.7, 0.8, 0.6, and 

0.7 centimeters per year (cm/yr). For coring site LM–5 (fig. 2), 

the mean annual sedimentation rate was estimated to be about 

1.4 cm/yr. However, the relatively short length of the box core 

and irregularities in the 210Pb data for this site rendered the 

sedimentation rate less certain. In comparison, Crisman (1986) 

estimated the sedimentation rate for 1974–84 at a site in the 

northern part of Lake Maxinkuckee to be about 0.4 cm/yr. 
Sediment-Quality Guidelines 7

Biological Analyses

To investigate the trophic condition and history of Lake 

Maxinkuckee, the same 51 sediment samples used for chemical analyses were analyzed for diatoms and cyanobacterial 

akinetes. Diatoms are microscopic algae that have a siliceous 

shell (frustule), consisting of two halves (valves), that may 

preserve in sediment. Because many diatom species are sensitive to changes in environmental conditions (for example, 

pH, light, temperature, and concentrations of nutrients and 

trace elements), changes in diatom species composition and 

abundance can be used as indicators of environmental changes 

(Dixit and others, 1992; Smol and Stoermer, 2010). Several 

diatom species are indicators of eutrophic (nutrient rich, high 

primary productivity) or oligotrophic (nutrient poor, low 

primary productivity) conditions (van Dam and others, 1994; 

Smol and Stoermer, 2010). Analysis of the sediment samples 

for diatoms was performed by Bio-Limno Research and 

Consulting, Inc., Halifax, Nova Scotia, Canada. For QC, three 

sediment samples (core LM–1, interval 0–2 cm; core LM–3G, 

interval 30–40 cm; core LM–6G, interval 60–70 cm) were 

counted for dominant species by PhycoTech, Inc., St. Joseph, 

Michigan, using the same prepared slides. On average, the 

duplicate counts for dominant species were within 3 percent. 

Cyanobacteria (also called blue-green algae) commonly 

are indicative of eutrophic conditions in lakes and reservoirs (Wetzel, 2001; Smol, 2008). Akinetes are thick-walled, 

resistant cells that represent the resting stage of cyanobacteria 

(Adams and Duggan, 1999; Wetzel, 2001). They provide an 

approximate estimate of past abundance of akinete-producing 

cyanobacteria (Rasanen and others, 2006a) and can be used to 

investigate the trophic history of a lake (van Geel and others, 1994; Kling, 1998). Akinetes preserve well in sediment 

as evidenced by past studies that documented preservation 

for periods ranging from decades (Livingstone and Jaworski, 

1980; Kling, 1998; Rasanen and others, 2006a) to centuries 

(Cronberg, 1986; van Geel and others, 1994). Analysis of the 

sediment samples for akinetes was performed by PhycoTech, 

Inc., St. Joseph, Michigan. 

Particle-size Analysis

Particle-size analyses were completed to determine the 

percentage of sand (particles greater than 63 micrometers 

[μm] in size), silt (particles 4 to 63 μm in size), and clay 

(particles less than 4 μm in size) in the bottom sediment. A 

total of 28 samples were analyzed at the USGS Geosciences 

and Environmental Change Science Center Soils Laboratory 

in Denver, Colorado, using a Malvern Mastersizer 2000 laser 

particle-size analyzer (Malvern, 2013). QC was provided by 

the duplicate analysis of three samples. On average, the duplicate results were within 9 percent. The particle-size and QC 

data are provided in table 1–4 in the appendix. 

Trend Analysis

Temporal trends in constituent concentrations (as 

compared to depth in the sediment profile) were assessed 

for nitrogen, phosphorus, the trace elements for which 

sediment-quality guidelines were available (table 2), diatoms, 

and cyanobacteria. A trend was described as “increasing” if 

constituent concentrations increased from the bottom (oldest) 

to the top (youngest) part of a sediment core. Conversely, a 

trend was described as “decreasing” if constituent concentrations decreased from the bottom to the top of a sediment 

core. For the chemical constituents, a trend was described as 

“pronounced” if the change in constituent concentrations was 

beyond the variability that could be explained by analytical 

variance (defined here as the mean constituent concentration 

in the sediment core plus or minus 10 percent). A trend was 

described as “possible” if most or all of the change in constituent concentrations was within the concentration range that 

could be explained by analytical variance. 

Sediment-Quality Guidelines

The U.S. Environmental Protection Agency (EPA) has 

adopted nonenforceable sediment-quality guidelines (SQGs) 

in the form of level-of-concern concentrations for several 

trace elements (U.S. Environmental Protection Agency, 1997). 

These level-of-concern concentrations were derived from 

biological-effects correlations made based on paired onsite 

and laboratory data to relate incidence of adverse biological 

effects in aquatic organisms to dry-weight sediment concentrations. Two such level-of-concern guidelines adopted by the 

EPA are referred to as the threshold-effects level (TEL) and 

the probable-effects level (PEL). The TEL is assumed to represent the concentration below which toxic aquatic biological 

effects rarely occur. In the range of concentrations between the 

TEL and PEL, toxic effects occasionally occur. Toxic effects 

usually or frequently occur at concentrations above the PEL. 

The EPA cautions that the TEL and PEL guidelines are 

intended for use as screening tools for possible hazardous concentrations of chemicals and are not regulatory criteria. This 

cautionary statement is made because, although biologicaleffects correlation identifies level-of-concern concentrations 

associated with the likelihood of adverse organism response, 

the comparison may not demonstrate that a particular chemical is solely responsible. In fact, biological-effects correlations 

may not indicate direct cause-and-effect relations because 

sediments may contain a mixture of chemicals that contribute 

to the adverse effects to some degree. Thus, for any given site, 

these guidelines may be over or underprotective (U.S. Environmental Protection Agency, 1997). 

MacDonald and others (2000) developed consensusbased SQGs for several trace elements that were computed as 
8 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

the geometric mean of several previously published SQGs. 

The consensus-based SQGs consist of a threshold-effect concentration (TEC) and a probable-effect concentration (PEC). 

The TEC represents the concentration below which adverse 

biological effects are not expected to occur, whereas the PEC 

represents the concentration above which adverse biological effects are expected to occur more often than not. An 

evaluation of the reliability of the SQGs indicated that most 

of the individual TECs and PECs provide an accurate basis 

for predicting the presence or absence of sediment toxicity 

(MacDonald and others, 2000). A comparison of the two sets 

of trace-element SQGs indicated some differences (table 2). 

The largest difference was for the zinc PEC and PEL. In this 

case, the PEC (459 mg/kg) was about 69 percent larger than 

the PEL (271 mg/kg). 

For each trace element for which SQGs were available, the larger of the two options for threshold effects and 

probable effects was selected for the purpose of assessing 

sediment quality (see shaded values in table 2). The options 

used to assess sediment quality are hereafter referred to as 

the threshold-effects guidelines (TEGs), which represent the 

concentrations above which toxic biological effects occasionally occur, and the probable-effects guidelines (PEGs), which 

represent the concentrations above which toxic biological 

effects usually or frequently occur. The guidelines used were 

selected to provide a less stringent assessment. 

Background Information for Selected 

Chemical Constituents, Diatoms, and 

Cyanobacteria

Nutrients and Total Organic Carbon

Nutrients, such as nitrogen and phosphorus, are necessary for growth and reproduction of plants. In most freshwater 

environments, phosphorus is one of the principal limiting 

factors for primary production (Hakanson and Jansson, 1983; 

Wetzel, 2001). If phosphorus concentrations are too high, algal 

growth may become excessive, and possibly result in the production of algal toxins and taste-and-odor compounds. Additionally, excessive algal growth may be detrimental to aquatic 

life and limit recreational use of a lake. Even small increases 

in phosphorus can cause increases in algal biomass provided 

that light limitation is not an issue (Dillon and Rigler, 1974; 

Jones and Bachmann, 1976; Jones and others, 2008). Primary 

human-related sources of nutrients include fertilizer application, livestock production, and sewage-treatment plants. 

Total organic carbon (TOC), an approximate determination of total organic material in a sediment sample, is important because various organic solutes can form complexes, 

which in turn affect trace-element solubilities (Hem, 1989). 

The TOC content of sediment also is important because many 

contaminants specifically sorb to the organic material in sediment (Karickhoff, 1984; Horowitz, 1991). 

Table 2. Sediment-quality guidelines for selected trace elements and associated bioaccumulation index.

[Values in milligrams per kilogram. Shading represents guidelines to which sediment concentrations were compared in this report. EPA, U.S. Environmental 

Protection Agency; TEL, threshold-effects level; PEL, probable-effects level; TEC, threshold-effect concentration; PEC, probable-effect concentration;

 --, not available]

Trace element EPA (1997) MacDonald and others (2000) Bioaccumulation 

index1 TEL PEL TEC PEC

Arsenic 7.24 41.6 9.79 33.0 moderate

Cadmium 0.676 4.21 0.99 4.98 moderate

Chromium 52.3 160 43.4 111 moderate

Copper 18.7 108 31.6 149 high

Lead 30.2 112 35.8 128 moderate

Mercury 0.13 0.696 0.18 1.06 high

Nickel 15.9 42.8 22.7 48.6 moderate

Silver 0.733 1.77 -- -- moderate

Zinc 124 271 121 459 high

1

Bioaccumulation index information for trace elements from Pais and Jones (1997).
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 9

Trace Elements

Trace elements are important determinants of sediment 

quality because of their potential toxicity to living organisms (Forstner and Wittmann, 1981; Smol, 2008; Luoma and 

Rainbow, 2008). Trace elements may be defined as elements 

that typically are present in the environment in relatively low 

(less than 0.1 percent) concentrations (Pais and Jones, 1997; 

Adriano, 2001). Using this definition, most of the elements 

analyzed in this study may be considered trace elements. 

Exceptions, which are some of the abundant rock-forming elements, include aluminum and iron (Adriano, 2001). 

Trace elements in sediment originate naturally from the 

rock and soil within a basin. Elevated concentrations of sediment-associated trace elements may be attributable to several 

human-related sources including fertilizers, liming materials, 

pesticides, irrigation water, animal and human wastes, coal 

combustion residues, leaching from landfills, mining, metalsmelting industries, and automobile emissions (Forstner and 

Wittmann, 1981; Davies, 1983; Adriano, 2001; Luoma and 

Rainbow, 2008). 

The health of living organisms is dependent on a sufficient intake of various trace elements. Many elements, such 

as cobalt, copper, iron, manganese, and zinc, are essential for 

plants, animals, and humans. Other elements, such as arsenic 

and chromium, are required by animals and humans, but are 

not essential for plants. Nonessential elements for plants, animals, and humans include cadmium, mercury, and lead (Lide, 

1993; Pais and Jones, 1997; Adriano, 2001; Marmiroli and 

Maestri, 2008). 

Toxicity is a function of several factors including the type 

of organism, availability of a trace element in the environment, 

and its potential to bioaccumulate once in the food chain. The 

daily intake of trace elements by animals and humans may be 

classified as deficient, optimal, or toxic. Most, if not all, trace 

elements may be toxic in animals and humans if the concentrations are sufficiently large (Pais and Jones, 1997; Smol, 

2008; Luoma and Rainbow, 2008). Information on the bioaccumulation index (Pais and Jones, 1997) for trace elements 

with available SQGs is provided in table 2. The bioaccumulation index indicates the relative potential of a trace element to 

bioaccumulate in organisms. 

Diatoms

Diatoms occur in almost all aquatic environments. 

Generally, in eutrophic water, the diatom community will 

be dominated by a few abundant species tolerant of nutrient 

and organic enrichment. In contrast, diatom communities in 

uncontaminated water (free of sewage or other organic enrichment caused by waste discharge) consist of a greater number 

of more equally abundant species (U.S. Environmental Protection Agency, 1977; John Smol, Queen’s University, Kingston, 

Ontario, Canada, written commun., 2007). Diatoms respond 

quickly to the onset of, and recovery from, eutrophication 

(Hall and Smol, 2010). 

Cyanobacteria

Cyanobacteria are common in freshwater ecosystems 

(Chorus and Bartram, 1999; Wetzel, 2001) and often are 

associated with eutrophic conditions (Smol, 2008). Abundant 

growth of cyanobacteria is a concern because it can limit 

recreational use of a lake, cause taste-and-odor problems for 

water suppliers, and produce toxins (for example, microcystins) which are a concern for human health (Chorus and 

Bartram, 1999). 

Occurrence and Trends of Selected 

Chemical Constituents, Diatoms, and 

Cyanobacteria in Bottom Sediment

This section describes the occurrence and trends of 

selected chemical and biological constituents in bottom-sediment samples collected from Lake Maxinkuckee. Sediment 

quality was assessed with reference to available SQGs for 

selected trace elements (table 2). 

Nutrients and Total Organic Carbon

Total nitrogen (TN) concentrations in the recent sediment of Lake Maxinkuckee ranged from 474 to 2,660 mg/kg 

(tables 1–5, 1–7, 1–9, and 1–11 to 1–13 in the appendix). 

At coring sites LM–1 and LM–2, pronounced and possible 

increasing trends in TN concentrations were indicated, respectively. However, at coring sites LM–3, LM–4, and LM–5, an 

initial increasing trend was followed by a decreasing trend 

(fig. 3). TN concentrations in the predevelopment sediment 

(sampled at coring sites LM–1, LM–2, LM–3, and LM–6) 

exhibited substantial variability within and among sites with 

an overall range of 615 to 6,190 mg/kg (tables 1–6, 1–8, 1–10, 

and 1–13 in the appendix). 

Total phosphorus (TP) concentrations in the recent sediment of Lake Maxinkuckee ranged from 384 to 735 mg/kg 

(tables 1–5, 1–7, 1–9, and 1–11 to 1–13). A possible increasing 

trend in TP concentrations within the past about 6 to 12 years 

was indicated at coring sites LM–1, LM–2, LM–3, and LM–4 

(fig. 4). No pronounced trend was evident at coring site LM–5. 

However, the largest TP concentration at site LM–5 was measured in the top (most recently deposited) interval of the core 

(fig. 4). For the predevelopment sediment, TP concentrations 

ranged from 462 to 1,090 mg/kg (tables 1–6, 1–8, 1–10, and 

1–13). 

Possible explanations for a recent increasing trend in TP 

in the bottom sediment of Lake Maxinkuckee include: (1) an 

increase in the amount of phosphorus available in the basin, 

(2) an increase in the delivery of phosphorus to the lake, 

and (3) postdepositional upward diffusion in the sediment 

(internal loading). Sources of phosphorus to lakes include 

background contributions from soil and bedrock, atmospheric 
10 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

contributions (wet and dry), fertilizer application (agricultural 

and urban), livestock production, septic systems, and effluent 

from wastewater treatment facilities (Wetzel, 2001). In the 

vicinity of Lake Maxinkuckee, the town of Culver’s wastewater treatment facilities are located downstream from the lake. 

Available information indicated that a substantial increase 

in the amount of available phosphorus within the past 10 to 

15 years, related to human activity in the basin, was unlikely. 

Since 1990, the population of Culver generally has been 

slowly declining (U.S. Census Bureau, 2014). From 1996 to 

2012, in Marshall County, corn production fluctuated year to 

year with no pronounced trend, whereas there was an overall 

decline in soybean production (fig. 5; U.S. Department of 

Agriculture, 2014). Corn and soybeans are the two principal 

crops grown in Marshall County, which is not a primary livestock producing area (Robert Yoder, Marshall County Extension Service, oral commun., 2014). 

An increase in precipitation over time could, in part, 

result in an increase in the delivery of phosphorus to Lake 

Maxinkuckee through direct atmospheric input and the 

mobilization and transport of phosphorus from the basin 

by runoff. To investigate this possibility, daily precipitation 

data (National Climatic Data Center, 2014) were obtained 

for Rochester and Winamac, Indiana (fig. 1), for 1960–2013. 

These two towns were the closest towns to Lake Maxinkuckee 

for which the desired multidecadal precipitation data were 

available. Respectively, Rochester and Winamac are located 

about 14 mi southeast and 15 mi southwest of the lake (fig. 1). 

The precipitation at these two locations was compared before 

(1960–86) and after (1993–2013) constructed wetlands were 

completed (1987–92) on the three primary tributaries to the 

lake (Curtiss, Kline, and Wilson Ditches; fig. 1). 

The comparison indicated that precipitation had 

increased. Respectively, at Rochester and Winamac, mean 

~1976

EXPLANATION

~ Approximately

~1996

~2002

~2007

~2012

~1982

~1996

~2006

~2009

~1972

~1993

~2004

~2008

~2012

~1975

~1988

~2008

~2012

~2006

~2012

0

1

(bottom) 2

3

4

5

6

7

8

(top) 9

10

A. Coring site LM–1

0

1

(bottom) 2

3

4

5

6

7

(top) 8

9

B. Coring site LM–2

C. Coring site LM–3

0 500 1,000 1,500 2,000 2,500 3,000

D. Coring site LM–4

0

1

(bottom) 2

3

4

5

(top) 6

7

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

E. Coring site LM–5 Total nitrogen, in milligrams per kilogram

0

(bottom) 1

2

3

4

5

6

7

(top) 8

9

0

1

(bottom) 2

3

4

5

6

7

8

(top) 9

10

0 500 1,000 1,500 2,000 2,500 3,000

Total nitrogen, in milligrams per kilogram

~1985

Figure 3. Variation in total nitrogen concentrations with 

depth of bottom-sediment samples in box cores collected 

from coring sites LM–1, LM–2, LM–3, LM–4, and LM–5 in 

Lake Maxinkuckee, northern Indiana, May 2013. 
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 11

annual precipitation was 12 and 7 percent greater during the 

postwetland period (1993–2013) compared to the prewetland 

period (1960–86). Moreover, the mean annual frequency 

of large rainfall events (equal to or greater than 1 in.) also 

increased. At Rochester, the frequency increased from 7.1 to 

9.6 events per year (35 percent increase). At Winamac, the 

frequency increased from 7.2 to 8.9 events per year (24 percent increase). Groisman and others (2001) determined that 

annual precipitation increased for most of the contiguous 

United States (including northern Indiana) during the twentieth century. An increasing trend in summer precipitation 

(1917–2008) was determined for multiple sites throughout 

Indiana by De Martino and others (2013). Therefore, since 

1960, an increase in precipitation for the Lake Maxinkuckee 

Basin was considered likely, and potentially contributed to an 

increase in phosphorus mobilization and transport. However, 

more recently, a comparison of mean annual precipitation and 

the mean annual frequency of large rainfall events for 1988–99 

and 2001–2012 indicated minimal change at Rochester and 

Winamac. Thus, a precipitation-related explanation to account 

for the post-2000 increase in TP concentrations in the recent 

sediment was not supported. 

In lakebed sediments, TP concentrations may be affected 

by postdepositional upward diffusion, which typically is 

evidenced by an increase in concentrations in the uppermost 

(most recently deposited) few centimeters of the sediment 

profile (Engstrom and Wright, 1984; Rydin, 2000; Ostrofsky, 

2012). Examination of the TP profiles for Lake Maxinkuckee 

indicated that such a pattern existed in the recent sediment for 

coring sites LM–1 through LM–4 and possibly also for coring 

site LM–5 (fig. 4). In each case, increased TP concentrations were measured in the uppermost few centimeters of the 

sediment profile. In the lower (older) part of each profile, TP 

concentrations generally were uniform. An exception to this 

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

Sediment-core interval, dimensionless

0

(bottom) 1

2

3

4

5

6

7

(top) 8

9

Sediment-core interval, dimensionless

0

(bottom) 1

2

3

4

5

(top) 6

7

Sediment-core interval, dimensionless

0 100 200 300 400 500 600 700 800 900 1,000

Constituent concentration, in milligrams per kilogram

0 100 200 300 400 500 600 700 800 900 1,000

Constituent concentration, in milligrams per kilogram

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1968

~1984

~1994

~2008

~2012

~2000

~2012

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

EXPLANATION

Phosphorus

Manganese

~ Approximately

Figure 4. Variation in total phosphorus and manganese 

concentrations with depth of bottom-sediment samples 

in box cores collected from coring sites LM–1, LM–2, 

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern 

Indiana, May 2013. 
12 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

pattern was a spike in TP concentration measured for interval 5 of core LM–4. Additional evidence in support of upward 

diffusion as the explanation was provided by the manganese 

profiles, which paralleled the TP profiles (fig. 4). Manganese, 

like phosphorus, may be affected by upward diffusion in 

lakebed sediments (Engstrom and Wright, 1984; Beutel and 

others, 2008; White and others, 2008). 

In sum, the available evidence indicated that postdepositional upward diffusion was the most likely explanation 

for the increase in TP concentrations in the uppermost few 

centimeters of cores LM–1 to LM–4. In the lower (older) section of the recent sediment, TP concentrations generally were 

uniform. Using the dating results for cores LM–1 to LM–4, 

it was determined that TP concentrations in the recent sediment generally were uniform from about 1970 to about 2000 

and indicated consistent inputs to the lake during that time. 

0

10,000

20,000

30,000

40,000

50,000

60,000

70,000

80,000

90,000

100,000

1994 1996 1998 2000 2002 2004 2006 2008 2010 2012 2014

Acres planted

Year

EXPLANATION

Corn

Soybeans

Figure 5. Corn and soybean acres planted in Marshall County, 

Indiana, 1996–2012. Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

(top) 8

9

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

(top) 6

7

1 2 3 4 5 6 7 8 9

Total organic carbon, in percent

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

1 2 3 4 5 6 7 8 9

Total organic carbon, in percent

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1968

~1984

~1994

~2008

~2012

~2000

~2012 EXPLANATION

~ Approximately

Figure 6. Variation in total organic carbon 

concentrations with depth of bottom-sediment samples 

in box cores collected from coring sites LM–1, LM–2, 

LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern 

Indiana, May 2013.
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 13

Subsequently, the history of TP deposition apparently was 

obscured by upward diffusion. 

Total organic carbon, estimated as total carbon minus 

total inorganic carbon, ranged from 4.0 to 5.9 percent in the 

recent sediment (tables 1–5, 1–7, 1–9, and 1–11 to 1–13). 

Overall, a pronounced and consistent trend was not evident for 

the five coring sites where the recent sediment was sampled 

(figs. 2 and 6). A possible increasing trend in the upper (most 

recently deposited) part of core LM–1 was indicated (fig. 6). 

In the predevelopment sediment, TOC was more variable 

with a range of 5.4 to 17.9 percent (tables 1–6, 1–8, 1–10, and 

1–13). 

Trace Elements

In this section, discussion is focused on the trace elements for which SQGs were available (table 2). Complete 

results for all elements analyzed are provided in tables 1–5 to 

1–13 in the appendix. For perspective, national baseline concentrations for selected trace elements in sediment are listed in 

table 3. The baseline concentrations were compiled using data 

from more than 400 sites with limited human effects (Horowitz and Stephens, 2008). 

Arsenic concentrations in the bottom sediment of Lake 

Maxinkuckee ranged from about 8 to 32 mg/kg (tables 1–5 

to 1–13). At coring sites LM–1 and LM–2, the concentration 

ranges for the recent and predevelopment samples were similar. At coring site LM–3, the concentration range for the predevelopment samples (about 8 to 10 mg/kg) was notably lower 

than the range for the recent samples (about 17 to 26 mg/kg). 

A consistent temporal trend in arsenic concentrations was not 

indicated for the five coring sites (LM–1 to LM–5) where the 

recent sediment was sampled (fig. 7). With two exceptions, the 

arsenic concentrations in the recent and predevelopment sediment exceeded the TEG (9.79 mg/kg), but were less than the 

PEG (41.6 mg/kg). The two exceptions were predevelopment 

samples collected at site LM–3, which were less than the TEG. 

Given that the arsenic concentrations in most of the predevelopment samples were similar to the recent samples, the source 

of arsenic likely was natural. 

Cadmium concentrations ranged between 0.1 and 

1.1 mg/kg (tables 1–5 to 1–13). In general, concentrations in 

the predevelopment samples were lower than the recent samples. With the exception of coring site LM–5, a pronounced or 

possible decreasing trend in cadmium concentrations was indicated for the recent sediment (fig. 8). The absence of a trend 

for coring site LM–5 likely was related to the fact that the box 

core only penetrated back to about the year 2000. Typically, 

cadmium concentrations in the recent and predevelopment 

samples were less than the TEG (0.99 mg/kg). 

The range in chromium concentrations was about 10 to 

24 mg/kg (tables 1–5 to 1–13). In general, concentrations in 

the predevelopment samples were similar to the recent samples. With the exception of coring site LM–5, a pronounced 

or possible decreasing trend in chromium concentrations 

was indicated for the recent sediment (fig. 9). All chromium 

concentrations in the recent and predevelopment samples were 

less than the TEG (52.3 mg/kg). 

Copper concentrations ranged from 9 to about 21 mg/kg 

(tables 1–5 to 1–13). Typically, concentrations in the predevelopment samples were lower than the recent samples. A consistent temporal trend in copper concentrations was not indicated 

for the recent sediment (fig. 10). All copper concentrations 

in the recent and predevelopment samples were less than the 

TEG (31.6 mg/kg). 

Lead concentrations in the recent samples ranged from 23 

to 69 mg/kg. In comparison, the predevelopment samples had 

lead concentrations that consistently were less than 10 mg/kg 

(tables 1–5 to 1–13). For all five coring sites where the recent 

sediment was sampled, a pronounced or possible decreasing trend in lead concentrations was indicated (fig. 11). The 

decreasing trend likely represents the environmental response 

to the history of leaded gasoline use in the United States. 

Leaded gasoline was first introduced in the 1920s and quickly 

became standard (Davies, 1990). The use of leaded gasoline 

increased and, during the period of maximum use (that is, 

the 1940s through the early 1980s), vehicle emissions were 

the dominant source of lead to the environment (Juracek and 

Ziegler, 2006). With the phase out of leaded gasoline legislated by the Clean Air Act of 1970, vehicle emissions declined 

(U.S. Environmental Protection Agency, 2000). At Lake 

Maxinkuckee, lead concentrations in the recently-deposited 

sediment have declined but remain higher than the predevelopment (that is, before leaded gasoline) concentrations. Juracek 

and Ziegler (2006) estimated that, assuming no new sources of 

lead, the time required for lead concentrations in newly-deposited bottom sediment to return to pre-1920s concentrations 

may be at least several decades. 

Table 3. National baseline concentrations for selected trace 

elements in sediment.

[Source: Horowitz and Stephens, 2008. mg/kg, milligrams per kilogram]

Trace 

element

Minimum

(mg/kg)

Maximum

(mg/kg)

Mean

(mg/kg)

Median

(mg/kg)

Arsenic 0.1 60 8.1 6.6

Cadmium 0.1 2.8 0.5 0.4

Chromium 6.3 270 66 58

Copper 1 150 24 20

Lead 2 200 24 20

Mercury 0.01 3.1 0.08 0.04

Nickel 1 160 28 23

Selenium 0.1 5.6 0.8 0.7

Silver 0.1 4.3 0.3 0.2

Zinc 5.2 430 100 91
14 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0 5 10 15 20 25 30 35

Arsenic, in milligrams per kilogram

0

2

3

4

5

6

7

8

10

0

2

3

4

5

6

7

9

0

2

3

4

5

6

7

8

10

0

2

3

4

5

7

0

2

3

4

5

6

7

8

10

0 5 10 15 20 25 30 35

Arsenic, in milligrams per kilogram

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1968

~1984

~1994

~2008

~2012

~2000

~2012 EXPLANATION

Threshold-effects guideline (9.79 milligrams per kilogram)

~ Approximately

(bottom) 1

(top) 9

(bottom) 1

(top) 8

(bottom) 1

(top) 9

(bottom) 1

(top) 6

(bottom) 1

(top) 9

Figure 7. Variation in arsenic concentrations with depth of bottom-sediment samples in box cores collected from coring sites LM–1, 

LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.

With respect to lead, the quality of the recent sediment 

in Lake Maxinkuckee has improved with time as lead concentrations have decreased. At coring sites LM–1, LM–2, and 

LM–4, the oldest (deepest) samples had lead concentrations 

that were higher than the TEG (35.8 mg/kg), whereas the 

youngest samples had concentrations that were less than the 

TEG. At coring site LM–3, lead concentrations for all recent 

samples were higher than the TEG. At coring site LM–5, 

concentrations for all samples were less than the TEG. For all 

recent and predevelopment samples, lead concentrations were 

less than the PEG (128 mg/kg; fig. 11; tables 1–5 to 1–13). 

The range in mercury concentrations was 0.02 to 

0.12 mg/kg (tables 1–5 to 1–13). The predevelopment samples 

had concentrations that were lower than the recent samples. In 

the recent sediment, mercury concentrations exhibited either 

a decreasing trend or no trend with time (fig. 12). All mercury 

concentrations in the recent and predevelopment samples were 

less than the TEG (0.18 mg/kg). 

Nickel concentrations ranged from less than 1 to about 

15 mg/kg (tables 1–5 to 1–13). Compared to the recent 

samples, the predevelopment samples had concentrations that 

were similar and occasionally higher. For the recent sediment, 
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 15

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

2

3

4

5

6

7

8

10

0

2

3

4

5

6

7

9

0

2

3

4

5

6

7

8

10

0

2

3

4

5

7

0

2

3

4

5

6

7

8

10

0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1

Cadmium, in milligrams per kilogram

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2000

~2012

(bottom) 1

(top) 9

(bottom) 1

(top) 8

(bottom) 1

(top) 9

(bottom) 1

(top) 6

(bottom) 1

(top) 9

EXPLANATION

~ Approximately

0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1

Cadmium, in milligrams per kilogram

~1968

Figure 8. Variation in cadmium concentrations with depth of bottom-sediment samples in box cores collected from coring sites 

LM–1, LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.

a pronounced or possible decreasing trend in nickel concentrations was indicated for coring sites LM–2, LM–3, and LM–4. 

However, a well-defined trend was not indicated for coring 

sites LM–1 and LM–5 (fig. 13). All nickel concentrations in 

the recent and predevelopment samples were less than the 

TEG (22.7 mg/kg). 

Sediment-quality guidelines were not available for 

selenium. However, Lemly (2002) proposed that a value of 

2.0 mg/kg be used as a toxic threshold for selenium concentrations in sediment. In Lake Maxinkuckee, selenium concentrations ranged from about 0.6 to about 3.0 mg/kg and typically 

were less than 2.0 mg/kg (tables 1–5 to 1–13). In the recent 

sediment, selenium concentrations exhibited either a possible 

decreasing trend or no trend with time (fig. 14). The predevelopment samples had concentrations that ranged from lower 

than to higher than the recent samples. 

Concentrations of silver in the recent and predevelopment sediment were less than 0.3 mg/kg (tables 1–5 to 

1–13). With the exception of a decreasing trend in the deepest (oldest) one-half of the core collected at coring site 

LM–4, no trend was indicated for silver concentrations in 

the recent sediment (fig. 15). All silver concentrations in the 
16 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

2

3

4

5

6

7

8

10

0

2

3

4

5

6

7

9

0

2

3

4

5

6

7

8

10

0

2

3

4

5

7

0

2

3

4

5

6

7

8

10

0 5 10 15 20 25 30

Chromium, in milligrams per kilogram

0 5 10 15 20 25 30

Chromium, in milligrams per kilogram

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2000

~2012 EXPLANATION

~ Approximately

~1968

(bottom) 1

(top) 9

(bottom) 1

(top) 8

(bottom) 1

(top) 9

(bottom) 1

(top) 6

(bottom) 1

(top) 9

Figure 9. Variation in chromium concentrations with depth of bottom-sediment samples in box cores collected from coring sites LM–1, 

LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.

recent and predevelopment samples were less than the TEG 

(0.733 mg/kg). 

Zinc concentrations ranged from about 27 to 151 mg/kg 

(tables 1–5 to 1–13). Typically, the predevelopment samples 

had concentrations that were lower than the recent samples. 

For the recent sediment, a pronounced trend in zinc concentrations was not evident at coring sites LM–1, LM–3, and LM–5. 

However, at coring site LM–4, a pronounced decreasing trend 

was indicated. At coring site LM–2, zinc concentrations initially decreased then stabilized (fig. 16). With two exceptions, 

zinc concentrations in the recent and predevelopment samples 

were less than the TEG (124 mg/kg). The exceptions were 

individual samples from coring sites LM–3 and LM–6, which 

exceeded the TEG but were well below the PEG (459 mg/kg; 

tables 1–5 to 1–13). 

Elevated trace element concentrations in recent, compared to predevelopment, sediment deposited in lakes may 

be indicative of human-related environmental contamination 

(Forstner and Wittmann, 1981; Baudo and others, 1990; Smol, 

2008). In addition to lead, elevated concentrations of cadmium, copper, mercury, and zinc were measured in the recent 

sediment deposited in Lake Maxinkuckee. Each of these trace 

elements may originate from human activity. For example, 

human-related sources of zinc include industrial activity (such 

as metal production), coal combustion, waste incineration, and 

vehicular tire wear (Luoma and Rainbow, 2008). 
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 17

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

2

3

4

5

6

7

8

10

0

2

3

4

5

6

7

9

0

2

3

4

5

6

7

8

10

0

2

3

4

5

7

0

2

3

4

5

6

7

8

10

0 5 10 15 20 25 30

Copper, in milligrams per kilogram

0 5 10 15 20 25 30

Copper, in milligrams per kilogram

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2000

~2012 EXPLANATION

~ Approximately

~1968

(bottom) 1

(top) 9

(bottom) 1

(top) 8

(bottom) 1

(top) 9

(bottom) 1

(top) 6

(bottom) 1

(top) 9

Figure 10. Variation in copper concentrations with depth of bottom-sediment samples in box cores collected from coring sites LM–1, 

LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.
18 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Figure 11. Variation in lead concentrations with depth of bottom-sediment samples in box cores collected from coring sites LM–1, 

LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013. Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

2

3

4

5

6

7

8

10

0

2

3

4

5

6

7

9

0

2

3

4

5

6

7

8

10

0

2

3

4

5

7

0

2

3

4

5

6

7

8

10

Lead, in milligrams per kilogram

Lead, in milligrams per kilogram

0 10 20 30 40 50 60 70 80

0 10 20 30 40 50 60 70 80

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2000

~2012 EXPLANATION

Threshold-effects guideline (35.8 milligrams per kilogram)

~ Approximately

~1968

(bottom) 1

(top) 9

(bottom) 1

(top) 8

(bottom) 1

(top) 9

(bottom) 1

(top) 6

(bottom) 1

(top) 9
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 19

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

2

3

4

5

6

7

8

10

0

2

3

4

5

6

7

9

0

2

3

4

5

6

7

8

10

0

2

3

4

5

7

0

2

3

4

5

6

7

8

10

Mercury, in milligrams per kilogram

Mercury, in milligrams per kilogram

0 0.02 0.04 0.06 0.08 0.1 0.12 0.14 0.16

0 0.02 0.04 0.06 0.08 0.1 0.12 0.14 0.16

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2000

~2012

~1968

(bottom) 1

(top) 9

(bottom) 1

(top) 8

(bottom) 1

(top) 9

(bottom) 1

(top) 6

(bottom) 1

(top) 9

Figure 12. Variation in mercury concentrations with depth of bottom-sediment samples in box cores collected from coring sites LM–1, 

LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.
20 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Figure 13. Variation in nickel concentrations with depth of bottom-sediment samples in box cores collected from coring sites LM–1, 

LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013. Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

2

3

4

5

6

7

8

10

0

2

3

4

5

6

7

9

0

2

3

4

5

6

7

8

10

0

2

3

4

5

7

0

2

3

4

5

6

7

8

10

Nickel, in milligrams per kilogram

Nickel, in milligrams per kilogram

0 2 4 6 8 10 12 14 16

0 2 4 6 8 10 12 14 16

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2000

~2012

~1968

(bottom) 1

(top) 9

(bottom) 1

(top) 8

(bottom) 1

(top) 9

(bottom) 1

(top) 6

(bottom) 1

(top) 9
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 21

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

2

3

4

5

6

7

8

10

0

2

3

4

5

6

7

9

0

2

3

4

5

6

7

8

10

0

2

3

4

5

7

0

2

3

4

5

6

7

8

10

Selenium, in milligrams per kilogram

Selenium, in milligrams per kilogram

0 0.2 0.4 0.6 0.8 1 1.2 1.4 1.6 1.8 2

0 0.2 0.4 0.6 0.8 1 1.2 1.4 1.6 1.8 2

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2000

~2012

~1968

(bottom) 1

(top) 9

(bottom) 1

(top) 8

(bottom) 1

(top) 9

(bottom) 1

(top) 6

(bottom) 1

(top) 9

Figure 14. Variation in selenium concentrations with depth of bottom-sediment samples in box cores collected from coring sites LM–1, 

LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.
22 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Figure 15. Variation in silver concentrations with depth of bottom-sediment samples in box cores collected from coring sites LM–1, 

LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013. Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

2

3

4

5

6

7

8

10

0

2

3

4

5

6

7

9

0

2

3

4

5

6

7

8

10

0

2

3

4

5

7

0

2

3

4

5

6

7

8

10

Silver, in milligrams per kilogram

Silver, in milligrams per kilogram

0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1

0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2000

~2012

~1968

(bottom) 1

(top) 9

(bottom) 1

(top) 8

(bottom) 1

(top) 9

(bottom) 1

(top) 6

(bottom) 1

(top) 9
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 23

Figure 16. Variation in zinc concentrations with depth of bottom-sediment samples in box cores collected from coring sites LM–1, 

LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013. Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

2

3

4

5

6

7

8

10

0

2

3

4

5

6

7

9

0

2

3

4

5

6

7

8

10

0

2

3

4

5

7

0

2

3

4

5

6

7

8

10

Zinc, in milligrams per kilogram

Zinc, in milligrams per kilogram

0 20 40 60 80 100 120 140 160

0 20 40 60 80 100 120 140 160

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1972

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2000

~2012

~1968

(bottom) 1

(top) 9

(bottom) 1

(top) 8

(bottom) 1

(top) 9

(bottom) 1

(top) 6

(bottom) 1

(top) 9
24 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Diatoms

A total of 188 different diatom species were identified 

in the bottom-sediment samples collected from Lake Maxinkuckee. Most of the species occurred rarely with a relative abundance of less than 1 percent. There were 13 species 

that had a relative abundance greater than 1 percent and 

together accounted for about 83 percent of the total abundance 

(table 4). The occurrence of multiple species, none of which 

were overwhelmingly dominant, was indicative of a minimally 

contaminated lake ecosystem (John Smol, Queen’s University, Kingston, Ontario, Canada, written commun., 2007). The 

13 relatively abundant species are the focus of the following 

discussion. Complete information on the occurrence of the 

13 species in each sediment sample is provided in tables 1–14 

to 1–22 in the appendix. A complete list of the rare diatom 

species identified is provided in table 1–23 in the appendix. 

For Achnanthidium minutissimum (formerly Achnanthes 

minutissima), an overall increasing trend in abundance in the 

recent sediment was indicated (fig. 17). However, this species is not considered a good indicator of eutrophic or oligotrophic conditions because it is cosmopolitan (van Dam and 

others, 1994; Rasanen and others, 2006b; Bigler and others, 

2007; Bennion and others, 2011). In other words, it is known 

to tolerate a wide range of environmental conditions including nutrient concentrations. In the predevelopment sediment, 

Achnanthidium minutissimum was less abundant or absent 

(tables 1–15, 1–17, 1–19, and 1–22). 

Amphora ovalis is an indicator of eutrophic conditions 

(van Dam and others, 1994; Jasprica and Hafner, 2005; Hadley 

and others, 2010). In the recent sediment, there was an overall 

decreasing trend in abundance (fig. 18), which indicated that 

the lake possibly became less productive in recent decades. 

Amphora ovalis typically was less abundant in the predevelopment sediment, if not absent (tables 1–15, 1–17, 1–19, and 

1–22). Two explanations may account for the lower abundance 

of Amphora ovalis in the predevelopment sediment. One possibility is that the lake was less productive during predevelopment times. A second possibility is that the abundance was 

reduced by dissolution of the diatoms in the water column or 

postdepositional dissolution and breakage of diatoms in the 

sediment, or both (Fritz and others, 1993). 

Asterionella formosa generally is considered an indicator 

of eutrophic conditions (Bradshaw and others, 2005; Pienitz and others, 2006; Battarbee and others, 2012). However, 

Yilmaz and Aykulu (2010), citing Rawson (1956) and Patrick 

and Reimer (1966), noted that it may be abundant in eutrophic, 

mesotrophic, or oligotrophic waters. In the recent sediment, 

there was a pronounced increase in the abundance of Asterionella formosa in the uppermost section of each core (fig. 19). 

Given the apparent ability of this species to thrive in a range 

of conditions, interpretation of the increase was not attempted. 

The abundance of Asterionella formosa in the predevelopment sediment, compared to the recent sediment, typically was 

either lower or absent (tables 1–15, 1–17, 1–19, and 1–22). 

Aulacoseira ambigua may be an indicator of eutrophic 

(van Dam and others, 1994; Heinsalu and others, 2008) or 

mesotrophic (Pienitz and others, 2006; Poister and others, 

2012) conditions. Rasanen and others (2006b) concluded that, 

given its tolerance to a wide range of environmental conditions, it may not be a good indicator for any lake type. In the 

recent sediment, the overall pattern for Aulacoseira ambigua

was a decrease in abundance followed by relative uniformity 

(fig. 20). A possible interpretation, that the lake became less 

productive in recent decades, would be consistent with the evidence provided by Amphora ovalis. However, the accuracy of 

this interpretation is debatable given the uncertainty as to what 

conditions are indicated by the changing presence of Aulacoseira ambigua. In the predevelopment sediment, Aulacoseira 

ambigua ranged from absent to moderately abundant (tables 

1–15, 1–17, 1–19, and 1–22). 

Cyclotella bodanica is an indicator of oligotrophic conditions (van Dam and others, 1994; Smol, 2008; Genkal and 

others, 2013). At coring sites LM–1 and LM–4, there was an 

increase in abundance of Cyclotella bodanica that indicated 

the lake had become more oligotrophic in recent decades. 

However, no such trend was evident at the other three coring sites (LM–2, LM–3, and LM–5; fig. 21). Thus, overall, 

the best interpretation of the evidence provided by Cyclotella 

bodanica may be that the lake had not become more productive in recent decades. Cyclotella bodanica in the predevelopment sediment, compared to the recent sediment, ranged from 

less abundant to much more abundant (tables 1–15, 1–17, 

1–19, and 1–22). 

Table 4. Relative abundance of the most frequently encountered 

diatom species in bottom-sediment samples collected from Lake 

Maxinkuckee, northern Indiana, May 2013.

Diatom species Relative abundance 

(percent)

Achnanthidium minutissimum 7.8

Amphora ovalis 3.1

Asterionella formosa 5.5

Aulacoseira ambigua 7.9

Cyclotella bodanica 8.7

Cyclotella ocellata 11.2

Cyclotella pseudostelligera 1.7

Fragilaria crotonensis 7.1

Pseudostaurosira brevistriata 12.9

Staurosira construens 3.0

Staurosira construens var. venter 8.9

Staurosirella pinnata 3.5

Synedra demerarae 1.3

All other species 17.4
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 25

Cyclotella ocellata was the second-most abundant species in the bottom sediment of Lake Maxinkuckee (table 4). 

There was a lack of consensus as to what conditions this 

species represents. It has been labelled as a mesotrophic to 

eutrophic indicator (van Dam and others, 1994), an oligotrophic indicator (Battarbee and others, 2012), and as a controversial or cosmopolitan species (Cremer and Wagner, 2003; 

Reed and others, 2010). In the recent sediment, a pronounced 

multidecadal increase in the abundance of Cyclotella ocellata

was followed by a decrease in abundance in the most recently 

deposited sediment. This pattern was consistent at all five 

coring sites where the recent sediment was sampled (fig. 22). 

Given the uncertainty as to what conditions are represented, 

interpretation of the pattern was not attempted. Cyclotella 

ocellata was absent in the predevelopment sediment (tables 

1–15, 1–17, 1–19, and 1–22). It is worth noting that Schlegel and Scheffler (1999) proposed that Cyclotella ocellata

abundance may be affected more by loss factors (for example, 

sinking and grazing) than growth-related factors (for example, 

light, temperature, and nutrients). 

Figure 17. Variation in occurrence of Achnanthidium minutissimum with depth of bottom-sediment samples in box cores collected 

from coring sites LM–1, LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.

0

2

3

4

5

6

7

9

0

2

3

4

5

7

(bottom) 1

(top) 8

(bottom) 1

(top) 6

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

Achnanthidium minutissimum, count

Achnanthidium minutissimum, count

0 20 40 60 80 100 120 140

0 20 40 60 80 100 120 140

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~1968 ~1972

~2000

~2012
26 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Cyclotella pseudostelligera typically is an indicator of 

eutrophic conditions (van Dam and others, 1994; Battarbee 

and others, 2012; Bennion and others, 2012). At coring sites 

LM–1 and LM–4, there was an overall decrease in abundance of Cyclotella pseudostelligera that indicated the lake 

had become less productive in recent decades (fig. 23). This 

interpretation was consistent with the evidence provided by 

Cyclotella bodanica for these two coring sites. Insufficient 

abundance of Cyclotella pseudostelligera at coring sites 

LM–2, LM–3, and LM–5 precluded an assessment of trends 

at these sites (tables 1–15, 1–17, 1–19, and 1–22). Cyclotella 

pseudostelligera in the predevelopment sediment, compared 

to the recent sediment, ranged from similar abundance (coring 

site LM–1) to rare (coring sites LM–2 and LM–3; tables 1–15, 

1–17, 1–19, and 1–22). 

Certain Fragilaria species (some of which have been 

renamed) generally are not considered to be reliable indicators 

of lake trophic status because they can tolerate a wide range of 

ecological conditions including nutrient concentrations (Bennion and others, 2001; Ampel and others, 2008; Fluin and others, 2010; Smol and Stoermer, 2010). In the recent sediment of 

Lake Maxinkuckee, such species present in relative abundance 

(with an occurrence greater than 1 percent of the total diatom 

abundance) included Pseudostaurosira brevistriata (formerly 

Fragilaria brevistriata), Staurosira construens (formerly 

Fragilaria construens), Staurosira construens var. venter

Figure 18. Variation in occurrence of Amphora ovalis with depth of bottom-sediment samples in box cores collected from coring sites 

LM–1, LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.

0

2

3

4

5

6

7

9

0

2

3

4

5

7

(bottom) 1

(top) 8

(bottom) 1

(top) 6

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0 10 20 30 40 50 60 70 80

Amphora ovalis, count

0 10 20 30 40 50 60 70 80

Amphora ovalis, count

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2012

~1968 ~1972

~2000
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 27

(formerly Fragilaria construens var. venter), and Staurosirella 

pinnata (formerly Fragilaria pinnata). Pseudostaurosira 

brevistriata was the most abundant species in the recent sediment (tables 1–14, 1–16, 1–18, 1–20, and 1–21). 

Fragilaria crotonensis may be an indicator of mesotrophic or eutrophic conditions (van Dam and others, 1994; 

Negro and de Hoyos, 2005; Pienitz and others, 2006; Bennion and others, 2011; Battarbee and others, 2012). At coring 

sites LM–1 and LM–4, there was a pronounced decrease in 

abundance of Fragilaria crotonensis that indicated the lake 

had become less productive in recent decades (fig. 24). This 

interpretation was consistent with the evidence provided by 

Cyclotella bodanica and Cyclotella pseudostelligera for these 

two coring sites. However, no such trend was evident at the 

other three coring sites (LM–2, LM–3, and LM–5; fig. 24). 

Fragilaria crotonensis in the predevelopment sediment, 

compared to the recent sediment, ranged from similar or lower 

abundance (coring sites LM–1 and LM–6) to absent (coring 

sites LM–2 and LM–3; tables 1–15, 1–17, 1–19, and 1–22). 

The final relatively abundant species identified in the 

bottom sediment of Lake Maxinkuckee was Synedra demerarae (table 4). Because a search of the literature uncovered 

no information regarding the utility of this species as an 

indicator of lake trophic status, it was not discussed further in 

this report. 

Figure 19. Variation in occurrence of Asterionella formosa with depth of bottom-sediment samples in box cores collected from coring 

sites LM–1, LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.

0

2

3

4

5

6

7

9

0

2

3

4

5

7

(bottom) 1

(top) 8

(bottom) 1

(top) 6

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

Asterionella formosa, count

Asterionella formosa, count

0 20 40 60 80 100 120

0 20 40 60 80 100 120

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2012

~1968 ~1972

~2000
28 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

In sum, the diversity of diatom species, and the relative 

abundance of multiple species, in the bottom sediment indicated that Lake Maxinkuckee was not substantially affected 

by nutrient enrichment. Moreover, the combined evidence 

provided by multiple species indicated that Lake Maxinkuckee 

had not become more productive in recent decades. This 

conclusion was based on the evidence provided by the following species: Amphora ovalis, Aulacoseira ambigua, Cyclotella bodanica, Cyclotella pseudostelligera, and Fragilaria 

crotonensis. 

Water-quality evidence for a stable, low-productivity lake 

condition was provided by the Indiana Clean Lakes Program. 

From 2000 to 2012, 33 water samples collected during the late 

spring or summer had very low chlorophyll-a concentrations 

that ranged from 0.15 to 4.60 micrograms per liter (μg/L) with 

a median of 2.06 μg/L (Indiana Clean Lakes Program, 2014). 

Chlorophyll-a concentrations less than 4 μg/L are indicative of 

oligotrophic conditions (Wetzel, 2001). 

Figure 20. Variation in occurrence of Aulacoseira ambigua with depth of bottom-sediment samples in box cores collected from coring 

sites LM–1, LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.

0

2

3

4

5

6

7

9

0

2

3

4

5

7

(bottom) 1

(top) 8

(bottom) 1

(top) 6

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

Aulacoseira ambigua, count

0 20 40 60 80 100 120 140 160 180

Aulacoseira ambigua, count

0 20 40 60 80 100 120 140 160 180

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1968

~1996

~2006

~2012

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2012

~1972

~2000
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 29

Cyanobacteria

In the bottom sediment of Lake Maxinkuckee, the preserved algal community was dominated by akinete-producing 

cyanobacteria. Thus, the akinete-producing cyanobacteria 

either were more abundant or better preserved than the 

diatoms. Cyanobacterial akinetes from the genera Anabaena, 

Aphanizomenon, and Gloeotrichia (species echinulata) (hereafter G. echinulata) were present. Among the three akineteproducing cyanobacteria, G. echinulata was dominant in the 

recent and predevelopment sediment. In the recent sediment, 

the relative abundance ranged from 68 to 97 percent with a 

mean of 88 percent (fig. 25). Similarly, in the predevelopment 

sediment, the relative abundance ranged from 79 to 96 percent 

with a mean of 93 percent. Complete information on the 

occurrence and abundance of cyanobacterial akinetes in each 

sediment sample is provided in table 1–24 in the appendix. 

G. echinulata is a species of cyanobacteria that has a 

unique life cycle. Unlike other species that primarily obtain 

phosphorus from the water column, G. echinulata acquires 

most of its phosphorus from the bottom sediment where 

it spends the first stage of its life before migrating up into 

the water column (Barbiero and Welch, 1992; Istvanovics 

and others, 1993; Karlsson, 2003). It is for this reason that 

Figure 21. Variation in occurrence of Cyclotella bodanica with depth of bottom-sediment samples in box cores collected from coring 

sites LM–1, LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.

0

2

3

4

5

6

7

9

0

2

3

4

5

7

(bottom) 1

(top) 8

(bottom) 1

(top) 6

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

Cyclotella bodanica, count

Cyclotella bodanica, count

0 10 20 30 40 50 60 70

0 10 20 30 40 50 60 70

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2012

~1972 ~1968

~2000
30 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Figure 22. Variation in occurrence of Cyclotella ocellata with depth of bottom-sediment samples in box cores collected from coring 

sites LM–1, LM–2, LM–3, LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.

G. echinulata can thrive in oligotrophic or mesotrophic lakes 

(Carey and others, 2008). In addition, there is evidence to 

indicate that the presence of G. echinulata in the water column 

can stimulate the growth of other phytoplankton (Carey and 

Rengefors, 2010; Carey and others, 2014). One possible 

explanation is the fact that the upward migration of G. echinulata can provide a substantial source of internal phosphorus 

loading (Barbiero and Welch, 1992; Istvanovics and others, 

1993). Because G. echinulata is potentially toxic (it is known 

to produce the cyanotoxin microcystin), it represents a possible health risk for aquatic organisms and humans (Carey and 

others, 2012). 

The consistency in the relative abundance of the three 

akinete-producing cyanobacteria genera in the recent and predevelopment sediment indicated that lake conditions may not 

have changed appreciably in recent decades and possibly have 

been similar dating back to at least the mid-1800s. If phosphorus concentrations in the lake had increased substantially 

in recent decades, a pronounced increase in the abundance 

of Anabaena or Aphanizomenon, or both, would be expected 

(van Geel and others, 1994; Kling, 1998). Such an increase 

was not indicated in the recent sediment (fig. 25). 

0

2

3

4

5

6

7

9

0

2

3

4

5

7

(bottom) 1

(top) 8

(bottom) 1

(top) 6

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

Cyclotella ocellata, count

Cyclotella ocellata, count

0 50 100 150 200 250

0 50 100 150 200 250

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2012

~ ~1968 1972

~2000
Occurrence and Trends of Selected Chemical Constituents, Diatoms, and Cyanobacteria in Bottom Sediment 31

Sediment-core interval, dimensionless

Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–4

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0 10 20 30 40 50 60 70 80

Cyclotella pseudostelligera, count

0 10 20 30 40 50 60 70 80

Cyclotella pseudostelligera, count

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1984

~1994

~2008

~2012

~1968

EXPLANATION

~ Approximately

Figure 23. Variation in occurrence of Cyclotella pseudostelligera with depth of bottom-sediment samples in box cores collected from 

coring sites LM–1 and LM–4 in Lake Maxinkuckee, northern Indiana, May 2013.

0

2

3

4

5

6

7

9

0

2

3

4

5

7

(bottom) 1

(top) 8

(bottom) 1

(top) 6

Sediment-core interval, dimensionless Sediment-core interval, dimensionless Sediment-core interval, dimensionless

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

0

(bottom) 1

2

3

4

5

6

7

8

(top) 9

10

Fragilaria crotonensis, count

Fragilaria crotonensis, count

0 50 100 150 200 250

0 50 100 150 200 250

EXPLANATION

~ Approximately

~1976

~1985

~1996

~2012

~1982

~1996

~2006

~2012

~1993

~2004

~2012

~1984

~1994

~2008

~2012

~2012

~1968 ~1972

~2000

Figure 24. Variation in occurrence of Fragilaria 

crotonensis with depth of bottom-sediment samples in 

box cores collected from coring sites LM–1, LM–2, LM–3, 

LM–4, and LM–5 in Lake Maxinkuckee, northern Indiana, 

May 2013.
32 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

0

20,000

40,000

60,000

80,000

100,000

120,000

1

(bottom

of core)

2 

(~1976)

3 4

(~1985)

5 6

(~1996)

7 8 9

(~2012)

(top of core)

1

(bottom

of core)

2

(~1982)

3 4

(~1996)

5 6

(~2006)

7 8 9

(~2012)

(top of core)

Count per gram of sediment

0

50,000

100,000

150,000

200,000

250,000

300,000

350,000

0

10,000

20,000

30,000

40,000

50,000

60,000

70,000

80,000

90,000

100,000

1

(~1972)

(bottom of core)

2 3

(~1993)

4 5

(~2004)

6 7 8

(~2012)

(top of core)

Count per gram of sediment

0

20,000

40,000

60,000

80,000

100,000

120,000

1

(~1968)

(bottom of core)

2 3

(~1984)

4 5

(~1994)

6 7

(~2008)

8 9

(~2012)

(top of core)

0

10,000

20,000

30,000

40,000

50,000

60,000

70,000

80,000

90,000

1

(~2000)

(bottom of core)

2 3 4 5 6

(~2012)

(top of core)

Count per gram of sediment

A. Coring site LM–1 B. Coring site LM–2

C. Coring site LM–3 D. Coring site LM–4

E. Coring site LM–5

Anabaena

Aphanizomenon

Gloeotrichia echinulata

Approximately

EXPLANATION

Sediment-core interval, dimensionless

Sediment-core interval, dimensionless

~

Figure 25. Variation in occurrence of Anabaena, 

Aphanizomenon, and Gloeotrichia echinulata akinetes 

with depth of bottom-sediment samples in box cores 

collected from coring sites LM–1, LM–2, LM–3, LM–4, 

and LM–5 in Lake Maxinkuckee, northern Indiana, 

May 2013.
References Cited 33

Summary and Conclusions

A 2-year study by the U.S. Geological Survey, in cooperation with the Lake Maxinkuckee Environmental Council 

and the Marshall County Soil and Water Conservation District, 

was begun in 2013 to investigate the past and present condition of Lake Maxinkuckee through an analysis of the lakebed 

sediment. The study was based on an analysis of bottomsediment cores that were collected from six sites in 2013. 

The cores were analyzed for total nitrogen, total phosphorus, 

carbon, 39 trace elements, diatoms, cyanobacterial akinetes, 

and 3 radionuclides. The primary results of this study are 

listed below: 

1. Total nitrogen concentrations in the recent sediment 

(since about 1970) were variable with no consistent 

trend indicated. 

2. Total phosphorus concentrations in the recent sediment generally were uniform from about 1970 to 

about 2000 and indicated consistent inputs to the 

lake during that time. Subsequently, the history of 

total phosphorus deposition apparently was obscured 

by postdepositional upward diffusion. 

3. Elevated concentrations of cadmium, copper, lead, 

mercury, and zinc in the recent sediment, compared 

to the predevelopment (pre-1863) sediment, indicated likely human-related contamination. 

4. Trace element concentrations were less than 

probable-effects guidelines (available for nine trace 

elements), which represent the concentrations above 

which toxic aquatic biological effects usually or 

frequently occur. 

5. Arsenic concentrations typically exceeded the 

threshold-effects guideline, which represents the 

concentration above which toxic aquatic biological 

effects occasionally occur, in the recent and predevelopment sediment. The arsenic likely originated 

from natural sources. 

6. Lead concentrations historically exceeded the 

threshold-effects guideline but since had decreased 

below it in the recent sediment at most coring sites. 

The decreasing trend likely was indicative of the 

effect of the phase out of leaded gasoline. 

7. The occurrence of multiple diatom species, none of 

which were overwhelmingly dominant, was indicative of a minimally contaminated lake ecosystem. 

8. The combined evidence of several diatom species in 

the recent sediment indicated that the lake had not 

become more productive in recent decades. 

9. The combined evidence provided by akinetes 

for three cyanobacterial genera in the recent and 

predevelopment sediment indicated similar nutrient 

conditions in the lake during the past 40 years and 

possibly back to at least the mid-1800s. 

References Cited

Adams, D.G., and Duggan, P.S., 1999, Tansley review 

no. 107—Heterocyst and akinete differentiation in cyanobacteria: New Phytology, v. 144, p. 3–33. 

Adriano, D.C., 2001, Trace elements in terrestrial environments—Biogeochemistry, bioavailability, and risks of metals (2d ed.): New York, Springer-Verlag, 866 p. 

Ampel, Linda, Wohlfarth, B., Risberg, J., and Veres, D., 2008, 

Paleolimnological response to millennial and centennial 

scale climate variability during MIS 3 and 2 as suggested 

by the diatom record in Les Echets, France: Quaternary Science Reviews, v. 27, p. 1493–1504. 

Appleby, P.G., 2001, Chronostratigraphic techniques in recent 

sediments, chap. 9, in Last, W.M., and Smol, J.P., eds., 

Tracking environmental change using lake sediments, 

volume 1—Basin analysis, coring, and chronological 

techniques: Dordrecht, The Netherlands, Kluwer Academic 

Publishers, p. 171–203. 

Appleby, P.G., and Oldfield, F., 1978, The calculation of lead210 dates assuming a constant rate of supply of unsupported 

210Pb to the sediment: Catena, v. 5, p. 1–8. 

Appleby, P.G., and Oldfield, F., 1983, The assessment of 210Pb 

data from sites with varying sediment accumulation rates: 

Hydrobiologia, v. 103, p. 29–35. 

Appleby, P.G., and Oldfield, F., 1992, Application of lead210 to sedimentation studies, chap. 21, in Ivanovich, M., 

and Harmon, R.S., eds., Uranium-series disequilibrium—

Applications to earth, marine, and environmental sciences 

(2d ed.): Oxford, United Kingdom, Clarendon Press, 

p. 731–778. 

Barbiero, R.P., and Welch, E.B., 1992, Contribution of benthic 

blue-green algal recruitment to lake populations and phosphorus translocation: Freshwater Biology, v. 27, p. 249–260. 

Battarbee, R.W., Anderson, N.J., Bennion, H., and Simpson, 

G.L., 2012, Combining limnological and palaeolimnological data to disentangle the effects of nutrient pollution and 

climate change on lake ecosystems—Problems and potential: Freshwater Biology, v. 57, p. 2091–2106. 
34 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Baudo, Renato, Giesy, J.P., and Muntau, H., 1990, Sediments—Chemistry and toxicity of in-place pollutants: Ann 

Arbor, Mich., Lewis Publishers, Inc., 405 p. 

Bennion, Helen, Appleby, P.G., and Phillips, G.L., 2001, 

Reconstructing nutrient histories in the Norfolk Broads, 

UK—Implications for the role of diatom-total phosphorus 

transfer functions in shallow lake management: Journal of 

Paleolimnology, v. 26, p. 181–204. 

Bennion, Helen, Simpson, G.L., Anderson, N.J., Clarke, G., 

Dong, X., Hobaek, A., Guilizzoni, P., Marchetto, A., Sayer, 

C.D., Thies, Hansjorg, and Tolotti, Monica, 2011, Defining 

ecological and chemical reference conditions and restoration targets for nine European lakes: Journal of Paleolimnology, v. 45, p. 415–431. 

Bennion, Helen, Carvalho, L., Sayer, C.D., Simpson, G.L., 

and Wischnewski, J., 2012, Identifying from recent sediment records the effects of nutrients and climate on diatom dynamics in Loch Leven: Freshwater Biology, v. 57, 

p. 2015–2029. 

Beutel, M.W., Leonard, T.M., Dent, S.R., and Moore, B.C., 

2008, Effects of aerobic and anaerobic conditions on P, N, 

Fe, Mn, and Hg accumulation in waters overlying profundal 

sediments of an oligo-mesotrophic lake: Water Research, 

v. 42, p. 1953–1962. 

Bigler, Christian, von Gunten, L., Lotter, A.F., Hausmann, S., 

Blass, A., Ohlendorf, C., and Sturm, M., 2007, Quantifying human-induced eutrophication in Swiss mountain lakes 

since AD 1800 using diatoms: The Holocene, v. 17, no. 8, 

p. 1141–1154. 

Blomqvist, Sven, 1985, Reliability of core sampling of soft 

bottom sediment—An in situ study: Sedimentology, v. 32, 

p. 605–612. 

Blomqvist, Sven, and Bostrom, Kurt, 1987, Improved sampling of soft bottom sediments by combined box and piston 

coring: Sedimentology, v. 34, p. 715–719. 

Bradshaw, E.G., Rasmussen, P., Nielsen, H., and Anderson, 

N.J., 2005, Mid- to late-Holocene land-use change and 

lake development at Dallund So, Denmark—Trends in lake 

primary production as reflected by algal and macrophyte 

remains: The Holocene, v. 15, no. 8, p. 1130–1142. 

Carey, C.C., Weathers, K.C., and Cottingham, K.L., 2008, 

Gloeotrichia echinulata blooms in an oligotrophic lake—

Helpful insights from eutrophic lakes: Journal of Plankton 

Research, v. 30, no. 8, p. 893–904. 

Carey, C.C., and Rengefors, K., 2010, The cyanobacterium 

Gloeotrichia echinulata stimulates the growth of other 

phytoplankton: Journal of Plankton Research, v. 32, no. 9, 

p. 1349–1354. 

Carey, C.C., Ewing, H.A., Cottingham, K.L., Weathers, K.C., 

Thomas, R.Q., and Haney, J.F., 2012, Occurrence and 

toxicity of the cyanobacterium Gloeotrichia echinulata in 

low-nutrient lakes in the northeastern United States: Aquatic 

Ecology, v. 46, p. 395–409. 

Carey, C.C., Cottingham, K.L., Weathers, K.C., Brentrup, J.A., 

Ruppertsberger, N.M., Ewing, H.A., and Hairston, N.G., Jr., 

2014, Experimental blooms of the cyanobacterium Gloeotrichia echinulata increase phytoplankton biomass, richness 

and diversity in an oligotrophic lake: Journal of Plankton 

Research, v. 36, no. 2, p. 364–377. 

Chorus, Ingrid, and Bartram, Jamie, eds., 1999, Toxic cyanobacteria in water—A guide to their public health consequences, monitoring and management: London, E & FN 

Spon, 416 p. 

Cremer, Holger, and Wagner, B., 2003, The diatom flora in the 

ultra-oligotrophic Lake El’gygytgyn, Chukotka: Polar Biology, v. 26, p. 105–114. 

Crisman, T.L., 1986, Historical analysis of the cultural 

eutrophication of Lake Maxinkuckee, Indiana: Gainesville, 

Fla., University of Florida, Department of Environmental 

Engineering Sciences, 141 p. 

Cronberg, Gertrud, 1986, Blue-green algae, green algae and 

chrysophyceae in sediments, chap. 25, in Berglund, B.E., 

ed., Handbook of Holocene palaeoecology and palaeohydrology: Chichester, England, John Wiley and Sons, 

p. 507–526. 

Davies, B.E., 1983, Heavy metal contamination from base 

metal mining and smelting—Implications for man and 

his environment, chap. 14, in Thornton, Iain, ed., Applied 

environmental geochemistry: New York, Academic Press, 

p. 425–462. 

Davies, B.E., 1990, Lead, chap. 9, in Alloway, B.J., ed., 

Heavy metals in soils: New York, John Wiley and Sons, 

p. 177–196. 

De Martino, Giuseppe, Fontana, N., Marini, G., and Singh, 

V.P., 2013, Variability and trend in seasonal precipitation in 

the continental United States: Journal of Hydrologic Engineering, v. 18, p. 630–640. 

Dillon, P.J., and Rigler, F.H., 1974, The phosphorus-chlorophyll relationship in lakes: Limnology and Oceanography, 

v. 19, p. 767–773. 

Dixit, S.S., Smol, J.P., Kingston, J.C., and Charles, D.F., 1992, 

Diatoms—Powerful indicators of environmental change: 

Environmental Science and Technology, v. 26, no. 1, 

p. 23–33. 
References Cited 35

Emery, K.O., and Hulsemann, J., 1964, Shortening of sediment cores collected in open barrel gravity corers: Sedimentology, v. 3, p. 144–154. 

Engstrom, D.R., and Wright, H.E., Jr., 1984, Chemical stratigraphy of lake sediments as a record of environmental 

change, chap. 1, in Haworth, E.Y., and Lund, J.W.G., eds., 

Lake sediments and environmental history—Studies in 

palaeolimnology and palaeoecology in honour of Winifred 

Tutin: Minneapolis, Minn., University of Minnesota Press, 

p. 11–67. 

Fluin, Jennie, Tibby, J., and Gell, P., 2010, The palaeolimnological record from Lake Cullulleraine, lower Murray 

River (south-east Australia)—Implications for understanding riverine histories: Journal of Paleolimnology, v. 43, 

p. 309–322. 

Forstner, Ulrich, and Wittmann, G.T.W., 1981, Metal pollution 

in the aquatic environment: New York, Springer-Verlag, 

486 p. 

Fritz, S.C., Kingston, J.C., and Engstrom, D.R., 1993, Quantitative trophic reconstruction from sedimentary diatom 

assemblages—A cautionary tale: Freshwater Biology, v. 30, 

p. 1–23. 

Furr, G.F., Jr., 1987, Soil survey of Fulton County, Indiana: 

U.S. Department of Agriculture, Soil Conservation Service, 

141 p. 

Genkal, S.I., Mitrophanova, E.Y., and Kulikovskiy, M.S., 

2013, Morphological variability, taxonomy, and distribution 

of Cyclotella bodanica Eulenstein (Bacillariophyta) in Russia: Inland Water Biology, v. 6, no. 2, p. 85–97. 

Gray, H.H., 2000, Physiographic divisions of Indiana: Indiana 

Geological Survey Special Report 61, 15 p. 

Groisman, P.Y., Knight, R.W., and Karl, T.R., 2001, Heavy 

precipitation and high streamflow in the contiguous United 

States—Trends in the twentieth century: Bulletin of the 

American Meteorological Society, v. 82, no. 2, p. 219–246. 

Gutschick, R.C., 1966, Bedrock geology, chap. 1, in Lindsey, 

A.A., ed., Natural features of Indiana: Indianapolis, Ind., 

Indiana Academy of Science, p. 1–20. 

Hadley, K.R., Douglas, M.S.V., Blais, J.M., and Smol, J.P., 

2010, Nutrient enrichment in the High Arctic associated 

with Thule Inuit whalers—A paleolimnological investigation from Ellesmere Island (Nunavut, Canada): Hydrobiologia, v. 649, p. 129–138. 

Hakanson, L., and Jansson, M., 1983, Principles of lake sedimentology: New York, Springer-Verlag, 316 p. 

Hall, R.I., and Smol, J.P., 2010, Diatoms as indicators of lake 

eutrophication, chap. 7, in Smol, J.P., and Stoermer, E.F., 

eds., The diatoms—Applications for the environmental and 

earth sciences (2d ed.): New York, Cambridge University 

Press, p. 122–151. 

Heinsalu, Atko, Luup, H., Alliksaar, T., Noges, P. and Noges, 

T., 2008, Water level changes in a large shallow lake as 

reflected by the plankton:periphyton-ratio of sedimentary 

diatoms: Hydrobiologia, v. 599, p. 23–30. 

Hem, J.D., 1989, Study and interpretation of the chemical 

characteristics of natural water (3d ed.): U.S. Geological 

Survey Water-Supply Paper 2254, 263 p. 

Hongve, Dag, and Erlandsen, A.H., 1979, Shortening of surface sediment cores during sampling: Hydrobiologia, v. 65, 

no. 3, p. 283–287. 

Horowitz, A.J., 1991, A primer on sediment-trace element 

chemistry (2d ed.): Chelsea, Mich., Lewis Publishers, 136 p. 

Horowitz, A.J., and Stephens, V.C., 2008, The effects of land 

use on fluvial sediment chemistry for the conterminous 

U.S.—Results from the first cycle of the NAWQA program—Trace and major elements, phosphorus, carbon, 

and sulfur: Science of the Total Environment, v. 400, 

p. 290–314. 

Indiana Clean Lakes Program, 2014, Volunteer lake data for 

Maxinkuckee: accessed July 2014 at http://www.indiana.

edu/~clp/volunteer_data/lake_volunteer.php?Lake_ID=763.

Indiana Department of Environmental Management, 2012, 

Indiana integrated water monitoring and assessment report 

to the U.S. EPA 2012: Indianapolis, Ind., Indiana Department of Environmental Management, Office of Water Quality, [variously paged]. 

Istvanovics, V., Pettersson, K., Rodrigo, M.M., Pierson, D., 

Padisak, J., and Colom, W., 1993, Gloeotrichia echinulata, 

a colonial cyanobacterium with a unique phosphorus uptake 

and life strategy: Journal of Plankton Research, v. 15, 

p. 531–552. 

Jasprica, Nenad, and Hafner, D., 2005, Taxonomic composition and seasonality of diatoms in three Dinaric karstic lakes 

in Croatia: Limnologica, v. 35, p. 304–319. 

JF New & Associates, 2006, Lake Maxinkuckee lake and 

watershed management plan: accessed July 2013 at http://

www.lakemax.org.

Jin, S., Yang, L., Danielson, P., Homer, C., Fry, J., and Xian, 

G., 2013, A comprehensive change detection method for 

updating the National Land Cover Database to circa 2011: 

Remote Sensing of Environment, v. 132, p. 159–175. 
36 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Jones, J.R., and Bachmann, R.W., 1976, Prediction of phosphorus and chlorophyll levels in lakes: Journal Water Pollution Control Federation, v. 48, p. 2176–2182. 

Jones, J.R., Obrecht, D.V., Perkins, B.D., Knowlton, M.F., 

Thorpe, A.P., Watanabe, Shohei, and Bacon, R.R., 2008, 

Nutrients, seston, and transparency of Missouri reservoirs 

and oxbow lakes—An analysis of regional limnology: Lake 

and Reservoir Management, v. 24, p. 155–180. 

Juracek, K.E., and Ziegler, A.C., 2006, The legacy of leaded 

gasoline in bottom sediment of small rural reservoirs: Journal of Environmental Quality, v. 35, p. 2092–2102. 

Karickhoff, S.W., 1984, Organic pollutant sorption in aquatic 

systems: Journal of Hydraulic Engineering, v. 110, no. 6, 

p. 707–735. 

Karlsson, I., 2003, Benthic growth of Gloeotrichia echinulata

cyanobacteria: Hydrobiologia, v. 506–509, p. 189–193. 

Kling, H.J., 1998, A summary of past and recent plankton of 

Lake Winnipeg, Canada using algal fossil remains: Journal 

of Paleolimnology, v. 19, p. 297–307. 

Lemly, A.D., 2002, Interpreting selenium concentrations, 

chap. 2, in Lemly, A.D., Selenium assessment in aquatic 

ecosystems—A guide for hazard evaluation and water quality criteria: New York, Springer, p. 18–38. 

Lide, D.R., ed., 1993, CRC handbook of chemistry and physics (74th ed.): Boca Raton, Fla., CRC Press, [variously 

paged]. 

Livingstone, David, and Jaworski, G.H.M., 1980, The viability 

of akinetes of blue-green algae recovered from the sediments of Rostherne Mere: European Journal of Phycology, 

v. 15, p. 357–364. 

Luoma, S.N., and Rainbow, P.S., 2008, Metal contamination 

in aquatic environments—Science and lateral management: 

New York, Cambridge University Press, 573 p. 

MacDonald, D.D., Ingersoll, C.G., and Berger, T.A., 2000, 

Development and evaluation of consensus-based sediment 

quality guidelines for freshwater ecosystems: Archives 

of Environmental Contamination and Toxicology, v. 39, 

p. 20–31. 

Malvern, 2013, Mastersizer 2000: accessed August 2013 at 

www.malvern.com. 

Marmiroli, Nelson, and Maestri, Elena, 2008, Health implications of trace elements in the environment and the food 

chain, chap. 2, in Prasad, M.N.V., ed., Trace elements as 

contaminants and nutrients—Consequences in ecosystems 

and human health: Hoboken, N. J., John Wiley and Sons, 

p. 23–53. 

Marot, M.E., and Smith, C.G., 2012, Radioisotopic data 

of sediment collected in Mobile and Bon Secour Bays, 

Alabama: U.S. Geological Survey Open-File Report 

2012–1172, 15 p. 

National Climatic Data Center, 2013, 1981–2010 U.S. climate 

normals: accessed July 2013 at www.ncdc.noaa.gov. 

National Climatic Data Center, 2014, Record of climatological 

observations: accessed January 2014 at www.ncdc.noaa.gov. 

Negro, A.I., and De Hoyos, C., 2005, Relationships between 

diatoms and the environment in Spanish reservoirs: Limnetica, v. 24, nos. 1–2, p. 133–144. 

Olsson, I.U., 1986, Radiometric dating, chap. 14, in Berglund, 

B.E., ed., Handbook of Holocene palaeoecology and palaeohydrology: Chichester, England, John Wiley and Sons, 

p. 273–312. 

Ostrofsky, M.L., 2012, Differential post-depositional mobility 

of phosphorus species in lake sediments: Journal of Paleolimnology, v. 48, p. 559–569. 

Pais, Istvan, and Jones, J.B., Jr., 1997, The handbook of trace 

elements: Boca Raton, Fla., St. Lucie Press, 223 p. 

Patrick, R., and Reimer, C.W., 1966, The diatoms of the 

United States, exclusive of Alaska and Hawaii, volume 1— 

Fragilariaceae, eunotiaceae, achnanthaceae, naviculaceae: 

Monographs of the Academy of Natural Sciences of Philadelphia, no. 13, 688 p. 

Peel, M.C., Finlayson, B.L., and McMahon, T.A., 2007, 

Updated world map of the Koppen-Geiger climate classification: Hydrology and Earth System Sciences, Discussion, 

v. 4, p. 439–473. 

Pienitz, Reinhard, Roberge, K., and Vincent, W.F., 2006, 

Three hundred years of human-induced change in an urban 

lake—Paleolimnological analysis of Lac Saint-Augustin, 

Quebec City, Canada: Canadian Journal of Botany, v. 84, 

p. 303–320. 

Poister, David, Kurth, A., Farrell, A., and Gray, S., 2012, 

Seasonality of Aulacoseira ambigua abundance and filament length—Biogeochemical implications: Plankton and 

Benthos Research, v. 7, no. 2, p. 55–63. 

Rasanen, Johanna, Kauppila, T., and Vuorio, K., 2006a, Sediment and phytoplankton records of the cyanobacterial genus 

Anabaena in boreal Lake Pyhajarvi: Hydrobiologia, v. 568, 

p. 455–465. 

Rasanen, Johanna, Kauppila, T., and Salonen, V.-P., 2006b, 

Sediment-based investigation of naturally or historically 

eutrophic lakes—Implications for lake management: Journal of Environmental Management, v. 79, p. 253–265. 
References Cited 37

Rawson, D.S., 1956, Algal indicators of trophic lake types: 

Limnology and Oceanography, v. 1, no. 1, p. 18–25. 

Reed, J.M., Cvetkoska, A., Levkov, Z., Vogel, H., and Wagner, 

B., 2010, The last glacial-interglacial cycle in Lake Ohrid 

(Macedonia/Albania)—Testing diatom response to climate: 

Biogeosciences Discussions, v. 7, p. 4689–4714. 

Ritchie, J.C., and McHenry, J.R., 1990, Application of 

radioactive fallout cesium-137 for measuring soil erosion 

and sediment accumulation rates and patterns—A review: 

Journal of Environmental Quality, v. 19, p. 215–233. 

Rydin, Emil, 2000, Potentially mobile phosphorus in Lake 

Erken sediment: Water Research, v. 34, no. 7, p. 2037–2042. 

Schlegel, Ines, and Scheffler, W., 1999, Seasonal development and morphological variability of Cyclotella ocellata

(Bacillariophyceae) in the eutrophic Lake Dagow (Germany): International Review of Hydrobiology, v. 84, no. 5, 

p. 469–478. 

Schneider, A.F., 1966, Physiography, chap. 3, in Lindsey, 

A.A., ed., Natural features of Indiana: Indianapolis, Ind., 

Indiana Academy of Science, p. 40–56. 

Schneider, A.F., and Johnson, G.H., 1966, Late Wisconsin glacial history of the area around Lake Maxinkuckee: Proceedings of the Indiana Academy of Science, v. 76, p. 328–334. 

Smallwood, B.F., 1980, Soil survey of Marshall County, 

Indiana: U.S. Department of Agriculture, Soil Conservation 

Service, 136 p. 

Smol, J.P., 2008, Pollution of lakes and rivers—A paleoenvironmental perspective (2d ed.): Malden, Mass., Blackwell 

Publishing, 383 p. 

Smol, J.P., and Stoermer, E.F., eds., 2010, The diatoms—

Applications for the environmental and earth sciences 

(2d ed.): New York, Cambridge University Press, 667 p. 

Taggart, J.E., Jr., ed., 2002, Analytical methods for chemical 

analysis of geologic and other materials, U.S. Geological 

Survey: U.S. Geological Survey Open-File Report 02–223, 

[variously paged]. 

U.S. Census Bureau, 2014, Population estimates: accessed 

February 2014 at www.census.gov. 

U.S. Department of Agriculture, 2014, National Agricultural 

Statistics Service—data and statistics: accessed February 

2014 at www.nass.usda.gov. 

U.S. Environmental Protection Agency, 1977, Algae and water 

pollution: Municipal Environmental Research Laboratory, 

Office of Research and Development, Report 600–77–036, 

122 p. 

U.S. Environmental Protection Agency, 1983, Methods for 

chemical analysis of water and wastes: U.S. Environmental Protection Agency Report 600–4–79–020, [variously 

paged]. 

U.S. Environmental Protection Agency, 1997, The incidence 

and severity of sediment contamination in surface waters 

of the United States, volume 1—National sediment quality survey: U.S. Environmental Protection Agency Report 

823–R–97–006, [variously paged]. 

U.S. Environmental Protection Agency, 2000, National air 

pollutant emission trends, 1900-1998: U.S. Environmental 

Protection Agency Report 454-R-00-002, [variously paged]. 

van Dam, Herman, Mertens, A., and Sinkeldam, J., 1994, A 

coded checklist and ecological indicator values of freshwater diatoms from the Netherlands: Netherlands Journal of 

Aquatic Ecology, v. 28, p. 117–133. 

van Geel, B., Mur, L.R., Ralska-Jasiewiczowa, M., and Goslar, 

T., 1994, Fossil akinetes of Aphanizomenon and Anabaena

as indicators for medieval phosphate-eutrophication of Lake 

Gosciaz (Central Poland): Review of Palaeobotany and 

Palynology, v. 83, p. 97–105. 

Van Metre, P.C., Callender, Edward, and Fuller, C.C., 1997, 

Historical trends in organochlorine compounds in river 

basins identified using sediment cores from reservoirs: 

Environmental Science & Technology, v. 31, no. 8, 

p. 2339–2344. 

Van Metre, P.C., Wilson, J.T., Fuller, C.C., Callender, E., and 

Mahler, B.J., 2004, Collection, analysis, and age-dating of 

sediment cores from 56 U.S. lakes and reservoirs sampled 

by the U.S. Geological Survey, 1992–2001: U.S. Geological 

Survey Scientific Investigations Report 2004–5184, 180 p. 

Wayne, W.J., 1966, Ice and land—A review of the Tertiary and 

Pleistocene history of Indiana, chap. 2, in Lindsey, A.A., 

ed., Natural features of Indiana: Indianapolis, Ind., Indiana 

Academy of Science, p. 21–39. 

Wetzel, R.G., 2001, Limnology—Lake and river ecosystems 

(3d ed.): New York, Academic Press, 1006 p. 

White, D.J., Noll, M.R., and Makarewicz, J.C., 2008, Does 

manganese influence phosphorus cycling under suboxic lake 

water conditions?: Journal of Great Lakes Research, v. 34, 

p. 571–580. 

Wise, S.M., 1980, Caesium-137 and lead-210—A review of 

the techniques and some applications in geomorphology, 

chap. 9, in Cullingford, R.A., Davidson, D.A., and Lewin, 

J., eds., Timescales in Geomorphology: New York, John 

Wiley and Sons, p. 109–127. 
38 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Yilmaz, Nese, and Aykulu, G., 2010, An investigation on 

the seasonal variation of the phytoplankton density on the 

surface water of Sapanca Lake, Turkey: Pakistan Journal of 

Botany, v. 42, no. 2, p. 1213–1224. 

YSI, 2013, YSI 6600V2 water-quality monitor: accessed June 

2013 at http://www.ysi.com/productsdetail.php?6600V2-1.
Appendix
40 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Table 1–1. Latitude and longitude coordinates and water depth for bottom-sediment coring sites at 

Lake Maxinkuckee, northern Indiana, May 2013.

Coring site number

 (fig. 2)

Date cored 

(month/day/year)

Latitude 

(decimal degrees)

Longitude 

(decimal degrees)

Water depth1

(feet)

LM–1 05/15/13 41.20472 86.40806 72

LM–2 05/15/13 41.21444 86.41472 45

LM–3 05/16/13 41.21500 86.39972 35

LM–4 05/16/13 41.20444 86.39611 54

LM–5 05/14/13 41.19417 86.39944 45

LM–6 05/16/13 41.20744 86.40397 88

1

Water depth is rounded to the nearest foot.

Table 1–2. Vertical profiles of water-quality parameters measured at bottom-sediment coring sites LM–1 through LM–5, Lake 

Maxinkuckee, northern Indiana, May 14, 2013.

[Location of coring sites shown in figure 2. μS/cm, microsiemens per centimeter at 25 degrees Celsius; mg/L, milligrams per liter; FNU, formazin nephelometric 

units; μg/L, micrograms per liter; cells/mL, cells per milliliter]

Depth 

(feet) pH

Temperature, 

in degrees 

Celsius

Specific 

conductance 

(μS/cm)

Dissolved 

oxygen 

(mg/L)

Turbidity 

(FNU)

Chlorophyll, 

total 

(μg/L)

Cyanobacteria 

(cells/mL)

Coring site LM–1

0 8.26 14.86 390 11.55 1.8 3.9 680

6 8.20 14.81 390 11.62 1.5 9.6 1,160

12 8.18 14.72 390 11.61 1.6 14.7 1,280

18 8.18 14.57 391 11.62 1.9 16.0 1,350

24 8.04 12.56 396 10.96 1.9 12.8 1,210

30 7.85 12.20 399 10.58 1.0 11.0 1,180

36 7.60 10.06 403 9.93 0.3 6.0 1,000

42 7.51 9.50 403 9.53 0.2 4.4 800

48 7.41 9.09 405 9.01 0.2 3.0 740

54 7.34 8.87 407 8.56 0.2 3.3 720

60 7.35 8.84 408 8.28 0.4 3.2 720

66 7.44 8.76 409 8.09 0.3 3.0 720

Coring site LM–2

0 7.87 15.11 389 11.61 1.5 3.7 490

4 7.85 15.05 390 11.63 1.3 5.1 800

8 7.85 14.98 390 11.61 1.5 11.0 1,150

12 7.87 14.95 390 11.71 1.6 13.4 1,200

16 7.89 14.96 390 11.62 1.5 14.1 1,320

20 7.93 14.87 390 11.50 1.7 14.9 1,400

24 7.98 14.40 390 11.59 1.5 15.4 1,250

28 7.94 11.31 400 10.04 1.4 13.3 1,150

32 7.49 10.24 402 9.60 0.7 6.4 980

36 7.48 10.12 404 9.56 0.5 6.0 1,150

40 7.40 9.70 405 8.90 0.5 5.1 810
Appendix 41

Depth 

(feet) pH

Temperature, 

in degrees 

Celsius

Specific 

conductance 

(μS/cm)

Dissolved 

oxygen 

(mg/L)

Turbidity 

(FNU)

Chlorophyll, 

total 

(μg/L)

Cyanobacteria 

(cells/mL)

Coring site LM–3

0 7.62 15.42 389 11.56 1.9 4.3 800

3 7.70 15.38 389 11.56 1.7 3.9 650

6 7.74 15.29 389 11.63 1.7 5.0 690

9 7.86 15.24 389 11.58 1.7 6.0 980

12 7.95 15.10 390 11.58 2.1 12.4 1,290

15 7.99 14.97 390 11.67 1.7 15.0 1,390

18 8.04 14.95 390 11.58 1.8 15.8 1,360

21 8.07 14.92 390 11.57 1.8 16.1 1,270

24 8.11 14.96 390 11.57 1.8 15.5 1,300

27 8.13 14.91 390 11.62 1.8 15.8 1,480

30 8.14 14.93 390 11.57 1.8 15.2 1,460

33 8.16 14.85 389 11.52 2.0 15.5 1,240

Coring site LM–4

0 8.37 15.27 390 11.63 1.7 5.0 800

5 8.32 15.21 390 11.61 1.6 10.2 950

10 8.31 15.00 390 11.70 1.6 12.5 1,200

15 8.29 14.89 390 11.63 1.7 14.8 1,280

20 8.30 14.87 390 11.66 1.6 15.5 1,300

25 8.30 14.87 390 10.62 1.6 15.1 1,280

30 7.81 9.79 401 10.50 0.5 5.3 800

35 7.62 9.63 403 9.77 0.1 3.8 750

40 7.58 9.46 404 9.56 0.2 3.3 700

45 7.52 9.17 406 9.22 0.4 3.1 610

50 7.51 9.06 407 9.05 0.1 2.4 680

Coring site LM–5

0 8.22 14.04 386 11.31 1.4 5.0 960

4 8.21 14.02 386 11.30 1.3 6.1 970

8 8.22 14.02 386 11.33 1.3 9.7 1,020

12 8.22 13.95 386 11.35 1.2 12.8 1,100

16 7.85 10.94 397 10.32 0.5 8.0 1,160

20 7.77 10.72 399 9.98 0.6 6.9 1,010

24 7.66 9.80 401 9.52 0.3 5.2 880

28 7.61 9.71 402 9.20 0.2 4.0 820

32 7.58 9.46 403 9.04 0.3 4.1 820

36 7.59 9.43 403 8.93 0.2 3.9 960

40 7.60 9.42 403 8.90 0.5 4.0 670

Table 1–2. Vertical profiles of water-quality parameters measured at bottom-sediment coring sites LM–1 through LM–5, Lake 

Maxinkuckee, northern Indiana, May 14, 2013.—Continued

[Location of coring sites shown in figure 2. μS/cm, microsiemens per centimeter at 25 degrees Celsius; mg/L, milligrams per liter; FNU, formazin nephelometric 

units; μg/L, micrograms per liter; cells/mL, cells per milliliter]
42 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Table 1–3. Activity of cesium-137, lead-210, and radium-226 in bottom-sediment samples collected from Lake Maxinkuckee, northern 

Indiana, May 2013.

[The parenthetical values are the analytical variability for each sample. cm, centimeters; dup, duplicate analysis; dpm/g, disintegrations per minute per gram; ±, 

plus or minus error; R, recent; ND, not detected; --, not applicable; P, predevelopment]

Coring site 

number1

(fig. 2)

Depth 

interval 

(cm)

Radionuclide activity (dpm/g) Relative 

age of 

sediment Cesium-137 Lead-210 Radium-226

LM–1 0–2 0.69 (± 0.12) 22.67 (± 0.78) 1.07 (± 0.15) R

2–4 0.77 (± 0.10) 19.53 (± 0.58) 0.93 (± 0.10) R

4–6 0.73 (± 0.07) 17.01 (± 0.44) 0.86 (± 0.08) R

8–10 0.86 (± 0.08) 13.98 (± 0.48) 0.81 (± 0.08) R

8–10dup 0.88 (± 0.11) 14.40 (± 0.58) 0.81 (± 0.10) R

12–14 1.03 (± 0.09) 11.64 (± 0.46) 0.96 (± 0.09) R

16–18 1.18 (± 0.11) 10.19 (± 0.50) 0.96 (± 0.11) R

20–22 1.38 (± 0.11) 9.22 (± 0.47) 0.92 (± 0.10) R

24–26 1.59 (± 0.13) 8.11 (± 0.47) 0.93 (± 0.11) R

28–30 1.95 (± 0.18) 8.21 (± 0.61) 1.15 (± 0.15) R

LM–1G 50–60 ND (--) 1.61 (± 0.35) 1.14 (± 0.13) P

70–80 ND (--) 1.77 (± 0.38) 1.30 (± 0.14) P

LM–2 0–2 1.08 (± 0.13) 13.77 (± 0.58) 1.01 (± 0.13) R

2–4 0.96 (± 0.10) 12.72 (± 0.50) 1.09 (± 0.11) R

4–6 1.04 (± 0.12) 12.09 (± 0.55) 0.88 (± 0.11) R

8–10 1.05 (± 0.12) 11.48 (± 0.53) 1.02 (± 0.12) R

12–14 1.21 (± 0.11) 10.26 (± 0.45) 0.88 (± 0.10) R

16–18 1.33 (± 0.14) 8.71 (± 0.49) 1.05 (± 0.16) R

20–22 1.84 (± 0.15) 7.08 (± 0.46) 1.05 (± 0.12) R

24–26 1.97 (± 0.13) 6.06 (± 0.38) 1.00 (± 0.10) R

28–30 2.38 (± 0.15) 6.31 (± 0.40) 1.25 (± 0.13) R

LM–2G 40–50 ND (--) 1.39 (± 0.40) 1.12 (± 0.17) P

60–70 ND (--) 1.85 (± 0.37) 1.14 (± 0.15) P

LM–3 0–2 1.48 (± 0.13) 12.82 (± 0.51) 1.19 (± 0.16) R

2–4 1.52 (± 0.14) 11.44 (± 0.54) 1.19 (± 0.16) R

4–6 1.55 (± 0.14) 10.67 (± 0.52) 1.09 (± 0.16) R

8–10 1.58 (± 0.14) 10.16 (± 0.52) 1.34 (± 0.18) R

12–14 1.85 (± 0.15) 9.21 (± 0.50) 1.32 (± 0.17) R

16–18 1.95 (± 0.11) 7.60 (± 0.34) 1.37 (± 0.12) R

20–22 2.22 (± 0.13) 6.78 (± 0.37) 1.40 (± 0.14) R

24–26 1.71 (± 0.12) 4.58 (± 0.32) 1.52 (± 0.15) R

LM–3G 30–40 ND (--) 1.25 (± 0.20) 1.40 (± 0.12) P

50–60 ND (--) 1.63 (± 0.27) 1.46 (± 0.15) P

70–80 ND (--) 1.59 (± 0.26) 1.07 (± 0.13) P
Appendix 43

Coring site 

number1

(fig. 2)

Depth 

interval 

(cm)

Radionuclide activity (dpm/g) Relative 

age of 

sediment Cesium-137 Lead-210 Radium-226

LM–4 0–2 0.97 (± 0.12) 16.36 (± 0.59) 1.14 (± 0.13) R

2–4 1.04 (± 0.14) 16.52 (± 0.67) 1.05 (± 0.14) R

4–6 1.02 (± 0.13) 14.76 (± 0.60) 0.91 (± 0.11) R

8–10 1.16 (± 0.09) 12.52 (± 0.42) 1.01 (± 0.09) R

8–10dup 0.98 (± 0.13) 12.48 (± 0.54) 0.97 (± 0.12) R

12–14 1.45 (± 0.14) 9.76 (± 0.49) 1.13 (± 0.12) R

16–18 1.73 (± 0.15) 8.22 (± 0.47) 1.05 (± 0.13) R

20–22 2.31 (± 0.15) 7.41 (± 0.41) 1.18 (± 0.11) R

24–26 3.07 (± 0.18) 5.87 (± 0.41) 1.20 (± 0.12) R

28–30 3.24 (± 0.14) 5.01 (± 0.32) 1.30 (± 0.10) R

LM–5 0–2 1.67 (± 0.13) 13.57 (± 0.70) 1.28 (± 0.14) R

0–2dup 1.82 (± 0.14) 13.22 (± 0.72) 1.22 (± 0.14) R

2–4 1.71 (± 0.12) 12.85 (± 0.61) 1.20 (± 0.12) R

4–6 1.81 (± 0.13) 13.17 (± 0.72) 1.08 (± 0.13) R

8–10 1.99 (± 0.14) 12.98 (± 0.71) 1.14 (± 0.13) R

12–14 2.04 (± 0.12) 11.29 (± 0.59) 1.06 (± 0.12) R

16–18 2.28 (± 0.14) 9.72 (± 0.67) 1.16 (± 0.13) R

LM–6G 40–50 1.28 (± 0.13) 6.03 (± 0.68) 2.53 (± 0.23) R

60–70 ND (--) 1.71 (± 0.45) 2.04 (± 0.19) P

80–90 ND (--) 2.34 (± 0.53) 2.56 (± 0.22) P

1

Coring site numbers ending in “G” indicate a gravity core. Other coring site numbers indicate a box core.

Table 1–3. Activity of cesium-137, lead-210, and radium-226 in bottom-sediment samples collected from Lake Maxinkuckee, northern 

Indiana, May 2013.—Continued

[The parenthetical values are the analytical variability for each sample. cm, centimeters; dup, duplicate analysis; dpm/g, disintegrations per minute per gram; ±, 

plus or minus error; R, recent; ND, not detected; --, not applicable; P, predevelopment]
44 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Table 1–4. Percentage of sand, silt, and clay in bottom-sediment samples collected from Lake 

Maxinkuckee, northern Indiana, May 2013.

[cm, centimeters; R, recent sediment; P, predevelopment sediment; dup, duplicate analysis]

Coring site 

number1

(fig. 2)

Depth interval in core, 

below sediment-water 

interface (cm)

Percentage 

of sand2

Percentage 

of silt2

Percentage 

of clay2

LM–1 8–10 (R) 4.54 65.42 30.04

12–14 (R) 2.42 65.61 31.96

16–18 (R) 2.67 66.70 30.63

20–22 (R) 2.57 67.26 30.17

24–26 (R) 1.97 65.94 32.09

LM–2 4–6 (R) 5.09 55.64 39.27

8–10 (R) 3.95 62.94 33.11

12–14 (R) 3.96 59.32 36.72

16–18 (R) 3.08 65.30 31.62

20–22 (R) 2.81 57.58 39.61

24–26 (R) 4.96 64.61 30.43

LM–3 4–6 (R) 9.17 60.06 30.77

8–10 (R) 8.27 61.03 30.71

12–14 (R) 10.82 56.36 32.82

16–18 (R) 10.97 61.26 27.77

20–22 (R) 12.82 58.25 28.93

24–26 (R) 7.82 61.12 31.06

LM–3G 70–80 (P) 4.02 62.56 33.43

70–80dup (P) 3.91 63.34 32.75

LM–4 4–6 (R) 3.84 59.38 36.79

8–10 (R) 4.11 60.37 35.53

8–10dup (R) 5.66 63.92 30.42

12–14 (R) 3.43 60.27 36.30

12–14dup (R) 3.14 61.89 34.97

16–18 (R) 7.14 67.42 25.44

20–22 (R) 4.97 55.92 39.11

24–26 (R) 3.15 62.85 34.00

LM–5 0–2 (R) 8.91 57.39 33.70

8–10 (R) 9.00 55.00 36.00

12–14 (R) 5.77 61.50 32.73

LM–6G 80–90 (P) 5.97 74.54 19.49

1

Coring site numbers ending in “G” indicate a gravity core. Other coring site numbers indicate a box core. 

2

Sand was defined as particles greater than 63 micrometers (μm) in size. Silt was defined as particles 4 to 63 μm in 

size. Clay was defined as particles less than 4 μm in size.
Appendix 45

Table 1–5. Concentrations of nutrients, carbon, and trace elements for bottom-sediment samples collected from coring site LM–1 in 

Lake Maxinkuckee, northern Indiana, May 2013.

[Shading indicates concentration greater than threshold-effects guideline listed in table 2. cm, centimeters; R, recent sediment; mg/kg, milligrams per kilogram; 

--, not available; %, percent dry weight; <, less than]

Constituent and unit 

of measurement

Constituent concentration

Interval 1 Interval 2 Interval 3 Interval 4 Interval 5 Interval 6 Interval 7 Interval 8 Interval 9

28–30 cm, 

R (bottom 

of core)

24–26 cm,

 R

20–22 cm, 

R

16–18 cm, 

R

12–14 cm, 

R

8–10 cm, 

R

4–6 cm, 

R

2–4 cm, 

R

0–2 cm, 

R (top of 

core)

Nutrients

Total nitrogen, mg/kg -- 642 956 474 1,130 893 1,010 1,300 1,290

Total phosphorus, mg/kg 489 505 469 488 499 525 582 628 735

Carbon

Carbon (total organic), % 4 4 4.1 4.2 4.2 4.6 4.5 4.9 5.4

Carbon (total), % 11.7 11.8 11.9 12.1 12.3 12.6 12.6 12.7 12.7

Trace elements

Aluminum, mg/kg 13,400 12,900 11,800 11,800 10,900 10,500 9,960 10,100 10,000

Antimony, mg/kg 0.49 0.48 0.41 0.38 0.36 0.39 0.34 0.4 0.38

Arsenic, mg/kg 26.2 25.1 22.3 21.8 21.7 20.8 20 18.8 15.9

Barium, mg/kg 333 334 315 328 326 331 318 318 324

Beryllium, mg/kg 0.42 0.35 0.35 0.35 0.35 0.33 0.25 0.34 0.3

Bismuth, mg/kg 0.09 0.11 0.07 0.09 <0.06 0.09 <0.06 0.12 <0.06

Cadmium, mg/kg 0.45 0.45 0.38 0.37 0.31 0.33 0.28 0.33 0.28

Calcium, mg/kg 256,000 242,000 248,000 245,000 264,000 253,000 260,000 247,000 255,000

Cerium, mg/kg 13.5 13.4 12.3 12.3 11.6 11.2 10.3 10.7 10.8

Cesium, mg/kg 1.1 1.1 0.91 0.94 0.86 0.86 0.77 0.86 0.81

Chromium, mg/kg 13 12.7 11.9 12 11 11 10.3 10.3 10.7

Cobalt, mg/kg 2.6 2.7 2.3 2.4 2.2 2.2 2.1 2.2 2.1

Copper, mg/kg 15.4 16.2 14.7 14.4 14.4 16.9 15.8 14.9 16.6

Gallium, mg/kg 3.3 3.2 2.9 2.9 2.8 2.6 2.4 2.4 2.4

Iron, mg/kg 11,800 11,400 10,800 10,700 10,700 10,500 10,300 10,100 9,730

Lanthanum, mg/kg 6.6 6.5 6.3 6 5.7 5.5 5 5.3 5.2

Lead, mg/kg 47.3 45.2 37.2 33.4 29.5 28.6 23.8 23.6 23.5

Lithium, mg/kg 9.1 6.4 8.9 7.1 7 4.4 6.8 5.1 6

Magnesium, mg/kg 9,250 9,030 9,060 9,100 9,320 9,330 9,270 9,210 9,080

Manganese, mg/kg 683 673 687 674 707 717 735 718 765

Mercury, mg/kg 0.05 0.05 0.05 0.04 0.05 0.04 0.04 0.04 0.05

Molybdenum, mg/kg 6 6.1 5.7 5.1 5.4 5.4 4.9 4.8 3.1

Nickel, mg/kg 2.6 3.4 2.3 2.4 0.9 2.9 1.6 2.7 3.7

Niobium, mg/kg 1.9 1.8 1.6 1.7 1.5 1.7 1.5 1.7 1.6

Potassium, mg/kg 4,510 4,330 4,010 3,990 3,780 3,650 3,530 3,500 3,520

Rubidium, mg/kg 21.7 20.2 19 18.3 17.5 16.6 16 15.6 16.5

Scandium, mg/kg 1.7 2.3 1.4 2 1.3 1.9 1.2 1.8 1.2

Selenium, mg/kg 1.25 1.37 1.2 1.34 1.27 1.42 1.32 1.43 1.32

Silver, mg/kg 0.019 0.101 0.01 0.096 <0.01 0.094 <0.01 0.116 <0.01

Sodium, mg/kg 1,240 1,180 1,150 1,160 1,120 1,050 1,030 1,020 1,070

Strontium, mg/kg 328 323 329 325 346 340 353 330 343

Sulfur, % 0.92 0.81 0.87 0.72 0.76 0.82 0.81 0.78 0.66

Thallium, mg/kg 0.22 0.21 0.2 0.18 0.16 0.16 0.15 0.19 0.15

Thorium, mg/kg 1.83 1.89 1.71 1.69 1.51 1.53 1.37 1.46 1.45

Titanium, mg/kg 567 521 480 501 436 469 413 427 434

Uranium, mg/kg 1.5 1.67 1.47 1.61 1.5 1.61 1.34 1.53 1.21

Vanadium, mg/kg 21 20.6 17.4 18.1 17.9 17.1 16.3 16.4 16.3

Yttrium, mg/kg 4.3 4.2 3.9 3.8 3.7 3.7 3.4 3.4 3.5

Zinc, mg/kg 71.5 70 63.7 62 60 60.3 61.1 59.3 78.3
46 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Table 1–6. Concentrations of nutrients, carbon, and trace 

elements for bottom-sediment samples collected from coring 

site LM–1G in Lake Maxinkuckee, northern Indiana, May 2013.

[Shading indicates concentration greater than threshold-effects guideline listed 

in table 2. cm, centimeters; P, pre-development sediment; mg/kg, milligrams 

per kilogram; %, percent dry weight; <, less than]

Constituent and unit of 

measurement

Constituent concentration

Interval 1

70–80 cm, P

Interval 2

50–60 cm, P

Nutrients

Total nitrogen, mg/kg 615 3,640

Total phosphorus, mg/kg 927 684

Carbon

Carbon (total organic), % 11.5 7.8

Carbon (total), % 15.6 14.7

Trace elements

Aluminum, mg/kg 14,400 10,400

Antimony, mg/kg 0.23 0.1

Arsenic, mg/kg 27.2 17.6

Barium, mg/kg 253 296

Beryllium, mg/kg 0.47 0.26

Bismuth, mg/kg <0.06 <0.06

Cadmium, mg/kg 0.25 0.16

Calcium, mg/kg 136,000 217,000

Cerium, mg/kg 16.3 11.9

Cesium, mg/kg 1.3 0.92

Chromium, mg/kg 14.2 10.6

Cobalt, mg/kg 4 2.8

Copper, mg/kg 13.5 9.7

Gallium, mg/kg 3.6 2.6

Iron, mg/kg 39,100 23,200

Lanthanum, mg/kg 8.1 5.8

Lead, mg/kg 7.03 5.78

Lithium, mg/kg 12.2 6.2

Magnesium, mg/kg 8,440 8,950

Manganese, mg/kg 619 666

Mercury, mg/kg 0.03 0.02

Molybdenum, mg/kg 9.3 4.7

Nickel, mg/kg 8.2 3.6

Niobium, mg/kg 1.8 1.5

Potassium, mg/kg 5,310 3,860

Rubidium, mg/kg 24.2 17.3

Scandium, mg/kg 2 2

Selenium, mg/kg 1.77 1.16

Silver, mg/kg <0.01 <0.01

Sodium, mg/kg 1,330 1,060

Strontium, mg/kg 190 258

Sulfur, % 0.63 0.26

Thallium, mg/kg 0.21 0.14

Thorium, mg/kg 2.22 1.6

Titanium, mg/kg 584 455

Uranium, mg/kg 1.59 1.02

Vanadium, mg/kg 25 17.8

Yttrium, mg/kg 5.3 3.9

Zinc, mg/kg 48.7 31.3
Appendix 47

Table 1–7. Concentrations of nutrients, carbon, and trace elements for bottom-sediment samples collected from coring site LM–2 in 

Lake Maxinkuckee, northern Indiana, May 2013.

[Shading indicates concentration greater than threshold-effects guideline listed in table 2. cm, centimeters; R, recent sediment; mg/kg, milligrams per kilogram; 

--, not available; %, percent dry weight; <, less than]

Constituent and unit 

of measurement

Constituent concentration

Interval 1 Interval 2 Interval 3 Interval 4 Interval 5 Interval 6 Interval 7 Interval 8 Interval 9

28–30 cm, 

R (bottom 

of core)

24–26 cm,

 R

20–22 cm, 

R

16–18 cm, 

R

12–14 cm, 

R

8–10 cm, 

R

4–6 cm, 

R

2–4 cm, 

R

0–2 cm, 

R (top of 

core)

Nutrients

Total nitrogen, mg/kg -- 1,370 649 709 1,000 2,290 1,350 1,520 --

Total phosphorus, mg/kg 467 500 468 488 512 565 593 607 608

Carbon

Carbon (total organic), % 4.3 4.5 4.4 4.4 4.7 4.4 4.7 4.6 5

Carbon (total), % 12.6 12.8 12.8 12.9 13.3 13 13.3 13.1 13.5

Trace elements

Aluminum, mg/kg 13,200 12,000 11,800 11,100 9,970 9,590 9,480 9,500 9,670

Antimony, mg/kg 0.69 0.55 0.54 0.51 0.4 0.41 0.38 0.37 0.34

Arsenic, mg/kg 19.2 18.7 17.6 16.4 14.3 14.8 16.5 18.6 19.5

Barium, mg/kg 349 327 339 329 334 321 338 332 346

Beryllium, mg/kg 0.45 0.37 0.41 0.35 0.33 0.27 0.29 0.31 0.35

Bismuth, mg/kg 0.13 0.09 0.11 0.07 0.09 0.06 0.08 0.07 0.08

Cadmium, mg/kg 0.66 0.55 0.66 0.47 0.45 0.4 0.39 0.38 0.38

Calcium, mg/kg 263,000 272,000 261,000 275,000 266,000 279,000 264,000 275,000 266,000

Cerium, mg/kg 15.9 13.3 13.1 12.1 11.7 10.9 11 10.5 10.9

Cesium, mg/kg 1.1 0.98 0.96 0.85 0.82 0.76 0.78 0.75 0.79

Chromium, mg/kg 14 12.9 12.5 12.4 11.3 10.9 11 10.5 10.7

Cobalt, mg/kg 2.7 2.5 2.5 2.3 2.2 2.1 2.1 2 2.2

Copper, mg/kg 16.8 16.2 17 15.6 15 16 15.4 17.8 18

Gallium, mg/kg 3.2 3.1 3 2.7 2.6 2.4 2.5 2.5 2.5

Iron, mg/kg 9,750 9,450 9,230 9,350 8,860 8,800 9,150 9,280 9,410

Lanthanum, mg/kg 7 6.6 6.4 6 5.7 5.3 5.4 5.2 5.4

Lead, mg/kg 61.8 54 50 43.5 37.5 33.9 33.7 32.5 32.6

Lithium, mg/kg 8.2 11.4 7.2 11.3 7.1 9.1 4.6 8.9 5.8

Magnesium, mg/kg 9,500 9,810 9,540 9,930 9,380 9,760 9,270 9,520 9,370

Manganese, mg/kg 678 701 688 715 726 783 845 919 932

Mercury, mg/kg 0.08 0.08 0.07 0.06 0.06 0.05 0.06 0.05 0.06

Molybdenum, mg/kg 2.8 2.4 2.4 2.3 1.7 1.2 0.97 0.89 0.9

Nickel, mg/kg 3.8 1.9 3.4 1.7 1.6 0.4 1.5 0.5 2.4

Niobium, mg/kg 1.9 2 1.7 1.8 1.6 1.4 1.5 1.6 1.6

Potassium, mg/kg 4,390 4,170 3,860 3,760 3,500 3,370 3,330 3,290 3,300

Rubidium, mg/kg 21.1 20.4 18.7 18.4 16.2 16.1 15.6 15.7 15.4

Scandium, mg/kg 2.4 1.6 2.1 1.3 1.8 1.1 1.8 2 1.8

Selenium, mg/kg 1.47 1.29 1.4 1.31 1.31 1.2 1.26 1.16 1.29

Silver, mg/kg 0.156 0.042 0.125 0.015 0.082 <0.01 0.073 <0.01 0.09

Sodium, mg/kg 1,200 1,180 1,080 1,070 979 970 944 980 958

Strontium, mg/kg 338 351 340 363 347 365 353 359 352

Sulfur, % 0.31 0.37 0.29 0.31 0.3 0.24 0.13 0.18 0.13

Thallium, mg/kg 0.23 0.22 0.2 0.19 0.17 0.16 0.15 0.16 0.16

Thorium, mg/kg 2 1.79 1.78 1.58 1.56 1.41 1.49 1.38 1.49

Titanium, mg/kg 562 535 528 499 448 427 429 439 440

Uranium, mg/kg 1.74 1.47 1.52 1.44 1.3 1.12 1.01 0.84 0.83

Vanadium, mg/kg 21.5 19.7 19.1 18.2 16.9 16.6 15.6 16.1 15.5

Yttrium, mg/kg 4.5 4.4 4.1 4 3.6 3.5 3.5 3.4 3.5

Zinc, mg/kg 92.6 87.7 83.1 78.8 71.2 70.8 70.1 70.4 71.4
48 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Table 1–8. Concentrations of nutrients, carbon, and trace 

elements for bottom-sediment samples collected from coring site 

LM–2G in Lake Maxinkuckee, northern Indiana, May 2013.

[Shading indicates concentration greater than threshold-effects guideline listed 

in table 2. cm, centimeters; P, pre-development sediment; mg/kg, milligrams 

per kilogram; %, percent dry weight; <, less than]

Constituent and unit 

of measurement

 Constituent concentration

Interval 1

60–70 cm, P

Interval 2

40–50 cm, P

Nutrients

Total nitrogen, mg/kg 6,190 4,670

Total phosphorus, mg/kg 714 535

Carbon

Carbon (total organic), % 17.9 9.3

Carbon (total), % 21.6 16.9

Trace elements

Aluminum, mg/kg 17,600 8,520

Antimony, mg/kg 0.38 0.1

Arsenic, mg/kg 25.5 13

Barium, mg/kg 264 287

Beryllium, mg/kg 0.53 0.26

Bismuth, mg/kg 0.09 <0.06

Cadmium, mg/kg 0.44 0.16

Calcium, mg/kg 117,000 237,000

Cerium, mg/kg 19.4 10.7

Cesium, mg/kg 1.8 0.82

Chromium, mg/kg 19.6 9.6

Cobalt, mg/kg 5.9 2.5

Copper, mg/kg 17.5 9

Gallium, mg/kg 4.7 2.4

Iron, mg/kg 21,400 12,700

Lanthanum, mg/kg 9.6 5.4

Lead, mg/kg 8.67 4.65

Lithium, mg/kg 6.7 3.5

Magnesium, mg/kg 8,380 7,880

Manganese, mg/kg 354 588

Mercury, mg/kg 0.04 0.02

Molybdenum, mg/kg 16.1 5.8

Nickel, mg/kg 14.9 2

Niobium, mg/kg 2.6 1.5

Potassium, mg/kg 7,090 3,120

Rubidium, mg/kg 32.5 15.5

Scandium, mg/kg 3.5 1.7

Selenium, mg/kg 2.97 1.06

Silver, mg/kg 0.082 0.011

Sodium, mg/kg 1,460 806

Strontium, mg/kg 200 300

Sulfur, % 0.75 0.27

Thallium, mg/kg 0.29 0.13

Thorium, mg/kg 3.05 1.55

Titanium, mg/kg 746 403

Uranium, mg/kg 2.71 1.15

Vanadium, mg/kg 32.5 15.8

Yttrium, mg/kg 6.7 3.6

Zinc, mg/kg 62 26.6
Appendix 49

Table 1–9. Concentrations of nutrients, carbon, and trace elements for bottom-sediment samples collected from coring site LM–3 in 

Lake Maxinkuckee, northern Indiana, May 2013.

[Shading indicates concentration greater than threshold-effects guideline listed in table 2. cm, centimeters; R, recent sediment; mg/kg, milligrams per kilogram; 

%, percent dry weight]

Constituent and unit 

of measurement

Constituent concentration

Interval 1 Interval 2 Interval 3 Interval 4 Interval 5 Interval 6 Interval 7 Interval 8

24–26 cm, 

R (bottom of 

core)

20–22 cm,

R

16–18 cm, 

R

12–14 cm, 

R

8–10 cm, 

R

4–6 cm, 

R

2–4 cm, 

R

0–2 cm, 

R (top of core)

Nutrients

Total nitrogen, mg/kg 691 922 2,660 1,690 1,310 1,130 598 1,140

Total phosphorus, mg/kg 384 469 407 467 465 542 513 573

Carbon

Carbon (total organic), % 4.6 4.6 5 5.8 5.3 5.2 5.4 5.1

Carbon (total), % 9.82 11 11.2 11.3 11.9 11.8 12 11.7

Trace elements

Aluminum, mg/kg 24,900 20,900 18,800 18,800 17,800 17,600 17,600 17,200

Antimony, mg/kg 1.5 0.68 0.67 0.56 0.57 0.49 0.49 0.4

Arsenic, mg/kg 25.9 20.7 19.4 18.9 17.3 17.3 17.5 21.8

Barium, mg/kg 370 357 353 348 348 340 344 347

Beryllium, mg/kg 0.63 0.65 0.48 0.57 0.44 0.5 0.43 0.49

Bismuth, mg/kg 0.14 0.14 0.14 0.12 0.12 0.11 0.13 0.11

Cadmium, mg/kg 0.6 0.64 0.62 0.56 0.55 0.53 0.53 0.51

Calcium, mg/kg 149,000 195,000 185,000 203,000 193,000 206,000 193,000 208,000

Cerium, mg/kg 28.1 23.3 21.3 21.4 19.4 20.7 20.2 20.5

Cesium, mg/kg 2 1.6 1.5 1.5 1.4 1.4 1.4 1.3

Chromium, mg/kg 24.2 20.3 20.4 19 19.1 18.3 18.7 18.4

Cobalt, mg/kg 5.4 4.8 4.5 4.4 4.2 4.1 4.2 4.1

Copper, mg/kg 18.6 19.5 18.7 19.6 19.2 20.2 21.2 19.1

Gallium, mg/kg 6 5.1 4.8 4.7 4.4 4.4 4.3 4.4

Iron, mg/kg 16,500 13,900 12,800 13,300 12,300 12,700 12,200 13,100

Lanthanum, mg/kg 13.5 11.1 10.1 10.2 9.2 10 9.5 9.9

Lead, mg/kg 50.2 53.4 49.3 46.9 42.9 43.3 42.5 40.1

Lithium, mg/kg 9.6 9.9 6 9.9 4.2 9.5 6 8

Magnesium, mg/kg 10,300 11,100 10,400 11,000 10,300 10,800 10,100 10,600

Manganese, mg/kg 508 584 560 603 624 675 670 865

Mercury, mg/kg 0.11 0.09 0.09 0.09 0.09 0.08 0.09 0.07

Molybdenum, mg/kg 3.4 2.2 2.3 2.2 1.5 1.3 1.2 1

Nickel, mg/kg 12.1 7.2 8.1 6.4 7.2 5.9 7.4 5.9

Niobium, mg/kg 4 3.1 3 3.1 2.9 3 3.1 2.9

Potassium, mg/kg 10,100 7,610 7,660 6,970 7,130 6,530 7,020 6,460

Rubidium, mg/kg 41.6 34.1 31.8 31.6 30 30 29.5 29.4

Scandium, mg/kg 4.2 3.5 3.2 3.2 3 3.1 3 3

Selenium, mg/kg 1.28 1.28 1.43 1.27 1.41 1.26 1.4 1.24

Silver, mg/kg 0.258 0.249 0.27 0.216 0.262 0.274 0.266 0.205

Sodium, mg/kg 3,200 2,750 2,510 2,490 2,300 2,210 2,210 2,210

Strontium, mg/kg 226 269 269 279 276 285 280 293

Sulfur, % 0.55 0.48 0.53 0.48 0.34 0.38 0.26 0.24

Thallium, mg/kg 0.4 0.34 0.33 0.31 0.29 0.29 0.3 0.28

Thorium, mg/kg 3.93 3.11 2.97 2.83 2.66 2.75 2.8 2.66

Titanium, mg/kg 1,220 1,010 897 930 872 896 860 893

Uranium, mg/kg 1.99 1.77 1.71 1.74 1.59 1.49 1.36 1.16

Vanadium, mg/kg 35.8 30.2 29.3 28.3 27.2 26.1 27 26.3

Yttrium, mg/kg 8.4 7.2 6.8 6.7 6.4 6.4 6.4 6.3

Zinc, mg/kg 102 113 105 105 151 101 98.6 97.6
50 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Table 1–10. Concentrations of nutrients, carbon, and trace elements for bottom-sediment samples 

collected from coring site LM–3G in Lake Maxinkuckee, northern Indiana, May 2013.

[Shading indicates concentration greater than threshold-effects guideline listed in table 2. cm, centimeters; P, predevelopment sediment; mg/kg, milligrams per kilogram; %, percent dry weight; <, less than]

Constituent and unit 

of measurement

 Constituent concentration

Interval 1

70–80 cm, P

Interval 2

50–60 cm, P

Interval 3

30–40 cm, P

Nutrients

Total nitrogen, mg/kg 2,640 2,730 2,160

Total phosphorus, mg/kg 555 486 462

Carbon

Carbon (total organic), % 7.8 7 5.4

Carbon (total), % 13.5 12.8 12.3

Trace elements

Aluminum, mg/kg 20,200 20,300 16,400

Antimony, mg/kg 0.2 0.2 0.1

Arsenic, mg/kg 10.3 8.9 8.3

Barium, mg/kg 329 332 325

Beryllium, mg/kg 0.54 0.49 0.42

Bismuth, mg/kg <0.06 <0.06 <0.06

Cadmium, mg/kg 0.19 0.17 0.12

Calcium, mg/kg 175,000 159,000 208,000

Cerium, mg/kg 24.4 23.9 20.2

Cesium, mg/kg 1.7 1.6 1.3

Chromium, mg/kg 19.6 19.1 15.3

Cobalt, mg/kg 4.7 4.4 3.6

Copper, mg/kg 10.7 10.6 10.1

Gallium, mg/kg 4.8 4.7 4

Iron, mg/kg 12,400 11,700 10,600

Lanthanum, mg/kg 11.8 11.4 9.5

Lead, mg/kg 8.89 9.4 8.01

Lithium, mg/kg 10 5.9 7.7

Magnesium, mg/kg 12,400 11,900 12,400

Manganese, mg/kg 444 446 553

Mercury, mg/kg 0.02 0.02 0.02

Molybdenum, mg/kg 6.5 5.8 3.8

Nickel, mg/kg 8.1 8.6 4.4

Niobium, mg/kg 3.1 3.1 2.5

Potassium, mg/kg 8,210 8,870 6,630

Rubidium, mg/kg 34.7 33.8 28.2

Scandium, mg/kg 3.6 3.6 3

Selenium, mg/kg 1.02 0.86 0.62

Silver, mg/kg 0.042 0.093 0.039

Sodium, mg/kg 2,560 2,810 2,290

Strontium, mg/kg 247 226 265

Sulfur, % 0.35 0.31 0.21

Thallium, mg/kg 0.25 0.26 0.2

Thorium, mg/kg 3.31 3.38 2.63

Titanium, mg/kg 946 948 782

Uranium, mg/kg 1.88 1.44 1.18

Vanadium, mg/kg 27.9 27.7 22.3

Yttrium, mg/kg 7.2 7.4 6.1

Zinc, mg/kg 45.9 43.6 36.6
Appendix 51

Table 1–11. Concentrations of nutrients, carbon, and trace elements for bottom-sediment samples collected from coring site LM–4 in 

Lake Maxinkuckee, northern Indiana, May 2013.

[Shading indicates concentration greater than threshold-effects guideline listed in table 2. cm, centimeters; R, recent sediment; mg/kg, milligrams per kilogram; 

--, not available; %, percent dry weight; <, less than]

Constituent and unit 

of measurement

Constituent concentration

Interval 1 Interval 2 Interval 3 Interval 4 Interval 5 Interval 6 Interval 7 Interval 8 Interval 9

28–30 cm, R 

(bottom of 

core)

24–26 cm,

 R

20–22 cm, 

R

16–18 cm, 

R

12–14 cm, 

R

8–10 cm, 

R

4–6 cm, 

R

2–4 cm, 

R

0–2 cm, 

R (top of 

core)

Nutrients

Total nitrogen, mg/kg -- 891 1,580 2,240 1,510 1,430 1,690 1,310 1,100

Total phosphorus, mg/kg 440 448 422 448 563 471 528 571 575

Carbon

Carbon (total organic), % 5.1 4.9 4.6 4.8 5 4.8 5 5.1 5.3

Carbon (total), % 12.3 12.4 12.5 12.8 13 12.9 13.2 13.3 13.3

Trace elements

Aluminum, mg/kg 15,600 14,800 12,500 11,900 13,700 9,820 9,350 9,310 9,550

Antimony, mg/kg 1.2 0.99 0.71 0.52 0.65 0.31 0.39 0.56 0.4

Arsenic, mg/kg 32.1 28.9 22.2 21.1 19.4 18.5 16.6 16.1 16

Barium, mg/kg 345 340 337 332 368 324 321 320 331

Beryllium, mg/kg 0.52 0.55 0.4 0.39 0.44 0.33 0.25 0.29 0.23

Bismuth, mg/kg 0.26 0.18 0.13 0.11 0.12 0.09 0.09 0.08 0.09

Cadmium, mg/kg 0.84 0.71 0.55 0.49 0.46 0.36 0.34 0.32 0.32

Calcium, mg/kg 215,000 233,000 230,000 252,000 308,000 255,000 240,000 247,000 240,000

Cerium, mg/kg 17 18.2 14.8 14.4 13.6 12.1 11.1 11.5 10.7

Cesium, mg/kg 1.4 1.3 1.2 1.1 1 0.89 0.82 0.83 0.86

Chromium, mg/kg 17.2 15.6 14.1 13.2 14.1 11.2 11.3 10.6 11.2

Cobalt, mg/kg 3.7 3.3 3 2.9 2.9 2.4 2.3 2.4 2.4

Copper, mg/kg 16.5 17.7 15 14.9 17.1 14.4 13.3 14.5 14.3

Gallium, mg/kg 4.2 3.9 3.3 3.2 3.2 2.7 2.6 2.6 2.5

Iron, mg/kg 13,300 12,500 11,100 10,800 11,900 9,770 9,300 9,570 9,360

Lanthanum, mg/kg 8.2 8.3 6.8 7 6.7 6 5.3 5.6 5.2

Lead, mg/kg 60 59.1 46.7 43.9 37.3 29.7 25.4 25.3 24.6

Lithium, mg/kg 4.6 9.5 3.3 7.5 7.8 7 1.2 4.8 <0.3

Magnesium, mg/kg 8,430 8,940 8,380 8,870 11,000 8,970 8,370 8,740 8,430

Manganese, mg/kg 607 622 599 656 771 659 644 675 692

Mercury, mg/kg 0.08 0.07 0.06 0.05 0.05 0.05 0.05 0.05 0.05

Molybdenum, mg/kg 5.3 5.1 4.3 4 3.5 4.1 3.7 3.4 2.8

Nickel, mg/kg 7.9 5.2 5.8 3.7 3.8 2.4 3.3 2.2 4.1

Niobium, mg/kg 2.5 3.4 2 2 1.8 1.6 1.5 1.6 1.5

Potassium, mg/kg 5,590 4,870 4,640 4,100 4,680 3,450 3,680 3,260 3,680

Rubidium, mg/kg 26.6 25.3 21.9 21.2 20 17.4 16.5 16.4 16.3

Scandium, mg/kg 2.9 2.7 2.4 2.3 2.1 1.8 1.8 1.8 1.8

Selenium, mg/kg 1.61 1.51 1.47 1.4 1.4 1.35 1.45 1.37 1.43

Silver, mg/kg 0.264 0.175 0.122 0.09 0.099 0.071 0.091 0.062 0.084

Sodium, mg/kg 1,330 1,300 1,120 1,090 1,230 979 916 967 960

Strontium, mg/kg 302 312 320 346 373 365 347 362 351

Sulfur, % 0.82 0.59 0.6 0.53 0.58 0.6 0.57 0.54 0.53

Thallium, mg/kg 0.4 0.34 0.24 0.21 0.2 0.18 0.18 0.15 0.17

Thorium, mg/kg 2.6 2.4 2.02 1.85 1.84 1.58 1.59 1.5 1.52

Titanium, mg/kg 680 723 566 569 590 471 427 455 425

Uranium, mg/kg 1.98 2.03 1.66 1.64 1.46 1.43 1.4 1.35 1.27

Vanadium, mg/kg 27.2 25.8 22.7 21.6 21.8 17.6 17.3 16.9 17.2

Yttrium, mg/kg 5.5 5.1 4.6 4.4 4.1 3.8 3.6 3.6 3.6

Zinc, mg/kg 101 95.6 78.7 76.4 73.2 63.5 60.9 60.7 59.6
52 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Table 1–12. Concentrations of nutrients, carbon, and trace elements for bottom-sediment samples 

collected from coring site LM–5 in Lake Maxinkuckee, northern Indiana, May 2013.

[Shading indicates concentration greater than threshold-effects guideline listed in table 2. cm, centimeters; 

R, recent sediment; mg/kg, milligrams per kilogram; --, not available; %, percent dry weight; <, less than]

Constituent and unit 

of measurement

Constituent concentration

Interval 1 Interval 2 Interval 3 Interval 4 Interval 5 Interval 6

16–18 cm, 

R (bottom of 

core)

12–14 cm,

 R

8–10 cm, 

R

4–6 cm, 

R

2–4 cm, 

R

0–2 cm, 

R (top of 

core)

Nutrients

Total nitrogen, mg/kg -- 844 2,400 1,920 -- 1,320

Total phosphorus, mg/kg 510 499 485 539 477 582

Carbon

Carbon (total organic), % 5.1 5.3 5.4 5.5 5.6 5.4

Carbon (total), % 13.4 13.6 13.7 13.8 14 13.7

Trace elements

Aluminum, mg/kg 10,800 9,540 9,410 9,250 8,590 9,350

Antimony, mg/kg 0.39 0.36 0.4 0.32 0.39 0.33

Arsenic, mg/kg 16.7 14.9 13.2 13.7 13.6 20.5

Barium, mg/kg 339 319 326 324 311 336

Beryllium, mg/kg 0.27 0.28 0.26 0.29 0.21 0.29

Bismuth, mg/kg 0.09 0.07 0.08 0.07 0.08 0.09

Cadmium, mg/kg 0.39 0.34 0.36 0.34 0.33 0.35

Calcium, mg/kg 305,000 258,000 246,000 259,000 234,000 262,000

Cerium, mg/kg 11.4 11.5 10.5 10.7 10.2 11.2

Cesium, mg/kg 0.86 0.8 0.86 0.78 0.77 0.82

Chromium, mg/kg 11.9 10.4 10.9 10.7 10.2 10.6

Cobalt, mg/kg 2.3 2.2 2.3 2.1 2.1 2.3

Copper, mg/kg 14.1 12.6 12.9 12.9 15.4 13.6

Gallium, mg/kg 2.5 2.4 2.4 2.4 2.1 2.4

Iron, mg/kg 9,170 8,680 8,820 8,680 8,230 9,410

Lanthanum, mg/kg 5.6 5.5 5.2 5.4 5 5.4

Lead, mg/kg 28.4 26.1 25.4 24.2 23 24.3

Lithium, mg/kg 7.4 6.5 1.8 5.7 1.8 5.7

Magnesium, mg/kg 9,590 9,060 8,450 8,890 7,970 9,070

Manganese, mg/kg 727 681 668 748 762 912

Mercury, mg/kg 0.05 0.05 0.05 0.04 0.05 0.04

Molybdenum, mg/kg 2.7 2.1 1.6 1.5 1.1 1.1

Nickel, mg/kg <0.3 1.8 4.2 1.7 3.8 1.7

Niobium, mg/kg 1.6 1.6 1.6 1.6 1.5 1.6

Potassium, mg/kg 3,760 3,360 3,590 3,300 3,310 3,340

Rubidium, mg/kg 16.8 16.1 15.8 15.7 14.5 15.9

Scandium, mg/kg 2 1.7 1.8 1.7 1.6 1.8

Selenium, mg/kg 1.41 1.33 1.44 1.32 1.42 1.33

Silver, mg/kg 0.088 0.055 0.089 0.056 0.099 0.063

Sodium, mg/kg 1,080 1,030 1,000 1,020 913 1,070

Strontium, mg/kg 363 347 333 338 315 354

Sulfur, % 0.54 0.44 0.35 0.41 0.37 0.22

Thallium, mg/kg 0.18 0.17 0.17 0.17 0.16 0.17

Thorium, mg/kg 1.57 1.57 1.52 1.39 1.44 1.53

Titanium, mg/kg 547 455 423 446 415 485

Uranium, mg/kg 1.35 1.33 1.08 1.07 0.84 0.85

Vanadium, mg/kg 18 15.9 16.2 15 14.9 15.9

Yttrium, mg/kg 3.7 3.6 3.6 3.5 3.3 3.6

Zinc, mg/kg 66.7 61.1 60.2 60.4 57 63.3
Appendix 53

Table 1–13. Concentrations of nutrients, carbon, and trace elements for bottom-sediment samples 

collected from coring site LM–6G in Lake Maxinkuckee, northern Indiana, May 2013.

[Shading indicates concentration greater than threshold-effects guideline listed in table 2. cm, centimeters; P, predevelopment sediment; R, recent sediment; mg/kg, milligrams per kilogram; %, percent dry weight; <, less than]

Constituent and unit 

of measurement

 Constituent concentration

Interval 1

80–90 cm, P

Interval 2

60–70 cm, P

Interval 3

40–50 cm, R

Nutrients

Total nitrogen, mg/kg 1,590 1,010 1,460

Total phosphorus, mg/kg 1,090 734 585

Carbon

Carbon (total organic), % 11.6 7.7 5.9

Carbon (total), % 15.5 14.2 11.1

Trace elements

Aluminum, mg/kg 13,600 12,200 22,700

Antimony, mg/kg 0.22 0.2 1.4

Arsenic, mg/kg 28.8 18.4 29.9

Barium, mg/kg 262 306 362

Beryllium, mg/kg 0.42 0.38 0.72

Bismuth, mg/kg 0.06 <0.06 0.21

Cadmium, mg/kg 0.19 0.19 1.1

Calcium, mg/kg 124,000 204,000 151,000

Cerium, mg/kg 15.2 14.3 24.3

Cesium, mg/kg 1.3 1.1 2

Chromium, mg/kg 14.3 12.1 22.5

Cobalt, mg/kg 4.1 3.4 5.1

Copper, mg/kg 13.2 10.7 20.6

Gallium, mg/kg 3.5 3.1 5.7

Iron, mg/kg 60,600 28,200 19,500

Lanthanum, mg/kg 7.4 7 11.3

Lead, mg/kg 7.06 8.7 68.6

Lithium, mg/kg 4.1 6.9 10.2

Magnesium, mg/kg 7,280 8,820 8,200

Manganese, mg/kg 823 697 537

Mercury, mg/kg 0.03 0.03 0.12

Molybdenum, mg/kg 8.1 4.7 8.1

Nickel, mg/kg 9 4.9 11.8

Niobium, mg/kg 1.9 1.8 3.4

Potassium, mg/kg 5,300 4,260 7,960

Rubidium, mg/kg 23.2 20.6 36.7

Scandium, mg/kg 2.6 2.3 4

Selenium, mg/kg 1.66 1.19 2

Silver, mg/kg 0.059 0.018 0.236

Sodium, mg/kg 1,200 1,180 1,910

Strontium, mg/kg 176 257 232

Sulfur, % 0.6 0.38 1.22

Thallium, mg/kg 0.22 0.18 0.48

Thorium, mg/kg 2.23 1.9 3.53

Titanium, mg/kg 545 536 977

Uranium, mg/kg 1.51 1.23 2.31

Vanadium, mg/kg 24.5 20.9 36.3

Yttrium, mg/kg 5.1 4.5 7

Zinc, mg/kg 49.3 37.2 130
54 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Table 1–14. Abundant diatom species in bottom-sediment samples collected from coring site LM–1 in Lake Maxinkuckee, northern 

Indiana, May 2013.

[cm, centimeters; R, recent sediment]

Diatom species

Diatom count

Interval 1 Interval 2 Interval 3 Interval 4 Interval 5 Interval 6 Interval 7 Interval 8 Interval 9

28–30 cm, 

R (bottom 

of core)

24–26 cm,

 R

20–22 cm, 

R

16–18 cm, 

R

12–14 cm, 

R

8–10 cm, 

R

4–6 cm, 

R

2–4 cm, 

R

0–2 cm, 

R (top of 

core)

Achnanthidium minutissimum 44 51 40 48 40 44 42 54 86

Amphora ovalis 8 2 11 6 10 1 3 3 0

Asterionella formosa 33 79 51 91 33 24 26 36 100

Aulacoseira ambigua 87 52 95 65 27 61 41 32 18

Cyclotella bodanica 12 9 19 18 29 27 37 45 27

Cyclotella ocellata 6 9 53 104 188 163 198 221 106

Cyclotella pseudostelligera 49 76 35 22 13 10 15 9 0

Fragilaria crotonensis 202 232 163 99 83 72 68 75 32

Pseudostaurosira brevistriata 25 48 28 24 24 29 49 23 18

Staurosira construens 0 1 0 3 2 1 3 7 0

Staurosira construens var.

venter

11 4 8 19 16 30 26 21 3

Staurosirella pinnata 27 12 14 7 22 4 20 7 14

Synedra demerarae 0 10 5 6 7 9 9 28 16

Table 1–15. Abundant diatom species in bottom-sediment 

samples collected from coring site LM–1G in Lake Maxinkuckee, 

northern Indiana, May 2013.

[cm, centimeters; P, predevelopment sediment]

Diatom species

Diatom count

Interval 1

70–80 cm, P

Interval 2

50–60 cm, P

Achnanthidium minutissimum 12 7

Amphora ovalis 1 6

Asterionella formosa 13 15

Aulacoseira ambigua 0 58

Cyclotella bodanica 251 341

Cyclotella ocellata 0 0

Cyclotella pseudostelligera 58 11

Fragilaria crotonensis 52 22

Pseudostaurosira brevistriata 1 3

Staurosira construens 5 0

Staurosira construens var.

venter

5 1

Staurosirella pinnata 5 7

Synedra demerarae 1 2
Appendix 55

Table 1–16. Abundant diatom species in bottom-sediment samples collected from coring site LM–2 in Lake Maxinkuckee, northern 

Indiana, May 2013. 

[cm, centimeters; R, recent sediment]

Diatom species

Diatom count

Interval 1 Interval 2 Interval 3 Interval 4 Interval 5 Interval 6 Interval 7 Interval 8 Interval 9

28–30 cm, 

R (bottom 

of core)

24–26 cm,

 R

20–22 cm, 

R

16–18 cm, 

R

12–14 cm, 

R

8–10 cm, 

R

4–6 cm, 

R

2–4 cm, 

R

0–2 cm, 

R (top of 

core)

Achnanthidium minutissimum 42 33 32 39 58 51 53 65 54

Amphora ovalis 13 24 33 21 17 20 14 24 17

Asterionella formosa 11 13 16 15 14 23 30 71 114

Aulacoseira ambigua 165 119 122 46 28 29 32 20 28

Cyclotella bodanica 37 28 20 25 39 24 27 27 31

Cyclotella ocellata 11 16 38 52 107 104 160 129 91

Cyclotella pseudostelligera 2 15 0 6 5 3 1 7 2

Fragilaria crotonensis 14 28 12 17 12 32 48 11 43

Pseudostaurosira brevistriata 143 116 117 124 89 86 68 72 37

Staurosira construens 17 29 12 18 35 20 22 0 7

Staurosira construens var.

venter

43 79 110 119 69 83 62 59 62

Staurosirella pinnata 36 69 18 23 20 21 50 27 9

Synedra demerarae 0 13 3 1 23 24 18 24 21

Table 1–17. Abundant diatom species in bottom-sediment 

samples collected from coring site LM–2G in Lake Maxinkuckee, 

northern Indiana, May 2013.

[cm, centimeters; P, predevelopment sediment]

Diatom species

Diatom count

Interval 1

60–70 cm, P

Interval 2

40–50 cm, P

Achnanthidium minutissimum 0 0

Amphora ovalis 0 0

Asterionella formosa 0 0

Aulacoseira ambigua 0 1

Cyclotella bodanica 213 9

Cyclotella ocellata 0 0

Cyclotella pseudostelligera 0 1

Fragilaria crotonensis 0 0

Pseudostaurosira brevistriata 8 1

Staurosira construens 0 0

Staurosira construens var.

venter

0 0

Staurosirella pinnata 3 0

Synedra demerarae 0 0
56 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Table 1–18. Abundant diatom species in bottom-sediment samples collected from coring site LM–3 in Lake Maxinkuckee, northern 

Indiana, May 2013.

[cm, centimeters; R, recent sediment]

Diatom species

Diatom count

Interval 1 Interval 2 Interval 3 Interval 4 Interval 5 Interval 6 Interval 7 Interval 8

24–26 cm, 

R (bottom of 

core)

20–22 cm,

 R

16–18 cm, 

R

12–14 cm, 

R

8–10 cm, 

R

4–6 cm, 

R

2–4 cm, 

R

0–2 cm, 

R (top of 

core)

Achnanthidium minutissimum 34 60 70 58 64 55 59 76

Amphora ovalis 69 51 45 43 43 29 24 27

Asterionella formosa 1 1 2 8 11 6 27 95

Aulacoseira ambigua 36 16 21 6 9 10 8 9

Cyclotella bodanica 16 11 25 21 22 16 28 16

Cyclotella ocellata 9 7 10 29 37 62 50 32

Cyclotella pseudostelligera 1 0 3 1 2 1 0 0

Fragilaria crotonensis 0 3 4 5 9 13 7 19

Pseudostaurosira brevistriata 190 177 174 177 125 144 141 101

Staurosira construens 41 47 55 36 76 78 51 21

Staurosira construens var. venter 109 122 110 109 129 97 98 42

Staurosirella pinnata 34 55 47 43 33 51 25 28

Synedra demerarae 5 4 0 1 4 4 4 7

Table 1–19. Abundant diatom species in bottom-sediment samples collected from coring 

site LM–3G in Lake Maxinkuckee, northern Indiana, May 2013.

[cm, centimeters; P, predevelopment sediment]

Diatom species

Diatom count

Interval 1

70–80 cm, P

Interval 2

50–60 cm, P

Interval 3

30–40 cm, P

Achnanthidium minutissimum 0 0 0

Amphora ovalis 0 0 2

Asterionella formosa 0 0 0

Aulacoseira ambigua 0 0 0

Cyclotella bodanica 13 5 9

Cyclotella ocellata 0 0 0

Cyclotella pseudostelligera 0 1 0

Fragilaria crotonensis 0 0 0

Pseudostaurosira brevistriata 0 0 1

Staurosira construens 0 0 2

Staurosira construens var. venter 0 0 4

Staurosirella pinnata 2 0 5

Synedra demerarae 0 0 1
Appendix 57

Table 1–20. Abundant diatom species in bottom-sediment samples collected from coring site LM–4 in Lake Maxinkuckee, northern 

Indiana, May 2013.

[cm, centimeters; R, recent sediment]

Diatom species

Diatom count

Interval 1 Interval 2 Interval 3 Interval 4 Interval 5 Interval 6 Interval 7 Interval 8 Interval 9

28–30 cm, 

R (bottom 

of core)

24–26 cm,

R

20–22 cm,

R

16–18 cm,

R

12–14 cm,

R

8–10 cm,

R

4–6 cm,

R

2–4 cm,

R

0–2 cm, R 

(top of

core)

Achnanthidium minutissimum 68 38 47 49 53 53 45 49 61

Amphora ovalis 22 24 18 24 21 12 15 17 13

Asterionella formosa 83 70 42 29 25 13 35 53 76

Aulacoseira ambigua 92 113 95 84 34 26 39 28 28

Cyclotella bodanica 33 34 23 43 31 45 58 42 55

Cyclotella ocellata 9 14 33 53 145 141 170 178 143

Cyclotella pseudostelligera 10 17 24 18 20 7 9 6 2

Fragilaria crotonensis 84 111 101 40 42 27 50 19 14

Pseudostaurosira brevistriata 31 59 63 101 78 108 113 73 98

Staurosira construens 19 16 33 20 4 44 37 11 9

Staurosira construens var. venter 18 40 56 67 74 63 17 47 24

Staurosirella pinnata 18 14 14 13 28 11 19 22 20

Synedra demerarae 4 8 11 11 4 0 13 16 4

Table 1–21. Abundant diatom species in bottom-sediment samples collected from coring site LM–5 

in Lake Maxinkuckee, northern Indiana, May 2013.

[cm, centimeters; R, recent sediment]

Diatom species

Diatom count

Interval 1 Interval 2 Interval 3 Interval 4 Interval 5 Interval 6

16–18 cm, 

R (bottom of 

core)

12–14 cm,

 R

8–10 cm, 

R

4–6 cm, 

R

2–4 cm, 

R

0–2 cm, 

R (top of 

core)

Achnanthidium minutissimum 65 51 57 75 68 112

Amphora ovalis 48 22 29 22 14 37

Asterionella formosa 5 4 18 13 25 90

Aulacoseira ambigua 18 7 21 26 7 10

Cyclotella bodanica 21 44 30 33 33 18

Cyclotella ocellata 3 78 89 124 87 54

Cyclotella pseudostelligera 5 2 4 1 5 7

Fragilaria crotonensis 6 12 10 20 17 15

Pseudostaurosira brevistriata 93 156 123 132 127 123

Staurosira construens 12 32 21 17 23 7

Staurosira construens var.

venter

100 122 126 70 81 86

Staurosirella pinnata 46 23 14 19 34 15

Synedra demerarae 7 9 10 15 4 15
58 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Table 1–22. Abundant diatom species in bottom-sediment samples collected from coring 

site LM–6G in Lake Maxinkuckee, northern Indiana, May 2013.

[cm, centimeters; P, predevelopment sediment; R, recent sediment]

Diatom species

Diatom count

Interval 1

80–90 cm, P

Interval 2

60–70 cm, P

Interval 3

40–50 cm, R

Achnanthidium minutissimum 13 12 31

Amphora ovalis 0 13 9

Asterionella formosa 8 13 78

Aulacoseira ambigua 27 24 246

Cyclotella bodanica 293 265 24

Cyclotella ocellata 0 0 9

Cyclotella pseudostelligera 7 4 10

Fragilaria crotonensis 66 14 102

Pseudostaurosira brevistriata 1 2 6

Staurosira construens 0 6 0

Staurosira construens var. 

venter

0 4 4

Staurosirella pinnata 2 2 2

Synedra demerarae 1 0 3
Appendix 59

Table 1–23. Rare diatom species in bottom-sediment samples collected from Lake Maxinkuckee, northern Indiana, May 2013.

Achnanthes laevis Cymbella microcephala Gyrosigma acuminatum Nitzschia heufleriana

Achnanthes lemmermannii Cymbella perpusilla Hantzschia amphioxys Nitzschia linearis

Achnanthes rosenstockii Cymbella subaequalis Hippodonta capitata Nitzschia palea

Achnanthes suchlandtii Cymbella tumidula Karayevia clevei Nitzschia paleacae

Achnanthidium exiguum Cymbella sp. Kobayasia subtilissima Nitzschia perminuta

Achnanthidium microcephalum Cymbopleura naviculiformis Mastogloia smithii Nitzschia recta

Adlafia miniscula Denticula kuetzingii Melosira varians Nitzschia subacicularis

Amphipleura pellucida Denticula subtilis Navicula agrestis Pinnularia maior

Amphora pediculus Diatoma ehrenbergii Navicula angusta Pinnularia microstauron

Amphora thumensis Diatoma tenuis 

var. elongatum

Navicula capitatoradiata Pinnularia microstauron 

var. adirondackensis

Amphora sp. Diatoma vulgare Navicula cincta Pinnularia viridis

Aneumastus tusculus Diploneis minuta Navicula cryptocephala Pinnularia sp.

Aulacoseira distans Diploneis petersenii Navicula cryptotenella Placoneis clementioides

Aulacoseira distans 

var. nivaloides

Diploneis puella Navicula goeppertiana Placoneis clementis

Aulacoseira granulata Encyonema caespitosum Navicula gregaria Planothidium delicatulum

Brachysira styriaca Encyonema silesiacum Navicula humerosa Planothidium lanceolatum

Brachysira vitrea Encyonopsis cesatii Navicula lenzii Psammothidium bioretti

Caloneis bacillum Entomoneis ornata Navicula menisculus Pseudostaurosira construens 

var. binodis

Caloneis ventricosa Eolimna minima Navicula oblonga Reimeria sinuata

Caloneis sp. Epithemia adnata Navicula porifera Rhoicosphenia abbreviata

Cavinula scutelloides Epithemia argus Navicula pseudanglica Rhopalodia gibba

Cocconeis neothumensis Epithemia sorex Navicula pseudolanceolata Sellaphora mutata

Cocconeis pediculus Eucocconeis flexella Navicula pseudotuscula Stauroneis smithii

Cocconeis placentula 

var. lineata

Eucocconeis flexella 

var. alpestris

Navicula radiosa Staurosirella lapponica

Craticula cuspidata Eunotia arcus Navicula rhynchocephala Staurosirella leptostauron

Ctenophora pulchella Eunotia bilunaris Navicula schadei Stephanodiscus alpinus

Cyclostephanos dubius Eunotia monodontiforma Navicula stroemii Stephanodiscus minutulus

Cyclotella comensis Eunotia pectinalis Navicula cf. sublucidula Stephanodiscus niagarae

Cyclotella hakanssoniae Fragilaria capucina Navicula subplacentula Stephanodiscus parvus

Cyclotella meneghiniana Fragilaria capucina 

var. mesolepta

Navicula tridentula Striatella flocculosa

Cyclotella michiganiana Fragilaria vaucheriae Navicula trivialis Surirella angusta

Cyclotella stelligera Fragilariforma virescens Navicula veneta Surirella biseriata 

var. bifrons f. amphioxys

Cymatopleura solea Frustulia rhomboides Navicula viridula Surirella patella

Cymbella affinis Geissleria decussis Navicula sp. Surirella sp.

Cymbella amphicephala Gomphoneis olivacea Navicymbula pusilla Synedra filiformis

Cymbella aspera Gomphonema acuminatum Neidium ampliatum Synedra filiformis var. exilis

Cymbella cistula Gomphonema angustatum Neidium iridis Synedra ostenfeldii

Cymbella cuspidata Gomphonema clavatum Nitzschia acicularis Synedra parasitica

Cymbella cymbiformis Gomphonema gracile Nitzschia amphibia Synedra radians

Cymbella delicatula Gomphonema minutum Nitzschia clausii Synedra rumpens

Cymbella descripta Gomphonema parvulum Nitzschia dissipata Synedra ulna

Cymbella ehrenbergii Gomphonema pumilum Nitzschia fonticola Synedra ulna var. biceps

Cymbella gaeumannii Gomphonema truncatum Nitzschia frustulum Tryblionella angustata

Cymbella heteropleura Gomphonema sp. Nitzschia gracilis
60 Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana

Table 1–24. Cyanobacterial akinetes in bottom-sediment samples collected from Lake Maxinkuckee, northern Indiana, May 2013. 

[cm, centimeters; R, recent sediment; %, percent; P, predevelopment sediment]

Coring site number1 

(fig. 2)

Depth interval 

(cm)

Number (relative percentage abundance) of cyanobacterial akinetes2

Gloeotrichia echinulata Anabaena Aphanizomenon

LM–1 0–2 (R) 40,700 (68%) 18,700 (31%) 550 (1%)

2–4 (R) 45,000 (69%) 19,200 (30%) 437 (1%)

4–6 (R) 75,900 (90%) 7,370 (9%) 567 (1%)

8–10 (R) 103,000 (94%) 6,840 (6%) 0 (0%)

12–14 (R) 100,000 (89%) 10,100 (9%) 1,840 (2%)

16–18 (R) 93,800 (90%) 10,000 (9%) 910 (1%)

20–22 (R) 74,800 (91%) 7,090 (9%) 0 (0%)

24–26 (R) 92,000 (89%) 11,300 (11%) 0 (0%)

28–30 (R) 74,200 (85%) 12,800 (15%) 0 (0%)

LM–1G 50–60 (P) 113,000 (91%) 11,600 (9%) 0 (0%)

70–80 (P) 118,000 (93%) 8,810 (7%) 0 (0%)

LM–2 0–2 (R) 38,700 (87%) 5,180 (12%) 345 (1%)

2–4 (R) 51,600 (91%) 4,300 (8%) 614 (1%)

4–6 (R) 62,000 (91%) 5,240 (8%) 437 (1%)

8–10 (R) 104,000 (94%) 6,110 (6%) 0 (0%)

12–14 (R) 173,000 (95%) 8,960 (5%) 0 (0%)

16–18 (R) 125,000 (87%) 17,300 (12%) 825 (1%)

20–22 (R) 332,000 (92%) 27,000 (8%) 0 (0%)

24–26 (R) 236,000 (97%) 8,130 (3%) 0 (0%)

28–30 (R) 175,000 (92%) 14,000 (7%) 1,080 (1%)

LM–2G 40–50 (P) 146,000 (95%) 7,520 (5%) 0 (0%)

60–70 (P) 126,000 (95%) 4,580 (3%) 2,290 (2%)

LM–3 0–2 (R) 47,500 (88%) 5,130 (10%) 1,030 (2%)

2–4 (R) 85,800 (94%) 4,210 (5%) 1,050 (1%)

4–6 (R) 75,000 (95%) 3,260 (4%) 466 (1%)

8–10 (R) 60,200 (92%) 4,330 (6%) 1,180 (2%)

12–14 (R) 77,600 (90%) 7,810 (9%) 1,040 (1%)

16–18 (R) 48,400 (83%) 8,000 (14%) 1,910 (3%)

20–22 (R) 78,300 (90%) 7,460 (9%) 1,060 (1%)

24–26 (R) 91,400 (91%) 9,410 (9%) 0 (0%)

LM–3G 30–40 (P) 114,000 (96%) 1,380 (1%) 3,450 (3%)

50–60 (P) 137,000 (96%) 5,850 (4%) 0 (0%)

70–80 (P) 197,000 (96%) 6,340 (3%) 1,270 (1%)
Appendix 61

Coring site number1 

(fig. 2)

Depth interval 

(cm)

Number (relative percentage abundance) of cyanobacterial akinetes2

Gloeotrichia echinulata Anabaena Aphanizomenon

LM–4 0–2 (R) 30,000 (87%) 3,220 (9%) 1,490 (4%)

2–4 (R) 57,900 (94%) 2,910 (5%) 728 (1%)

4–6 (R) 62,000 (87%) 3,190 (4%) 6,380 (9%)

8–10 (R) 114,000 (78%) 29,000 (20%) 3,310 (2%)

12–14 (R) 91,900 (93%) 5,590 (6%) 1,240 (1%)

16–18 (R) 95,500 (86%) 13,900 (13%) 1,460 (1%)

20–22 (R) 62,100 (80%) 8,870 (12%) 6,500 (8%)

24–26 (R) 92,800 (80%) 17,100 (15%) 5,940 (5%)

28–30 (R) 95,800 (91%) 7,590 (7%) 1,900 (2%)

LM–5 0–2 (R) 24,100 (81%) 4,960 (17%) 709 (2%)

2–4 (R) 58,900 (91%) 5,030 (8%) 457 (1%)

4–6 (R) 81,400 (96%) 2,940 (3%) 490 (1%)

8–10 (R) 56,200 (93%) 2,250 (4%) 1,690 (3%)

12–14 (R) 58,400 (92%) 4,170 (7%) 596 (1%)

16–18 (R) 59,100 (90%) 4,400 (7%) 1,890 (3%)

LM–6G 40–50 (R) 88,400 (83%) 12,600 (12%) 5,200 (5%)

60–70 (P) 88,200 (79%) 19,600 (17%) 4,200 (4%)

80–90 (P) 91,300 (94%) 4,800 (5%) 1,370 (1%)

1

Coring site numbers ending in “G” indicate a gravity core. Other coring site numbers indicate a box core.

2

For each depth interval, the relative percentage abundances were rounded to sum to 100 percent.

Table 1–24. Cyanobacterial akinetes in bottom-sediment samples collected from Lake Maxinkuckee, northern Indiana, May 2013.—

Continued

[cm, centimeters; R, recent sediment; %, percent; P, predevelopment sediment]
Publishing support provided by: 

Rolla Publishing Service Center

For additional information concerning this publication, contact: 

Director, USGS Kansas Water Science Center 

4821 Quail Crest Place 

Lawrence, KS 66049 

(785) 842–9909

Or visit the Kansas Water Science Center Web site at: 

http://ks.water.usgs.gov

Juracek—Occurrence and trends of selected constituents in bottom sediment, Lake Maxinkuckee, Indiana—SIR 2014–5199

ISSN 2328-0328 (online)

http://dx.doi.org/10.3133/sir20145199