U.S. Department of the Interior

U.S. Geological Survey

Prepared in cooperation with the

CITY OF OLATHE, KANSAS, and the

KANSAS DEPARTMENT OF HEALTH AND ENVIRONMENT

Sediment Deposition and

Selected Water-Quality

Characteristics in Cedar Lake and

Lake Olathe, Northeast Kansas,

2000

Water-Resources Investigations Report 02–4073

Cover photograph: Shoreline of Lake Olathe, northeast Kansas, October 2001.
U.S. Department of the Interior

U.S. Geological Survey

Sediment Deposition and

Selected Water-Quality

Characteristics in Cedar Lake and

Lake Olathe, Northeast Kansas,

2000

By DAVID P. MAU

Water-Resources Investigations Report 02–4073

Prepared in cooperation with the

CITY OF OLATHE, KANSAS, and the

KANSAS DEPARTMENT OF HEALTH AND ENVIRONMENT

Lawrence, Kansas

2002
U.S. Department of the Interior

Gale A. Norton, Secretary

U.S. Geological Survey

Charles G. Groat, Director

For additional information write to: Copies of this report can be purchased fro

District Chief U.S. Geological Survey

U.S. Geological Survey Information Services

4821 Quail Crest Place Building 810

Lawrence, KS 66049–3839 Box 25286, Federal Center

Denver, CO 80225–0286

The use of brand, trade, or firm names in this report is for identification purposes only and does not constitute endorsem

by the U.S. Geological Survey.
Content

CONTENTS

Abstract.................................................................................................................................................................................. 

Introduction ........................................................................................................................................................................... 

Previous Investigations ................................................................................................................................................ 

Description of Current Investigation ........................................................................................................................... 

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

Acknowledgments ....................................................................................................................................................... 

Description of Lake Olathe Watershed.................................................................................................................................. 

Methods ................................................................................................................................................................................. 

Bathymetric Surveys.................................................................................................................................................... 

Estimation of Bottom-Sediment Depth and Volume ................................................................................................... 

Reservoir Sediment-Core Collection, Processing, and Analysis................................................................................. 

Analysis of Diatoms in Reservoir Sediment................................................................................................................ 

Quality Control............................................................................................................................................................ 

Trend Analysis............................................................................................................................................................. 

Sediment Deposition in Cedar Lake and Lake Olathe........................................................................................................... 

Calculated Bottom-Sediment Volume and Mass ......................................................................................................... 

Comparisons of Sediment Deposition Among Cedar Lake, Lake Olathe, and Hillsdale Lake................................... 

Water-Quality Characteristics................................................................................................................................................ 

Phosphorus................................................................................................................................................................... 

Concentrations in Reservoir Bottom Sediment ................................................................................................. 

Estimates of Phosphorus Loads and Yields in Lake Olathe Watershed ............................................................ 

Nitrogen ....................................................................................................................................................................... 

Trace Elements ............................................................................................................................................................ 

Selected Pesticides....................................................................................................................................................... 

Diatoms as Indicators of Lake Eutrophication ...................................................................................................................... 

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

References ............................................................................................................................................................................. 

Supplemental Information ..................................................................................................................................................... 

FIGURES

1. Maps showing location of Lake Olathe watershed in northeast Kansas and bottom-sediment coring sites in

Cedar Lake and Lake Olathe................................................................................................................................... 

2. Map showing land use in Lake Olathe watershed, 1993......................................................................................... 

3. Graphs showing number of acres harvested and livestock in Johnson County, Kansas, for selected years

between 1960 and 1999........................................................................................................................................... 

4–8. Maps showing:

4. Average length of bottom-sediment cores collected from coring sites in Cedar Lake and

Lake Olathe, 2000.............................................................................................................................................. 

5. Bathymetric contours for Lake Olathe, 2000 .................................................................................................... 

6. Estimated thickness of sediment in Lake Olathe, 1956–2000........................................................................... 

7. Mean concentrations of total phosphorus in bottom-sediment core samples collected from

Cedar Lake and Lake Olathe, 2000 ................................................................................................................... 

8. Mean particle-size composition of bottom-sediment cores collected from Cedar Lake and Lake Olathe, 2000 

9. Graphs showing relation between concentrations of cesium-137 and depths of bottom-sediment samples

from coring site 3 in Cedar Lake, 1938–2000, and coring site 5 in Lake Olathe, 1956–2000 ............................... 
IV Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

FIGURES—Continued

10. Graph showing relation between total phosphorus concentrations in bottom-sediment samples and depth

of samples from coring site 5 in Lake Olathe, 1956–2000..........................................................................

11. Map showing mean concentrations of total ammonia plus organic nitrogen as nitrogen in bottom-sedime

samples from Cedar Lake and Lake Olathe, 2000.......................................................................................

12–18. Graphs showing:

12. Relation between concentrations of total ammonia plus organic nitrogen as nitrogen in bottom-sedim

samples and depths of samples from coring site 5 in Lake Olathe, 1956–2000 ....................................

13. Relation between selected trace element concentrations in bottom-sediment samples and depths of sa

from coring site 3 in Cedar Lake, 2000..................................................................................................

14. Relation between selected trace element concentrations in bottom-sediment samples and depths of sa

from coring site 5 in Olathe Lake, 2000 ................................................................................................

15. Relation between selected pesticide concentrations in bottom-sediment samples and depths of sampl

from coring site 3 in Cedar Lake, 2000..................................................................................................

16. Relation between selected pesticide concentrations in bottom-sediment samples and depths of sampl

from coring site 5 in Lake Olathe, 2000 ................................................................................................

17. Relation between total number of identified diatom species in bottom-sediment samples and depths o

samples from coring site 3 in Cedar Lake, 1938–2000, and coring site 5 in Lake Olathe, 1956–2000 

18. Relation between total number of valves of identified diatom species per gram of material in bottom

sediment samples and depths of samples from coring site 3 in Cedar Lake, 1938–2000, and coring si

Lake Olathe, 1956–2000 ........................................................................................................................

TABLES

1. Location of bottom-sediment coring sites in Cedar Lake and Lake Olathe, northeast Kansas, 2000 .........

2. Analytical results and percentage differences for selected trace elements in split replicate samples of bot

sediment from coring site 5, Lake Olathe, northeast Kansas, 2000 ............................................................

3. Sediment deposition, loads, and yields estimated for Cedar Lake, Lake Olathe, and Hillsdale Lake, north

Kansas..........................................................................................................................................................

4. Estimated mean sediment bulk densities in both in-channel and out-of-channel bottom sediment, Cedar 

and Lake Olathe, northeast Kansas, 2000....................................................................................................

5. Trend test analysis of concentrations of total phosphorus and total ammonia plus organic nitrogen (N) in

bottom sediment from coring site 5 in Lake Olathe, northeast Kansas, 2000 .............................................

6. Total phosphorus sediment loads and yields estimated for Cedar Lake, Lake Olathe, and other selected

reservoir watersheds in Kansas....................................................................................................................

7. Mean concentrations and sediment-quality guidelines for selected trace elements in bottom-sediment sa

from Cedar Lake and Lake Olathe, northeast Kansas, 2000 .......................................................................

8. Mean concentrations of selected pesticides in bottom-sediment samples from Cedar Lake and Lake Olat

northeast Kansas, 2000 ................................................................................................................................

9. Relative percentage abundance of six most-prevalent diatom species in bottom-sediment samples from C

Lake, 1938–2000, and Lake Olathe, 1956–2000, northeast Kansas............................................................

10. Relation between relative abundance of selected species of diatoms and concentrations of total phospho

total ammonia plus organic nitrogen as nitrogen (N), and depths of samples from selected bottom-sedim

cores from Cedar Lake and Lake Olathe, northeast Kansas, 2000..............................................................

11. Selected diatom species and their presence under various water-quality conditions ..................................

12. Laboratory analysis methods for reservoir bottom-sediment constituents ..................................................

13. Nutrients analyzed in bottom sediment from Cedar Lake and Lake Olathe, northeast Kansas, 2000 ........

14. Selected metals and trace elements analyzed in bottom sediment from Cedar Lake and Lake Olathe,

northeast Kansas, 2000 ................................................................................................................................

15. Radiochemical analyzed for age dating bottom sediment from Cedar Lake and Lake Olathe, northeast K

2000 .............................................................................................................................................................
Conten

TABLES—Continued

16. Statistical summary of concentrations and comparison to sediment-quality guidelines for selected metals and

trace elements in bottom-sediment sample from Cedar Lake coring site 3, northeast Kansas, 2000 .................... 

17. Statistical summary of concentrations and comparison to sediment-quality guidelines for selected metals and

trace elements in bottom-sediment sample from Lake Olathe coring site 5, northeast Kansas, 2000 ................... 

18. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Cedar Lake coring site 3, northeast Kansas, 2000 ............................................................. 

19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000 ............................................................ 

1

Temperature in degrees Fahrenheit (oF) can be converted to degrees Celsius (oC) by the equation:

oC = 5/9 (oF - 32).

Sea level: In this report, “sea level” refers to the National Geodetic Vertical Datum of 1929—a geodetic

datum derived from a general adjustment of the first-order level nets of the United States and Canada,

formerly called Sea Level Datum of 1929.

CONVERSION FACTORS, ABBREVIATIONS, AND VERTICAL DATUM

Multiply By To obtain

acre 4,047 square meter

acre 640 square mile (mi2)

acre-foot (acre-ft) 1,233 cubic meter

acre-foot per year (acre-ft/yr) 1,233 cubic meter per year

acre-foot per year per square mile [(acre-ft/yr)/mi2

] 476.1 cubic meter per year per square kilometer

cubic foot (ft3

) 0.02832 cubic meter

degree Fahrenheit (o

F) (1) degree Celsius

foot (ft) 0.3048 meter

inch (in.) 2.54 centimeter

meter (m) 3.281 foot

microgram per gram (μg/g) 1.0000 x 10-6 ounce per ounce

mile (mi) 1.609 kilometer

milligram (mg) 0.0000353 ounce

milligram per kilogram (mg/kg) 0.000016 ounce per pound

millimeter (mm) 0.03937 inch

pound (lb) 453.6 gram

pound per acre per year [(lb/acre)/yr] 1.121 kilogram per hectare per year

pound per cubic foot (lb/ft3

) 16.02 kilogram per cubic meter

pound per year (lb/yr) 453.6 gram per year

pound per year per square mile [(lb/yr)/mi2] 175.1 gram per year per square kilometer

square mile (mi2

) 2.590 square kilometer
VI Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000
Abstrac

Sediment Deposition and Selected Water-Quality

Characteristics in Cedar Lake and Lake Olathe, Northeast

Kansas, 2000

By David P. Mau

Abstract

The Lake Olathe watershed, located in northeast Kansas, was investigated using bathymetric

survey data and reservoir bottom-sediment cores

to determine sediment deposition, water-quality

trends, and transport of nutrients (phosphorus and

nitrogen species), selected trace elements,

selected pesticides, and diatoms as indicators of

eutrophic (organic-enriched and depleted oxygen

supply) conditions. To determine sediment deposition and loads, bathymetric data from Cedar

Lake and Lake Olathe, both located in the Lake

Olathe watershed, were collected in 2000 and

compared to historical topographic data collected

when the lakes were built.

Approximately 338 acre-feet of sediment deposition has occurred in Cedar Lake since dam closure in 1938, and 317 acre-feet has occurred at

Lake Olathe since 1956. Mean annual sediment

deposition was 5.45 acre-feet per year (0.89 acrefeet per year per square mile) for Cedar Lake and

7.0 acre-feet per year (0.42 acre-feet per year per

square mile) for Lake Olathe. Mean annual sediment loads for the two reservoirs were 9.6 million

pounds per year for Cedar Lake and 12.6 million

pounds per year for Lake Olathe.

Mean concentrations of total phosphorus in

bottom-sediment samples from Cedar Lake

ranged from 1,370 to 1,810 milligrams per kilogram, and concentrations in bottom-sediment

samples from Lake Olathe ranged from 588 to

1,030 milligrams per kilogram. The implication

of large total phosphorus concentrations in the

bottom sediment of Cedar Lake is that inflow 

Cedar Lake is rich in phosphorus and that adv

water-quality conditions could affect water qu

ity in downstream Lake Olathe through discha

of water from Cedar Lake to Lake Olathe via

Cedar Creek.

Mean annual phosphorus loads transporte

from the Lake Olathe watershed were estimate

be 14,700 pounds per year for Cedar Lake and

9,720 pounds per year for Lake Olathe. The m

annual phosphorus yields were estimated to b

3.74 pounds per acre per year for Cedar Lake 

0.91 pound per acre per year for Lake Olathe.

Phosphorus yields in the Cedar Lake watershe

were largest of the six Kansas impoundment

watersheds recently studied.

Concentrations of total ammonia plus org

nitrogen as nitrogen in bottom sediment increa

from upstream to downstream in both Cedar L

and Lake Olathe. Mean concentrations of tot

ammonia plus organic nitrogen as nitrogen (N

ranged from 2,000 to 2,700 milligrams per kil

gram in bottom-sediment samples from Cedar

Lake and from 1,300 to 2,700 milligrams per k

gram in samples from Lake Olathe. There wa

statistical significance between total ammonia

plus organic nitrogen as nitrogen and depth of

bottom sediment.

Concentrations of six trace elements in bo

tom sediment from Cedar Lake and Lake Ola

(arsenic, chromium, copper, lead, nickel, and

zinc) exceeded the U.S. Environmental Protec
2 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

Agency Threshold Effects Levels (TELs) sediment-quality guidelines for aquatic organisms in

sediment except for one lead concentration. Probable Effects Levels (PELs) for trace elements,

however, were not exceeded at either lake.

Organochlorine and organophosphate insecticides were not detected in bottom-sediment samples from either Cedar Lake or Lake Olathe, but

the acetanilide herbicides alachlor and metolachlor were detected in sediment from both

lakes. The U.S. Environmental Protection

Agency has not proposed TEL or PEL

guideline concentrations for bottom sediment

for any of the organophosphate, acetanilide, or

triazine pesticides.

The diatoms (microscopic, single-celled

organisms) Cyclotella bodanica, an indicator of

low organic-enriched water, and Cyclotella

meneghiniana, an indicator of organic-enriched

water, were both present in bottom sediment from

Lake Olathe. The presence of both of these diatoms suggests varying periods of low and high

eutrophication in Lake Olathe from 1956 to 2000.

The concentrations of two species in bottom sediment from Cedar Lake, Aulacoseira cf alpigena

and Cyclotella meneghiniana, as well as two species in sediment from Lake Olathe, Aulacoseira cf

alpigena and Stephanodiscus nigare, increased in

sediment cores from the older bottom material to

the more recent deposition near the top of the sediment cores. These diatom species indicate

eutrophic conditions, and the increased concentration of these diatom species from the bottom of

the cores to the sediment/water interface suggests

that historically these lakes have been and continue to be eutrophic at times.

 Comparison of constituent trends between

Cedar Lake and Lake Olathe using reservoir bottom sediment was not possible because sediment

from Cedar Lake was suspected of having been

disturbed. However, trends that may be reflective

of historical changes in water quality were not

detected in sediment from either Cedar Lake or

Lake Olathe for total phosphorus, trace elements

(except lead), and organochlorine or organophosphate pesticides. A slight increasing trend in the

concentration of total ammonia plus organic

nitrogen as nitrogen was seen in the sedim

file from Lake Olathe but not in the profil

Cedar Lake. The acetanilide herbicides al

and metolachlor were more prevalent in m

recently deposited sediment in Cedar Lak

and Lake Olathe, as was the triazine herbi

atrazine in Lake Olathe bottom sediment, 

ing a possible increasing trend in lake-infl

water concentrations.

Trends in water-quality characteristics 

used by the Lake Olathe watershed manag

document historical changes in the waters

such as changes in land use, the suspensio

use of chlorinated insecticides, such as DD

chlordane, and the use of hydrophobic fer

The investigation described in this report p

a baseline of water-quality information to 

pare future changes in water quality or oth

watershed activities. With the addition of 

metric surveys and the inclusion of additi

ervoirs, reservoir sediment investigations 

used to estimate historical loads of phosp

and other constituents in future water-qua

assessments throughout Kansas.

INTRODUCTION

The effects of land use on water quality i

ronmental issue that has gained increased pub

awareness. Point-source discharges to stream

municipal wastewater-treatment facilities and 

point-source discharges from residential septi

tems, runoff from crop and livestock producti

stormwater contributions from urban areas, m

in contaminant transport to surface and groun

and ultimately to downstream reservoirs.

Many water-quality constituents adhere t

ment particles and are deposited in reservoirs

act as sinks for these constituents. Large sedi

concentrations frequently observed in Kansas 

voirs are responsible for turbidity levels that c

reduce light penetration in the euphotic zone 

of a water body in which there is sufficient lig

tration to support photosynthesis). Large turb

els in combination with the presence of nutrie

pesticides may have detrimental effects on hu

who use reservoirs as a drinking-water supply 

aquatic organisms, and can reduce the recreat
Introductio

value of the reservoir. Two reservoirs currently under

investigation, Cedar Lake and Lake Olathe, are located

in northeast Kansas (fig. 1). Lake Olathe serves as a

supplemental drinking-water supply for approximately

90,000 residents in the city of Olathe and as a recreational resource for the community.

Cedar Lake was constructed by the city of Olathe

in 1938 (Carly Adams, city of Olathe, written commun., 2001) and used as a supplemental water-supply

source, but rapid sedimentation reduced the waterstorage capacity of the lake. In response to the

increasing water requirements of the city of Olathe,

Lake Olathe was constructed in 1956 as a watersupply reservoir and to provide recreational use for

boating, fishing, and swimming. As residential and

commercial development increases in the Lake Olathe

watershed, there is considerable interest in maintaining acceptable water quality in Lake Olathe for water

supply and recreation.

Previous Investigations

Rapid urbanization and its potential effects on

water quality in the Lake Olathe watershed led the city

of Olathe to conduct a study of Lake Olathe in

1982–83 to determine the relation between nutrient

loads and eutrophication (nutrient enrichment). The

study was done with support from the U.S. Environmental Protection Agency (USEPA) Clean Lakes Program under section 314–A of the Federal Clean Water

Act of 1972. The 13-month study (1982–83) examined the limnology and water quality of the lake, estimated nutrient loads into the lake as well as sources of

nutrients in the watershed, and estimated nutrient

loads for 2000. Recommendations were made in

regard to management and long-term monitoring of

the lake and watershed (Lee and Sears, 1985). During

the 1982–83 study, the population for the city of

Olathe was about 46,500 (Lee and Sears, 1985).

On the basis of a 1983 bathymetric survey and

comparison to historical topographic maps, Lee and

Sears (1985) estimated sediment deposition since

1956 to be about 16 acre-ft. Sediment loads to Lake

Olathe were estimated to be about 23.6 million lb/yr

and did not include the trapping of sediment in the

more than 60 small impoundments in the watershed.

Phosphorus loads calculated from water samples

and estimates of streamflow were estimated to be

1,450 lb/yr and were expected to increase to

1,850 lb/yr by 2000 because of anticipated increa

urbanization (Lee and Sears, 1985).

Tissue from channel catfish and other predator 

species were analyzed for selected trace elements 

pesticides, and detectable concentrations of these 

stituents were found. However, reservoir bottom 

ment was not analyzed, and water-quality analysis 

limited to nutrients and algal determinations. The

1982–83 study concluded by recommending a fut

phase-two monitoring effort to include comprehen

lake water-quality sampling during the summer

months at multiple locations and depths.

The U.S. Geological Survey (USGS) has inve

gated reservoir sediment in Kirwin, Webster, and

Cheney Reservoirs, and Waconda, Tuttle Creek, a

Hillsdale Lakes (see fig. 1, index map) (Juracek, 1

Christensen, 1999; Mau, 2001). These investigat

included analysis of part or all of the following co

stituents: nutrients, selected trace elements, and p

cides. Sediment deposition varied considerably

among the reservoirs investigated, increasing from

west to east across the State along with increasing 

cipitation. Mean annual phosphorus yield showe

similar increases from west to east with the lowes

yield determined for Webster Reservoir, in the we

part of Kansas, and the highest yield for Hillsdale

Lake, located in the northeast part (Mau and Chri

tensen, 2000).

Bathymetric surveys were done in 2000 for

23 small municipal lakes in Kansas, including La

Olathe, by the U.S. Army Corps of Engineers, wo

ing for the Kansas Water Office. The total sedim

deposition to Lake Olathe from 1956 to 2000, est

mated on the basis of these surveys, was 30 acre-

0.67 acre-ft of sediment deposition per year (Kan

Water Office, 2001, p. 31).

Description of Current Investigation

In response to concerns of rapid sedimentatio

rates reducing the storage capacity and the quality 

water in Lake Olathe, the USGS began a coopera

investigation in 2000 with the city of Olathe and t

Kansas Department of Health and Environment

(KDHE), with support from USEPA. The purpos

the current investigation was to provide a comple

lake and watershed assessment of the Lake Olathe

watershed. One of the objectives of the 2000 inve

gation described in this report was to identify tren

concentrations of selected water-quality constitue
4 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

Creek

94°53' 94°50'

38°53'

38°51'

52'

52' 51'

Cedar

Cedar

Lake

0

0 0.5 KILOMETER

0.25 0.5 MILE

0.25

56

35

OLATHE

OLATHE

Cedar Creek

EXPLANATION

Lake Olathe

5

4

3 2

1 

1 

2

3

3

Webster Reservoir

Tuttle Creek

Lake

Cheney Reservoir

Hillsdale

Lake

KANSAS

Index map

Lake Olathe

watershed

Johnson

County

City limits of Olathe

Base from U.S. Geological Survey digital data, 1:24,000, 1995

Universal Transverse Mercator projection,

Zone 15

Boundary of Lake Olathe watershed

Direction of flow

Coring site and number

Waconda

Lake

Kirwin Reservoir

Figure 1. Location of Lake Olathe watershed in northeast Kansas and bottom-sediment coring sites in Cedar

Lake and Lake Olathe.
Description of Lake Olathe Watershe

Through chemical analysis and age dating of sediment

cores, both baseline conditions and trends in waterquality constituents were determined to help identify

the effects of land use on receiving water bodies as

well as to help document the effectiveness of landmanagement practices.

The investigation also determined the transport of

various constituents to Cedar Lake and Lake Olathe

that can be useful in the establishment of total maximum daily loads (TMDLs). The Federal Clean Water

Act of 1972 requires that all States implement

TMDLs, which are an estimate of the maximum contaminant load (material transported during a specified

time period) from point and nonpoint sources that a

receiving water can accept without exceeding waterquality criteria. TMDL concerns at Lake Olathe

include eutrophication (nutrient enrichment) and suspended sediment that affect water quality, clarity, and

storage capacity of the lake. Nutrient enrichment and

suspended sediment ultimately may affect taste and

odor of the drinking-water supply from the lake and

the trophic (nutrient status) condition of the lake.

Additional objectives of the investigation included

estimation of the volume of accumulated sediment in

both Cedar Lake and Lake Olathe since dam closures

and estimation of the loads of selected water-quality

constituents transported from the watershed to the lake

bed. Some of the water-quality constituents may be

toxic to aquatic organisms or possibly could bioaccumulate in the food chain.

The lack of long-term water-quality data for the

Lake Olathe watershed can make interpretation of any

trends in the watershed difficult. However, because

many water-quality constituents attach to suspended

sediment and are transported and deposited in a reservoir, an examination of reservoir bottom sediment was

one method used to determine trends in water-quality

constituents.

Purpose and Scope

The purposes of this report are to: (1) document

the volume of sediment deposition in Cedar Lake and

Lake Olathe, (2) determine transport (loads and yields)

of selected water-quality constituents in the Lake

Olathe watershed, and (3) evaluate trends in nutrients

(phosphorus and nitrogen species), selected trace elements, selected pesticides, and diatom species (microscopic, single-celled organisms). The investigation

included bathymetric surveys of both Cedar Lake and

Lake Olathe as well as bottom-sediment coring at

selected locations in both lakes. Data collection w

done during June through August 2000.

The results of this investigation will provide e

mates of the rate of sedimentation and estimates o

loads of selected chemical constituents transporte

Cedar Lake and Lake Olathe. Results also will he

watershed managers understand contamination

sources and provide a baseline to evaluate future

progress made toward reduction in contaminant lo

Date markers were placed on top of the bottom se

ment at one location in each lake to indicate the c

rent (2000) sediment layer for future sampling

reference. These markers will provide a definite t

reference for future sediment sampling at these lo

tions. The results from this investigation will sup

Federal, State, and local goals toward implementi

watershed strategies to improve water quality. Th

results also may be used by various government a

cies to establish TMDLs and to evaluate bestmanagement practices (BMPs) designed to mitiga

nonpoint-source contamination. These data can b

used to determine the degree of success obtained

through the current and future implementation of

BMPs.

Acknowledgments

The author thanks Mr. Kevin Dobbs with the 

sas Biological Survey for his assistance with geographic information system (GIS) technology in

determining historic storage volume and sedimen

deposition at Lake Olathe. The author also thanks 

Carly Adams with the city of Olathe for her assist

in obtaining reference material and other study ne

DESCRIPTION OF LAKE OLATHE WATERSHED

Cedar Lake has a surface area of about 54 acr

and a current (2000) water-storage volume of

334 acre-ft at the dam crest elevation of 1,001.0 f

above sea level. Lake Olathe has a surface area o

about 170 acres and a current storage volume of

3,102 acre-ft at the dam crest elevation of 937.5 f

above sea level. The watershed area of 16.9 mi2

(10,800 acres) encompasses both Cedar Lake and

Lake Olathe as well as Cedar Creek, the main tribu

joining the two lakes (fig. 1).
6 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

There are approximately 1,000 people in the

watershed, most of whom live in single-family residences and farms in the area (Carly Adams, city of

Olathe, written commun., 2001). Lake Olathe is

located within the Olathe city limits, and there are no

other towns in the watershed. A public, 18-hole golf

course abuts Lake Olathe on the east.

The mean annual temperature in Olathe is about

55 oF, with a mean monthly range of 28 oF in January

to 78 oF in July (National Oceanic and Atmospheric

Administration, 1966–98). Mean annual precipitation

(1961–90) is about 40 in., which occurs primarily during the growing season from April through September

(National Oceanic and Atmospheric Administration,

1966–98).

The Lake Olathe watershed is underlain by sedimentary bedrock deposited during late Pennsylvanian

time (about 285 to 300 million years ago) (Lee and

Sears, 1985). The bedrock is mostly shale, with

some prominent limestone layers and sandstone.

Pre-Illinoian glacial till and a thin lens of loess (windblown Pleistocene deposits) cover the bedrock. Soils

in the watershed were formed from windblown loess,

glacial outwash, and residuals derived from the

weathering of shale and limestone bedrock (Lee

and Sears, 1985).

Land use in the Lake Olathe watershed is primarily agricultural cropland and grassland, which represent 83 percent of the watershed (fig. 2) (Kansas

Geological Survey, 1993). Crop-production statistics

were not available for the Lake Olathe watershed;

therefore, the following statistics were based on figures for Johnson County where the watershed is

located (fig. 1, index map). Crop production in the

county declined from 108,000 acres of harvested cropland in 1960 to 71,000 acres harvested cropland in

2000 (fig. 3A) (Kansas State Board of Agriculture and

U.S. Department of Agriculture, 1960–95; Kansas

Department of Agriculture and U.S. Department of

Agriculture, 1996–2000). Production of wheat, rye,

corn, oats, and sorghum declined between 1960 and

1999 (fig. 3A). However, soybean and all hay production increased during the same period. Residential and

commercial land use in Johnson County increased during the 40-year period from 1960–99, and similar residential and commercial growth was evident in the

Lake Olathe watershed, from 2.0 percent of the watershed in 1985 to 15 percent in 1999 (Lee and Sears,

1985; Kevin Dobbs, Kansas Biological Survey, written

commun., 2001).

Livestock production in Johnson County 

relatively stable for cattle and calves, averagi

25,600 head annually from 1960 to 1999. Ho

annual inventories of hogs, sheep and lambs, 

chickens declined during the same period (fig

(Kansas State Board of Agriculture and U.S. 

ment of Agriculture, 1960–95; Kansas Depar

Agriculture and U.S. Department of Agricultu

1996–2000).

METHODS

To meet the objectives of the investigatio

described in this report required information 

voir sedimentation (depth and volume) relativ

impoundment topography, density of sedimen

vertical variability in sediment chemical com

tion. Bathymetric surveys, or mapping of the 

bottom, provided the sedimentation informati

calculation of mean sediment depth and volum

iment core samples collected at selected sites 

Cedar Lake and Lake Olathe provided sedime

sity and chemical and biological information 

mine historical trends and transport of sedime

selected water-quality constituents.

Bathymetric Surveys

Bathymetric surveys were done by the US

both Cedar Lake and Lake Olathe in 2000 usi

ferential global positioning system (GPS) and 

mal depth-sounder recording fathometer. Bo

these instruments were connected to a portab

computer, and the data collected from the ins

were filtered and manipulated through a comp

software package. The GPS measured spatial 

in latitude and longitude with an accuracy of 

zontal control points were established each da

beginning of the surveys to maintain accuracy

fathometer measured depth with an accuracy 

the fathometer was calibrated at the start of e

to maintain accuracy. The computer software 

was used for survey planning, survey executio

storage and editing of data. The software pack

was used to generate preliminary contour map

lake bottoms that were exported to a GIS soft

gram where final editing and curve smoothing 

contour lines were completed.
Method

94°53'

38°53'

38°48'

52'

51'

50'

49'

52' 51' 50' 49' 94°48'

Lake Olathe 

Cedar

Lake

0

0 1 2 KILOMETERS

1 2 MILES

Cedar Creek

OLATHE

Land use modified from Kansas Applied Remote Sensing digital data 

1:100,000, 1993, Landsat Thematic Mapper raster imagery;

Kansas Geological Survey (1993)

Land use in Lake Olathe watershed

Base from U.S. Geological Survey digital data, 1:24,000, 1995

Universal Transverse Mercator projection,

Zone 15

Boundary of Lake 

 Olathe watershed

Commercial/industrial

Cropland

Grassland

Residential

Woodland

Water

Roads and quarries

EXPLANATION

City limits

of Olathe

City limits

of Olathe

Creek

Cedar

Figure 2. Land use in Lake Olathe watershed, 1993.
8 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

All hay

Soybean

Cattle and calves

Corn

Oats

Sorghum

Rye

Wheat

Hogs

Sheep and lambs

Chickens

1960 1970 1965 1980 1985 1975 1990 1995 1999

Number of acres harvested

A.

Number of livestock

B.

0

5,000

10,000

15,000

20,000

25,000

30,000

35,000

0

10,000

20,000

30,000

40,000

50,000

60,000

70,000

80,000

The bathymetric surveys of both lakes were done

using a pontoon boat on which the GPS and fathometer were mounted. Information on range lines used in

the 1983 bathymetric survey of Lake Olathe by Lee

and Sears (1985) was not used in the 2000 surveys

because many of the temporary endpoints use

identify the range lines could not be found. T

arbitrary range lines were assigned every 250 

pendicular to the longitudinal axis of each lak

Figure 3. Number of (A) acres harvested and (B) livestockin Johnson County, Kansas, for selected years between

1960 and 1999 (sources of data: Kansas State Board of Agriculture and U.S. Department of Agriculture, 1960–95;

Kansas Department of Agriculture and U.S. Department of Agriculture, 1996–2000).
Method

Estimation of Bottom-Sediment Depth and

Volume

Estimation of bottom-sediment volume in Cedar

Lake and Lake Olathe required area and depth of sediment deposition in each lake. The area was determined from historic contour maps and GIS map

coverage of the lakes, and depth of sediment deposition was estimated by comparing topographic maps of

lake areas prior to impoundment to 2000 bathymetric

information for each lake.

A historic contour map of Cedar Lake prior to

impoundment (1938) was obtained from the Kansas

Department of Agriculture, Division of Water

Resources (map on file with the USGS office,

Lawrence, Kansas). The original design water-storage

capacity for the lake (1938) was obtained from the historic contour map and was compared to the 2000 storage capacity, and the difference was assumed to be

attributed to sediment deposition.

Historical and 2000 GIS map coverages were

available for Lake Olathe. The 2000 map coverage

was digitally overlayed on the historical (1954) map

coverage, and using GIS, an elevation grid with 1-m

cell sizes was created for each map. The elevation

grid was used to interpolate the bathymetric point data

between the contour lines and to calculate the net gain

or loss of sediment volume for each cell. The cells

were summed to provide either a net gain or loss of

sediment volume for Lake Olathe (Kevin Dobbs, Kansas Biological Survey, written commun., 2001).

Reservoir Sediment-Core Collection, Processing,

and Analysis

Reservoir bottom-sediment cores were collected

and analyzed to provide a history of water quality in

the watershed. The depth of bottom material was used

as an indicator of sediment loads transported to the

lakes and loss of water-storage capacity. Sediment

mass in and chemical analysis of the bottom-sediment

cores were used to estimate mass loads of chemical

constituents transported into the lakes as well as to

determine temporal and spatial trends of selected constituents in the watershed.

A gravity corer was used to collect bottomsediment cores from Cedar Lake from one in-channel

(historic stream channel prior to dam impoundment)

coring site (Cedar Lake coring site 3) and two out-ofchannel coring sites (Cedar Lake coring sites 1 and 2)

(table 1, fig. 4). In-channel and out-of-channel se

ment cores were collected to determine if there w

any chemical or biological differences in sedimen

from the two topographical areas. Similarly, five 

ment cores were collected from Lake Olathe from

three in-channel coring sites (Lake Olathe coring 

1, 2, and 5) and two out-of-channel coring sites (L

Olathe coring sites 3 and 4) (table 1, fig. 4). The l

used in the gravity corer was transparent tubing m

of cellulose acetate butyrate with a 2.88-in. outsid

diameter and a 2.63-in. inside diameter. Dependi

upon the required analyses, three to four sedimen

cores were collected at each coring site to provide 

ficient material and briefly chilled prior to process

During this investigation all of the sediment c

used in the analyses were thought to have penetra

to pre-reservoir material. This was evident by a

change in physical appearance of the sediment, di

ences in sediment grain-size composition, and the

presence of pre-reservoir organic material such as 

hairs, plant material, or small sticks. The presenc

pre-reservoir material indicated that a complete se

ment record had been collected for each core.

The sediment cores were processed at the US

laboratory in Lawrence, Kansas. The plastic liner

were cut longitudinally in two places and 180o ap

The cuts were partially completed using a rotary h

saw and finished with a retractable razor knife set 

depth to minimize penetration of the sediment co

The cores were split in half by pulling a tightly he

nylon string through the length of the two cuts an

allowing the halves to separate. Depending upon 

type of analysis as well as available bottom materi

each core, the cores then were subsectioned into e

length intervals, and sediment samples from each

Table 1. Location of bottom-sediment coring sites in Cedar L

and Lake Olathe, northeast Kansas, 2000

Coring site

(fig. 1)

U.S. Geological Survey

site identification number

Latitude Longi

(degrees, minutes, seco

Cedar Lake

1 385039094503800 38o50'39" 94o50

2 385049094505300 38o

50'49" 94o50

3 385050094505100 38o

50'50" 94o50

Lake Olathe

1 385216094521500 38o52'16" 94o52

2 385232094521600 38o

52'32" 94o52

3 385230094522600 38o

52'30" 94o52

4 385246094521600 38o

52'46" 94o52

5 385254094523100 38o

52'54" 94o52
10 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

94°53' 94°50'

38°53'

38°51'

52'

52' 51'

Cedar

Lake

0

0 0.5 KILOMETER

0.25 0.5 MI

0.25

56

35

OLATHE

OLATHE

Cedar Creek

Length of core,

 in feet

Coring site and number—Asterisk 

 indicates that core includes only part

 of the sediment interval

EXPLANATION

Lake Olathe

Base from U.S. Geological Survey digital data, 1:24,000, 1995

Universal Transverse Mercator projection,

Zone 15

0

1.0

2.0

3.0

4.0

5.0

4.2

0

1.0

2.0

3.0

4.0

5.0

6.0

4.8

0

1.0

2.0

3.0

4.0

5.0

4.1 0

1.0

2.0

3.0

4.0

5.0

4.0

0

1.0

2.0

3.0

4.0

5.0

4.0

0

1.0

2.0

3.0

4.0

5.0

6.0

5.5

0

1.0

2.0

3.0

4.0

0.9

0

1.0

2.0

3.0

4.0

2.5

0

1.0

2.0

3.0

4.0

3.5

5

4

3 2

1

1

3*

2 3*

City limits of Olathe

Creek

Cedar

Figure 4. Average length of bottom-sediment cores collected from coring sites in Cedar Lake and Lake Olathe, 2000.
Methods 

interval were removed for physical and chemical

determinations (Cedar Lake coring site 3 and Lake

Olathe coring site 5; fig. 1).

Analysis requirements from selected bottomsediment sampling sites (Cedar Lake coring sites 1–2

and Lake Olathe coring sites 1–4; fig. 1) consisted of a

mean chemical determination for the entire sediment

core. In these instances, equal volumes of sediment

from each interval were removed from the sediment

core, placed in a mixing bowl, and mechanically

homogenized. A sample of the homogenized mass

then was sent to the USGS National Water-Quality

Laboratory (NWQL) in Denver, Colorado, for chemical analysis.

Sediment mass (in pounds) is a product of sediment volume (cubic feet) and sediment bulk density

(pounds per cubic foot). Sediment bulk densities were

determined from selected sediment cores. These sediment cores were subsectioned, weighed, and oven

dried to remove all moisture. The dried subsectioned

cores were reweighed, and the weights divided by the

subsection volume to determine bulk density. Mean

bulk densities for the entire sediment core were determined from the subsectioned mean bulk densities.

Sediment-core mean bulk densities were used to calculate average bulk density for each lake.

Subsections of selected cores were analyzed for

bulk density at the USGS laboratory in Lawrence,

Kansas, according to methods presented in Guy

(1969). Subsections also were analyzed for percentage of sand and silt and (or) clay at the USGS sediment laboratory in Iowa City, Iowa, according to

methods presented in Guy (1969). Core subsections

from selected sites were analyzed at the NWQL in

Denver, Colorado, for total phosphorus, total ammonia

plus organic nitrogen as nitrogen, and selected trace

elements according to procedures presented in Fishman (1993). Analytical methods and reporting limits

are presented in tables 12–14 ( in “Supplemental

Information” section of this report). In addition, organochlorine insecticides, organophosphate insecticides,

and acetanilide and triazine herbicides were analyzed

for selected core subsections at the USGS Organic

Geochemistry Research Laboratory in Lawrence, Kansas, on the basis of procedures given in Mills and

Thurman (1992).

The use of a gravity corer, such as used during this

investigation, may produce a “core-shortening” phenomenon (Blomqvist, 1985). Core shortening refers

to the difference between the depth of sediment

penetration by the sample tube and the length of t

core inside the sample tube. This phenomenon ha

been documented at length and is described as be

caused by friction of the sediment against the inn

wall of the sample tube as the gravity corer penet

the sediment (Emery and Hulseman, 1964; Blomq

and Bostrom, 1987). The friction causes the core 

ple to underrepresent the entire thickness of the p

trated sediment bed, presumably through a thinnin

individual sediment layers during the penetration 

cess. Compression of the sediment and loss of w

content have been suggested as mechanisms that

would explain core shortening, especially in very 

muds (Hongve and Erlandsen, 1979). If compres

of sediment is a dominant physical mechanism to

explain the core-shortening phenomenon, then se

ment densities and, ultimately, calculations of tot

mass presented in this report may be biased. How

for most sediment cores collected from Cedar Lak

and Lake Olathe, very soft muds were evident on

the upper few inches of the cores. Although core

shortening affects the length of the retrieved sedim

core (fig. 4), the entire core sample represents a c

plete sediment profile and, thus, a potential record 

historical trends in water-quality constituents.

Reservoir bottom sediment may undergo mix

during storms or periods of flooding. This mixing 

create difficulties in the analysis of trends in wate

quality constituents. To determine whether bottom

sediment had been disturbed, sediment cores from

both Cedar Lake (coring site 3) and Lake Olathe 

ing site 5) (fig. 4) were analyzed for cesium-137 b

NWQL (table 15, in “Supplemental Information” 

tion of this report). Cesium-137, a by-product of 

monuclear-weapons testing in the 1950s and early

1960s, was widely dispersed by atmospheric depo

tion and potentially sorbed to soil particles (prima

clay). Detectable cesium-137 concentrations in s

ment began about 1952 and peaked in 1963–64, f

lowed by a steady decline in concentrations.

Identifiable spikes outside of the 1963–64 peak in

cesium-137 concentrations in the bottom-sedimen

core profile may be indicative of turbulence and r

pension of sediment. Analysis of sediment for ch

cal trends would not be appropriate under these

conditions.

Because of its wide dispersal, cesium-137 also 

be used to date sediment layers (Holmes, 1998). 

ability to date sediment layers is important in dete

mining the effectiveness of BMPs in managing
12 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

chemical inputs to reservoirs. For example, if particular pesticides are not permitted for use, identification

of a nonpermitted pesticide near the water-sediment

interface may suggest continued use of the pesticide in

the watershed.

Physical markers (commercially available blue

plastic tarps) were placed on top of the bottom sediment over a 30-by-30-ft area in both Cedar Lake and

Lake Olathe. The intent was to place this minimal

degradable material as a layer on top of the reservoir

bottom sediment and return in several years to those

locations and remove sediment cores. The tarps would

be identified by distinct blue layers in the sediment

cores, and any sediment above the markers attributed

to sediment deposition since 2000. The locations of

the tarps were marked using a handheld GPS.

Analysis of Diatoms in Reservoir Sediment

Bottom-sediment cores from Cedar Lake and Lake

Olathe were subsectioned and analyzed for diatom

species. Diatoms are microscopic algae that have a

siliceous shell and occur in both freshwater and

marine environments. Diatoms are sensitive to environmental changes such as changes in nutrient concentrations, and therefore, identification of diatom taxa

may indicate periods of eutrophication in lakes. Ten

subsamples from one sediment core from each lake

were submitted to BSA Environmental Services, Inc.

(BSA), Beachwood, Ohio, where a subsample weighing 10 to 12 mg was extracted and cleaned using

30-percent hydrogen peroxide and concentrated nitric

acid (Stoermer and others, 1995). The clean diatom

subsample was suspended in glass-distilled water,

placed in evaporation chambers similar to those

devised by Battarbee (1973), and prepared on slides

using NAPHRAXTM. For each sampling date, diatom

valves were counted along 18-mm transects using a

microscope at 1000X magnification.

The number of identified and counted valves varied from 133 to 639 for the subsample from Cedar

Lake and from 373 to 952 valves for the subsample

from Lake Olathe. The counts were converted to percentage abundance within the subsample. An estimate

of the total number of valves per gram of dry sediment

also was made by relating the number of valves

counted on a slide to the proportion of the area on the

slide that was counted, taking into account dilution

factors and the weight of sediment processed.

Quality Control

Multiple cores were collected at various s

both Cedar Lake and Lake Olathe to provide s

sediment for both physical and chemical anal

Quality control in the collection of bottom-se

cores included evaluating laboratory analytica

ability (precision and reproducibility).

Analytical precision and reproducibility w

determined by analyzing split replicate sampl

tom-sediment cores. Split replicate samples w

pared by homogenizing like core subsections

splitting each homogenized subsection into tw

ples. By homogenizing the sample and then 

it into two samples, both samples should have 

chemically equivalent, and any differences co

attributed to variability within the laboratory 

dure. Percentage differences between split re

concentrations were calculated as the absolute 

the quotient of the difference in replicate con

tions divided by the summation of replicate c

tions, multiplied by 100.

Analysis of split replicate samples from L

Olathe coring site 5 showed little or no variab

among the selected trace elements analyzed, w

median percentage difference of 1.71 percent 

Percentage differences in holmium and silver 

equal to or greater than 20 percent; however, 

centrations of these water-quality constituent

very low. The results generally indicate that l

tory precision and reproducibility differences 

small (0 to 9.1 percent) and probably not a con

this investigation.

Trend Analysis

Concentrations of total phosphorus and to

ammonia plus organic nitrogen as nitrogen in 

sediment cores from Cedar Lake and Lake O

were analyzed to determine the existence of t

with depth in the sediment profile and whethe

phorus or nitrogen usage in the watershed wa

ing or decreasing. Simple linear regression w

along with Kendall’s tau (τ), because each tes

different advantages over the other. A simple 

regression commonly is used to learn somethi

the relation between two variables, or estimat

dict values of one variable on the basis of kno

of another variable (Helsel and Hirsch, 1992)

dall’s tau is more resistant to the effects of ex
Sediment Deposition in Cedar Lake and Lake Olathe 

values and to deviations from a linear relation, and

may be more appropriate than simple linear regression

for sample sizes less than 20 (Helsel and Hirsch,

1992). A positive Kendall’s tau correlation on an x-y

graph, where x is the horizontal axis and y is the vertical axis, indicates that y values increase more often

than decrease as x values increase. A negative Kendall’s tau correlation indicates the opposite; y values

decrease more often than increase as x values increase.

Kendall’s tau was calculated for bottom-sediment

cores from both lakes, and trends were considered significant if p-values (probability values) were less than

0.05 (p<0.05).

SEDIMENT DEPOSITION IN CEDAR LAKE AND

LAKE OLATHE

One of the reasons for determining volume an

mass of sediment deposition was to evaluate wate

storage capacity and changes in capacity since

impoundment. Cedar Lake and Lake Olathe serv

ferent purposes, but decreased water-storage capa

from sediment deposition in each lake can affect 

allocations used for flood control, drinking-water 

plies for the city of Olathe, recreation, and wildlif

habitat. Estimates of sediment mass also provide

information that can be used with chemical conce

tions to determine watershed loads (mass) and yie

Table 2. Analytical results and percentage differences for selected trace elements in split replicate samples of bottom sediment from

coring site 5, Lake Olathe, northeast Kansas, 2000

[R, split replicate sample; μg/g, micrograms per gram; <, less than; --, not applicable]

l

Trace element and unit

of measurement

Concentration

Percentage differenceCoring site 5

(fig. 1)

Coring site

5R

Aluminum, percent 8.9 9.2 1.7

Antimony, μg/g 1.2 1.2 0

Arsenic, μg/g 15 15 0

Barium, μg/g 780 780 0

Beryllium, μg/g 2.6 2.6 0

Bismuth, μg/g <1.0 <1.0 --

Cadmium, μg/g .37 .44 8.6

Calcium, percent 1.1 .98 5.8

Cerium, μg/g 88 89 .56

Chromium, μg/g 88 88 0

Cobalt, μg/g 10 10 0

Copper, μg/g 36 34 2.9

Europium, μg/g 1.5 1.8 9.1

Gallium, μg/g 20 21 2.4

Gold, μg/g <1.0 <1.0 --

Holmium, μg/g 1.2 1.8 20

Iron, percent 4 4 0

Lanthanum, μg/g 58 54 3.6

Lead, μg/g 36 32 5.9

Lithium, μg/g 45 46 1.1

l

Trace element and unit

of measurement

Concentration

Percenta

feren

Coring site 5

(fig. 1)

Coring site

5R

Magnesium, percent 0.84 0.87 1.8

Manganese, μg/g 1,000 1,000 0

Molybdenum, μg/g .97 1.0 1.5

Neodymium, μg/g 44 46 2.2

Nickel, μg/g 35 36 1.4

Niobium, μg/g 21 20 2.4

Potassium, percent 1.9 2.1 5.0

Scandium, μg/g 15 15 0

Silver, μg/g .43 .28 21

Sodium, percent .39 .4 1.3

Strontium, μg/g 130 130 0

Tantalum, μg/g 1.8 1.5 9.1

Thallium, μg/g 1 1 0

Thorium, μg/g 16 16 0

Tin, μg/g 3.4 3.3 1.5

Titanium, percent .53 .45 8.2

Uranium, μg/g 4.3 4.1 2.4

Vanadium, μg/g 130 130 0

Ytterbium, μg/g 2.8 3 3.4

Yttrium, μg/g 30 34 6.3

Zinc, μg/g 140 130 3.7

Median 1.7
14 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

(mass per unit area of watershed) of chemical constituents to the lakes.

Calculated Bottom-Sediment Volume and Mass

Total sediment volume deposited in Cedar Lake

from 1938 through 2000 was approximately 338 acreft. This volume was calculated as the difference

between the 1938 design volume for the lake

(672 acre-ft)(Kansas Department of Agriculture;

information on file at USGS office in Lawrence, Kansas) and the Cedar Lake reservoir volume determined

from the 2000 bathymetric survey (334 acre-ft). The

1938 design plan of Cedar Lake available to the author

did not provide information on water-surface elevation

but did show the lake-surface area at the conservation

pool (55.5 acres). The lake-surface area of Cedar

Lake during the 2000 bathymetric survey was

54 acres; therefore, similar lake elevations were

assumed for the two periods for the calculation of

sediment deposition.

The mean annual sediment deposition rate to

Cedar Lake for the 62-year period (1938–2000), calculated on the basis of 338 acre-ft of total sediment deposition, was 5.45 acre-ft/yr, or 0.89 (acre-ft/yr)/mi2 of

watershed, when divided by the 6.14 mi2 (3,930 acres)

of contributing-drainage area to Cedar Lake (Lee and

Sears, 1985). The sediment deposition in Cedar Lake

has reduced the water-storage capacity of the lake by

approximately 50 percent in the past 62 years. At the

current rate of sediment deposition, Cedar Lake will

be fully silted in an additional 62 years.

Total sediment deposition in Lake Olathe was

determined to be approximately 317 acre-ft. The sediment volume was calculated as the difference between

the 1954 Lake Olathe design volume (3,419 acre-ft)

determined from GIS coverage and the reservoir volume determined from the 2000 bathymetric survey at a

water-surface elevation of 937.5 ft above sea level

(3,102 acre-ft) (figs. 5–6). The mean annual sediment

deposition rate for the period from 1956 through 2000

(45 years), calculated on the basis of 317 acre-ft, was

7.0 acre-ft/yr, or 0.42 (acre-ft/yr)/mi2, when divided

by the 16.6 mi2

 (10,630 acres) of contributingdrainage area from the watershed to Lake Olathe.

On the basis of the water-storage capacity design volume for Lake Olathe, the total sediment deposition in

45 years has reduced the water-storage capacity of

Lake Olathe by approximately 10 percent. In contrast,

approximately 2,100 acre-ft of total sediment deposition was estimated for Hillsdale Lake (approx

15 mi south of Lake Olathe, fig. 1) for the per

1981–96, or 0.97 (acre-ft/yr)/mi2

, when divid

144 mi2 of contributing-drainage area from th

shed to the lake (Juracek, 1997).

Total sediment deposition was determine

Lake Olathe in two previous studies—the Ka

Clean Lakes Program (1982–83) (Lee and Se

1985) and the U.S. Army Corps of Engineers 

done in 2000 for the Kansas Water Office (KW

(Kansas Water Office, 2001). The Kansas Cl

Lakes Program estimation of sediment deposi

based on a bathymetric survey done using a p

depth finder and stopwatch (Lee and Sears, 1

The completed bathymetric map then was com

the 1954 Lake Olathe topographic map to det

the sediment deposition during the intervening 

Total sediment deposition estimated from Lee 

Sears (1985) was 16.3 acre-ft, substantially le

the 317 acre-ft determined during the 2000 in

tion described in this report. Differences in de

can be attributed in large part to technologica

advancements available in 2000 that were not 

able in 1982. Insufficient information describ

methods used to determine sediment depositi

1982 preclude further comparison of the two 

 The U.S. Army Corps of Engineers study 

Kansas Water Office was done in 2000 using 

beam transducer and GPS system similar to th

method used by the USGS, and total sedimen

tion from this study was estimated to be 30 ac

(Kansas Water Office, 2001, p. 31), about 9 p

the 317 acre-ft determined by the USGS. Da

from the U.S. Army Corps of Engineers study 

made available to the USGS by KWO and ind

substantial differences in elevations used to d

reservoir bottom (E. Lewis, Kansas Water Of

commun., 2001). Elevation differences that w

based on different reference datums may expl

some, but not all, of the discrepancies betwee

USGS and U.S. Army Corps of Engineers stu

The USGS bathymetric study of Lake Olathe 

used the 1935 reference datum (1,036.00 ft) 

tour mapping to determine reservoir volume. 

1982–83 Kansas Clean Lakes Program used t

reference datum in their study. On the basis o

ervoir bottom elevations used by the U.S. Arm

of Engineers, it is not clear how sediment dep

was calculated or whether historic design info

from 1954 was used.
Sediment Deposition in Cedar Lake and Lake Olathe 

Bathymetric contour —Shows altitude of reservoir bottom.

 Contour interval is 4 feet. Datum is sea level

EXPLANATION

921.5

Lake Olathe

Water-surface elevation : 937.5 feet

Base from U.S. Geological Survey digital data, 1:24,000, 1995

Universal Transverse Mercator projection,

Zone 15

933.5

94 ̊52'30" 20" 10" 52' 94 ̊51'50"

38 ̊52'50" 

38 ̊52'10" 

40" 

30" 

20" 

933.5

933.5

933.5

933

933.5

.5

929.5

929.5

929.5

929.5 929.5

929.5

925.5

925.5

925.5

925.5

921.5

921.5

921.5

921.5

917.5

917.5

917.5

917.5

913.5

913.5

913.5

909.5

909.5

909.5

905.5

905.5

905.5

901.5

897.5

893.5

925.5

933.5 905.5

901.5

897.5

893.5

921.5

933.5

0

0 0.05 0.10 0.20 0.15 0.25 KILOMETER

0.05 0.10 0.15 0.20 0.25 MILE

Figure 5. Bathymetric contours for Lake Olathe, 2000.
16 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

EXPLANATION

Estimated thickness of sediment, in feet

Less than -6

-6 to -4

-4 to -2

-2 to 0

0 to 2

2 to 4

4 to 6

6 to 8

Greater than 8

Lake

Olathe

Base from U.S. Geological Survey digital data, 

Digital orthophoto quarter quadrangles 1:24,000, 

Universal Transverse Mercator projection,

Zone 15

0

0 0.10 0.20 0.30 KILOMETER

0.10 0.20 0.30 MILE

94°52'40" 30" 20" 10" 50" 40" 94°51

38°53'

30"

20"

40"

50"

38°52'10"

52'

Figure 6. Estimated thickness of sediment in Lake Olathe, 1956–2000.
Sediment Deposition in Cedar Lake and Lake Olathe 

The total masses of bottom-sediment material in

Cedar Lake and Lake Olathe were calculated by multiplying the bottom-sediment volume (total sediment

deposition) from each lake by the mean sediment bulk

densities (and appropriate conversion factor) as determined from the sediment cores from each lake

(table 3). The mean bulk densities for each lake were

calculated by averaging the mean bulk densities in the

sediment cores from the in- and out-of-channel coring

sites (table 4).

The total mass of bottom-sediment material for

Cedar Lake was estimated to be 595 million lb and for

Lake Olathe, 567 million lb. The mean annual sediment load for each lake, determined by dividing the

sediment mass by the number of years of sedimen

deposition, was 9.6 million lb of bottom-sedimen

deposition per year for Cedar Lake and 12.6 millio

of bottom-sediment deposition per year for Lake

Olathe.

Comparisons of Sediment Deposition Among

Cedar Lake, Lake Olathe, and Hillsdale Lake

Comparisons of Cedar Lake, Lake Olathe, an

Hillsdale Lake were made to determine difference

sediment deposition among the three lakes. Hills

Lake was chosen because it is located close to the

Lake Olathe watershed, and the two watersheds h

similar topographic features and land-use patterns

The total sediment deposition at Hillsdale La

was 2,100 acre-ft (from 1981–96), more than six t

greater than either Cedar Lake or Lake Olathe (tab

Juracek, 1997). When the comparison was made 

the basis of mean annual sediment yield (mean an

sediment deposition divided by the contributingdrainage area), the Hillsdale Lake watershed was 

largest contributor of sediment but not substantial

greater than the mean annual sediment yield from 

drainage area to Cedar Lake (table 3). If the drain

area to Cedar Lake was excluded from the Lake O

watershed, the mean annual sediment yield to Lak

Olathe would increase from 0.76 to 1.2 million

(lb/yr)/mi2, which is a more comparable yield rel

to those determined for the Cedar Lake watershed

[1.56 million (lb/yr)/mi2

] and the nearby Hillsdal

Lake watershed [1.84 million (lb/yr)/mi2]. The im

cation of this calculation is that sediment depositi

Table 3. Sediment deposition, loads, and yields estimated for Cedar Lake, Lake Olathe, and Hillsdale Lake, northeast Kansas

[mi2, square miles; acre-ft, acre-feet; lb/ft3, pounds per cubic foot; lb, pounds; lb/yr, pounds per year; (lb/yr)/mi2, pounds per year per square mile; --

applicable]

Lake

Drainage

area (mi2)

Number of

years since

dam closure

Total sediment

deposition

(acre-ft)

Mean

sediment bulk

density

(lb/ft3)

Total sediment

mass

(million lb)

Mean annual

sediment load

(million lb/yr)

Mean a

sedimen

[mill

(lb/yr)

Cedar Lake 6.14 62 338 40.4 595 9.6 1.

Lake Olathe 16.6 45 317 40.9 567 12.6 .

a. Kansas Clean Lakes

Program (1982–83)1

1

Lee and Sears (1985).

-- -- 16.3 -- -- -- --

b. Kansas Water Office

(2001)

-- -- 30 -- -- -- --

Hillsdale Lake2

2

Juracek (1997).

144 15 2,100 -- 3,973 265 1.

Table 4. Estimated mean sediment bulk densities in both inchannel and out-of-channel bottom sediment, Cedar Lake and Lake

Olathe, northeast Kansas, 2000

[lb/ft3, pounds per cubic foot]

Coring sites

(fig. 1)

Mean bulk density

(lb/ft3)

Cedar Lake

1 (out-of-channel) 42.1

2 (out-of-channel) 45.7

3 (in-channel) 33.3

Mean 40.4

Lake Olathe

1 (in-channel) 60.8

2 (in-channel) 56.4

3 (out-of-channel) 27.5

4 (out-of-channel) 29.5

5 (in-channel) 30.3

Mean 40.9
18 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

would be more substantial in Lake Olathe if Cedar

Lake did not intercept much of the sediment yield

from the watershed. Also, the contributing-drainage

area to Cedar Lake represents only 37 percent of the

watershed, and yet the mean annual sediment yield is

almost twice that contributed to Lake Olathe (table 3).

WATER-QUALITY CHARACTERISTICS

Analysis of reservoir bottom sediment can provide

insight into water-quality characteristics of a reservoir

watershed. These characteristics include historical

perspectives on sediment and chemical transport and

potential toxicological effects on aquatic organisms.

Areal distribution of sediment in the lakes and physical and chemical composition were examined during

this investigation to quantify chemical concentrations,

identify trends in chemical deposition, and evaluate

chemical composition in relation to sediment-quality

guidelines for the protection of aquatic organisms.

Identified trends in water-quality constituents were

related to known watershed land-use and humanrelated characteristics.

Phosphorus

Phosphorus is a nutrient essential for the growth

and reproduction of plants. It is used as an energy

source in the cells of plants and animals and can have

a direct effect on the production of phytoplankton populations, an important component of the food chain.

Phosphorus availability is also a critical factor in

eutrophication because it is often the limiting nutrient

that controls biological production rates (Hem, 1992,

p. 128). Excessive phosphorus in water bodies, where

nitrogen is not a limiting factor, can accelerate

eutrophication. Eutrophication is characterized by

extensive algal growth (algal blooms) that may reduce

the aesthetic and recreational value of water, and in

severe cases may stress or kill aquatic organisms as a

result of dissolved-oxygen depletion when algal

blooms die.

Common sources of human-related phosphorus

include inorganic phosphates added to agricultural

soils as fertilizer, manure from confined animalfeeding operations, and treated human sewage disposed directly into receiving streams. Excessive phosphorus concentrations in soils from both natural and

human-related sources can have detrimental effects on

lakes located downgradient from the source a

can promote excessive algal growth that lead 

and-odor problems in treated drinking water.

Phosphorus may be associated with sedim

loads that are transported to lakes. Found pri

with the finer sediment fractions, the incorpor

phosphorus into sediment effectively remove

phorus from the water column, and the reserv

ment becomes the primary sink or trap for ph

(Morris and Fan, 1998, p. 4.18).

Concentrations in Reservoir Bottom Sediment

Reservoir sediment may contain large qu

of phosphorus. This phosphorus may have be

ported into the lake in both particulate and di

forms. Analysis of the sediment was used in d

ing the extent of phosphorus deposition and t

ate historical trends.

Mean concentrations of total phosphorus 

bottom-sediment cores from Cedar Lake rang

1,370 mg/kg at coring site 1, located upstream 

lake, to 1,810 mg/kg at coring site 3, located 

dam (fig. 7). The mean total phosphorus conc

in bottom-sediment samples from the three co

sites was 1,540 mg/kg. Although Cedar Lake 

longer used as a drinking-water supply, under 

conditions (low dissolved-oxygen concentrati

phosphorus released from the sediment to the 

column could encourage algal blooms and les

suitability of water in the lake for aquatic hab

recreation. Cedar Lake also discharges water 

Olathe through Cedar Creek when the water e

of Cedar Lake exceeds the spillway elevation

(1,001.0 ft above sea level); therefore, advers

quality conditions in Cedar Lake during such 

could easily affect the water quality of the Lak

drinking-water supply.

Mean concentrations of total phosphorus 

bottom-sediment cores from Lake Olathe rang

588 mg/kg at coring site 1, located the farthes

upstream in the lake, to 1,030 mg/kg at coring 

located near the dam (fig. 7). The mean total 

rus concentration in samples from the five cor

was 774 mg/kg. It is possible that in-lake enr

of phosphorus from phytoplankton growth an

tion as well as from lake hydraulics are contri

the upstream-to-downstream increases in tota

phorus concentrations in Lake Olathe bottom 

ment. External sources such as the public go

and public latrines at the golf course and swim
Water-Quality Characteristics 

94°53' 94°50'

38°53'

38°51'

52'

52' 51'

Cedar

Lake

0

0 0.5 KILOMETER

0.25 0.5 MILE

0.25

56

35

OLATHE

OLATHE

Cedar Creek

Mean concentration

 of total phosphorus, in

 milligrams per kilogram

Coring site and number—Asterisk 

 indicates that core includes only part

 of the sediment interval

EXPLANATION

Lake Olathe

Base from U.S. Geological Survey digital data, 1:24,000, 1995

Universal Transverse Mercator projection,

Zone 15

400

0

800

1,200

1,600

400

0

800

1,200

1,600

2,000

1,430

400

0

800

1,200

1,600

2,000

1,370

2,000

400

0

800

1,200

1,600

2,000

1,370

5

4

3

2

1

1

3*

2

3*

1,600

2,000

0

400

800

1,200

1,030

1,600

2,000

0

400

800

1,200

905

1,600

2,000

0

400

800

1,200

758

1,600

2,000

0

400

800

1,200

588

1,600

2,000

0

400

800

1,200

589

City limits of Olathe

Creek

Cedar

1,810

Figure 7. Mean concentrations of total phosphorus in bottom-sediment core samples collected from Cedar Lake and

Lake Olathe, 2000.
20 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

beach also may contribute to the increased total phosphorus concentrations seen in the sediment cores near

the dam (Carly Adams, city of Olathe, oral commun.,

2001). There also may be some upstream-to-downstream transport of phosphorus through adsorption to

silt and clay particles and the subsequent transport of

these particles within the lake.

The difference in total phosphorus concentrations

in bottom sediment between the two lakes may be

related to historic agricultural and human-related practices. Fertilizer application to cropland as well as animal waste from livestock likely would include

phosphorus compounds that could be transported to

Cedar Lake, adsorbed to sediment, and deposited in

the lake. It is also possible that septic systems from

nearby farms and residences that existed or were

developed in the 1930s, when Cedar Lake was created,

may have leached phosphorus and other compounds

into the lake. Cedar Lake also acts as a sediment trap

for Lake Olathe, receiving sediment deposition that

otherwise would be transported to Lake Olathe. Sediment transport of phosphorus and other hydrophobic

compounds (compounds that adsorb to sediment) may

be more prevalent in Cedar Lake than in Lake Olathe,

where total sediment deposition is less.

Two previous reservoir-sediment studies of

Cheney Reservoir in south-central Kansas (Pope,

1998; Mau, 2001) showed a strong linear relation

between bottom-sediment particle size and total phosphorus concentration. The regression analysis by

Pope (1998) was repeated in this investigation of

Cedar Lake and Lake Olathe to determine whether a

relation existed between the size of bottom-sediment

particles and total phosphorus concentration.

Regression analysis is one method used to determine whether a relation exists between two variables.

The correlation coefficient, r, is used as a measure of

the strength of the relation and ranges from –1.0 to

1.0 depending on whether the relation is negative

(indirect) or positive (direct). The closer the correlation coefficient is to –1.0 or 1.0, the stronger the relation between the two variables. The p-value

(probability value) is used as a measure of the statistical significance of a relation. The statistical significance of a correlation increases as the p-value

decreases. A 0.05 level of significance is used in this

study to define statistically significant correlations.

Regression analysis to determine a relation

between bottom-sediment particle size and total phosphorus concentration was inconclusive primarily

because of a lack of variability in particle size

than 97 percent of the sediment particle-size d

tion in both lakes was represented by sedimen

cles less than 0.062 mm in diameter, the silt a

clay fractions (fig. 8). The p-values for both 

indicate that there is no statistical significance

relating bottom-sediment particle size to total

phosphorus concentrations.

The depositional trend of phosphorus in b

Cedar Lake and Lake Olathe was compared t

cesium-137 data. Cedar Lake was built in 19

therefore, the cesium-137 profile of Cedar La

expected to be zero near the bottom of the co

followed by increasing concentration until the

nuclear test ban treaty, with a long period of d

concentrations to the present day at the top of 

The actual cesium-137 profile peaked at the b

the core (oldest sediment) and steadily decline

slight inflection near the middle of the core (fi

Two possible explanations may account for th

cesium-137 profile of Cedar Lake: (1) an inco

bottom-sediment core was obtained, or (2) dr

activity occurred in Cedar Lake, and sedimen

ing older cesium-137 concentrations was rem

The sediment core obtained from Cedar Lake 

nearly 5 ft long. The initial core analysis show

plete core-barrel penetration through the sedim

the original bottom material, indicating that a 

plete bottom-sediment core was obtained. Al

there was no confirmation of dredging, repair 

the dam face occurred in 1995, following sign

water-seepage loss through the earthen dam o

24-hour period in 1994 (Carly Adams, city of 

oral commun., 2001). Repair-work document

indicate the use of lake sediment to shore the 

face. However, because it is possible that sed

near the dam was disturbed either during the r

of water from the lake or during repair work o

dam, comparison of constituent trends using a

results from coring site 3, located closest to C

Lake Dam would be inconclusive.

The depositional trend of phosphorus at L

Olathe was supported by the cesium-137 anal

(fig. 9). Cesium-137 data in bottom sediment 

a peak in cesium-137 concentrations near the 

of the core followed by a gradual decrease to 

recent deposition. Dredging activity and rem

3 acre-ft of bottom sediment that occurred in t

end of Lake Olathe in 1980 (Lee and Sears, 19

have disturbed the sediment profile and accou
Water-Quality Characteristics 

94°53' 94°50'

38°53'

38°51'

52'

52' 51'

Cedar

Lake

0

0 0.5 KILOMETER

0.25 0.5 MILE

0.25

56

35

OLATHE

OLATHE

Cedar Creek

EXPLANATION

Lake Olathe

Base from U.S. Geological Survey digital data, 1:24,000, 1995

Universal Transverse Mercator projection,

Zone 15

Mean particle-size composition,

 in percent (%)

 Silt and clay (less than 0.062 millimeter 

 in diameter)

 

 Sand (greater than 0.062 millimeter 

 in diameter) 

Coring site and number—Asterisk 

 indicates that core includes only part

 of the sediment interval

2.3%

97.7%

City limits of Olathe

99.3%

0.7%

0.7%

2.8%

97.3%

2.7%

0.8%

99.3%

97.2%

99.7%

0.3%

2.3%

0.9%

97.7%

99.1%

99.2%

1

3*

2 3*

5

4

3

2

1

Creek

Cedar

Figure 8. Mean particle-size composition of bottom-sediment cores collected from Cedar Lake and Lake Olathe, 2000.
22 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

5.5

0 0.5 1.0 1.5 0 0.5 1.0 

4.4

3.3

2.2

1.1

0

3.5

2.8

2.1

1.4

0.7

0

Lake Olathe

coring site 5

Cedar Lake

coring site 3

Depth of sample, in feet

Cesium-137 concentration, in picocuries per gram

Water/sediment

interface

Bottom of core

2000

1956

1960–65

slight variations in the

cesium-137 profile near

the top of the core. The

cesium-137 data from the

sediment core indicate that

substantial disturbance of

sediment layers has not

occurred in Lake Olathe and,

therefore, would not affect

time-trend analysis.

Total phosphorus concentrations in a bottomsediment core from Lake

Olathe appeared to be

increasing slightly from the

older sediment to the newer

sediment near the top of the

core (fig. 10). However, the

Kendall’s tau trend test of the

data set did not identify a

trend (table 5). If there is a

trend, the most likely source

is leaking septic systems

from residences located near

Lake Olathe, which were

identified in the 1982–83

Kansas Clean Lakes Program investigation of Lake

Olathe (Lee and Sears, 1985). Additional sources of

total phosphorus to Lake Olathe could include phosphorus adsorbed to suspended sediment particles

transported from Cedar Lake via Cedar Creek, as well

as fertilizer usage from either agricultural or urban

sources. The extent of suspended sediment and nutrient transport from Cedar Lake to Lake Olathe via

Cedar Creek is being investigated.

Estimates of Phosphorus Loads and Yields in Lake Olathe

Watershed

Sediment loads and yields provide important

information on the water-storage capacity and ecosystem of a reservoir, as well as activities within the

watershed. Additionally, the evaluation of loads and

yields of hydrophobic constituents, such as phosphorus, can be used by reservoir and watershed managers

to help determine the effectiveness of BMPs or to

implement new policies aimed at reducing the use or

distribution of these constituents.

Phosphorus loads and yields in the Lake Olathe

watershed were calculated on the basis of total

sediment deposition previously reported in ta

The total sediment deposition then was multip

the mean total phosphorus concentration in b

sediment from each lake and, using the appro

conversion factors to convert from Internation

tem to inch-pound units of measurement, divi

the number of years of sediment deposition to 

mine the annual mean phosphorus load in pou

year (table 6). The mean annual phosphorus y

determined by dividing the mean annual phos

load by the drainage area to each lake. The re

the sediment-based phosphorus yields for the 

Lake and Lake Olathe watersheds were comp

to yields determined for the Webster Reservo

Cheney Reservoir, Tuttle Creek Lake, and Hi

Lake watersheds.

Results of the load and yield calculations 

Cedar Lake and Lake Olathe indicated that m

annual phosphorus loads for Cedar Lake, 14,7

were more than 50 percent larger than for Lak

9,720 lb/yr, and that mean annual phosphorus 

were about four times larger for Cedar Lake,

Figure 9. Relation between concentrations of cesium-137 and depths of bottom-sediment 

from coring site 3 in Cedar Lake, 1938–2000, and coring site 5 in Lake Olathe, 1956–2000. Lo

coring sites shown in figure 1.
Water-Quality Characteristics 

Lake Olathe

coring site 5

800 1,000 1,200

3.5

2.8

2.1

1.4

0.7

0

Depth of sample, in feet

Total phosphorus concentration,

in milligrams per kilogram

r = 0.60

p-value = 0.07

Water/sediment

interface

Bottom of core

2000

1960–65

1956

3.74 (lb/acre)/yr compared to 0.91 (lb/acre)/yr for

Lake Olathe (table 6). The differences probably can

be attributed to different agricultural and residential

practices in the watershed as previously discussed in

this report. The implication is that Cedar Lake acts as

a water-quality buffer for Lake Olathe and that water

quality in Lake Olathe would be changed substantially

if Cedar Lake were removed and presumably wou

increase loads and yields to Lake Olathe.

Recent studies of phosphorus transported to W

ster Reservoir (Mau and Christensen, 2000), Chen

Reservoir (Mau, 2001), Tuttle Creek Lake (Mau a

Christensen, 2000), and Hillsdale Lake (Juracek,

1997) offer comparisons for the estimates of phos

rus transported into Cedar Lake and Lake Olathe. 

mean annual phosphorus yield of the Cedar Lake 

watershed, 3.74 (lb/acre)/yr, was larger than the m

annual phosphorus yield from the other reservoir

watersheds that were studied. The Lake Olathe w

shed also transported more phosphorus annually p

acre of drainage area, 0.91 (lb/acre)/yr, than the o

reservoir watersheds studied by the USGS in Kan

with the exception of Hillsdale Lake in northeast 

sas (Mau, 2001). However, if the Cedar Lake sub

tershed was considered a noncontributing-drainag

area to Lake Olathe, the mean annual phosphorus

yield of the Lake Olathe watershed would be

1.41 (lb/acre)/yr, a difference of about 28 percent

from the phosphorus yield estimated for Hillsdale

Lake. On the basis of phosphorus deposited in re

voir bottom sediment, mean annual phosphorus y

were estimated to be 0.04 (lb/acre)/yr for the Web

Reservoir watershed (Mau and Christensen, 2000

0.38 (lb/acre)/yr for the Cheney Reservoir waters

(Mau, 2001), 0.41 (lb/acre)/yr for the Tuttle Creek

Lake watershed (Mau and Christensen, 2000), an

1.7 (lb/acre)/yr for the Hillsdale Lake watershed

(Juracek, 1997).

Nitrogen

The presence of nitrogen, along with phospho

is essential for plant growth. Nitrogen also is imp

tant because it is used to synthesize proteins and,

along with carbohydrates and fats, constitutes the

major part of living substances (Reid and Wood,

1976). Nitrogen differs from phosphorus in that n

gen is very mobile and not highly absorbed by so

with the exception of ammonia (NH3), which tend

adsorb to clay or organic particles (Morris and Fa

1998). Contributions of nitrogen and phosphorus

compounds to water bodies can lead to excessive 

growth, which may produce taste-and-odor proble

in drinking water, stress aquatic organisms, and

decrease the aesthetic and recreational value of th

water body.

Figure 10. Relation between total phosphorus

concentrations in bottom-sediment samples and depths of

samples from coring site 5 in Lake Olathe, 1956–2000.

Location of coring site shown in figure 1.

Table 5. Trend test analysis of concentrations of total phosphorus

and total ammonia plus organic nitrogen (N) in bottom sediment

from coring site 5 in Lake Olathe, northeast Kansas, 2000

Coring site

(fig. 1) Constituent

Number of

samples

with

detections

Kendall’s

tau

Trend test at a

0.05 level of

significance

LakeOlathe

coring site 5

total phosphorus 10 0.378 no trend

total ammonia

plus organic

nitrogen

10 .089 no trend
24 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

There are many potential sources of nitrogen in

the Lake Olathe watershed including leachate from

septic systems, runoff from livestock wastes, runoff

from agricultural and residential application of synthetic fertilizers, and atmospheric deposition (Carly

Adams, city of Olathe, oral commun., 2001; Wetzel,

2001, p. 226). Leachate from public latrines, as well

as leachate from private residential septic systems,

may contribute nitrogen compounds to the watershed

and lake. The application of synthetic fertilizers

in Kansas has increased about 10-fold in the past

40 years (Kansas Department of Agriculture and U.S.

Department of Agriculture, 1996). Nitrogen fertilizers

not incorporated into the soil or used by plants can be

washed off by excessive rains into nearby streams or

infiltrate into ground water. Atmospheric deposition is

another source of nitrogen in the watershed. Nitrogen

represents 79 percent of the atmosphere and can be

converted to ammonia and nitrate by cosmic radiation

and subsequently deposited on soil through precipitation (Manahan, 1994, p. 160).

Mean concentrations of total ammonia plus

organic nitrogen as nitrogen (N) ranged from 2,000 to

2,700 mg/kg in bottom-sediment samples from Cedar

Lake and from 1,300 to 2,700 mg/kg in samples from

Lake Olathe (fig. 11). The values are similar to concentrations of mean total ammonia plus organic nitrogen as nitrogen (N) analyzed in bottom-sediment cores

collected in 1998 from Kirwin, Webster, and Cheney

Reservoirs, and Waconda Lake (Christensen, 1999;

Mau, 2001).

Total ammonia plus organic nitrogen as n

(N) concentrations in bottom sediment were a

using the sediment profile at coring site 5 in L

Olathe to determine whether trends existed fr

older sediment deposited at the bottom of the 

the newer sediment at the top of the core. An 

tion of the correlation coefficient and p-value 

simple linear regression indicated that there w

statistical significance between total ammonia 

organic nitrogen as nitrogen (N) concentratio

depth (fig. 12). The application of Kendall’s t

total ammonia plus organic nitrogen as nitrog

data set for both lakes did not indicate trends 

lake (table 5).

Trace Elements

Trace element concentrations occur at lev

few hundred micrograms per kilogram or less

trace elements are essential constituents of va

enzymatic and cellular processes found in pla

animals but can be toxic in large concentratio

and Jones, 1997). Found naturally in bottom 

ment, trace elements can be enriched by hum

ties, such as those associated with industrial o

commercial areas (Pais and Jones, 1997). Re

bottom sediment serves as a sink or trap for tr

ments from the entire watershed, and therefor

sis of the sediment can be used to evaluate th

potential effects of watershed management pr

and changes in land use.

Table 6. Total phosphorus sediment loads and yields estimated for Cedar Lake, Lake Olathe, and other selected reservoir water

Kansas

[million lb, million pounds; mg/kg, milligrams per kilogram; lb/yr, pounds per year; (lb/acre)/yr, pounds per acre per year]

Reservoir watershed or

subwatershed Number of years

Total sediment

deposition (million lb)

Mean phosphorus

concentration in

sediment

(mg/kg)

Mean annual

phosphorus load

(lb/yr)

Mean 

phospho

[(lb/ac

Cedar Lake 62 595 1,540 14,700 3.74

Lake Olathe 45 567 774 9,720 .9

Webster Reservoir1

1

Christensen (1999); Mau and Christensen (2000).

42 3,300 374 29,400 .04

Cheney Reservoir2

2

Mau (2001).

34 15,400 480 226,000 .38

Tuttle Creek Lake3

3

Data on file with U.S. Geological Survey, Lawrence, Kansas; Mau and Christensen (2000).

37 194,000 481 2,520,000 .4

Hillsdale Lake4

4

Juracek (1997); Mau and Christensen (2000).

15 4,000 583 154,000 1.7
Water-Quality Characteristics 

City limits of Olathe

94°53' 94°50'

38°53'

38°51'

52'

52' 51'

Cedar

Lake

0

0 0.5 KILOMETER

0.25 0.5 MILE

0.25

56

35

OLATHE

OLATHE

Cedar Creek

Mean concentration

 of total ammonia plus

 organic nitrogen as

 nitrogen, in milligrams

 per kilogram

Coring site and number—Asterisk 

 indicates that core includes only part

 of the sediment interval

EXPLANATION

Lake Olathe

Base from U.S. Geological Survey digital data, 1:24,000, 1995

Universal Transverse Mercator projection,

Zone 15

0

500

1,000

1,500

2,000

2,500

3,000

3500

2,000

0

500

1,000

1,500

2,000

2,500

3,000

3,500

1,300

0

500

1,000

1,500

2,000

2,500

3,000

3,500

2,400

0

500

1,000

1,500

2,000

2,500

3,000

3,500

1,500

0

500

1,000

1,500

2,000

2,500

3,000

3,500

2,000

0

500

1,000

1,500

2,000

2,500

3,000

3,500

2,500

0

500

1,000

1,500

2,000

2,500

3,000

3,500

2,700

0

500

1,000

1,500

2,000

2,500

3,000

3,500

2,700

0

500

1,000

1,500

2,000

2,500

3,000

3,500

2,700

5

4

3

2

1

1

3*

2

3*

Creek

Cedar

Figure 11. Mean concentrations of total ammonia plus organic nitrogen as nitrogen in bottom-sediment samples from

Cedar Lake and Lake Olathe, 2000.
26 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

0 1,000 2,000 3,000 4,000

3.5

2.8

2.1

1.4

0.7

0

r = 0.10

p-value = 0.78

2000

1960–65

1956

Depth of sample, in feet

Total ammonia plus organic nitrogen as nitrogen

concentration, in milligrams per kilogram

Water/sediment

interface

Bottom of core

Lake Olathe

coring site 5

One bottom-sediment core from both Cedar Lake

and Lake Olathe was analyzed for trace elements

(table 7; tables 16–17, in “Supplemental Information”

section of this report). Each core was divided into five

equal subsections and analyzed for trace elements.

The mean value of each trace element analyzed from

the five subsections was used in the discussion that follows. The data from one core in each lake did not provide sufficient information to determine whether any

upstream-to-downstream trends in trace element concentrations existed.

The USEPA (1998) has established two sets of

sediment-quality guidelines for selected trace elements—the Threshold Effects Level (TEL) and the

Probable Effects Level (PEL). The smaller of the two

guidelines (the TEL) is assumed to represent the concentrations below which toxic effects rarely occur. In

the range between the TEL and PEL, toxic effects

occasionally occur, and above the PEL guideline toxic

effects frequently occur. The guidelines are used by

the USEPA as screening tools and are not inte

have any regulatory implications. This cautio

statement is made because, although biologica

correlation to trace element concentrations id

levels-of-concern concentrations associated w

likelihood of adverse organism response, the p

procedure used may not demonstrate that a pa

chemical is solely responsible. Biological-eff

relations may not indicate direct cause-and-ef

tionships because coring sites may contain a m

of chemicals that contribute to the adverse eff

differing degrees. Therefore, for any given si

guidelines may be over- or underprotective.

Mean concentrations of trace elements in 

sediment samples from Cedar Lake and Lake 

exceeded the USEPA TEL sediment-quality g

for six of the eight trace elements that had gu

(figs. 13–14, table 7). Mean concentrations of 

chromium, copper, lead, nickel, and zinc exce

TELs in samples from Cedar Lake coring site 

from Lake Olathe coring site 5, placing them 

range where toxic effects occasionally occur. 

mium and mercury concentrations in bottom-

samples from both lakes were less than the TE

ment-quality guidelines. In addition, none of 

guidelines were exceeded in samples from eit

Mean concentrations of arsenic in bottom

sediment samples from both Cedar Lake and 

Olathe were more than twice the TEL guideli

arsenic but much less than the PEL guideline (

Arsenic has been used extensively as a pestic

bicide, and soil sterilant in agricultural soils i

United States, but it has only a moderate bioa

tion effect because it is not very mobile (Pais 

Jones, 1997, p. 86).

Mean chromium concentrations exceeded 

guideline by 79 percent in the bottom-sedime

ples from Cedar Lake and by 73 percent in sa

from Lake Olathe (table 7). Chromium is a to

metal used in industry and is released in indu

wastewaters. The watershed does not support 

trial activity; therefore, the source of chromiu

watershed is not well understood. However, ch

also is naturally present in the environment an

be a by-product of agricultural application of 

ers. The content of chromium in most fertiliz

ranges from 2 to 1,000 μg/g (Pais and Jones, 

Mean copper concentrations in bottom se

from both Cedar Lake and Lake Olathe excee

TEL guideline for copper (table 7). Copper i

Figure 12. Relation between concentrations of total

ammonia plus organic nitrogen as nitrogen in bottomsediment samples and depths of samples from coring site 5

in Lake Olathe, 1956–2000. Location of coring site shown in

figure 1.
Water-Quality Characteristics 

essential micronutrient for plants and commonly is

found in soil, and although the TEL concentration

guidelines were exceeded by 84 percent in bottomsediment samples from both Cedar Lake and Lake

Olathe, the mean concentrations were substantially

less than the PEL for copper (table 7).

Lead is a metal introduced primarily into the

atmosphere through volatilization and combustion of

leaded gasoline (Pais and Jones, 1997). Lead also can

be introduced to the environment through agricultural

fertilizer use; the lead content of fertilizers frequently

ranges between 2 and 225 μg/g (Pais and Jones, 1997).

Lead is not very mobile in soils or soluble in water.

Mean lead concentrations exceeded the TEL guideline

of 30 μg/g in bottom-sediment samples from both

Cedar Lake and Lake Olathe by 10 and 13 percent,

respectively, but were substantially less than the PEL

guideline of 110 μg/g for lead (table 7).

Lead concentrations in bottom-sediment samples

from Cedar Lake varied little with depth in the sediment profile (fig. 13), which may be related to the possible sediment disturbance from dam repair work in

1995. In contrast, the sediment profile from bottom

sediment in Lake Olathe showed a slight decrease in

lead concentrations from sediment in the bottom of the

core to the water/sediment interface (fig. 14). The

decrease in lead concentrations may be a result of the

discontinued use of leaded gasoline in the early 1970s.

The typical total nickel content in uncontaminated

soil is 25 μg/g, although concentrations in soil can

range from 1 to 200 μg/g (Kabata-Pendias and Pendias, 1994; Pais and Jones, 1997, p. 124). Recent

research suggests that nickel is an essential micronutrient for both plants and animals; however, in large

concentrations it can be toxic (Pais and Jones, 1997,

p. 125). Mean concentrations of nickel in bottomsediment samples from both Cedar Lake and Lake

Olathe were more than double the TEL guideline for

nickel and slightly less than the PEL (table 7,

figs. 13–14). With no apparent industrial source o

nickel in the watershed, it may be that seepage fro

residential septic systems and surface runoff are c

tributing and concentrating nickel in the reservoir 

tom sediment (Sedlack and others, 1997).

Zinc is an essential micronutrient for both pla

and animals and is fairly uniformly distributed in 

(Pais and Jones, 1997, p. 147). Toxicity can occu

from elevated zinc levels in industrial wastes or s

age sludge that can contain zinc at concentrations 

excess of 1,700 μg/g (Pais and Jones, 1997, p. 14

Zinc also can be released to the atmosphere by el

tric-utility coal-burning operations as well as from 

burning of industrial wastes (U.S. Public Health S

vice, 1994). The lack of industrial sources in the L

Olathe watershed suggests that seepage from leak

septic systems may be a possible source of zinc in 

reservoir bottom sediment. Concentrations of zin

bottom-sediment samples from both Cedar Lake 

Lake Olathe exceeded the TEL guideline for zinc 

30 percent and 18 percent, respectively, but were 

stantially less than the PEL guideline of 270 μg/g

(table 7, figs. 13–14).

An examination of the subsectioned bottomsediment cores from Lake Olathe for trends in fiv

of the six selected trace elements was inconclusiv

(fig. 14). Arsenic, chromium, copper, nickel, and 

fluctuated with depth with no apparent increasing 

decreasing trend. The concentrations of these tra

elements that exceed the TEL guidelines may be

related more to natural conditions than to point or 

point sources. The Lake Olathe watershed does n

have any large urban areas, an industrial base, or l

population centers; therefore, any significant cont

tions from these sources would be limited.

Table 7. Mean concentrations and sediment-quality guidelines for selected trace elements in bottom-sediment samples from Cedar 

and Lake Olathe, northeast Kansas, 2000

[all values in micrograms per gram]

Coring site (fig. 1) Arsenic Cadmium Chromium Copper Lead Mercury Nickel Z

Cedar Lake coring site 3 15 0.30 93 35 33 0.07 35 15

Lake Olathe coring site 5 16 .33 90 35 34 .06 37 14

Sediment-quality guidelines

TEL1

1

TEL, Threshold Effects Level; PEL, Probable Effects Level (U.S. Environmental Protection Agency, 1998).

7.2 .68 52 19 30 .13 16 12

PEL1 42 4.2 160 110 110 .70 43 27
28 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

Selected Pesticides

Pesticides are used

in the United States to

control weeds, insects,

and other organisms.

About 80 percent of

pesticide application is

used on agricultural

land, and although

crop production has

been enhanced, the use

of pesticides has raised

concerns about potential adverse effects on

human health and the

environment (Nowell

and others, 1999).

This investigation analyzed the occurrence

of 70 pesticides in reservoir bottom sediment

from both Cedar Lake

and Lake Olathe that

could pose a current

(2001) or future risk.

Bottom-sediment

cores from both Cedar

Lake and Lake Olathe

were collected and

analyzed for selected

pesticides including

organochlorine insecticides, organophosphate insecticides,

acetanilide herbicides,

and triazine herbicides

(table 8). Organochlorine insecticides can be

found in reservoir bottom sediment in watersheds where these

compounds are used

extensively to control

insect damage to crops

such as corn, wheat,

and sorghum (Elder

and Mattraw, 1984; Smith and others, 1987; Kalkhoff

and Van Metre, 1997). These compounds also are

used to control insects such as ants, termites, beetles,

fleas, lice, mites, and mosquitos. The

organophosphate insecticides have uses simil

organochlorine insecticides, may be used on h

food crops such as fruits and vegetables, and 

Figure 13. Relation between selected trace element concentrations in bottom-sediment samples 

depths of samples from coring site 3 in Cedar Lake, 2000. Location of coring site shown in figure 

Sediment-quality guidelines from U.S. Environmental Protection Agency (1998) (TEL, Threshold E

Level; PEL, Probable Effects Level).

0 2 4 6 8 10 12 14 16 18 5.5

4.4

3.3

2.2

1.1

0

Depth of sample, in feet

Water/sediment

interface

Water/sediment

interface

Bottom of core

Bottom of core

0 5 10 15 20 25 30 35 40 45

Concentration, in micrograms per gram (μg/g)

0 40 80 120 

0 5 10 15 20 25 30 

5.5

4.4

3.3

2.2

1.1

0

0 5 10 15 20 25 30 35 40 45

0 10 20 30 40 50 60 70 80 90 100

Arsenic Chromium Copper

TEL=7.2 μg/g

Lead Nickel Zinc

TEL=30 μg/g TEL=16 μg/g

PEL=43 μg/g

TEL=120 μg/g

TEL=52 μg/g TEL=19 μ
Water-Quality Characteristics 

water soluble and less persistent than organochlorine

compounds (U.S. Environmental Protection Agency,

1989). The acetanilide and triazine herbicides are

used for weed and

grass control on cr

such as corn, sorghum, and soybea

and along roadwa

and railroad rights

way (U.S. Environ

mental Protection

Agency, 1989).

There were no

detections of selec

organochlorine or

organo-phosphate

insecticides in bot

sediment samples 

Cedar Lake or Lak

Olathe (table 8). T

is surprising becau

of their widesprea

and prevalence in 

environment. Dur

the past 30 years, m

than 400 scientific

studies including fi

national programs

have looked for pe

cides in stream se

ment or aquatic bi

Most of the compounds detected in

these studies were

organochlorine in

cides or their degr

tion products, whi

were detected in a

92 percent of the s

ies (Nowell and ot

1999). The result

these studies are a

reflection of the h

phobic nature and 

sistence of these

compounds, and t

fact that most of th

monitoring progra

analyzed for organochlorine compounds.

Some acetanilide and triazine herbicides were

detected at low concentrations in bottomsediment samples from Cedar Lake and Lake Ola

Figure 14. Relation between selected trace element concentrations in bottom-sediment samples and

depths of samples from coring site 5 in Lake Olathe, 2000. Location of coring site shown in figure 1.

Sediment-quality guidelines from U.S. Environmental Protection Agency (1998) (TEL, Threshold Effects

Level; PEL, Probable Effects Level). Depth of sample, in feet

Water/sediment

interface

Water/sediment

interface

Bottom of core

Bottom of core

0 2 4 6 8 10 12 16 18 14 20 22 3.5

2.8

2.1

1.4

0.7

0

5 10 15 20 25 30 35 40 45 0 25 75 100 50 125 150 175

Concentration, in micrograms per gram (μg/g)

0 5 10 15 20 25 30 35 40 45

3.5

2.8

2.1

1.4

0.7

0 

0 5 10 15 20 25 30 35 40 45 50

0 10 20 30 40 50 60 70 100 80 90

Arsenic Chromium Copper

TEL=7.2 μg/g

Lead Nickel Zinc TEL=30 μg/g

TEL=16 μg/g

PEL=43 μg/g

TEL=120 μg/g

TEL=52 μg/g TEL=19 μg/g
30 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

Table 8. Mean concentrations of selected pesticides in bottom-sediment samples from Cedar Lake and Lake Olathe, northeast 

2000—Continued

Pesticide

Method reporting limit

(μg/kg)

Cedar Lake Lake Olathe

Number of analyses

Mean concentration1

(μg/kg) Number of analyses

Mean con

(μ

Organochlorine insecticides

Alpha-HCH <0.20 5 <0.20 7 <0.20

Beta-HCH <.20 5 <.20 7 <.20

Delta-HCH <.20 5 <.20 7 <.20

Lindane <.20 5 <.20 7 <.20

Heptachlor <.20 5 <.20 7 <.20

Aldrin <.20 5 <.20 7 <.20

Heptachlor epoxide <.20 5 <.20 7 <.20

Chlordane <.20 5 <.20 7 <.20

Endosulfan I <.20 5 <.20 7 <.20

Dieldrin <.20 5 <.20 7 <.20

pp-DDE <.20 5 <.20 7 <.20

Endrin <.20 5 <.20 7 <.20

Endosulfan II <.20 5 <.20 7 <.20

pp-DDD <.20 5 <.20 7 <.20

Endrin aldehyde <.20 5 <.20 7 <.20

Endosulfan sulfate <.20 5 <.20 7 <.20

pp-DDT <.20 5 <.20 7 <.20

Methoxychlor I <.20 5 <.20 7 <.20

Methoxychlor II <.20 5 <.20 7 <.20

Organophosphate insecticides

Azinfos ethyl <.20 5 <.20 5 <.20

Carbophenothion <.20 5 <.20 5 <.20

Chlorfenvinfos <.20 5 <.20 5 <.20

Chlorpyrifos <.20 5 <.20 5 <.20

Chlorpyrifos methyl <.20 5 <.20 5 <.20

Coumafos <.20 5 <.20 5 <.20

Diazinon <.20 5 <.20 5 <.20

Dichlorvos <.20 5 <.20 5 <.20

Dicrotofos <.20 5 <.20 5 <.20

Ethion <.20 5 <.20 5 <.20

Ethoprop <.20 5 <.20 5 <.20

Fenchlorfos <.20 5 <.20 5 <.20

Fenitrothion <.20 5 <.20 5 <.20

Fensulfothion <.20 5 <.20 5 <.20

Fonofos <.20 5 <.20 5 <.20

Table 8. Mean concentrations of selected pesticides in bottom-sediment samples from Cedar Lake and Lake Olathe, northeast 

[μg/kg, micrograms per kilogram; <, less than indicated method reporting limit]
Water-Quality Characteristics 

Organophosphate insecticides—Continued

Leptofos <0.20 5 <0.20 5 <0.20

Malathion <.20 5 <.20 5 <.20

Methidiathion <.20 5 <.20 5 <.20

Methyl parathion <.20 5 <.20 5 <.20

Mevinphos <.20 5 <.20 5 <.20

Monocrotofos <.20 5 <.20 5 <.20

Oxydemeton methyl <.20 5 <.20 5 <.20

Parathion <.20 5 <.20 5 <.20

Stirofos <.20 5 <.20 5 <.20

Sulfotepp <.20 5 <.20 5 <.20

Sulprofos <.20 5 <.20 5 <.20

Thionazin <.20 5 <.20 5 <.20

Tokuthion <.20 5 <.20 5 <.20

Tribufos <.20 5 <.20 5 <.20

Tributyl phosphate <.20 5 <.20 5 <.20

Trichlornate <.20 5 <.20 5 <.20

Acetanilide herbicides

Acetochlor <.20 5 <.20 7 <.20

Alachlor <.20 5 4.3 7 14

Metolachlor <.20 5 .57 7 .60

Propachlor <.20 5 <.20 7 <.20

Trifluralin <.20 5 <.20 7 .80

Triazine herbicides

Ametryn <.20 5 2.0 7 6.0

Atrazine <.20 5 1.3 7 1.6

Cyanazine <.20 5 <.20 7 <.20

Cyanazine amide <.20 5 <.20 7 <.20

Deethylatrazine <.20 5 <.20 7 <.20

Deisopropylatrazine <.20 5 <.20 7 <.20

Dimethenamid <.20 5 <.20 7 <.20

Flufenacet <.20 5 <.20 7 <.20

Metribuzin <.20 5 <.20 7 <.20

Pendamethalin <.20 5 <.20 7 <.20

Prometon <.20 5 <.20 7 <.20

Prometryn <.20 5 <.20 7 <.20

Propazine <.20 5 <.20 7 <.20

Simazine <.20 5 <.20 7 .35

Terbutryn <.20 5 <.20 7 .25

1Mean concentration reported as <0.20 μg/kg when all analyses were less than the method reporting limit.

Table 8. Mean concentrations of selected pesticides in bottom-sediment samples from Cedar Lake and Lake Olathe, northeast Kansa

2000—Continued

Pesticide

Method reporting limit

(μg/kg)

Cedar Lake Lake Olathe

Number of analyses

Mean concentration1

(μg/kg) Number of analyses

Mean concentr

(μg/kg)
32 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

5.50

4.95

4.40

3.85

3.30

2.75

2.20

1.65

1.10

0.55

5.50

4.95

4.40

3.85

3.30

2.75

2.20

1.65

1.10

0.55

0

0 5 10 15 20 25 30 35 40 45 50

Water/sediment

interface

Water/sediment

interface

Bottom of core

Bottom of core 0 0.2 0.4 0.6 0.8 1.0 1.2 1.4 1.6 1.8 2.0 0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0

Concentration, in micrograms per kilogram (μg/kg)

Alachlor

Metolachlor Trifluralin

Depth of sample, in feet

0

01234 5 6 7 8 9 10

Concentration one-half

 method reporting limit 

 of 0.20 microgram per 

 kilogram

EXPLANATION

0 0.5 1.0 1.5 2.0 2.5 3.0

Ametryn Atrazine

(table 8) (figs. 15–16). Trends in concentrations of

pesticides in bottom sediment from Cedar Lake will

not be compared to concentrations of pesticides in bottom sediment from Lake Olathe because of the uncertainty associated with the sediment data from 

Lake previously discussed.

Concentrations of alachlor in bottom sedi

from Cedar Lake were higher in subsamples f

upper one-third of the sediment core (from 0.

Figure 15. Relation between selected pesticide concentrations in bottom-sediment samples and depths of

samples from coring site 3 in Cedar Lake, 2000. Location of coring site shown in figure 1.
Water-Quality Characteristics 

3.50

3.15

2.80

2.45

2.10

1.75

1.40

1.05

0.70

0.35

0

0 5 10 15 20 25 30 35 40 45 50 0 0.4 0.8 1.2 1

0 0.2 0.4 0.6 0.8 1.0

Water/sediment

interface

Water/sediment

interface

Bottom of core

Bottom of core

Depth of sample, in feet

3.50

3.15

2.80

2.45

2.10

1.75

1.40

1.05

0.70

0.35

0

01234 5 6 7 8 9 10 0 0.5 1.0 1.5 2.0 2.5 3.0

0

0.25

0.50

0.75

1.00

1.25

1.50

1.75

2.0

0 0.2 0.4 0.6 0.8 1.0

Alachlor Ametryn Atrazine

Simazine Terbutryn Trifluralin

Metolachlor

Concentration, in micrograms per kilogram (μg/kg)

Concentration one

 method reporting 

 of 0.20 microgra

 kilogram

EXPLANATIO

1.65 ft below the water/sediment interface) and, in bottom sediment from Lake Olathe, were higher in

subsamples from the upper one-half of the sediment

core (from 0.35 to 1.75 ft below the water/sediment

interface). Concentrations of alachlor in Cedar Lake

bottom sediment increased from less than 0.20 to

21 μg/kg as the water/sediment interface was

approached (fig. 15). Similarly, concentrations of

alachlor in Lake Olathe bottom sediment increase

from 1.3 to 46 μg/kg as the water/sediment interf

was approached (fig. 16). Alachlor was commerc

Figure 16. Relation between selected pesticide concentrations in bottom-sediment samples and depths of samples from coring site 

Lake Olathe, 2000. Location of coring site shown in figure 1.
34 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

introduced to the United States in 1969 for weed control (Ahrens, 1994).

Concentrations of metolachlor in bottom sediment

from Cedar Lake were higher in subsamples from the

upper one-third of the sediment core (from 0.55 to

1.65 ft below the water/sediment interface) and in

Lake Olathe were higher in subsamples from the upper

one-half of the sediment core (from 0.35 to 1.75 ft

below the water/sediment interface). Concentrations

of metolachlor in Cedar Lake sediment increased from

less than 0.20 to 1.8 μg/kg as the water/sediment interface was approached (fig. 15). Concentrations of

metolachlor in bottom sediment from Lake Olathe

increased from less than 0.20 to 1.9 μg/kg in subsamples from the upper one-half of the sediment core as

the water/sediment interface was approached (fig. 16).

Metolachlor was commercially introduced to the

United States in 1977 for weed control (Ahrens,

1994). The presence of metolachlor above detection

levels in the bottom-sediment profile suggests that

about one-half (2.75 ft) of the total sediment deposition to Lake Olathe has occurred sometime since the

introduction of metolachlor in 1977.

Bottom-sediment samples from Cedar Lake and

Lake Olathe also showed detections of the triazine herbicide atrazine. Concentrations of atrazine in Cedar

Lake sediment ranged from 1.4 μg/kg, near the bottom

of the sediment core farthest from the water/sediment

interface, to 1.8 μg/kg, near the water/sediment interface (fig. 15). Concentrations of atrazine in Lake

Olathe ranged from less than 0.20 μg/kg, near the bottom of the sediment core farthest from the water/sediment interface, to 2.4 μg/kg near the water/sediment

interface (fig. 16). Atrazine became commercially

available in the United States in 1958, 2 years after

dam impoundment of Lake Olathe, and its continued

and increased usage in the watershed is indicated in

the bottom-sediment profile. However, the detection of

atrazine in Cedar Lake at the bottom of the sediment

core suggests that the sediment was disturbed because

atrazine was not commercially available in 1938 when

the dam was constructed.

Although the detected herbicides have large solubilities, they degrade rapidly (1 to 2 months), and

probably have little long-term water-quality implications for aquatic organisms in either lake as a result of

chemical storage in bottom sediment. However, there

may be degradation compounds from the detected herbicides in the sediment that are toxic to aquatic organisms. Some, but not all, of the degradation compounds

were analyzed. The USEPA has not proposed 

PEL guideline concentrations in bottom sedim

any of the organochlorine, organophosphate, 

ide, or triazine pesticides.

DIATOMS AS INDICATORS OF LAKE

EUTROPHICATION

Lake eutrophication is the most widespre

of lake pollution on a global scale, can negati

affect aquatic ecosystems (Harper, 1992), and 

costly economic problem. Excessive algal gr

in response to eutrophication, can increase wa

treatment costs and sometimes cause treatmen

ties to malfunction (Vaughn, 1961; Hayes and 

1984). In addition, algal blooms (including d

blooms) can create taste-and-odor problems

(Mason, 1991).

Diatoms are microscopic algae that occur 

water and marine environments. They have a 

shell, or frustule, consisting of two valves (ha

that generally is preserved well in sediment (P

others, 1998). Diatoms occur in a variety of h

including open water, on plants and macroalg

on sediment. Diatoms are abundant and diver

freshwater lakes and may play an important ro

aquatic food chain (Round and others, 1990). 

fore, the response of diatoms to lake eutrophi

may have implications for other components 

aquatic ecosystem. Diatoms are ideal for lake 

ication studies because individual species are 

to environmental changes such as changes in

nutrient concentrations and, therefore, can qu

environmental changes that accompany eutrop

(Stoermer and Smol, 1999).

Diatom species were identified and count

subsections of bottom-sediment cores from bo

Lake and Lake Olathe. The number of diatom 

identified in the subsections ranged from12 to 

the sediment core collected from Cedar Lake 

27 to 50 in the sediment core collected from L

Olathe (fig. 17) (tables 18–19 in “Supplemen

mation” section of this report). However, the 

were much greater than 0.05, suggesting no s

cance to the relation between depth and numb

tom species in the bottom sediment.

Estimates of the number of diatom valves 

gram of sediment, a measurement of diatom d

sediment, ranged from 1.8 million to about 65 

valves per gram of material in bottom-sedime
Diatoms as Indicators of Lake Eutrophication 

Lake Olathe

coring site 5

Cedar Lake

coring site 3

0 10 20 30 40 50

5.5

4.4

3.3

2.2

1.1

0

3.5

2.8

2.1

1.4

0.7

0

Depth of sample, in feet

r = 0.34

p-value = 0.33

Water/sediment

interface

Bottom of core

0 10 20 30 40 60 50

Number of species

r = 0.40

p-value = 0.25

samples from Cedar Lake and from about 5.3 million

to 26 million valves per gram of material in samples

from Lake Olathe (fig. 18). Bottom-sediment samples

from both lakes showed a general increase in diatom

densities closer to the water/sediment interface compared to the bottom of the sediment core, especially at

Lake Olathe, which had a correlation coefficient, r, of

0.72 and a p-value equal to 0.02. This trend may

reflect an increase in the productivity of the diatom

community over the time period represented by the

sediment cores. However, some or all of the changes

may be a result of other factors, such as variable sedimentation rates or preservation of the valves in the

sediment (Pyle and others, 1998). At slower sedimentation rates, for example, there may be more valves per

gram of material for the same rate of diatom productivity because there is less sediment to “dilute” the

density of the valves.

Generally, in eutrophic water, the diatom community will be dominated by a few abundant species tolerant to nutrient and organic enrichment. In contrast,

diatom communities in uncontaminated water (free of

sewage or other organic enrichment due to waste discharge) consist of a great

number of more equally

abundant species (U.S. E

ronmental Protection Age

1977). The abundance o

tom valves per gram of m

rial, represented by the s

most-prevalent diatom sp

cies from each lake,

accounted for relative pe

centage abundances rang

from 37 to 89 percent

(median; 74 percent) of t

total diatoms in the botto

sediment sample from C

Lake and from 51 to 87 p

cent (median; 77 percent

the sample from Lake Ol

(tables 9–11). These dat

indicate that, on the basis 

a general definition of

eutrophic water using dia

densities, both Cedar Lak

and Lake Olathe probabl

have experienced eutroph

conditions throughout th

history. However, diatom

concentrations and the diversity of diatom species 

can be affected by other factors such as turbidity, 

perature, and solar intensity.

Selected diatom species in reservoir bottom s

ment were compared to nutrient concentrations to

determine whether a relation existed between the 

variables. Six diatom species were selected that h

the largest relative percentage abundance and that

were found in most sediment-core subsections. D

tom abundances were compared to the total phosp

rus concentrations, total ammonia plus organic

nitrogen as nitrogen (N) concentrations, and samp

depths from the sediment profile (table 10). Desc

tions of each of the six diatom species and the env

mental conditions that promote their growth are

presented in table 11.

An analysis for trends using Kendall’s tau did 

indicate any trend in bottom-sediment samples fro

Cedar Lake between total valves per gram of mat

for the six diatom species and concentrations of t

phosphorus or total ammonia plus organic nitroge

nitrogen (N) (table 10). The lack of any trend in 

ples from Cedar Lake may indicate that the diatom

Figure 17. Relation between total number of identified diatom species in bottom-sediment samples

and depths of samples from coring site 3 in Cedar Lake, 1938–2000, and coring site 5 in Lake Olathe,

1956–2000. Location of coring sites shown in figure 1.
36 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

0 20

5.5

4.4

3.3

2.2

1.1

0

3.5

2.8

2.1

1.4

0.7

0

Depth of sample, in feet

r = 0.52

p-value = 0.12

Water/sediment

interface

Bottom of core

40 80 60 0

Millions of valves per gram of material

r = 0.72

p-value = 0.02

Lake Olathe

coring site 5

Cedar Lake

coring site 3

10 20

species are independent of

nutrient concentrations or that

the lake has historically been

eutrophic. The dam repair

work at Cedar Lake in 1995

also may have disturbed the

deposition of bottom sediment and diatoms, and

masked the occurrence of any

possible trends. The presence

of Cyclotella bodanica suggests water-quality conditions

free of organic enrichment,

whereas the presence of Aulacoseira cf alpigena and

Cyclotella meneghiniana suggests just the opposite—a

water body enriched with

organic material. The apparent discrepancy may be

related to seasonal waterquality variations in the lake.

Water may be low in organic

material part of the year, indicating perhaps less eutrophic

conditions that encourage the

growth of Cyclotella bodanica, and higher in organic material during other times

of the year, encouraging the growth of Aulacoseira cf

alpigena and Cyclotella meneghiniana. The genus

Aulacoseira is a heavily silicified diatom that requires

turbulence to maintain its presence in the water column. Increased turbulence along with increased nutrient concentrations during low lake stage can favor this

genus over other planktonic species (Stoermer and

Smol, 1999, p.188). Both Cyclotella bodanica and

Cyclotella meneghiniana showed a negative correlation to total phosphorus concentration in Lake Olathe,

indicating that the densities of both species decreased

in the presence of total phosphorus concentrations

(table 10). However, Cyclotella meneghiniana typically increases in the presence of phosphorus and

organic-enriched material. This factor, in addition to

the lack of a trend in total phosphorus concentration in

the bottom-sediment profile, indicate that the Kendall’s tau trend test may be inaccurate in this situation,

possibly because of very little variability in abundance

of Cyclotella meneghiniana in the bottom sediment of

Lake Olathe.

An analysis of trends of the diatom speci

anodiscus nigarae in bottom-sediment sampl

Lake Olathe indicated a relation between tota

per gram of material of the species and total a

plus organic nitrogen as nitrogen (N) (table 1

Stephanodiscus nigarae is present in eutrophi

and is noted for imparting unacceptable taste 

(U.S. Environmental Protection Agency, 1977

Stephanodiscus nigarae was not present in ea

sediment-core subsection and had a low relati

centage abundance.

Diatom concentrations of Aulacoseira cf a

Cyclotella meneghiniana, and Cyclotella stria

lated well with depths of sediment samples fr

Cedar Lake (table 10). Concentrations of Aul

cf alpigena and Stephanodiscus nigarae in bo

sediment samples from Lake Olathe similarly 

lated well with depths of samples. Concentra

these four diatoms were largest at the water/s

interface (more recent deposition) and smalle

bottom of the cores (older sediment). The pre

the diatom species Aulacoseira cf alpigena in 

sediment from Cedar Lake suggests degradin

Figure 18. Relation between total number of valves of identified diatom species per gram 

material in bottom-sediment samples and depths of samples from coring site 3 in Cedar 

1938–2000, and coring site 5 in Lake Olathe, 1956–2000. Location of coring sites shown in 
Diatoms as Indicators of Lake Eutrophication 

Table 9. Relative percentage abundance of six most-prevalent diatom species in bottom-sediment samples from Cedar Lake, 1938–2

and Lake Olathe, 1956–2000, northeast Kansas

Cedar Lake coring site 3 (fig. 1) Lake Olathe coring site 5 (fig. 1)

Depth

(feet)

Relative percentage

abundance

Depth

(feet)

Relative perce

abundanc

Water/sediment interface 0.55 89 0.35 73

1.10 87 .70 51

1.65 77 1.05 62

2.20 66 1.40 86

2.75 76 1.75 82

3.30 70 2.10 78

3.85 81 2.45 76

4.40 73 2.80 79

4.95 72 3.15 87

Bottom of core 5.50 37 3.50 73

Median 75 77

Table 10. Relation between relative abundance of selected species of diatoms and concentrations of total phosphorus, total ammoni

organic nitrogen as nitrogen (N), and depths of samples from selected bottom-sediment cores from Cedar Lake and Lake Olathe, nort

Kansas, 2000

[--, incomplete data set]

Diatom species Reservoir

Total phosphorus

concentration

Total ammonia plus organic

nitrogen as N Depths of samples

Kendall’s tau

Trend test at

0.05 level of

significance Kendall’s tau

Trend test at

0.05 level of

significance Kendall’s tau

Trend te

0.05 lev

significa

Aulacoseira cf alpigena Cedar Lake -0.178 no -0.267 no -0.622 yes

Lake Olathe -.333 no -.311 no -.600 yes

Aulacoseira granulata Cedar Lake .044 no -.200 no -.244 no

Lake Olathe -.067 no .133 no -.067 no

Cyclotella bodanica Cedar Lake -- -- -- -- -- --

Lake Olathe -.511 yes -.178 no -.289 no

Cyclotella meneghiniana Cedar Lake -.044 no -.289 no -.422 yes

Lake Olathe -.444 yes -.111 no -.356 no

Cyclotella striata Cedar Lake -.244 no -.156 no -.556 yes

Lake Olathe -- -- -- -- -- --

Stephanodiscus nigarae Cedar Lake -- -- -- -- -- --

Lake Olathe -.200 no .600 yes -.644 yes
38 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

quality conditions in the lake. However, because sediment in the lake may have been disturbed during dam

repair work, trend analysis may be invalid for this

lake, and water quality in Cedar Lake may or may not

be degrading. The increased concentration of the

eutrophic-indicator diatom species from the bottom of

the cores to the water/sediment interface suggests that

over time these lakes are eutrophic more often or

eutrophic for longer periods.

SUMMARY AND CONCLUSIONS

This report describes sediment deposition, waterquality trends, transport (loads and yields) of nutrients

(phosphorus and nitrogen species), selected trace elements, selected pesticides, and diatoms as indicators

of water-quality conditions within the Lake Olathe

watershed in northeast Kansas. Bathymetric survey

data from both Cedar Lake and Lake Olathe were collected during 2000 by the U.S. Geological Survey and

compared to the available historic topographic data for

each lake provided by the city of Olathe. The information was used to estimate total sediment deposition in

each lake since dam closure.

Three bottom-sediment cores were collected from

Cedar Lake, and five bottom-sediment cores were collected from Lake Olathe in 2000 and analyzed for

selected inorganic and organic constituents and diatoms. The results showed that phosphorus, total

ammonia plus organic nitrogen as nitrogen, selected

trace elements, and a few organic pesticides were

present in the bottom sediment of each lake. 

centage of finer grained sediment (silt and cla

fairly uniform throughout each lake and repre

more than 97 percent of the sediment particle

tribution. Silt and clay provide more efficien

tion sites for many water-quality constituents

phosphorus and many trace elements.

The total estimated sediment deposition s

dam closure, calculated on the basis of bathym

data and bottom-sediment cores, was 338 acr

Cedar Lake and 317 acre-ft for Lake Olathe. 

annual sediment deposition was 5.45 acre-ft/y

[0.89 acre-ft/yr)/mi2] for Cedar Lake and 7.0 a

[0.42 (acre-ft/yr)/mi2

] for Lake Olathe. Mean 

sediment loads for the two lakes were 9.6 mill

for Cedar Lake and 12.6 million lb/yr for Lak

Although the percentage of finer grained 

in both lakes was fairly uniform, the concentr

total phosphorus in bottom sediment increase

upstream to downstream in the lakes. In sedi

samples from Cedar Lake, mean concentratio

total phosphorus ranged from 1,370 mg/kg up

to 1,810 mg/kg near the dam. Mean concentr

total phosphorus in samples from Lake Olath

from 588 mg/kg upstream to 1,030 mg/kg nea

dam. The implications of large total phospho

centrations in bottom-sediment samples from 

Lake are that adverse water-quality condition

Cedar Lake could easily affect the quality of 

Lake Olathe drinking-water supply through d

Table 11. Selected diatom species and their presence under various water-quality conditions

[Source of information: U.S. Environmental Protection Agency, 1977]

Diatom species Type of diatom Water-quality conditions

Aulacoseira cf alpigena Freshwater planktonic Present in mesotrophic and eutrophic water.

Aulacoseira granulata Freshwater planktonic Reliable indicator of eutrophic conditions; can clog water-treatment filters a

screens.

Cyclotella bodanica Freshwater planktonic Uncontaminated water indicator; water free of sewage or other organic enri

due to waste discharge.

Cyclotella meneghiniana Freshwater planktonic Indicator of contamination; can clog water-treatment filters and screens. Pr

water containing treated or untreated domestic sewage and related organi

Cyclotella striata Freshwater planktonic None specified.

Stephanodiscus nigarae Freshwater planktonic Indicator of taste problems; can impart vegetable to oily taste to water; abu

shallow eutrophic lakes of southwestern Minnesota.
Summary and Conclusions 

of water from Cedar Lake to Lake Olathe via

Cedar Creek.

On the basis of calculations of deposited sediment

in each lake, the mean annual phosphorus load transported to Cedar Lake was estimated to be 14,700 lb/yr

and was estimated to be 9,720 lb/yr to Lake Olathe.

The mean annual phosphorus yield to Cedar Lake calculated from sediment deposition was 3.74 (lb/acre)/yr

and was 0.91 (lb/acre)/yr to Lake Olathe. The difference may be attributed to different historical agricultural and residential practices in the respective

subwatersheds.

Land use can have a considerable effect on sediment loading to a lake. Intense agricultural use in a

watershed can be a source of sediment loading, and

chemical constituents such as phosphorus can be

transported with the sediment to downstream lakes.

Comparisons of phosphorus yields from the Lake

Olathe watershed [0.91 (lb/acre)/yr] to the Webster

Reservoir, Cheney Reservoir, Tuttle Creek Lake,

and Hillsdale Lake watersheds showed that the

Webster Reservoir watershed had the smallest yield

[0.04 (lb/acre)/yr] and that the Cedar Lake watershed

had the largest [3.74 (lb/acre)/yr].

Mean concentrations of total ammonia plus

organic nitrogen as nitrogen (N) ranged from 2,000 to

2,700 mg/kg in bottom-sediment samples from Cedar

Lake and from 1,300 to 2,700 mg/kg in samples from

Lake Olathe. The relation between total ammonia plus

organic nitrogen as nitrogen (N) and bottom-sediment

particle size was inconclusive for sediment samples

from both Cedar Lake and Lake Olathe. Concentrations of total ammonia plus organic nitrogen as nitrogen (N) in samples from both lakes increased from

upstream to downstream, although there was no trend

in sediment particle-size distribution. Even though

fertilizer application in Kansas has increased substantially during the past 40 years, a regression analysis

between total ammonia plus organic nitrogen as nitrogen (N) and bottom-sediment particle size showed no

discernible trend for the sediment profile from Cedar

Lake, but a slight increasing trend was seen for the

sediment profile from Lake Olathe.

Mean concentrations of six trace elements in bottom-sediment samples from Cedar Lake and Lake

Olathe exceeded the U.S. Environmental Protection

Agency (USEPA) Threshold Effects Levels (TELs)

sediment-quality guidelines for aquatic organisms.

Those trace elements exceeding TEL guidelines were

arsenic, chromium, copper, lead, nickel, and zinc

Probable Effects Levels (PELs) for trace element

were not exceeded in samples from either lake.

Implications of large trace element concentra

are uncertain because the USEPA guidelines are

nonenforceable; however, it is assumed that toxic

effects frequently occur when trace elements exce

the PEL guidelines. A program to monitor trace e

ment concentrations in lake sediment every few y

would facilitate a better understanding of tempora

trends in trace element concentrations.

Reservoir bottom-sediment samples collected 

2000 were analyzed for selected pesticides, includ

organochlorine and organophosphate insecticides

acetanilide and triazine herbicides. There were n

detections of the organochlorine and organophosp

insecticides, but the acetanilide herbicides alachlo

and metolachlor were detected in sediment from b

lakes with larger concentrations corresponding to 

more recent deposition. The USEPA has not prop

TEL or PEL guideline concentrations in bottom s

ment for any of the organochlorine, organophosph

acetanilide, or triazine compounds.

Diatom species in reservoir bottom-sediment 

ples were identified and used as indicators of lake

eutrophication. The diatom Cyclotella bodanica, 

indicator of low organic-enriched water, and Aula

coseira cf alpigena and Cyclotella meneghiniana, 

cators of organic-enriched water, were identified i

sediment from Lake Olathe. The presence of thes

diatoms suggests varying periods of low and high

eutrophication in Lake Olathe from 1956 to 2000. 

concentration of two species in bottom sediment 

Cedar Lake, Aulacoseira cf alpigena and Cyclote

meneghiniana, as well as two species in sediment 

Lake Olathe, Aulacoseira cf alpigena and Stephan

discus nigarae, increased in sediment cores from 

older bottom material to the more recent depositio

near the top of the sediment core. These diatoms 

cate eutrophic conditions, and the increased conce

tion of these eutrophic diatom species from the bo

of the cores to the sediment/water interface sugge

that historically these lakes have been and continu

be eutrophic at times.

Trends in water-quality characteristics can be 

by the Lake Olathe watershed managers to docum

historical changes in the watershed such as chang

land use, the suspension of the use of chlorinated

insecticides, such as DDT and chlordane, and the 
40 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

of hydrophobic fertilizers. The investigation described

in this report provides a baseline of water-quality

information to compare future changes in water quality or other watershed activities. With the addition of

bathymetric surveys and the inclusion of additional

reservoirs, reservoir sediment investigations can be

used to estimate historical transport of phosphorus and

other constituents in future water-quality assessments

throughout Kansas.

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Supplemental Information 

Supplemental Information
44 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000
Supplemental Information 

Table 12. Laboratory analysis methods for reservoir bottom-sediment constituents

[USGS, U.S. Geological Survey; GC/MS, gas chromatography/mass spectrometry]

Constituent or constituent group Analysis method Method reference

Nutrients Various methods Fishman (1993)

Trace elements

(USGS schedule 2420)

Inductively coupled plasma-mass

spectrometry

Fishman (1993)

Cesium-137

(USGS laboratory

code 2307)

Gamma counting American Society for Testing and

Materials (2000)

Pesticides GC/MS liquid extraction with

methanol and water

Mills and Thurman (1992)

Table 13. Nutrients analyzed in bottom sediment from

Cedar Lake and Lake Olathe, northeast Kansas, 2000

[mg/kg, milligrams per kilogram]

Nutrient

Method reporting

limit

Units of

measurement

Total ammonia plus organic

nitrogen as nitrogen

20 mg/kg

Phosphorus 40 mg/kg
46 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

Metal or trace element LRL

Unit of

measurement

Aluminum 0.005 pct

Antimony .1 μg/g

Arsenic .1 μg/g

Barium 1 μg/g

Beryllium .1 μg/g

Bismuth 1 μg/g

Cadmium .1 μg/g

Calcium .005 pct

Cerium 1 μg/g

Chromium 1 μg/g

Cobalt 1 μg/g

Copper 1 μg/g

Europium 1 μg/g

Gallium 1 μg/g

Gold 1 μg/g

Holmium 1 μg/g

Iron .005 pct

Lanthanum 1 μg/g

Lead 4 μg/g

Lithium 1 μg/g

Magnesium .005 pct

Manganese 4 μg/g

Mercury 0.02 μg/g

Molybdenum 2 μg/g

Neodymium 1 μg/g

Nickel 2 μg/g

Niobium 4 μg/g

Potassium .005 pct

Scandium 2 μg/g

Selenium .1 μg/g

Silver .1 μg/g

Sodium .005 pct

Strontium 2 μg/g

Sulfur .05 pct

Tantalum 1 μg/g

Thallium 1 μg/g

Thorium 1 μg/g

Tin 1 μg/g

Titanium .005 pct

Uranium .1 μg/g

Vanadium 2 μg/g

Ytterbium 1 μg/g

Yttrium 1 μg/g

Zinc 4 μg/g

Metal or trace element LRL

Unit of

measurement

Table 14. Selected metals and trace elements analyzed in bottom sediment from Cedar Lake and Lake Olathe, northeast

Kansas, 2000

[LRL, laboratory reporting level; pct, percent; μg/g, micrograms per gram]

Table 15. Radiochemical analyzed for age dating

bottom sediment from Cedar Lake and Lake Olathe,

northeast Kansas, 2000

[pCi/g, picocuries per gram]

Radiochemical

Method reporting

limit

Units of

measurement

Cesium-137 0.05 pCi/g
Supplemental Information 

Table 16. Statistical summary of concentrations and comparison to sediment-quality guidelines for selected metals and

trace elements in bottom-sediment sample from Cedar Lake coring site 3, northeast Kansas, 2000—Continued

Metal or trace element and

unit of measurement

Concentration Sediment-quality guidelines1

Minimum Median Maximum TEL PEL

Aluminum, percent 8 8.1 8.4 -- --

Antimony, μg/g 1 1.1 1.1 -- --

Arsenic, μg/g 13 14 16 7.2 42

Barium, μg/g 730 760 800 -- --

Beryllium, μg/g 2.1 2.3 2.7 -- --

Bismuth, μg/g <1.0 .5 <1.0 -- --

Cadmium, μg/g .23 .31 .36 .68 4.2

Calcium, percent 1 1.1 1.9 -- --

Cerium, μg/g 83 84 87 -- --

Chromium, μg/g 90 90 98 52 160

Cobalt, μg/g 9.5 11 11 -- --

Copper, μg/g 32 32 45 19 110

Europium, μg/g 1.4 1.5 1.6 -- --

Gallium, μg/g 19 20 20 -- --

Gold, μg/g <1.0 .5 <1.0 -- --

Holmium, μg/g 1.2 1.2 1.3 -- --

Iron, percent 4.1 4.2 4.4 -- --

Lanthanum, μg/g 48 50 51 -- --

Lead, μg/g 32 33 35 30 110

Lithium, μg/g 44 45 49 -- --

Magnesium, percent .75 .77 .83 -- --

Manganese, μg/g 760 800 980 -- --

Mercury, μg/g .05 .05 .14 .13 .70

Molybdenum, μg/g .92 1 1.2 -- --

Neodymium, μg/g 40 42 43 -- --

Nickel, μg/g 32 34 39 16 43

Niobium, μg/g 20 21 21 -- --

Potassium, percent 1.6 1.6 1.7 -- --

Scandium, μg/g 14 14 14 -- --

Selenium, μg/g .86 .99 1.1 -- --

Silver, μg/g .2 .21 .24 -- --

Sodium, percent .3 .35 .35 -- --

Strontium, μg/g 130 140 160 -- --

Sulfur, percent .07 .09 .14 -- --

Tantalum, μg/g 1.5 1.5 1.5 -- --

Thorium, μg/g 15 15 16 -- --

Thallium, μg/g <1.0 1 1 -- --

Table 16. Statistical summary of concentrations and comparison to sediment-quality guidelines for selected metals and

trace elements in bottom-sediment sample from Cedar Lake coring site 3, northeast Kansas, 2000

[μg/g, micrograms per gram; TEL, Threshold Effects Level; PEL, Probable Effects Level; <, less than; --, no value assigned]
48 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

Tin, μg/g 3.2 3.2 3.4 -- --

Titanium, percent .38 .39 .39 -- --

Uranium, μg/g 4 4.4 4.8 -- --

Vanadium, μg/g 130 130 140 -- --

Ytterbium, μg/g 2.8 2.9 3 -- --

Yttrium, μg/g 30 31 32 -- --

Zinc, μg/g 150 150 170 120 270

1Guidelines from U.S. Environmental Protection Agency (1998).

Table 16. Statistical summary of concentrations and comparison to sediment-quality guidelines for selected metals an

trace elements in bottom-sediment sample from Cedar Lake coring site 3, northeast Kansas, 2000—Continued

Metal or trace element and

unit of measurement

Concentration Sediment-quality guidelines1

Minimum Median Maximum TEL PEL
Supplemental Information 

Table 17. Statistical summary of concentrations and comparison to sediment-quality guidelines for selected metals and

trace elements in bottom-sediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Metal or trace element and

unit of measurement

Concentration Sediment-quality guidelines1

Minimum Median Maximum TEL PEL

Aluminum, percent 8.5 8.7 9.0 -- --

Antimony, μg/g 1.1 1.2 1.4 -- --

Arsenic, μg/g 15 16 18 7.2 42

Barium, μg/g 710 760 780 -- --

Beryllium, μg/g 2 2.3 2.6 -- --

Bismuth, μg/g <1.0 <1.0 <1.0 -- --

Cadmium, μg/g .27 .33 .41 .68 4.2

Calcium, percent 1.1 1.3 2.6 -- --

Cerium, μg/g 88 91 93 -- --

Chromium, 88 89 94 52 160

Cobalt, μg/g 10 11 12 -- --

Copper, μg/g 32 36 38 19 110

Europium, μg/g 1.4 1.4 1.5 -- --

Gallium, μg/g 20 21 21 -- --

Gold, μg/g <1.0 <1.0 <1.0 -- --

Holmium, μg/g 1.1 1.1 1.2 -- --

Iron, percent 4 4.1 4.2 -- --

Lanthanum, μg/g 54 56 58 -- --

Lead, μg/g 28 36 40 30 110

Lithium, μg/g 44 45 48 -- --

Magnesium, percent .79 .84 .86 -- --

Manganese, μg/g 890 1,000 1,200 -- --

Mercury, μg/g .05 .05 .07 .13 .70

Molybdenum, μg/g .93 1.0 1.1 -- --

Neodymium, μg/g 40 43 44 -- --

Nickel, μg/g 35 37 39 16 43

Niobium, μg/g 20 21 21 -- --

Potassium, percent 1.8 1.8 1.9 -- --

Scandium, μg/g 15 15 15 -- --

Selenium, μg/g .95 .99 1.2 -- --

Silver, μg/g .43 .44 .48 -- --

Sodium, percent .33 .36 .39 -- --

Strontium, μg/g 130 140 170 -- --

Sulfur, percent .07 .11 .16 -- --

Tantalum, μg/g 1.7 1.8 1.9 -- --

Thorium, μg/g 14 15 16 -- --

Thallium, μg/g <1.0 .5 1.0 -- --

Table 17. Statistical summary of concentrations and comparison to sediment-quality guidelines for selected metals and

trace elements in bottom-sediment sample from Lake Olathe coring site 5, northeast Kansas, 2000

[μg/g, micrograms per gram; TEL, Threshold Effects Level; PEL, Probable Effects Level; <, less than; --, no value assigned]
50 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

Tin, μg/g 3.2 3.2 3.4 -- --

Titanium, percent .5 .52 .53 -- --

Uranium, μg/g 3.7 4 4.3 -- --

Vanadium, μg/g 130 130 140 -- --

Ytterbium, μg/g 2.7 2.8 3 -- --

Yttrium, μg/g 28 30 30 -- --

Zinc, μg/g 140 140 150 120 270

1

Guidelines from U.S. Environmental Protection Agency (1998).

Table 17. Statistical summary of concentrations and comparison to sediment-quality guidelines for selected metals an

trace elements in bottom-sediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Metal or trace element and

unit of measurement

Concentration Sediment-quality guidelines1

Minimum Median Maximum TEL PEL
Supplemental Information 

Table 18. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottom-sediment

sample from Cedar Lake coring site 3, northeast Kansas, 2000

Depth of sample

(feet) Taxa

Number of

valves

counted

Relative percentage

abundance

Valves per gram of

material1

0.55 Achnanthidium minutissimum 2 0.6 176,000

Amphora inariensis 2 .6 176,000

Aulacoseira cf alpigena 159 48.0 14,000,000

Aulacoseira granulata 101 30.5 8,910,000

Brachysira vitrea 1 .3 88,200

Cocconeis placentula 2 .6 176,000

Cyclotella sp. 1 (small) 1 .3 88,200

Cyclotella meneghiniana 17 5.1 1,500,000

Cyclotella ocellata 1 .3 88,200

Cyclotella striata 17 5.1 1,500,000

Gomphonema gracile 1 .3 88,200

Gomphonema grovei 1 .3 88,200

Gomphonema parvulum 1 .3 88,200

Mastogloia smithii 1 .3 88,200

Navicula cryptotenella 1 .3 88,200

Navicula cryptocephala 1 .3 88,200

Navicula geoppertiana 1 .3 88,200

Navicula gregaria 2 .6 176,000

Navicula tripunctata 1 .3 88,200

Navicula trivialis 1 .3 88,200

Neidium affine 2 .6 176,000

Nitzschia acicularis 1 .3 88,200

Nitzschia inconspicua 2 .6 176,000

Nitzschia subacicularis 1 .3 88,200

Pinnularia interrupta 2 .6 176,000

Stephanodiscus nigarae 4 1.2 353,000

Surirella angusta 2 .6 176,000

Surirella brebissonii 1 .3 88,200

Synedra delicatissima 1 .3 88,200

Synedra ulna 1 .3 88,200

Total 331 1001 29,200,000
52 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

1.10 Achnanthes bioreti 1 0.2 101,000

Achnanthes deflexa 2 .3 203,000

Achnanthes exigua 8 1.3 812,000

Achnanthidium minutissimum 4 .6 406,000

Aulacoseira cf alpigena 383 59.9 38,900,000

Aulacoseira granulata 128 20.0 13,000,000

Bacillaria paradoxa 1 .2 101,000

Cocconeis placentula 2 .3 203,000

Cyclotella sp. 1 (small) 1 .2 101,000

Cyclotella cf stelligera 4 .6 406,000

Cyclotella meneghiniana 27 4.2 2,740,000

Cyclotella ocellata 2 .3 203,000

Cyclotella striata 21 3.3 2,130,000

Denticula kuetzingii 2 .3 203,000

Gomphonema angustum 1 .2 101,000

Gomphonema minutum 4 .6 406,000

Gomphonema parvulum 1 .2 101,000

Gomphonema sp. 2 .3 203,000

Gomphonema sp. (heterovalvie) 3 .5 305,000

Melosira sp. 3 .5 305,000

Melosira varians 3 .5 305,000

Navicula absoluta 1 .2 101,000

Navicula cincta 1 .2 101,000

Navicula cryptocephala 3 .5 305,000

Navicula geoppertiana 1 .2 101,000

Navicula halophila 1 .2 101,000

Navicula miniscula 2 .3 203,000

Navicula ordinaria 1 .2 101,000

Navicula striata 1 .2 101,000

Nitzschia acicularis 4 .6 406,000

Nitzschia dissipatta 2 .3 203,000

Nitzschia inconspicua 2 .3 203,000

Nitzschia linearis 2 .3 203,000

Nitzschia palea 7 1.1 711,000

Nitzschia recta 2 .3 203,000

Nitzschia subacicularis 1 .2 101,000

Stephanodiscus nigarae 4 .6 406,000

Synedra delicatissima 1 .2 101,000

Total 639 1001 64,900,000

Table 18. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottom-sed

sample from Cedar Lake coring site 3, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves

counted

Relative percentage

abundance

Valves per gram of

material1
Supplemental Information 

1.65 Achnanthes deflexa 2 0.3 89,800

Achnanthes exigua 4 .7 180,000

Achnanthes spp. 8 1.3 359,000

Achnanthidium minutissimum 4 .7 180,000

Amphora montana 2 .3 89,800

Aulacoseira cf alpigena 272 45.5 12,200,000

Aulacoseira granulata 106 17.7 4,760,000

Cocconeis placentula 2 .3 89,800

Cyclotella sp. 1 (small) 8 1.3 359,000

Cyclotella cf stelligera 2 .3 89,800

Cyclotella meneghiniana 50 8.4 2,240,000

Cyclotella ocellata 6 1.0 269,000

Cyclotella striata 32 5.4 1,440,000

Denticula kuetzingii 6 1.0 269,000

Encyonema minutum 4 .7 180,000

Fragilaria capucina 6 1.0 269,000

Gomphoneis sp. 4 .7 180,000

Gomphonema minutum 2 .3 89,800

Gomphonema sp. 2 .3 89,800

Melosira varians 26 4.4 1,170,000

Navicula capitata 2 .3 89,800

Navicula cryptocephala 2 .3 89,800

Navicula geoppertiana 2 .3 89,800

Navicula gregaria 2 .3 89,800

Navicula halophila 4 .7 180,000

Navicula lanceolata 2 .3 89,800

Navicula miniscula 2 .3 89,800

Navicula cf salinarium 3 .5 135,000

Navicula trivialis 2 .3 89,800

Nitzschia amphibia 5 .8 224,000

Nitzschia clausii 3 .5 135,000

Nitzschia dissipatta 3 .5 135,000

Nitzschia inconspicua 2 .3 89,800

Nitzschia littoralis 2 .3 89,800

Nitzschia palea 2 .3 89,800

Nitzschia perminuta 6 1.0 269,000

Planothidium lanceolatum 2 .3 89,800

Surirella angusta 1 .2 44,900

Surirella brebissonii 1 .2 44,900

Surirella ovalis 1 .2 44,900

Synedra delicatissima 1 .2 44,900

Total 598 1001 26,800,000

Table 18. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottom-sediment

sample from Cedar Lake coring site 3, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves

counted

Relative percentage

abundance

Valves per gram of

material1
54 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

2.20 Achnanthidium minutissimum 8 6.0 107,000

Aulacoseira cf alpigena 8 6.0 107,000

Aulacoseira ambigua 4 3.0 53,300

Aulacoseira granulata 52 39.1 694,000

Aulacoseira lirata 8 6.0 107,000

Bacillaria paradoxa 1 .8 13,300

Cyclotella meneghiniana 8 6.0 107,000

Cyclotella ocellata 8 6.0 107,000

Cyclotella striata 20 15.0 267,000

Melosira varians 8 6.0 107,000

Navicula cincta 4 3.0 53,300

Planothidium lanceolatum 4 3.0 53,300

Total 133 1001 1,780,000

Table 18. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottom-sed

sample from Cedar Lake coring site 3, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves

counted

Relative percentage

abundance

Valves per gram of

material1
Supplemental Information 

2.75 Achnanthes bioreti 1 0.2 36,000

Achnanthes deflexa 3 .5 108,000

Achnanthes spp. 1 .2 36,000

Achnanthidium minutissimum 6 1.0 216,000

Amphora montana 6 1.0 216,000

Amphora ovalis 6 1.0 216,000

Aulacoseira cf alpigena 31 5.4 1,120,000

Aulacoseira distans 6 1.0 216,000

Aulacoseira granulata 350 60.8 12,600,000

Cyclotella sp. 1 (small) 30 5.2 1,080,000

Cyclotella meneghiniana 8 8.3 1,730,000

Cyclotella striata 12 2.1 432,000

Denticula kuetzingii 8 1.4 288,000

Denticula tenuis 6 1.0 216,000

Encyonema lange-bertalotii 3 .5 108,000

Encyonema silesiacum 3 .5 108,000

Fragilaria capucina 3 .5 108,000

Navicula geoppertiana 9 1.6 324,000

Planothidium lanceolatum 3 .5 108,000

Stephanodiscus sp. 1 25 4.3 899,000

Stephanodiscus nigarae 3 .5 108,000

Synedra delicatissima 4 .7 144,000

Synedra ulna 9 1.6 324,000

Total 576 1001 20,700,000

Table 18. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottom-sediment

sample from Cedar Lake coring site 3, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves

counted

Relative percentage

abundance

Valves per gram of

material1
56 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

3.30 Achnanthes bioreti 1 0.2 34,900

Achnanthes deflexa 1 .2 34,900

Achnanthidium minutissimum 12 2.4 419,000

Amphora ovalis 9 1.8 314,000

Aulacoseira distans 21 4.2 733,000

Aulacoseira granulata 219 43.5 7,640,000

Bacillaria paradoxa 3 .6 105,000

Coscinodiscus sp. 3 .6 105,000

Craticula cuspidata 3 .6 105,000

Cyclotella sp. 1 (small) 21 4.2 733,000

Cyclotella cf stelligera 9 1.8 314,000

Cyclotella meneghiniana 42 8.3 1,470,000

Cyclotella ocellata 3 .6 105,000

Cyclotella striata 93 18.5 3,250,000

Cymbella delicatula 3 .6 105,000

Denticula kuetzingii 3 .6 105,000

Diploneis oblongella 3 .6 105,000

Diploneis pupula 3 .6 105,000

Fragilaria sp. 6 1.2 209,000

Gomphonema sp. (heterovalvie) 7 1.4 244,000

Gyrosigma obtusatum 3 .6 105,000

Hantzschia amphioxys 3 .6 105,000

Melosira varians 4 .8 140,000

Nitzschia dissipatta 2 .4 69,800

Nitzschia linearis 2 .4 69,800

Planothidium lanceolatum 1 .2 34,900

Stephanodiscus sp. 1 9 1.8 314,000

Stephanodiscus nigarae 6 1.2 209,000

Surirella brebissonii 3 .6 105,000

Synedra delicatissima 2 .4 69,800

Synedra ulna 3 .6 105,000

Total 503 1001 17,600,000

Table 18. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottom-sed

sample from Cedar Lake coring site 3, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves

counted

Relative percentage

abundance

Valves per gram of

material1
Supplemental Information 

3.85 Achnanthes bioreti 1 0.2 26,900

Achnanthidium minutissimum 4 1.0 108,000

Amphipleura pellucida 1 .2 26,900

Aulacoseira cf alpigena 60 14.6 1,620,000

Aulacoseira ambigua 12 2.9 323,000

Aulacoseira distans 8 1.9 215,000

Aulacoseira granulata 228 55.3 6,140,000

Bacillaria paradoxa 4 1.0 108,000

Cocconeis placentula 4 1.0 108,000

Cyclotella cf areolata 4 1.0 108,000

Cyclotella meneghiniana 32 7.8 862,000

Cyclotella ocellata 4 1.0 108,000

Cyclotella striata 16 3.9 431,000

Navicula geoppertiana 4 1.0 108,000

Stephanodiscus sp. 1 1 .2 26,900

Stephanodiscus nigarae 20 4.9 539,000

Surirella sp. 1 .2 26,900

Synedra delicatissima 8 1.9 215,000

Total 412 1001 11,100,000

Table 18. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottom-sediment

sample from Cedar Lake coring site 3, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves

counted

Relative percentage

abundance

Valves per gram of

material1
58 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

4.40 Achnanthes spp. 8 2.3 108,000

Achnanthidium minutissimum 8 2.3 108,000

Aulacoseira cf alpigena 32 9.2 431,000

Aulacoseira distans 28 8.0 377,000

Aulacoseira granulata 218 62.6 2,940,000

Bacillaria paradoxa 4 1.1 53,900

Cocconeis pediculus 2 .6 26,900

Cocconeis placentula 4 1.1 53,900

Cyclostephanos cf dubius 2 .6 26,900

Cyclotella meneghiniana 4 1.1 53,900

Cyclotella striata 2 .6 26,900

Cymbella delicatula 2 .6 26,900

Encyonema gracile 2 .6 26,900

Fragilaria capucina 2 .6 26,900

Gomphonema parvulum 2 .6 26,900

Gyrosigma spencerii 6 1.7 80,800

Hantzschia amphioxys 2 .6 26,900

Navicula geoppertiana 2 .6 26,900

Navicula placentula 2 .6 26,900

Navicula rhynchocephala 2 .6 26,900

Nitzschia littoralis 2 .6 26,900

Pinnularia borealis 2 .6 26,900

Rhoicosphenia curvata 2 .6 26,900

Sellaphora pupula 2 .6 26,900

Stephanodiscus nigarae 2 .6 26,900

Synedra delicatissima 2 .6 26,900

Synedra ulna 2 .6 26,900

Total 348 1001 4,690,000

Table 18. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottom-sed

sample from Cedar Lake coring site 3, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves

counted

Relative percentage

abundance

Valves per gram of

material1
Supplemental Information 

4.95 Achnanthes bioreti 3 0.6 64,600

Achnanthes deflexa 2 .4 43,100

Achnanthes sp. 5 1.0 108,000

Achnanthidium minutissimum 10 2.0 215,000

Amphipleura pellucida 3 .6 64,600

Amphora montana 3 .6 64,600

Aulacoseira distans 27 5.4 582,000

Aulacoseira granulata 358 71.2 7,710,000

Bacillaria paradoxa 13 2.6 280,000

Cyclotella bodanica 5 1.0 108,000

Cyclotella meneghiniana 8 1.6 172,000

Cyclotella striata 1 .2 21,500

Encyonema lange-bertalotii 3 .6 64,600

Encyonema minutum 3 .6 64,600

Fragilaria capucina 8 1.6 172,000

Fragilaria cf zeilleri 3 .6 64,600

Gomphoneis sp. 5 1.0 108,000

Hantzschia amphioxys 5 1.0 108,000

Melosira sp. 5 1.0 108,000

Navicula geoppertiana 10 2.0 215,000

Navicula mutica 5 1.0 108,000

Navicula rhynchocephala 2 .4 43,100

Nitzschia amphibia 2 .4 43,100

Nitzschia capitellata 0 0 0

Pinnularia borealis 2 .4 43,100

Planothidium lanceolatum 2 .4 43,100

Stephanodiscus nigarae 3 .6 64,600

Synedra delicatissima 2 .4 43,100

Synedra ulna 5 1.0 108,000

Total 503 1001 10,800,000

Table 18. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottom-sediment

sample from Cedar Lake coring site 3, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves

counted

Relative percentage

abundance

Valves per gram of

material1
60 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

5.50 Achnanthes bioreti 10 2.4 442,000

Achnanthidium minutissimum 40 9.5 1,770,000

Aulacoseira distans 155 36.6 6,850,000

Aulacoseira granulata 125 29.6 5,520,000

Aulacoseira lirata 30 7.1 1,330,000

Cocconeis pediculus 1 .2 44,200

Cocconeis placentula 1 .2 44,200

Cyclotella cf areolata 25 5.9 1,100,000

Cyclotella bodanica 1 .2 44,200

Cyclotella meneghiniana 30 7.1 1,330,000

Cyclotella ocellata 5 1.2 221,000

Diadesmis contenta 15 3.5 663,000

Fragilaria capucina 15 3.5 663,000

Frustulia rhomboides 5 1.2 221,000

Gyrosigma spencerii 5 1.2 221,000

Hantzschia amphioxys 3 .7 133,000

Navicula cryptotenella 5 1.2 221,000

Navicula geoppertiana 10 2.4 442,000

Nitzschia dissipatta 1 .2 44,200

Nitzschia linearis 10 2.4 442,000

Nitzschia palea 5 1.2 221,000

Sellaphora pupula 10 2.4 442,000

Stephanodiscus sp. 1 5 1.2 221,000

Stephanodiscus nigarae 30 7.1 1,330,000

Total 423 1001 23,900,000

1Numbers are rounded to three significant figures.

Table 18. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottom-sed

sample from Cedar Lake coring site 3, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves

counted

Relative percentage

abundance

Valves per gram of

material1
Supplemental Information 

Table 19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000

Depth of sample

(feet) Taxa

Number of

valves counted

Relative percentage

abundance

Valves per gram of

material1

0.35 Achnanthes bioreti 4 0.4 109,000

Achnanthidium minutissimum 16 1.7 436,000

Asterinella formosa 30 3.1 818,000

Aulacoseira cf alpigena 446 46.8 12,200,000

Aulacoseira granulata 32 3.4 873,000

Bacillaria paradoxa 4 .4 109,000

Caloneis limosa 8 .8 218,000

Cocconeis pediculus 2 .2 54,500

Cyclostephanos cf dubius 12 1.3 327,000

Cyclotella bodanica 58 6.1 1,580,000

Cyclotella cf fottii 6 .6 164,000

Cyclotella cf stelligera 12 1.3 327,000

Cyclotella meneghiniana 116 12.2 3,160,000

Cyclotella ocellata 6 .6 164,000

Cymatopleura solea 2 .2 54,500

Denticula kuetzingii 2 .2 54,500

Diadesmis contenta 4 .4 109,000

Diploneis pupula 2 .2 54,500

Encyonema silesiacum 2 .2 54,500

Fragilaria capucina 4 .4 109,000

Fragilaria nanana 12 1.3 327,000

Gomphonema olivaceum 4 .4 109,000

Gomphonema parvulum 2 .2 54,500

Hantzschia amphioxys 4 .4 109,000

Navicula cryptotenella 14 1.5 382,000

Navicula gregaria 4 .4 109,000

Navicula subrhynchocephala 2 .2 54,500

Navicula tripunctata 2 .2 54,500

Navicula trivialis 2 .2 54,500

Nitzschia acicularis 8 .8 218,000

Nitzschia amphibia 6 .6 164,000

Nitzschia dissipatta 16 1.7 436,000

Nitzschia dubia 2 .2 54,500

Nitzschia inconspicua 4 .4 109,000

Nitzschia linearis 6 .6 164,000

Nitzschia littoralis 2 .2 54,500

Nitzschia palea 2 .2 54,500

Nitzschia perminuta 2 .2 54,500
62 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

0.35 Nitzschia subacicularis 8 0.8 218,000

Reimeria sinuata 2 .2 54,500

Stephanodiscus cf neoastraea 4 .4 109,000

Stephanodiscus nigarae 48 5.0 1,310,000

Stephanodiscus sp. 1 4 .4 109,000

Stephanodiscus sp. 2 4 .4 109,000

Surirella brebissonii 4 .4 109,000

Surirella minuta 2 .2 54,500

Surirella ovalis 2 .2 54,500

Surirella sp. 4 .4 109,000

Synedra delicatissima 2 .2 54,500

Synedra ulna 6 .6 164,000

Total 952 1001 26,000,000

Table 19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves counted

Relative percentage

abundance

Valves per gram o

material1
Supplemental Information 

0.70 Achnanthes bioreti 8 2.0 217,000

Achnanthidium minutissimum 12 3.0 325,000

Asterinella formosa 38 9.5 1,030,000

Aulacoseira cf alpigena 42 10.5 1,140,000

Aulacoseira distans 2 .5 54,200

Aulacoseira granulata 26 6.5 704,000

Caloneis bacillum 2 .5 54,200

Cyclostephanos cf dubius 14 3.5 379,000

Cyclotella bodanica 36 9.0 975,000

Cyclotella cf stelligera 4 1.0 108,000

Cyclotella meneghiniana 60 15.0 1,630,000

Cyclotella ocellata 26 6.5 704,000

Cymbella tumida 2 .5 54,200

Denticula tenuis 2 .5 54,200

Encyonema lange-bertalotii 2 .5 54,200

Fragilaria capucina 16 4.0 434,000

Gomphonema sp. (heterovalvie) 2 .5 54,200

Hantzschia amphioxys 2 .5 54,200

Navicula cryptotenella 4 1.0 108,000

Navicula geoppertiana 2 .5 54,200

Navicula halophila 2 .5 54,200

Navicula trivialis 2 .5 54,200

Nitzschia acicularis 2 .5 54,200

Nitzschia capitellata 4 1.0 108,000

Nitzschia constricta 2 .5 54,200

Nitzschia dissipatta 2 .5 54,200

Nitzschia inconspicua 2 .5 54,200

Nitzschia linearis 4 1.0 108,000

Nitzschia palea 2 .5 54,200

Nitzschia perminuta 4 1.0 108,000

Sellaphora pupula 4 1.0 108,000

Stephanodiscus nigarae 40 10.0 1,080,000

Stephanodiscus sp. 1 2 .5 54,200

Stephanodiscus sp. 2 2 .5 54,200

Surirella minuta 2 .5 54,200

Synedra delicatissima 22 5.5 596,000

Total 400 1001 10,800,000

Table 19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves counted

Relative percentage

abundance

Valves per gram of

material1
64 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

1.05 Achnanthidium minutissimum 2 1.7 282,000

Asterinella formosa 70 11.8 1,980,000

Aulacoseira cf alpigena 134 22.6 3,780,000

Aulacoseira distans 6 1.0 169,000

Aulacoseira granulata 110 18.5 3,110,000

Caloneis bacillum 4 .7 113,000

Cyclostephanos cf dubius 4 .7 113,000

Cyclotella bodanica 52 8.8 1,470,000

Cyclotella cf fottii 4 .7 113,000

Cyclotella cf stelligera 4 .7 113,000

Cyclotella meneghiniana 46 7.8 1,300,000

Cyclotella ocellata 54 9.1 1,520,000

Encyonema prostrata 2 .3 56,500

Encyonema silesiacum 2 .3 56,500

Fragilaria capucina 16 2.7 452,000

Hantzschia amphioxys 2 .3 56,500

Navicula cryptotenella 2 .3 56,500

Navicula gregaria 2 .3 56,500

Navicula rhynchocephala 4 .7 113,000

Navicula tripunctata 2 .3 56,500

Nitzschia dissipatta 2 .3 56,500

Nitzschia linearis 2 .3 56,500

Stephanodiscus nigarae 26 4.4 734,000

Stephanodiscus sp. 1 2 .3 56,500

Surirella minuta 2 .3 56,500

Synedra delicatissima 28 4.7 790,000

Synedra ulna 1 .2 28,200

Total 593 1001 16,700,000

Table 19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves counted

Relative percentage

abundance

Valves per gram o

material1
Supplemental Information 

1.40 Achnanthes bioreti 2 0.4 54,800

Achnanthidium minutissimum 8 1.5 219,000

Aulacoseira cf alpigena 168 31.1 4,600,000

Aulacoseira distans 4 .7 110,000

Aulacoseira granulata 254 47.0 6,960,000

Bacillaria paradoxa 4 .7 110,000

Caloneis bacillum 4 .7 110,000

Cyclostephanos cf dubius 6 1.1 164,000

Cyclotella bodanica 12 2.2 329,000

Cyclotella meneghiniana 6 1.1 164,000

Cyclotella ocellata 2 .4 54,800

Cymatopleura solea 2 .4 54,800

Diploneis pupula 2 .4 54,800

Encyonema prostrata 2 .4 54,800

Fragilaria capucina 4 .7 110,000

Gomphonema angustum 2 .4 54,800

Gomphonema minutum 2 .4 54,800

Gomphonema pavulum 2 .4 54,800

Gomphonema sp. 6 1.1 164,000

Gomphonema sp. (heterovalvie) 2 .4 54,800

Navicula clementis 2 .4 54,800

Navicula cryptotenella 2 .4 54,800

Nitzschia commutata 2 .4 54,800

Nitzschia linearis 2 .4 54,800

Nitzschia perminuta 4 .7 110,000

Stephanodiscus cf neoastraea 2 .4 54,800

Stephanodiscus nigarae 24 4.4 657,000

Stephanodiscus sp. 1 2 .4 54,800

Stephanodiscus sp. 2 2 .4 54,800

Synedra ulna 4 .7 110,000

Total 540 1001 14,800,000

Table 19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves counted

Relative percentage

abundance

Valves per gram of

material1
66 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

1.75 Achnanthes bioreti 6 0.7 165,000

Achnanthidium minutissimum 28 3.2 768,000

Amphipleura pellucida 2 .2 54,800

Asterinella formosa 8 .9 219,000

Aulacoseira cf alpigena 406 46.7 11,100,000

Aulacoseira granulata 118 13.6 3,240,000

Aulacoseira italica 12 1.4 329,000

Cyclostephanos cf dubius 14 1.6 384,000

Cyclotella bodanica 78 9.0 2,140,000

Cyclotella cf stelligera 4 .5 110,000

Cyclotella meneghiniana 72 8.3 1,970,000

Eunotia musicola 8 .9 219,000

Fragilaria capucina 2 .2 54,800

Gomphonema parvulum 2 .2 54,800

Melosira varians 8 .9 219,000

Navicula clementis 2 .2 54,800

Navicula decussis 2 .2 54,800

Navicula mutica 8 .9 219,000

Navicula rhynchocephala 2 .2 54,800

Navicula tripunctata 2 .2 54,800

Navicula viridula 4 .5 110,000

Nitzschia dissipatta 4 .5 110,000

Nitzschia dubia 2 .2 54,800

Nitzschia filaformis 2 .2 54,800

Nitzschia perminuta 4 .5 110,000

Sellaphora pupula 2 .2 54,800

Stephanodiscus cf neoastraea 4 .5 110,000

Stephanodiscus nigarae 40 4.6 1,100,000

Stephanodiscus sp. 1 4 .5 110,000

Stephanodiscus sp. 2 2 .2 54,800

Synedra delicatissima 16 1.8 439,000

Synedra ulna 2 .2 54,800

Total 870 1001 23,900,000

Table 19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves counted

Relative percentage

abundance

Valves per gram o

material1
Supplemental Information 

2.10 Achnanthes bioreti 1 0.2 27,800

Achnanthidium minutissimum 6 1.3 167,000

Amphipleura pellucida 1 .2 27,800

Asterinella formosa 10 2.2 278,000

Aulacoseira cf alpigena 62 13.6 1,730,000

Aulacoseira granulata 225 49.3 6,260,000

Aulacoseira italica 2 .4 55,700

Caloneis limosa 2 .4 55,700

Cyclostephanos cf dubius 7 1.5 195,000

Cyclotella bodanica 11 2.4 306,000

Cyclotella meneghiniana 17 3.7 473,000

Cyclotella ocellata 2 .4 55,700

Diadesmis contenta 2 .4 55,700

Diatoma vulgare 2 .4 55,700

Encyonema silesiacum 1 .2 27,800

Fragilaria capucina 1 .2 27,800

Navicula cryptocephala 2 .4 55,700

Navicula cryptotenella 1 .2 27,800

Navicula geoppertiana 3 .7 83,500

Navicula mutica 17 3.7 473,000

Navicula trivialis 2 .4 55,700

Navicula viridula 1 .2 27,800

Nitzschia acicularis 1 .2 27,800

Nitzschia dissipatta 5 1.1 139,000

Nitzschia linearis 4 .9 111,000

Planothidium lanceolatum 1 .2 27,800

Stephanodiscus cf neoastraea 8 1.8 223,000

Stephanodiscus nigarae 40 8.8 1,110,000

Stephanodiscus sp. 1 3 .7 83,500

Synedra delicatissima 11 2.4 306,000

Synedra ulna 5 1.1 139,000

Total 456 1001 12,700,000

Table 19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves counted

Relative percentage

abundance

Valves per gram of

material1
68 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

2.45 Achnanthes bioreti 6 1.3 159,000

Achnanthidium minutissimum 12 2.5 318,000

Amphora inariensis 1 .2 26,500

Amphora ovalis 1 .2 26,500

Asterinella formosa 4 .8 106,000

Aulacoseira cf alpigena 207 43.4 5,480,000

Aulacoseira granulata 100 21.0 2,650,000

Aulacoseira italica 20 4.2 529,000

Bacillaria paradoxa 2 .4 52,900

Cyclostephanos cf dubius 10 2.1 26,500

Cyclotella bodanica 11 2.3 291,000

Cyclotella meneghiniana 20 4.2 529,000

Cyclotella ocellata 2 .4 52,900

Encyonmea caespitosa 1 .2 26,500

Fragilaria capucina 4 .8 106,000

Gomphonema parvulum 1 .2 26,500

Gyrosigma obtusatum 2 .4 52,900

Gyrosigma spencerii 1 .2 26,500

Hantzschia amphioxys 3 .6 79,400

Hantzschia rhaetica 1 .2 26,500

Navicula geoppertiana 2 .4 52,900

Navicula rhynchocephala 1 .2 26,500

Navicula viridula 1 .2 26,500

Nitzschia clausii 1 .2 26,500

Nitzschia linearis 3 .6 79,400

Planothidium lanceolatum 2 .4 52,900

Stauroneis anceps 1 .2 26,500

Stephanodiscus nigarae 25 5.2 662,000

Stephanodiscus sp. 1 3 .6 79,400

Stephanodiscus sp. 2 1 .2 26,500

Synedra delicatissima 21 4.4 556,000

Synedra parasitica 1 .2 26,500

Synedra ulna 4 .8 106,000

Thalassiosira cf weissflogii 2 .4 52,900

Total 477 1001 12,600,000

Table 19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves counted

Relative percentage

abundance

Valves per gram o

material1
Supplemental Information 

2.80 Achnanthes bioreti 4 0.6 56,200

Achnanthes sp. 10 1.4 140,000

Achnanthidium minutissimum 16 2.3 225,000

Amphora inariensis 2 .3 28,100

Asterinella formosa 4 .6 56,200

Aulacoseira cf alpigena 76 10.7 1,070,000

Aulacoseira granulata 296 41.8 4,160,000

Caloneis limosa 4 .6 56,200

Cyclostephanos cf dubius 2 .3 28,100

Cyclotella bodanica 50 7.1 702,000

Cyclotella cf fottii 4 .6 56,200

Cyclotella cf stelligera 16 2.3 225,000

Cyclotella meneghiniana 100 14.1 1,400,000

Cyclotella ocellata 4 .6 56,200

Cymbella tumida 2 .3 28,100

Denticula tenuis 2 .3 28,100

Diadesmis contenta 4 .6 56,200

Diploneis pupula 2 .3 28,100

Eunotia curvata 2 .3 28,100

Eunotia musicola 4 .6 56,200

Fragilaria capucina 4 .6 56,200

Gomphonema parvulum 2 .3 28,100

Gyrosigma spencerii 4 .6 56,200

Hantzschia amphioxys 4 .6 56,200

Hantzschia rhaetica 2 .3 28,100

Meridion circulare 2 .3 28,100

Navicula capitata 2 .3 28,100

Navicula cryptotenella 6 .8 84,200

Navicula mutica 4 .6 56,200

Navicula tripunctata 2 .3 28,100

Nitzschia dissipatta 2 .3 28,100

Nitzschia linearis 2 .3 28,100

Pinnularia microstauron 6 .8 84,200

Planothidium lanceolatum 6 .8 84,200

Stephanodiscus nigarae 40 5.6 562,000

Stephanodiscus sp. 1 8 1.1 112,000

Stephanodiscus sp. 2 2 .3 28,100

Surirella brebissonii 2 .3 28,100

Synedra delicatissima 2 .3 28,100

Synedra ulna 2 .3 28,100

Total 708 1001 9,940,000

Table 19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves counted

Relative percentage

abundance

Valves per gram of

material1
70 Sediment Deposition and Selected Water-Quality Characteristics in Cedar Lake and Lake Olathe, Northeast Kansas, 2000

3.15 Achnanthes bioreti 2 0.5 28,300

Achnanthidium minutissimum 8 2.1 113,000

Amphipleura pellucida 1 .3 14,100

Amphora inariensis 2 .5 28,300

Aulacoseira cf alpigena 88 23.6 1,240,000

Aulacoseira distans 2 .5 28,300

Aulacoseira granulata 76 20.4 1,070,000

Aulacoseira italica 1 .3 14,100

Cyclotella bodanica 50 13.4 707,000

Cyclotella cf fottii 1 .3 14,100

Cyclotella cf stelligera 5 1.3 70,700

Cyclotella meneghiniana 75 20.1 1,060,000

Cyclotella ocellata 1 .3 14,100

Diadesmis contenta 1 .3 14,100

Diploneis pupula 1 .3 14,100

Fragilaria capucina 2 .5 28,300

Gomphonema parvulum 1 .3 14,100

Gomphonema sp. 1 .3 14,100

Hantzschia amphioxys 1 .3 14,100

Navicula cryptotenella 4 1.1 56,500

Navicula gregaria 1 .3 14,100

Nitzschia acicularis 1 .3 14,100

Nitzschia clausii 1 .3 14,100

Nitzschia littoralis 3 .8 42,400

Pinnularia borealis 3 .8 42,400

Stephanodiscus nigarae 36 9.7 509,000

Stephanodiscus sp. 1 2 .5 28,300

Stephanodiscus sp. 2 1 .3 14,100

Synedra delicatissima 1 .3 14,100

Synedra ulna 1 .3 14,100

Total 373 1001 5,270,000

Table 19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves counted

Relative percentage

abundance

Valves per gram o

material1
Supplemental Information 

3.50 Achnanthes bioreti 5 1.0 70,400

Achnanthidium minutissimum 34 7.1 479,000

Amphora inariensis 3 .6 42,300

Aulacoseira cf alpigena 97 20.3 1,370,000

Aulacoseira granulata 160 33.4 2,250,000

Aulacoseira italica 27 5.6 380,000

Caloneis limosa 4 .8 56,300

Cyclostephanos cf dubius 1 .2 14,100

Cyclotella bodanica 30 6.3 423,000

Cyclotella cf fottii 1 .2 14,100

Cyclotella meneghiniana 35 7.3 493,000

Cyclotella ocellata 2 .4 28,200

Diploneis pupula 1 .2 14,100

Gomphonema parvulum 1 .2 14,100

Hantzschia amphioxys 3 .6 42,300

Meridion circulare 2 .4 28,200

Navicula cf lapidosa 1 .2 14,100

Navicula cryptotenella 4 .8 56,300

Navicula trivialis 2 .4 28,200

Nitzschia inconspicua 22 4.6 310,000

Nitzschia linearis 1 .2 14,100

Nitzschia palea 1 .2 14,100

Pinnularia borealis 5 1.0 70,400

Pinnularia microstauron 1 .2 14,100

Planothidium lanceolatum 1 .2 14,100

Stephanodiscus nigarae 29 6.1 408,000

Stephanodiscus sp. 1 1 .2 14,100

Stephanodiscus sp. 2 2 .4 28,200

Surirella minuta 2 .4 28,200

Synedra ulna 1 .2 14,100

Total 479 1001 6,750,000

1

Numbers are rounded to three significant figures.

Table 19. Diatom taxa, relative percentage abundance, and total number of valves per gram of material in bottomsediment sample from Lake Olathe coring site 5, northeast Kansas, 2000—Continued

Depth of sample

(feet) Taxa

Number of

valves counted

Relative percentage

abundance

Valves per gram of

material1