Fall River Lake

Fall River

U.S. Department of the Interior

U.S. Geological Survey

Scientific Investigations Report 2008–5019

Sedimentation and Occurrence and Trends of Selected

Nutrients, Other Chemical Constituents, and Diatoms 

in Bottom Sediment, Fall River Lake, Southeast 

Kansas, 1948−2006

Prepared in cooperation with the

KANSAS DEPARTMENT OF HEALTH AND ENVIRONMENT
Cover. Digital ortho photography of Fall River Lake, near Fall River, Kansas, 2006 (Photography from U.S. Department of Agriculture, 

 Farm Service Agency, Aerial Photography Field Office, Salt Lake City, Utah).
Sedimentation and Occurrence and Trends 

of Selected Nutrients, Other Chemical 

Constituents, and Diatoms in Bottom 

Sediment, Fall River Lake, Southeast 

Kansas, 1948–2006

By Kyle E. Juracek

Prepared in cooperation with the Kansas Department of Health and Environment

Scientific Investigations Report 2008–5019

U.S. Department of the Interior

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

DIRK KEMPTHORNE, Secretary

U.S. Geological Survey

Mark D. Myers, Director

U.S. Geological Survey, Reston, Virginia: 2008

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Suggested citation:

Juracek, K.E., 2008, Sedimentation and occurrence and trends of selected nutrients, other chemical constituents, and 

diatoms in bottom sediment, Fall River Lake, southeast Kansas, 1948–2006: U.S. Geological Survey Scientific Investigations Report 2008–5019, 29 p.
iii

Contents

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

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

 Description of Fall River Lake Basin...............................................................................................2

 Acknowledgments.............................................................................................................................4

Methods...........................................................................................................................................................4

 Estimation of Bottom-Sediment Volume, Mass, Mean Annual Net Deposition, and Mean 

Annual Net Yield......................................................................................................................4

 Sediment-Core Collection and Processing ...................................................................................4

 Physical Analyses..............................................................................................................................6

 Chemical Analyses, Quality Control, and Age Dating..................................................................6

 Estimation of Nutrient Loads and Yields ........................................................................................7

 Trend Analysis ....................................................................................................................................8

 Sediment-Quality Guidelines ...........................................................................................................8

 Diatom Analysis..................................................................................................................................8

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

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

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

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

Sedimentation...............................................................................................................................................10

Occurrence of, and Trends in, Selected Chemical Constituents and Diatoms..................................12

 Nutrients and Total Organic Carbon .............................................................................................12

 Trace Elements.................................................................................................................................12

 Diatoms..............................................................................................................................................14

Summary and Conclusions.........................................................................................................................16

References Cited..........................................................................................................................................17

Supplemental Information..........................................................................................................................21

Figures

1–2. Maps showing: 

 1. Location of Fall River Lake Basin, Fall River Lake, and land use (1988–90) in Fall 

 River Lake Basin, southeast Kansas ..................................................................................3

 2. Location of bottom-sediment coring sites in Fall River Lake, southeast Kansas .......5

3. Graphs showing variation in mean annual flow for Otter Creek at Climax, Fall River 

near Eureka, and Fall River at Fredonia, Kansas...................................................................11

4. Graph showing variation in total phosphorus concentrations with depth of bottom sediment samples collected from coring site F–2B in Fall River Lake, southeast Kansas, 

October 2006................................................................................................................................14

5. Graph showing variation in cesium-137 activity with depth of bottom-sediment samples 

collected from coring site F–2B in Fall River Lake, southeast Kansas, October 2006.....15
iv

Tables

1. Chemical analyses performed on bottom-sediment samples from Fall River Lake, 

southeast Kansas .........................................................................................................................6

2. Relative percentage differences for constituent concentrations in split-replicate 

samples from bottom sediment cores from Fall River Lake, southeast Kansas.................7

3. Sediment-quality guidelines for selected trace elements and associated bioaccumulation index........................................................................................................................................9

4. Sediment yield, precipitation, and land use for selected reservoir basins in Kansas. ...10

5. Results of trend tests on concentrations of selected constituents in bottom-sediment 

samples collected from Fall River Lake core F–2B, southeast Kansas, October 2006....13

A1. Latitude and longitude coordinates, water depth, estimated sediment thickness, length 

of recovered core, and estimated recovery percentage for bottom-sediment coring 

sites at Fall River Lake, southeast Kansas .............................................................................22

A2. Estimated bulk density of bottom sediment at coring sites in Fall River Lake, southeast 

Kansas ..........................................................................................................................................22

A3. Percentage of silt and clay and constituent concentrations for bottom-sediment samples collected from core F–2B at coring site F–2 in Fall River Lake, southeast Kansas, 

October 2006................................................................................................................................23

A4. Percentage of silt and clay and constituent concentrations for bottom-sediment 

samples collected from coring site F–4 in Fall River Lake, southeast Kansas, October 

2006 ...............................................................................................................................................26

A5. Percentage of silt and clay and constituent concentrations for bottom-sediment 

samples collected from coring site F–5 in Fall River Lake, southeast Kansas, October 

2006 ...............................................................................................................................................27

A6. Diatom species, number of valves counted, and relative percentage abundance in 

bottom-sediment samples collected from core F–2B at coring site F–2 in Fall River 

Lake, southeast Kansas, October 2006 ...................................................................................28
v

Conversion Factors, Abbreviations, and Datum

Multiply By To obtain

Length

centimeter (cm) 0.3937 inch (in.)

foot (ft) 0.3048 meter (m)

inch (in.) 2.54 centimeter (cm)

mile (mi) 1.609 kilometer (km)

millimeter (mm) 0.03937 inch (in.)

Area

acre 4,047 square meter (m2)

acre 0.4047 hectare (ha)

acre 0.004047 square kilometer (km2)

square foot (ft2) 0.09290 square meter (m2)

square mile (mi2) 259.0 hectare (ha)

square mile (mi2) 2.590 square kilometer (km2) 

Volume

acre-foot (acre-ft) 1,233 cubic meter (m3)

cubic centimeter (cm3) 0.06102 cubic inch (in3)

cubic foot (ft3) 0.02832 cubic meter (m3) 

Flow rate

cubic foot per second (ft3/s) 0.02832 cubic meter per second (m3/s)

Mass

gram (g) 0.03527 ounce (oz)

milligram per liter (mg/L) 1.0 part per million (ppm)

pound (lb) 0.4536 kilogram (kg) 

Density

pound per cubic foot (lb/ft3) 16.02 kilogram per cubic meter (kg/m3)

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

follows:

°F=(1.8×°C)+32

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

follows:

°C=(°F-32)/1.8

Horizontal coordinate information is referenced to the North American Datum of 

1983 (NAD 83). 

Sedimentation and Occurrence and Trends of Selected 

Nutrients, Other Chemical Constituents, and Diatoms 

in Bottom Sediment, Fall River Lake, Southeast Kansas, 

1948–2006

By Kyle E. Juracek

Abstract

A combination of available bathymetric-survey information and bottom-sediment coring was used to investigate 

sedimentation and the occurrence of selected nutrients (total 

nitrogen and total phosphorus), organic and total carbon, 25 

trace elements, diatoms, and the radionuclide cesium-137 in 

the bottom sediment of Fall River Lake, southeast Kansas. 

The total estimated volume and mass of bottom sediment 

deposited from 1948 through 2006 in the original conservation pool of the reservoir was 470 million cubic feet and 18.8 

billion pounds, respectively. The estimated sediment volume 

occupied about 36 percent of the original conservation-pool, 

water-storage capacity of the reservoir. Mean annual net sediment deposition since 1948 in the original conservation pool 

of the reservoir was estimated to be 324 million pounds per 

year. Mean annual net sediment yield from the Fall River Lake 

Basin was estimated to be 585,000 pounds per square mile 

per year. 

The mean annual net loads of total nitrogen and total 

phosphorus deposited in the bottom sediment of Fall River 

Lake were estimated to be 648,000 pounds per year and 

267,000 pounds per year, respectively. The estimated mean 

annual net yields of total nitrogen and total phosphorus from 

the Fall River Lake Basin were 1,170 pounds per square mile 

per year and 480 pounds per square mile per year, respectively. 

Throughout the history of Fall River Lake, total nitrogen and 

total phosphorus concentrations in the deposited sediment 

were relatively uniform. 

Trace element concentrations in the bottom sediment of 

Fall River Lake generally were uniform over time. Arsenic, 

chromium, nickel, and zinc concentrations typically exceeded 

the threshold-effects guidelines, which represent the concentrations above which toxic biological effects occasionally occur. Trace element concentrations did not exceed the 

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

which represent the concentrations above which toxic biological effects usually or frequently occur. 

Diatom occurrence in the bottom sediment of Fall River 

Lake was dominated by the species Aulacoseira granulata, 

which is an indicator of eutrophic (nutrient-rich) conditions. 

The abundance of the diatom Aulacoseira granulata, combined with cyanobacteria evidence and historical water-quality 

data, indicated that Fall River Lake likely has been eutrophic 

throughout much of its history. 

Introduction

Reservoirs provide many benefits including flood control, 

water supply, recreation, and habitat for fish and wildlife. The 

effective management of reservoirs requires several types of 

information including water quality, sedimentation, and sediment quality. 

Water-quality information is necessary for determining 

the suitability of the water in a reservoir in meeting various 

needs. Trends in water quality are useful for describing the 

overall effect of human activity in a reservoir basin, for providing an indication of the effectiveness of regulatory decisions 

and changes in land-management practices, and for providing 

a warning of potential future water-quality problems. 

The volume and quality of sediment deposited in a reservoir also are important. Sedimentation affects the useful life 

and the aesthetic quality of a reservoir. Sediment quality is an 

important environmental concern because sediment may act as 

a sink for water-quality constituents and, under certain conditions, as a source of constituents to the overlying water column 

and biota (Baudo and others, 1990; Zoumis and others, 2001). 

Sediment-associated constituents of concern include nutrients 

(for example, phosphorus), trace elements, and several pesticides. Once in the food chain, some sediment-derived constituents may pose an even greater concern because of bioaccumulation (Pais and Jones, 1997; Smol, 2002). An analysis of 

reservoir bottom sediment can provide historical information 

on sediment deposition as well as the occurrence of sedimentbound constituents. Such information may be used to partly 
2 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

reconstruct historical sediment-quality and water-quality 

records and to determine a present-day baseline with which to 

evaluate long-term changes in reservoir sediment and water 

quality that may be related to changes in human activity in 

the basin (Charles and Hites, 1987; Van Metre and Callender, 

1996; Van Metre and Mahler, 2004). 

Fall River Lake is a Federal impoundment on the Fall 

River in Greenwood County, southeast Kansas (fig. 1). The 

reservoir officially was completed in May 1949 by the U.S. 

Army Corps of Engineers (USCOE) with an original design 

life of 50 years. Water storage began in August 1948. The 

reservoir is used for several purposes including flood control, 

water supply, recreation, low-flow regulation, water-quality 

control, and fish and wildlife (Gary Simmons, U.S. Army 

Corps of Engineers, written commun., 2007). 

In 2006, Fall River Lake was listed under Section 303(d) 

of the Federal Clean Water Act of 1972 for eutrophication (as 

well as dissolved oxygen and siltation) (Kansas Department 

of Health and Environment, 2007). A eutrophic lake contains 

nutrient-rich water and supports high biotic productivity (Cole, 

1994). Typically, eutrophic lakes support algal growth that, if 

excessive, can cause taste-and-odor problems for water suppliers. Also, excessive algal growth may be detrimental to aquatic 

life and discourage recreational use of a lake. 

The 303(d) list is a priority list that identifies water bodies that do not meet water-quality standards that are based on 

the use of the water bodies. For each impaired water body on 

the 303(d) list, a State is required by the Federal Clean Water 

Act to develop a total maximum daily load (TMDL), which is 

an estimate of the maximum pollutant load (material transported during a specified time period) from point and nonpoint 

sources that a receiving water can accept without exceeding water-quality standards (U.S. Environmental Protection 

Agency, 1991). 

To provide information in support of the TMDL process, a 2-year study by the U.S. Geological Survey (USGS), 

in cooperation with the Kansas Department of Health and 

Environment (KDHE), was begun in 2006 to investigate 

sedimentation in Fall River Lake as well as the deposition of 

selected chemical constituents and diatoms. The specific study 

objectives were to: 

1. Estimate the volume, mass, mean annual net deposition, 

and mean annual net yield of sediment for the reservoir;

2. Determine the occurrence and trends of selected waterquality constituents in the bottom sediment of the reservoir; 

3. Determine the mean annual net loads and yields of 

selected nutrients from the reservoir basin; and

4. Determine the occurrence and relative abundance of diatoms in the bottom sediment as an indication of eutrophication over the life of the reservoir. 

The purpose of this report is to present the results of 

the USGS study to estimate sedimentation and to determine 

the occurrence of, and temporal trends in, selected chemical constituents and diatoms in the bottom sediment of Fall 

River Lake for 1948 through 2006. Study objectives were 

accomplished by using available bathymetric information from 

USCOE and by the collection and analysis of sediment cores 

in October 2006. Results presented in this report will assist 

KDHE in the evaluation, development, and implementation of 

TMDLs for constituents determined to contribute to waterquality impairment in the reservoir. From a national perspective, the methods and results presented provide guidance and 

perspective for future reservoir studies concerned with the 

issues of sedimentation and water quality. 

Description of Fall River Lake Basin

The Fall River Lake Basin is an area of about 554 mi2 that 

drains part of southeast Kansas (fig. 1). In 1948, Fall River 

Lake had an original surface area of about 2,620 acres and a 

water-storage capacity of about 30,400 acre-ft at the conservation-pool elevation of 948.5 ft above the National Geodetic 

Vertical Datum (NGVD) of 1929. In 1990, the surface area 

and water-storage capacity at the conservation-pool elevation 

were about 2,330 acres and 22,600 acre-ft, respectively (Sarah 

Harris, U.S. Army Corps of Engineers, written commun., 

2006). The decreases in surface area and storage capacity are 

the result of ongoing sedimentation. In addition to the Fall 

River, several small tributaries contribute flow directly to Fall 

River Lake (fig. 1). 

The Fall River Lake Basin is located in the Osage Plains 

Section of the Central Lowland physiographic province 

(Fenneman, 1946; Schoewe, 1949). Within the Osage Plains 

Section, most of the basin is located in the Osage Cuestas 

physiographic division with the exception of the extreme western part of the basin that is located in the Flint Hills Upland. 

The Osage Cuestas generally consist of a series of irregular 

northeast-southwest trending escarpments between which are 

flat to gently rolling plains. The topography of the Flint Hills 

Upland is characterized as gently rolling. Throughout the 

Osage Plains, the underlying bedrock is primarily limestone 

and shale of Permian and Pennsylvanian age (Schoewe, 1949). 

Slopes in the basin range from nearly level to gently sloping 

on the flood plains and from gently sloping to steep in the 

uplands. Generally, slopes are less than 10 percent but locally 

may be as steep as 20 to 30 percent (U.S. Department of Agriculture, Soil Conservation Service, 1982). 

Long-term mean annual precipitation at Eureka, located 

in the central part of the Fall River Lake Basin (fig. 1), is 

about 38 in. (period of record 1954–2005) (High Plains 

Regional Climate Center, 2007). Most of the annual precipitation is received during the growing season (generally 

April–September). 

Land use (1988–90) in the Fall River Lake Basin is 

mostly agricultural with grassland accounting for about 90 

percent of the basin. Cropland and woodland account for 

about 4 and 3 percent of the basin, respectively. Urban land 
Introduction 3

96°35' 96°

38°5'

35'

37°30'

55'

50'

45'

40'

38°

30' 25' 20' 15' 10' 05'

Otis Creek

Reservoir

West Branch

Fall River

Ivanpah Creek

Hog Creek

Cat Creek

Battle Creek

Otis Creek

Oleson Creek

East Branch Fall River

Swing

Creek

Silver Creek

Spring Creek Burnt Creek

Kitty Creek

Spring

Creek Fall River

Fall River

Lake

Honey Creek

Otter Creek

North

Branch

Otter Creek

South Branch

Otter Creek

Watson Branch

Tadpole Creek

Casner Creek

Badger Creek

Van Horn Branch

Durham

Creek

Fall River

Base from U.S. Geological Survey digital data, 1:100,000, 1999

Universal Transverse Mercator projection,

Zone 14

Horizontal coordinate information is referenced to the North American

 Datum of 1983 (NAD 83)

Climax

Fall River

Coyville

Eureka

Hamilton

Virgil

Toronto

New Albany

Fredonia

Yates Center

Severy

Cropland

Grassland

Woodland

Urban

Water

Other

Land use

U.S. Geological Survey streamflow-

 gaging station and number

EXPLANATION

Boundary of

Fall River Lake

drainage basin 

07167500

07167000

07169500

07169500

0 2 4 6 8 MILES

0 2 4 6 8 KILOMETERS

Land-use data from Kansas Applied Remote Sensing Program (1993)

ELK COUNTY

WILSON COUNTY

BUTLER

COUNTY

GREENWOOD COUNTY

WOODSON COUNTY

 CHASE COUNTY

KANSAS

NEBRASKA

OKLAHOMA

Fall River Lake

drainage basin

Index map COLORADO

MISSOURI

55' 95°50'

Figure 1. Location of Fall River Lake Basin, Fall River Lake, and land use (1988–90) in the Fall River Lake Basin, southeast Kansas 

(source of land-use data: Kansas Applied Remote Sensing Program, 1993).
4 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

use occupies less than 1 percent of the basin (fig. 1) (Kansas 

Applied Remote Sensing Program, 1993). 

Acknowledgments

This study was made possible in part by support from 

the Kansas Department of Health and Environment (KDHE) 

and the Kansas State Water Plan Fund. The author gratefully acknowledges topographic and bathymetric information 

provided by USCOE as well as water-quality data provided by 

KDHE. The author also thanks Jennifer Graham (USGS) 

for her assistance in interpreting the diatom and related 

biological information. 

Methods

The objectives of this study were accomplished using 

available and newly collected information. Available information included original and updated reservoir water-storage 

capacity data from USCOE and historical water-quality data 

from KDHE. New information was obtained through the collection and analysis of multiple bottom-sediment cores. 

Estimation of Bottom-Sediment Volume, Mass, 

Mean Annual Net Deposition, and Mean Annual 

Net Yield

The bottom-sediment volume (sediment plus pore water 

and gases) in the conservation pool of Fall River Lake was 

estimated by subtracting the updated water-storage capacity 

from the original water-storage capacity for the reservoir. The 

water-storage capacity originally was estimated by USCOE 

in 1948 with subsequent updates in 1973 and 1990. Thus, the 

bottom-sediment volume was estimated as the 1948 waterstorage capacity minus the 1990 water-storage capacity. The 

mean annual volume of sediment deposited (1948–1990) was 

computed as the total bottom-sediment volume divided by the 

number of years of deposition (42 years). Then, to provide 

an estimate of the current (2006) bottom-sediment volume, 

the mean annual volume of sediment deposited (1948–1990) 

was multiplied by the age of the reservoir (58 years). A partial 

bathymetric survey completed by USGS in October 2006 

indicated that using the mean annual volume of sediment 

deposited (1948–1990) to estimate the total current (2006) 

bottom-sediment volume was reasonable. 

Bottom-sediment mass was estimated by multiplying the 

current (2006) bottom-sediment volume by the representative 

bulk density. The representative bulk density for the reservoir was computed as the average of the mean bulk densities 

that were determined from sediment cores (see discussion in 

“Physical Analyses” section later in this report). Because bulk 

density varies with location and the representative bulk density 

accounts only for three sites in the reservoir, the estimated 

total bottom-sediment mass has a potential error of unknown 

magnitude. 

The mean annual mass of sediment (dry weight) deposited was estimated as the bottom-sediment mass divided by 

the age of the reservoir. Mean annual sediment yield from the 

reservoir basin was estimated by dividing the mean annual 

mass of sediment deposited by the area of the basin. Because 

sediment losses are not accounted for (for example, as a result 

of reservoir outflow), the estimated mean annual sediment 

deposition and yield represent net, rather than total, values. 

However, given that sediment trap efficiencies for large 

reservoirs typically are greater than 90 percent (Brune, 1953; 

Vanoni, 2006), the sediment losses likely are minimal. 

Sediment-Core Collection and Processing

Bottom-sediment cores were collected in October 2006 

at three sites (fig. 2) within Fall River Lake. Two cores were 

collected at site F–2 to provide sufficient sediment mass for 

planned physical, chemical, and diatom analyses. Of the four 

cores collected at Fall River Lake, one was used for chemical and diatom analyses (core B at site F–2, hereafter referred 

to as core F–2B), two were used for chemical analysis and 

bulk-density determinations (cores F–4 and F–5), and one was 

used for bulk-density determinations only (core A at site F–2, 

hereafter referred to as core F–2A) (fig. 2). 

The cores were collected from a pontoon boat using a 

gravity corer. The liner used for all cores was cellulose acetate 

butyrate transparent tubing with a 2.625-in. inside diameter. 

The latitude and longitude for each coring site, obtained using 

GPS technology, are provided in table A1 in the “Supplemental Information” section at the back of this report. 

When using a gravity corer, a phenomenon referred to as 

“core shortening” occurs that results in a recovered sediment 

core that may be only about one-half of the actual thickness of 

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

shortening is caused by the friction of the sediment against the 

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

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

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

lake-bottom sediment, which is characterized by uniform 

texture with decreasing water content at depth, core shortening 

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

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

Because of the substantial thickness of the bottom sediment at the locations cored in Fall River Lake, penetration of 

the entire sediment thickness was not achieved for all cores. 

In fact, complete penetration was achieved only for core F–2B 

as evidenced by differences in moisture content, texture, and 

organic matter content at the boundary between the sediment 

deposited in the reservoir and the underlying original (prereservoir) land-surface material. Penetration was believed to 

be nearly complete for nearby core F–2A. Complete penetra-
Methods 5

tion was not achieved for cores F–4 and F–5. A comparison of 

the length of core recovered by gravity coring to the thickness 

of sediment penetrated indicated that recovery was about 65 to 

70 percent for core F–2B. Sediment thickness at site F–2 was 

estimated at about 10 ft. At coring sites F–4 and F–5, USCOE 

bathymetric information indicated that the sediment thickness 

in the submerged river channel was at least 20 ft (on the basis 

of the 1990 bathymetric survey and extrapolating to 2006). For 

cores F–2A, F–4, and F–5 it was assumed that the sediment 

recovered provided representative information for the entire 

sediment thickness at each site. Average length for the four 

cores collected was about 7 ft (table A1). 

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

and refrigerated (at 4–5 oC) until processed. The core liners 

were cut lengthwise in two places 180 degrees apart. The cuts 

were completed with a 4-in. hand-held circular saw with the 

blade set at a depth to minimize penetration of the sediment 

cores. The cores were split in half by pulling a tightly held 

nylon string through the length of the cores and allowing the 

halves to separate. Once split, the relatively undisturbed inner 

parts of the cores were exposed for examination and sampling. 

On the basis of differences in moisture content, texture, and 

organic matter content (for example, root hairs, sticks, seed 

pods, leaves), the boundary between the sediment deposited 

in the reservoir and the underlying original (pre-reservoir) 

land-surface material was determined. Typically, the bottom 

sediment was characterized by higher moisture content, finer 

texture, and little if any visible organic matter as compared to 

the original material. 

0 0.25 0.50 0.75 1.0 MILE

0 0.25 0.50 0.75 1.0 KILOMETER

37°41'

37°39'

40'

96°8' 07' 06' 05' 04' 96°3'

Fall River Lake

Fall River

Casner Creek

Badger Creek

Base from U.S. Geological Survey digital data, 1:100,000, 1999

Universal Transverse Mercator projection,

Zone 14

Horizontal coordinate information is referenced to the North American

 Datum of 1983 (NAD 83) EXPLANATION

F–2

Coring site and identifier F–2

F–4

F–5

River channel

Figure 2. Location of bottom-sediment coring sites in Fall River Lake, southeast Kansas.
6 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

Physical Analyses

Physical analyses included bulk-density determinations 

and particle-size analyses. Cores F–2A, F–4, and F–5 from 

Fall River Lake were analyzed to determine bulk density. For 

this purpose, each core was divided into six or seven intervals 

of equal length. The number of intervals was dependent on the 

length of each core. From each interval, a 1-in. thick cylindrical volume of sediment was removed using a putty knife, 

weighed to the nearest 0.10 gram, oven dried at about 45 oC 

for 96 hours, and reweighed. Oven drying of the sample continued as it was reweighed on a daily basis until no additional 

moisture loss was observed. Bulk density was computed as 

follows:

 Db = m/v, (1)

where Db is the bulk density (in grams per cubic centimeter), 

m is the mass (dry weight) of the sample (in grams), and v is 

the volume of the sample (in cubic centimeters). The volume 

for a cylindrical sample was computed as: 

 v = h(πd2/4), (2)

where v is the volume of the sample (in cubic centimeters), 

h is the height (length) of the sample (in centimeters), and d

is the diameter of the sample (in centimeters) (Gordon and 

others, 1992). In all, 20 bulk-density determinations were 

completed at the USGS laboratory in Lawrence, Kansas (table 

A2 at the back of this report). 

Results for all sampled intervals were averaged to determine the mean bulk density for each core. The bulk densities 

then were converted to pounds per cubic foot for use in subsequent computations. The representative bulk density was computed as the average of the mean bulk densities determined for 

the three individual cores. 

Particle-size analysis was performed to determine the 

percentage of sand (that is, particles larger than 0.063 mm in 

diameter) and silt and (or) clay (that is, particles smaller than 

0.063 mm in diameter) in the sediment cores. The sediment 

samples used for constituent analyses also were used for particle-size analyses. The particle-size analyses were completed at 

the USGS Sediment Trace Element Partitioning Laboratory in 

Atlanta, Georgia, according to the methods presented in Guy 

(1969) and Grosbois and others (2001). 

Chemical Analyses, Quality Control, and Age 

Dating

The number of samples for chemical analysis removed 

from each core was dependent on the length of the core, the 

intended use of the core, and the amount of material required 

for analyses. In all cases, care was taken to avoid sampling the 

sediment that came into contact with the core liner and the saw 

blade. Each core was divided into multiple intervals of equal 

length. An approximately equal volume of sediment (defined 

as the space occupied by the sediment particles, water, and 

gases as measured in cubic units) was removed lengthwise 

from both halves of each interval and combined using a plastic 

spatula. The combined sediment volume for each interval was 

homogenized and sampled for subsequent chemical analyses. 

The sediment samples were analyzed for nutrients (total 

nitrogen and total phosphorus), organic and total carbon, 

and 25 trace elements. A complete list of the constituents for 

which analyses were performed is provided in table 1. Core 

F–2B was divided into 12 intervals of equal length, sampled, 

and analyzed to assess trends in constituent deposition during 

Table 1. Chemical analyses performed on bottom-sediment samples from Fall River Lake, southeast Kansas.

[Number in parentheses is the method reporting limit for each constituent. mg/kg, milligrams per kilogram; %, percent dry weight; 

pCi/g, picocuries per gram]

Nutrients

Total nitrogen (100 mg/kg) Total phosphorus (50 mg/kg)

Carbon

Carbon, total organic (0.1%) Carbon, total (0.1%)

Trace elements

Aluminum (0.1%) Cobalt (1.0 mg/kg) Nickel (1.0 mg/kg) Titanium (0.01%)

Antimony (0.1 mg/kg) Copper (1.0 mg/kg) Selenium (0.1 mg/kg) Uranium (50 mg/kg)

Arsenic (0.1 mg/kg) Iron (0.1%) Silver (0.5 mg/kg) Vanadium (1.0 mg/kg)

Barium (1.0 mg/kg) Lead (1.0 mg/kg) Strontium (1.0 mg/kg) Zinc (1.0 mg/kg)

Beryllium (0.1 mg/kg) Lithium (1.0 mg/kg) Sulfur (0.1%)

Cadmium (0.1 mg/kg) Manganese (10.0 mg/kg) Thallium (50 mg/kg)

Chromium (1.0 mg/kg) Molybdenum (1.0 mg/kg) Tin (1.0 mg/kg)

Radionuclide

Cesium-137 (0.05 pCi/g)
Methods 7

the life of the reservoir. Cores F–4 and F–5 were divided into 

3 intervals of equal length, sampled, and analyzed for constituents. Constituent analyses of bottom-sediment samples were 

performed at the USGS Sediment Trace Element Partitioning 

Laboratory in Atlanta, Georgia. Analyses of sediment samples 

for total nitrogen and carbon concentrations were performed 

using the methods described by Horowitz and others (2001). 

Analyses for total phosphorus and trace elements were performed using the methods described by Fishman and Friedman 

(1989), Arbogast (1996), and Briggs and Meier (1999). 

Quality control for the chemical analyses of sediment 

samples was provided by an evaluation of variability that 

involved an analysis of split-replicate samples collected from 

Fall River Lake. Split-replicate samples were analyzed for 

cores F–4 and F–5. For each core, a representative volume 

of sediment was removed, homogenized, and sampled twice. 

Both samples were analyzed for the various constituents. The 

relative percentage difference between the replicate sample 

concentrations was computed as:

 Drp = [|C1 - C2| / (C1 + C2)] * 100, (3)

where Drp is the relative percentage difference, C1 is the first 

replicate sample concentration, and C2 is the second replicate 

sample concentration. 

The relative percentage differences computed for the constituents detected in the split-replicate samples are provided 

in table 2. With the exception of tin, analytical variability was 

minimal with mean relative percentage differences less than 4 

percent. Tin had a mean relative percentage difference of 22.2 

percent. 

Age dating of the bottom sediment was accomplished 

by determining the activity of cesium-137 (137Cs). 137Cs is 

a radioactive isotope that is a by-product of above-ground 

nuclear weapons testing. Measurable activity of this isotope 

first appeared in the atmosphere in about 1952, peaked during 1963–64, and has since declined (Ritchie and McHenry, 

1990). Measurable activity in soils began about 1954 (Wise, 

1980). 137Cs is an effective marker for age dating bottom sediment in reservoirs constructed before 1963–64. It also can be 

used to demonstrate that the sediment is relatively undisturbed 

if the 1963–64 peak is well-defined and a generally uniform, 

exponential decrease in 137Cs activity follows the peak (Van 

Metre and others, 1997). Age dating of sediment using 137Cs 

was attempted for Fall River Lake cores F–2B and F–5. 

Analysis of sediment samples for 137Cs activity was performed 

at the USGS Florida Integrated Science Center in St. Petersburg, Florida, using gamma-ray spectrometry (Holmes and 

others, 2001). 

Estimation of Nutrient Loads and Yields

The mean annual load and yield of total nitrogen (TN) 

and total phosphorus (TP) was estimated for Fall River Lake 

for the period 1948 to 2006. For each nutrient, mean annual 

Table 2. Relative percentage differences for constituent 

concentrations in split-replicate samples from bottom 

sediment cores from Fall River Lake, southeast Kansas. 

[Location of coring sites shown in figure 2. --, not calculated because 

constituent was not detected in one or both of the split-replicate samples]

Constituent Relative percentage difference

F–4 F–5 Mean

Nutrients

Total nitrogen 0 0 0

Total phosphorus 0 .7 .4

Carbon

Carbon, total organic 0 0 0

Carbon, total 2.2 0 1.1

Trace elements

Aluminum 0 .6 .3

Antimony 0 7.7 3.9

Arsenic 0 1.5 .8

Barium 0 0 0

Beryllium 1.8 0 .9

Cadmium 0 0 0

Chromium .5 .6 .6

Cobalt 0 0 0

Copper 0 2.1 1.1

Iron 0 0 0

Lead 0 1.8 .9

Lithium .8 0 .4

Manganese 0 .6 .3

Molybdenum -- -- --

Nickel 1.2 1.4 1.3

Selenium 0 0 0

Silver -- -- --

Strontium 0 0 0

Sulfur 0 0 0

Thallium -- -- --

Tin 11.1 33.3 22.2

Titanium 0 2.0 1.0

Uranium -- -- --

Vanadium 0 0 0

Zinc 0 0 0
8 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

load was estimated as the representative sediment concentration multiplied by the mean annual mass of sediment deposited in the reservoir. The representative sediment concentration 

was computed as the median of the sample intervals analyzed 

for cores F–2B, F–4, and F–5. 

The mean annual yield for each nutrient was estimated 

by dividing the mean annual load by the area of the Fall River 

Lake Basin. Because sediment losses are not accounted for 

(for example, as a result of reservoir outflow), the computed 

loads and yields represent net, rather than total, values. 

Trend Analysis

Core F–2B was used for trend analyses. This core was 

analyzed for nutrients, carbon, trace elements, and diatoms. 

The statistical significance of possible trends in constituent concentrations and diatom occurrence was determined 

by computing a nonparametric Spearman’s rho correlation 

coefficient. An advantage of Spearman’s rho is that, because 

it is based on ranks, it is more resistant to outlier effects than 

the more commonly used Pearson’s r correlation coefficient 

(Helsel and Hirsch, 1992). Trends were considered to be significantly positive (constituent concentration or diatom occurrence increased toward the top of the sediment core) or negative (constituent concentration or diatom occurrence decreased 

toward the top of the sediment core) if the probability (twosided p-value) of rejecting a correct hypothesis (in this case, 

no trend) was less than or equal to 0.05. In the results, a 

possible trend in constituent concentration will be considered 

meaningful only if the change in constituent concentration is 

beyond the variability that could be explained by analytical 

variance (defined here as the mean constituent concentration 

in the sediment core plus or minus 10 percent). 

Sediment-Quality Guidelines

The U.S. Environmental Protection Agency (USEPA) 

has adopted nonenforceable sediment-quality guidelines 

(SQGs) in the form of level-of-concern concentrations for 

several trace elements (U.S. Environmental Protection Agency, 

1997). These level-of-concern concentrations were derived 

from biological-effects correlations made on the basis of 

paired onsite and laboratory data to relate incidence of adverse 

biological effects in aquatic organisms to dry-weight sediment 

concentrations. Two such level-of-concern guidelines adopted 

by USEPA are referred to as the threshold-effects level (TEL) 

and the probable-effects level (PEL). The TEL is assumed 

to represent the concentration below which toxic biological 

effects rarely occur. In the range of concentrations between the 

TEL and PEL, toxic effects occasionally occur. Toxic effects 

usually or frequently occur at concentrations above the PEL. 

USEPA cautions that the TEL and PEL guidelines are 

intended for use as screening tools for possible hazardous 

levels of chemicals and are not regulatory criteria. This cautionary statement is made because, although biological-effects 

correlation identifies level-of-concern concentrations associated with the likelihood of adverse organism response, the 

comparison may not demonstrate that a particular chemical is 

solely responsible. In fact, biological-effects correlations may 

not indicate direct cause-and-effect relations because sediments may contain a mixture of chemicals that contribute to 

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

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

MacDonald and others (2000) developed consensusbased SQGs that were computed as the geometric mean of 

several previously published SQGs. The consensus-based 

SQGs consist of a threshold-effect concentration (TEC) and a 

probable-effect concentration (PEC). The TEC represents the 

concentration below which adverse effects are not expected 

to occur, whereas the PEC represents the concentration above 

which adverse effects are expected to occur more often than 

not. An evaluation of the reliability of the SQGs indicated that 

most of the individual TECs and PECs provide an accurate 

basis for predicting the presence or absence of sediment toxicity (MacDonald and others, 2000). 

A comparison of the two SQGs indicated that the 

differences were generally small (table 3). The largest 

difference was for the zinc PEL and PEC. In this case, the 

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

(271 mg/kg). For this study, the SQGs used were selected 

to provide a less-stringent assessment. Thus, for each trace 

element for which SQGs were available, the larger of the two 

options for threshold effects and probable effects was selected 

for the purpose of assessing sediment quality (see shaded values in table 3). In this report, the options used to assess sediment quality are referred to as the threshold-effects guideline 

and the probable-effects guideline. 

Diatom Analysis

Analysis of the sediment samples for diatoms was 

performed by Dr. Yangdong Pan, Portland State University, 

Portland, Oregon. Analyses for diatoms were performed using 

equipment and methods described by Acker and others (2002), 

Krammer and Lange-Bertalot (1986, 1988, 1991a, 1991b), and 

Patrick and Reimer (1966, 1975). Core F–2B was analyzed 

for diatoms using the same 12 intervals that were analyzed for 

constituents. 

Background Information for Selected Chemical 

Constituents and Diatoms 

Nutrients and Total Organic Carbon

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

environments, phosphorus is the principal limiting factor for 
Methods 9

primary production (Hakanson and Jansson, 1983; Wetzel, 

2001). If phosphorus concentrations are too large, algal growth 

may become excessive and cause taste-and-odor problems for 

water suppliers. Additionally, excessive algal growth may be 

detrimental to aquatic life and discourage recreational use of 

a lake. Major human-related sources of nutrients include 

fertilizer application, livestock production, and sewage-treatment plants. 

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

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

The organic carbon content of sediment also is important 

because many contaminants specifically sorb to the organic 

material in sediment (Karickhoff, 1984; Horowitz, 1991). 

Trace Elements

Trace elements are important determinants of sediment 

quality because of their potential toxicity to living organisms 

(Forstner and Wittmann, 1981). Trace elements may 

be defined as elements that typically are present in the 

environment in relatively low (less than 0.1 percent) concentrations (Adriano, 1986; Pais and Jones, 1997). Using this 

definition, most of the elements analyzed in this study may be 

considered trace elements. Exceptions, which are some of the 

abundant rock-forming elements, include aluminum and iron 

(Adriano, 1986). 

Trace elements in sediment originate naturally from the 

rock and soil within a basin. Also, sediment enrichment of 

certain trace elements may be attributable to several human-related sources including fertilizers, liming materials, pesticides, 

irrigation water, animal and human wastes, coal combustion 

residues, leaching from landfills, mining, metal-smelting 

industries, and automobile emissions (Forstner and Wittmann, 

1981; Davies, 1983; Adriano, 1986). 

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

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

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

and chromium, are required by animals and humans but are 

not essential for plants. Nonessential elements for plants, 

animals, and humans include cadmium, mercury, and lead 

(Adriano, 1986; Lide, 1993; Pais and Jones, 1997). 

Toxicity is a function of several factors including the type 

of organism, the availability of a trace element in the environment, and the potential of the trace element to bioaccumulate 

in organisms. The daily intake of trace elements by animals 

and humans may be classified as deficient, optimal, or toxic. 

Most, if not all, trace elements may be toxic in animals and 

humans if the concentrations are sufficiently large (Forstner 

and Wittmann, 1981; Pais and Jones, 1997; Smol, 2002). 

Information on the bioaccumulation index (Pais and Jones, 

1997) for the trace elements with available SQGs is provided 

in table 3. The bioaccumulation index indicates the relative 

potential of a trace element to bioaccumulate in organisms. 

Diatoms

Diatoms are microscopic algae that occur in almost all 

aquatic environments. They have a siliceous shell, or frustule, 

consisting of two valves (halves), that is preserved in sediment. Because many diatom species are sensitive to changes in 

environmental conditions (for example, pH, light, temperature, 

and concentrations of nutrients, trace elements, and pesticides), changes in diatom species composition and abundance 

can be used as indicators of environmental changes (Dixit and 

others, 1992; Stoermer and Smol, 1999). 

Table 3. Sediment-quality guidelines for selected trace elements and associated 

bioaccumulation index.

[Values in milligrams per kilogram. Shading represents guidelines to which sediment concentrations were 

compared in this report. USEPA, U.S. Environmental Protection Agency; TEL, threshold-effects level; PEL, 

probable-effects level; TEC, threshold-effects concentration; PEC, probable-effects concentration; --, not 

available]

USEPA (1997) MacDonald and others 

(2000)

Bio-accumulation index1

Trace element TEL PEL TEC PEC

Arsenic 7.24 41.6 9.79 33.0 moderate

Cadmium .676 4.21 .99 4.98 moderate

Chromium 52.3 160 43.4 111 moderate

Copper 18.7 108 31.6 149 high

Lead 30.2 112 35.8 128 moderate

Nickel 15.9 42.8 22.7 48.6 moderate

Silver .733 1.77 -- -- moderate

Zinc 124 271 121 459 high

1

Bioaccumulation index information for trace elements from Pais and Jones (1997).
10 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

Diatoms are useful for assessing the trophic condition 

and trophic history of a lake. For example, a lake may be 

characterized as eutrophic (nutrient rich, high primary productivity) or oligotrophic (nutrient poor, low primary productivity) (Horne and Goldman, 1994). Several diatom species are 

indicators of eutrophic and oligotrophic conditions (Stoermer 

and Smol, 1999). Generally, in eutrophic water, the diatom 

community will be dominated by a few abundant species 

tolerant of nutrient and organic enrichment. In contrast, diatom 

communities in uncontaminated water (free of sewage or other 

organic enrichment caused by waste discharge) consist of a 

greater number of more equally abundant species (U.S. Environmental Protection Agency, 1977; John Smol, Queen’s University, Kingston, Ontario, Canada, written commun., 2007). 

Sedimentation

Based on the mean annual volume of water-storage 

capacity lost to sedimentation from 1948 to 1990, and extrapolating to 2006, the total volume of bottom sediment in the 

original conservation pool of Fall River Lake (as of 2006) was 

estimated to be about 470 million ft3 or about 10,800 acre-ft. 

The estimated sediment volume occupied about 36 percent of 

the original conservation-pool, water-storage capacity of the 

reservoir. Water-storage capacity in the conservation pool has 

been lost to sedimentation at a rate of less than 1 percent annually. Because most of the deposited sediment is contributed 

by large inflows, an indication of the year-to-year variability 

in sedimentation is provided by the year-to-year variability in 

streamflow. Variability in the mean annual flow at three locations within the Fall River Basin is shown in figure 3. 

Mean annual net sediment yield, computed as the total 

volume of deposited sediment (10,800 acre-ft) divided by 

basin size (554 mi2) and reservoir age (58 years), was estimated to be 0.34 acre-ft/mi2

/yr. A comparison of the volumetric sediment yield with other selected reservoir basins in 

Kansas is provided in table 4. Among the reservoirs compared, 

the sediment yield for Fall River Lake was relatively low. In an 

analysis that included the other 11 reservoirs listed in table 4, 

a statistically significant positive correlation (significant at the 

0.001 level) between sediment yield and mean annual precipitation (Spearman’s rho = 0.86) was indicated (Juracek, 2004). 

In the same analysis, no statistically significant correlation (at 

the 0.05 level) was indicated for the relation between sediment 

yield and mean soil permeability, mean slope, or land use. 

Within a given basin, sediment yield is a result of the complex 

interaction among several natural and human-related factors. 

Table 4. Sediment yield, precipitation, and land use for selected reservoir basins in Kansas.

[Reservoir basins are ordered from largest to smallest in sediment yield. Information for reservoirs other than Fall River Lake from 

Juracek, 2004]

Reservoir basin Sediment yield (acre-feet per 

square mile per year)

Mean annual precipitation (inches)Land use

Cropland (percent)Grassland 

and woodland 

(percent)

Small reservoir basins

Mound City Lake 2.03 40 16.3 79.5

Crystal Lake 1.72 40 10.7 66.0

Mission Lake 1.42 35 69.9 26.4

Gardner City Lake .85 39 30.8 46.4

Otis Creek Reservoir .71 33 .1 96.5

Lake Afton .66 30 81.0 15.2

Large reservoir basins

Perry Lake 1.59 37 40.0 57.0

Hillsdale Lake .97 41 35.4 57.3

Tuttle Creek Lake .40 30 66.0 32.0

Fall River Lake .34 38 4.0 93.0

Cheney Reservoir .22 27 72.7 25.4

Webster Reservoir .03 21 61.1 38.3
Sedimentation 11

The total mass of bottom sediment, computed as the 

total volume of bottom sediment multiplied by the representative bulk density of the sediment (40 lb/ft3

), was estimated 

to be 18.8 billion lb. Mean annual net sediment deposition in 

the conservation pool of the reservoir, computed as the total 

bottom-sediment mass divided by reservoir age (58 yrs), was 

estimated to be 324 million lb/yr. Mean annual net sediment 

yield, computed as the mean annual net deposition divided by 

basin area (554 mi2), was estimated to be 585,000 (lb/mi2)/yr. 

In comparison, Juracek (2004) used similar methods to estimate a mean annual net sediment yield of 964,000 (lb/mi2

)/yr 

for Otis Creek Reservoir (completed in 1971), which is located 

within the Fall River Lake Basin (fig. 1). Several factors may 

account for the difference in sediment yield including topography, land-management practices, sediment storage, and the 

time period analyzed (that is, 1948 to 2006 for Fall River Lake 

versus 1971 to 2002 for Otis Creek Reservoir). Moreover, the 

difference may be indicative of the variability of sediment 

yield throughout the Fall River Lake Basin and the fact that 

a small percentage of a basin can account for a large percentage of the sediment yield (Morris and Fan, 1998; Russell and 

others, 2001). 

The particle-size composition of the bottom sediment 

sampled in Fall River Lake was uniform. At every site and 

sampling depth, the silt and (or) clay content of the sediment 

was greater than 99 percent (tables A3, A4, and A5 at the back 

of this report). 

(B) Fall River near Eureka, KS (07167000)

(C) Fall River at Fredonia, KS (07169500)

(A) Otter Creek at Climax, KS (07167500)

0

0

0

200

1930 1940 1950 1960 1970 1980 1990 2000 2010

400

600

800

1,000

1,200

1,400

50

100

200

300

400

Mean annual discharge, in cubic feet per second

500

600

100

150

200

250

300

Figure 3. Variation in mean annual flow for Otter Creek at Climax, Fall River near Eureka, and Fall River at Fredonia, Kansas.
12 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

Occurrence of, and Trends in, Selected 

Chemical Constituents and Diatoms

This section describes the occurrence of, and trends 

in, selected chemical constituents and diatoms in bottomsediment samples collected from Fall River Lake in southeast 

Kansas. Chemical analyses were performed using sediment 

samples from cores F–2B, F–4, and F–5 (fig. 2). Only the 

near-dam core F–2B was analyzed for diatoms. 

Nutrients and Total Organic Carbon

TN concentrations in the bottom sediment of Fall River 

Lake were remarkably uniform. For all sample intervals of 

cores F–2B, F–4, and F–5, the TN concentration was 2,000 

mg/kg (tables A3, A4, and A5 at the back of this report). The 

mean annual net load of TN deposited in the bottom sediment 

of Fall River Lake, computed as the mean annual net sediment 

deposition multiplied by the representative TN concentration 

(2,000 mg/kg), was estimated to be 648,000 lb/yr. The mean 

annual net yield of TN from the Fall River Lake Basin, computed as the mean annual net load divided by basin area, was 

estimated to be 1,170 (lb/mi2)/yr. 

In comparison, the TN concentrations in a 5-interval sediment core collected from Otis Creek Reservoir (and analyzed 

using the same laboratory methods) essentially were uniform 

with a median of 2,300 mg/kg. The estimated mean annual net 

yield of TN from the Otis Creek Reservoir Basin was 2,210 

(lb/mi2)/yr (Juracek, 2004). 

TP concentrations for the sample intervals of Fall River 

Lake cores F–2B, F–4, and F–5 ranged from 730 to 910 mg/kg 

(tables A3, A4, and A5). The mean TP concentration for cores 

F–2B, F–4, and F–5 was 820, 810, and 740 mg/kg, respectively. Computed using the sample intervals for all three Fall 

River Lake cores (that is, 18 intervals), the respective mean 

and median TP concentration was 810 and 820 mg/kg. Using 

the median concentration, the mean annual net load and yield 

of TP was estimated to be 267,000 lb/yr and 480 (lb/mi2)/yr, 

respectively. 

In comparison, the median TP concentration in a 5-interval core collected from Otis Creek Reservoir (and analyzed 

using the same laboratory methods) was 620 mg/kg. The 

estimated mean annual net yield of TP from the Otis Creek 

Reservoir Basin was about 600 (lb/mi2)/yr (Juracek, 2004). 

Nutrient concentrations in sediment, as well as estimated 

nutrient yields, vary substantially throughout the State. For 

example, in a study of bottom sediments collected from 10 

small reservoirs in eastern Kansas (and analyzed using the 

same laboratory methods), median TN and TP concentrations 

ranged from 1,400 to 3,700 mg/kg and from 550 to 1,300 

mg/kg, respectively. Mean annual net TN and TP yields, 

estimated for five of the small reservoirs, had respective ranges 

of 2,210 to 6,800 (lb/mi2)/yr and 598 to 2,420 (lb/mi2)/yr 

(Juracek, 2004). Statistical analysis, with a significance level 

of 0.05, indicated no significant correlations between median 

TN and TP concentrations in bottom sediment and land use. 

Likewise, a comparison of TN and TP yields with land use for 

the five small reservoirs for which nutrient yields were estimated also indicated no discernible relation (Juracek, 2004). 

The variability in nutrient concentrations in sediment may be 

caused, in part, by factors for which information is not readily 

available. Such information includes background nutrient contributions from soils and bedrock, historical land-management 

practices, historical application of fertilizers, historical livestock production, sediment sources, and in-reservoir processes. 

For Fall River Lake core F–2B, a statistically significant positive trend in TP concentrations (TP concentration 

increased toward the top of the sediment core) was indicated 

(fig. 4, tables 5 and A3). Because the 137Cs activity has a welldefined 1963–64 peak followed by a uniform, exponential 

decrease (fig. 5), it was concluded that the bottom sediment 

at coring site F–2B is relatively undisturbed, and any trends 

may be considered meaningful. However, despite the statistical significance, the trend in TP concentration may not be 

representative of an actual trend because of analytical variance (defined here as the mean constituent concentration for 

the sediment core plus or minus 10 percent). This conclusion 

was based on the fact that most of the intervals in core F–2B 

had a TP concentration that was within 10 percent of the mean 

TP concentration. No trend in TP concentrations was evident 

for the 5-interval core collected from Otis Creek Reservoir 

(Juracek, 2004). 

TOC concentrations for the sample intervals of the three 

cores ranged from 1.5 to 1.8 percent (tables A3, A4, and A5) 

and were characterized by minimal variability within each 

core. A statistically significant trend in TOC concentrations 

was not indicated for core F–2B (table 5). 

Trace Elements

Generally, trace element concentrations in the bottom 

sediment of Fall River Lake were uniform over time (tables 

A3, A4, and A5). A statistically significant positive trend was 

indicated for cobalt, iron, manganese, and nickel concentrations in Fall River Lake core F–2B (table 5). However, because 

for each element all or most of the core intervals had concentrations that were within 10 percent of the mean concentration, the trends may be a result of analytical variance. Trace 

element concentrations in a 5-interval core collected from 

Otis Creek Reservoir (and analyzed using the same laboratory 

methods) generally were uniform over time, though typically 

smaller (Juracek, 2004). 

Available SQGs allowed for the assessment of sediment 

quality with respect to eight trace elements. Silver was not 

detected in the bottom sediment of Fall River Lake. Cadmium, 

copper, and lead concentrations were less than the respective 

threshold-effects guidelines. All or most arsenic, chromium, 

nickel, and zinc concentrations were greater than the respective threshold-effects guidelines. No trace element concentrations exceeded the probable-effects guidelines (tables 3, A3, 

A4, and A5). 
Occurrence of, and Trends in, Selected Chemical Constituents and Diatoms 13

Table 5. Results of trend tests on concentrations of selected constituents in 

bottom-sediment samples collected from Fall River Lake core F–2B, southeast 

Kansas, October 2006. 

[--, not determined]

Constituent Spearman’s rho Trend test at 0.05 level of significance (two-sided p-value)

Nutrients

Total nitrogen 0 no trend (--)

Total phosphorus 0.98 positive trend (0)

Carbon

Carbon, total organic .06 no trend (0.861)

Carbon, total - .34 no trend (0.287)

Trace elements

Aluminum .20 no trend (0.542)

Antimony .14 no trend (0.653)

Arsenic .53 no trend (0.077)

Barium - .47 no trend (0.120)

Beryllium .38 no trend (0.227)

Cadmium .27 no trend (0.397)

Chromium .49 no trend (0.104)

Cobalt .89 positive trend (0.0001)

Copper .43 no trend (0.160)

Iron .83 positive trend (0.0008)

Lead .08 no trend (0.809)

Lithium .34 no trend (0.285)

Manganese .66 positive trend (0.019)

Molybdenum -- --

Nickel .61 positive trend (0.037)

Selenium - .05 no trend (0.874)

Silver -- --

Strontium - .57 no trend (0.053)

Sulfur .05 no trend (0.889)

Tin .42 no trend (0.176)

Thallium -- --

Titanium - .39 no trend (0.208)

Uranium -- --

Vanadium .39 no trend (0.206)

Zinc .32 no trend (0.312)
14 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

Diatoms

At site F–2 in Fall River Lake (fig. 2), 20 different diatom 

species were identified in core F–2B. For 5 of the 12 core 

intervals analyzed, no diatoms were detected. For the remaining seven intervals the number of diatom species identified 

ranged from 1 to 18. Complete information on the occurrence 

and relative abundance of diatom species in each interval is 

provided in table A6 at the back of this report. 

Abundant diatoms were identified only in the top (most 

recent) and bottom (oldest) intervals of the core. In the top 

interval the diatom Aulacoseira granulata was dominant with 

a relative abundance of 60.3 percent. This diatom is indicative of eutrophic conditions (Hall and Smol, 1999; Blais and 

others, 2000; Dixit and others, 2000). Other relatively abundant diatoms in the top interval included Aulacoseira ambigua

(16.8 percent) and Aulacoseira alpigena (16.0 percent) (table 

A6). Aulacoseira ambigua has been recognized as an indicator of either meso-eutrophic or eutrophic conditions (van 

Dam and others, 1994; Blais and others, 2000; Clerk and 

others, 2000). Both Aulacoseira granulata and Aulacoseira 

ambigua typically are found in high nutrient, low light waters 

(Kling, 1998). In contrast, Aulacoseira alpigena is indicative of oligotrophic conditions (van Dam and others, 1994). 

The dominance of Aulacoseira granulata in the top interval 

indicates that conditions at Fall River Lake during the past few 

years were frequently, if not typically, eutrophic. The presence of Aulacoseira alpigena indicates that conditions were 

less eutrophic at times. The remaining 15 species identified in 

the top interval had relative abundances of less than 2 percent 

(table A6). 

Total phosphorus concentration, in milligrams per kilogram (mg/kg)

Core F–2B at site F–2 (fig. 2)

Sediment-core interval, dimensionless (bottom to top of core)

(bottom) 1

2

3

4

5

6

7

9

8

10

11

(top) 12

0 100 200 300 400 500 600 700 800 900

1948

2006

1,000

Figure 4. Variation in total phosphorus concentrations with depth of bottom-sediment samples collected from 

coring site F–2B in Fall River Lake, southeast Kansas, October 2006.
Occurrence of, and Trends in, Selected Chemical Constituents and Diatoms 15

In the bottom interval Aulacoseira granulata again was 

dominant with a relative abundance of 58.5 percent. Aulacoseira alpigena also was relatively abundant (27.5 percent) 

(table A6). Thus, similar to the recent past, it appears that conditions during the early history of Fall River Lake also were 

generally eutrophic with occasionally less eutrophic periods. 

The remaining 11 species identified in the bottom interval had 

relative abundances of less than 5 percent (table A6). 

In the middle of the core, diatoms were sparse and five 

intervals contained no diatoms (table A6). Possible explanations to account for the absence of diatoms in the middle of the 

core include changes in pH, light, temperature, and (or) concentrations of nutrients, trace elements, and pesticides; grazing 

pressure and (or) competition from other aquatic organisms; 

and lack of preservation in the sediment (Stoermer and Smol, 

1999; Cohen, 2003). Because the concentrations of nutrients 

(total nitrogen and total phosphorus) and trace elements generally were uniform with depth in core F–2B (table A3), the 

absence of diatoms does not appear to be related to nutrient or 

trace element concentrations in the sediment. Comprehensive 

historical data on pH, light, temperature, and pesticide concentrations were not available to assess changes over the entire 

life of the reservoir. However, as part of its Lake and Wetland 

Monitoring Program, KDHE sampled the water in Fall River 

Lake one day during the summer approximately every 3 years 

from 1975 to 2004. During that 30-year period, pH consistently ranged from 7.4 to 8.2. Pesticides, when analyzed, were 

not detected (Ed Carney, Kansas Department of Health and 

Environment, written commun., 2007). 

Light limitation caused by turbidity in the water column is a possible explanation for the reduced abundance of 

diatoms in the middle of the sediment core (Bradbury and 

Figure 5. Variation in cesium-137 activity with depth of bottom-sediment samples collected from coring site F–2B 

in Fall River Lake, southeast Kansas, October 2006.

Cesium-137 activity, in picocuries per gram

Sediment-core interval, dimensionless (bottom to top of core)

(bottom) 1

2

3

4

5

6

7

9

8

10

11

(top) 12

0 0.2 0.4 0.6 0.8 1.0 1.2 1.4 1.6 1.8 2.0

Core F–2B at site F–2 (fig. 2)

1948

2006

1963−64
16 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

Van Metre, 1997; Wetzel, 2001). Causes of turbidity include 

sediment delivered by reservoir inflows and wind-induced 

sediment resuspension. Fall River Lake has been characterized 

as typically turbid and the resulting light limitation is believed 

to limit primary production in the reservoir despite plentiful 

supplies of nitrogen and phosphorus in the water (U.S. Army 

Corps of Engineers, 1999). Measurements made by KDHE 

about once every 3 years from 1975 to 2004 indicated a range 

in turbidity of only 12 to 77 NTU (nephelometric turbidity 

units) (Ed Carney, Kansas Department of Health and Environment, written commun., 2007). Given the sampling frequency, 

the representativeness of the turbidity data is uncertain. 

Because diatoms generally are ubiquitous in the environment, it seems unlikely that they would be completely absent 

in the reservoir for years at a time. Thus, another possibility 

that could account for the absence of diatoms in the sediment is that the diatoms were present in the reservoir but not 

preserved. In other words, the diatoms may have disappeared 

because of dissolution in the water column and (or) postdepositionally in the sediment (Battarbee and others, 2001; Cohen, 

2003). Pronounced evidence of postdepositional dissolution 

(for example, diatom valves with corroded edges) was not 

observed in the sediment samples analyzed (Yangdong Pan, 

Portland State University, written commun., 2007). Kling 

(1998), however, stated that a core consisting of alternating 

intervals of relative abundance and absence of diatoms was 

evidence in support of dissolution. 

To further investigate historical conditions given the 

absence of diatoms in the middle of the core, the top interval 

(relatively abundant diatoms), a middle interval (no diatoms), 

and the bottom interval (relatively abundant diatoms) were 

analyzed for the presence of cyanobacteria (blue-green algae). 

In all three intervals, similar abundances of the cyanobacteria 

Anabaena were detected (Ann St. Amand, PhycoTech, written commun., 2007). The abundance of Anabaena in the top, 

middle, and bottom intervals was about 14,200, 13,400, and 

13,600 per gram of sediment, respectively. Anabaena, and 

cyanobacteria in general, are indicative of eutrophic conditions (Wetzel, 2001). Thus, the presence of Anabaena in all 

three intervals provides evidence for the existence of eutrophic 

conditions during the early, middle, and recent history of the 

reservoir. Given the abundance of Anabaena, and the presence 

of other cyanobacteria, it is likely that algal blooms occur in 

the reservoir that may result in taste-and-odor compounds and 

possibly algal toxins. 

Chlorophyll-a is used as a surrogate indicator of eutrophication (Wetzel, 2001; Wehr and Sheath, 2003). From 1975 to 

2004, measurements made by KDHE about once every 3 years 

indicated that chlorophyll-a concentrations in the water ranged 

from about 4 to 36 parts per billion (ppb) and typically were 

less than 13 ppb. KDHE classifies the trophic condition of a 

lake using the following chlorophyll-a criteria: oligotrophic 

(0 to 2.4 ppb), mesotrophic (2.4 to 7.2 ppb), slightly eutrophic 

(7.2 to 12 ppb), eutrophic (12 to 20 ppb), very eutrophic (20 to 

30 ppb), and hypereutrophic (greater than 30 ppb) (Ed Carney, 

Kansas Department of Health and Environment, written commun., 2007). Based on these criteria, Fall River Lake generally 

varied from mesotrophic to eutrophic from 1975 to 2004. Fall 

River Lake also was classified as eutrophic based on the total 

phosphorus content in the water (U.S. Army Corps of Engineers, 1999; Wetzel, 2001). From 1981 to 2004, measurements 

made by KDHE about once every 3 years indicated that total 

phosphorus concentrations in the water ranged from 0.04 to 

0.15 milligrams per liter (Ed Carney, Kansas Department of 

Health and Environment, written commun., 2007). Together, 

the diatom and cyanobacteria evidence, combined with the 

available water-quality data, indicated that Fall River Lake 

likely has been eutrophic throughout much of its history.

Summary and Conclusions

A 2-year study by the U.S. Geological Survey, in cooperation with the Kansas Department of Health and Environment, was begun in 2006 to investigate sedimentation in, and 

the occurrence of selected chemical constituents and diatoms 

in bottom sediment of, Fall River Lake, southeast Kansas, for 

1948 through 2006. The study used a combination of available 

bathymetric-survey information and bottom-sediment coring 

completed in 2006. The major results of this study are listed 

below:

1. The total estimated volume and mass of bottom sediment 

in the original conservation pool of Fall River Lake was 

470 million ft3 and 18.8 billion lb, respectively. 

2. The estimated sediment volume occupied about 36 

percent of the original conservation-pool, water-storage 

capacity of Fall River Lake. 

3. Mean annual net sediment deposition in the original conservation pool of Fall River Lake was estimated to be 324 

million lb/yr.

4. Mean annual net sediment yield from the Fall River Lake 

Basin was estimated to be 585,000 (lb/mi2)/yr. 

5. Total nitrogen in the bottom sediment of Fall River 

Lake was uniform over time with a concentration of 

2,000 mg/kg. 

6. The mean annual net load and yield of total nitrogen 

deposited in the bottom sediment of Fall River Lake 

was estimated to be 648,000 lb/yr and 1,170 (lb/mi2)/yr, 

respectively. 

7. Total phosphorus in the bottom sediment of Fall River 

Lake generally was uniform over time with a median 

concentration of 820 mg/kg. 

8. The mean annual net load and yield of total phosphorus 

deposited in the bottom sediment of Fall River 

Lake was estimated to be 267,000 lb/yr and 480 

(lb/mi2)/yr, respectively. 
References Cited 17

9. Trace element concentrations in the bottom sediment of 

Fall River Lake generally were uniform over time. 

10. Arsenic, chromium, nickel, and zinc concentrations in the 

bottom sediment of Fall River Lake typically exceeded 

the threshold-effects guidelines, which represent the 

concentrations above which toxic biological effects 

occasionally occur. 

11. Trace element concentrations did not exceed the probableeffects guidelines (available for eight trace elements), 

which represent the concentrations above which toxic 

biological effects usually or frequently occur. 

12. Occurrence of the diatom Aulacoseira granulata and the 

cyanobacteria Anabaena in the bottom sediment of Fall 

River Lake, combined with historical water-quality data, 

indicated that Fall River Lake likely has been eutrophic 

throughout much of its history. 

13. Diatoms were absent in the middle part of a Fall River 

Lake sediment core possibly as a result of lack of preservation caused by dissolution. 

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Supplemental Information
22 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

Table A1. Latitude and longitude coordinates, water depth, estimated sediment thickness, length of recovered core, and 

estimated recovery percentage for bottom-sediment coring sites at Fall River Lake, southeast Kansas.

[--, not determined]

Coring site number (fig. 2)Date cored 

(month/day/ 

year)

Latitude 

(decimal 

degrees)

Longitude 

(decimal 

degrees)

Water 

depth 

(feet)

Estimated 

penetration 

depth (feet)

Length of recovered core (feet)Estimated recovery percentage1

F–2A 10/24/06 37.65408 96.06714 20.5 -- 7.4 --

F–2B 10/24/06 37.65422 96.06717 20.5 10.0 6.6 66

F–4 10/24/06 37.66775 96.08036 20.5 -- 7.1 --

F–5 10/24/06 37.66386 96.09533 9.0 -- 6.6 --

1

Recovery percentage could not be estimated for cores that did not penetrate to the original (pre-reservoir) land-surface material. 

Table A2. Estimated bulk density of bottom sediment at coring sites in Fall 

River Lake, southeast Kansas.

[lb/ft3, pounds per cubic foot; --, not applicable]

Coring site number (fig. 2)Depth interval 

(inches)

Estimated bulk 

density (lb/ft3)

Computed mean 

bulk density1

(lb/ft3)

F–2A 0–12.3 26.9 --

12.3–24.6 28.3 --

24.6–36.9 32.2 --

36.9–49.2 34.1 --

49.2–61.5 33.7 --

61.5–73.8 38.4 --

73.8–86.0 38.7 --

33.2

F–4 0–12 30.9 --

12–24 35.8 --

24–36 35.1 --

36–48 39.1 --

48–60 42.0 --

60–72 47.1 --

72–84 43.5 --

39.1

F–5 0–12.3 44.4 --

12.3–24.6 43.4 --

24.6–36.9 44.0 --

36.9–49.2 47.8 --

49.2–61.5 53.8 --

61.5–74.0 53.6 --

47.8

1

Mean bulk density computed as the average of the bulk densities for the individual depth 

intervals for each core.
Supplemental Information 23

Table A3. Percentage of silt and clay and constituent concentrations for bottom-sediment samples collected from 

core F–2B at coring site F–2 (fig. 2) in Fall River Lake, southeast Kansas, October 2006. 

[Shading indicates concentration greater than threshold-effects guideline listed in table 3. >, greater than; mg/kg, milligrams per kilogram; %, percent dry weight; <, less than]

Constituent and unit of 

measurement

Constituent concentration

Interval 1 (bottom of 

core)

Interval 2 Interval 3 Interval 4

Percentage of silt and clay >99 >99 >99 >99

Nutrients

Total nitrogen, mg/kg 2,000 2,000 2,000 2,000

Total phosphorus, mg/kg 750 730 800 810

Carbon

Carbon (total organic), % 1.8 1.7 1.7 1.6

Carbon (total), % 2.3 2.3 2.3 2.3

Trace elements

Aluminum, % 9.6 9.1 10.0 9.9

Antimony, mg/kg .7 .8 .7 .7

Arsenic, mg/kg 12 12 13 13

Barium, mg/kg 620 620 610 610

Beryllium, mg/kg 2.9 2.8 3.0 3.0

Cadmium, mg/kg .4 .5 .5 .4

Chromium, mg/kg 99 95 100 100

Cobalt, mg/kg 16 16 17 17

Copper, mg/kg 25 24 26 25

Iron, % 4.6 4.3 4.9 4.9

Lead, mg/kg 29 28 31 30

Lithium, mg/kg 69 65 74 72

Manganese, mg/kg 920 860 890 1,100

Molybdenum, mg/kg <1 <1 <1 <1

Nickel, mg/kg 42 40 44 44

Selenium, mg/kg .7 .7 .7 .6

Silver, mg/kg <.5 <.5 <.5 <.5

Strontium, mg/kg 190 190 190 200

Sulfur, % .08 .09 .06 .06

Thallium, mg/kg <50 <50 <50 <50

Tin, mg/kg 4 3 4 4

Titanium, % .48 .50 .48 .48

Uranium, mg/kg <50 <50 <50 <50

Vanadium, mg/kg 130 120 130 130

Zinc, mg/kg 130 120 130 130
24 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

Table A3. Percentage of silt and clay and constituent concentrations for bottom-sediment samples collected from 

core F–2B at coring site F–2 (fig. 2) in Fall River Lake, southeast Kansas, October 2006.—Continued

[Shading indicates concentration greater than threshold-effects guideline listed in table 3. >, greater than; mg/kg, milligrams per kilogram; %, percent dry weight; <, less than]

Constituent and unit of 

measurement

Constituent concentration

Interval 5 Interval 6 Interval 7 Interval 8

Percentage of silt and clay >99 >99 >99 >99

Nutrients

Total nitrogen, mg/kg 2,000 2,000 2,000 2,000

Total phosphorus, mg/kg 820 820 830 840

Carbon

Carbon (total organic), % 1.6 1.6 1.6 1.7

Carbon (total), % 2.3 2.1 2.2 2.2

Trace elements

Aluminum, % 10.0 9.9 10.0 9.9

Antimony, mg/kg .8 .7 .8 .8

Arsenic, mg/kg 13 13 14 13

Barium, mg/kg 610 610 610 620

Beryllium, mg/kg 3.1 3.1 3.1 3.0

Cadmium, mg/kg .4 .4 .4 .4

Chromium, mg/kg 100 100 100 99

Cobalt, mg/kg 17 17 17 17

Copper, mg/kg 26 26 26 27

Iron, % 5.0 5.0 5.0 5.0

Lead, mg/kg 31 32 33 32

Lithium, mg/kg 73 73 74 73

Manganese, mg/kg 970 1,000 1,100 1,100

Molybdenum, mg/kg <1 <1 <1 <1

Nickel, mg/kg 45 45 45 44

Selenium, mg/kg .6 .6 .7 .7

Silver, mg/kg <.5 <.5 <.5 <.5

Strontium, mg/kg 200 200 180 190

Sulfur, % .06 .06 .06 .07

Thallium, mg/kg <50 <50 <50 <50

Tin, mg/kg 4 3 4 4

Titanium, % .49 .49 .48 .48

Uranium, mg/kg <50 <50 <50 <50

Vanadium, mg/kg 130 130 130 130

Zinc, mg/kg 140 130 140 140
Supplemental Information 25

Table A3. Percentage of silt and clay and constituent concentrations for bottom-sediment samples collected from 

core F–2B at coring site F–2 (fig. 2) in Fall River Lake, southeast Kansas, October 2006.—Continued

[Shading indicates concentration greater than threshold-effects guideline listed in table 3. >, greater than; mg/kg, milligrams per kilogram; %, percent dry weight; <, less than]

Constituent and unit of 

measurement

Constituent concentration

Interval 9 Interval 10 Interval 11 Interval 12 (top of 

core)

Percentage of silt and clay >99 >99 >99 >99

Nutrients

Total nitrogen, mg/kg 2,000 2,000 2,000 2,000

Total phosphorus, mg/kg 830 850 860 910

Carbon

Carbon (total organic), % 1.6 1.7 1.7 1.8

Carbon (total), % 2.1 2.2 2.3 2.3

Trace elements

Aluminum, % 9.9 10.0 9.8 9.9

Antimony, mg/kg .8 .7 .8 .7

Arsenic, mg/kg 13 13 13 13

Barium, mg/kg 610 610 610 610

Beryllium, mg/kg 3.0 3.1 3.0 3.0

Cadmium, mg/kg .4 .5 .5 .5

Chromium, mg/kg 100 100 100 100

Cobalt, mg/kg 17 18 18 18

Copper, mg/kg 26 26 25 26

Iron, % 5.0 5.0 5.0 5.0

Lead, mg/kg 31 30 29 29

Lithium, mg/kg 73 74 71 73

Manganese, mg/kg 970 1,000 1,100 1,100

Molybdenum, mg/kg <1 <1 <2 <1

Nickel, mg/kg 45 45 44 45

Selenium, mg/kg .7 .7 .7 .6

Silver, mg/kg <.5 <.5 <1.0 <.5

Strontium, mg/kg 180 190 180 180

Sulfur, % .06 .08 .08 .07

Thallium, mg/kg <50 <50 <100 <50

Tin, mg/kg 3 5 4 5

Titanium, % .48 .48 .48 .48

Uranium, mg/kg <50 <50 <100 <50

Vanadium, mg/kg 130 130 130 130

Zinc, mg/kg 130 140 130 130
26 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

Table A4. Percentage of silt and clay and constituent concentrations for bottom-sediment 

samples collected from coring site F–4 (fig. 2) in Fall River Lake, southeast Kansas, 

October 2006.

[Shading indicates concentration greater than threshold-effects guideline listed in table 3. >, greater than; 

mg/kg, milligrams per kilogram; %, percent dry weight; <, less than]

Constituent and unit of 

measurement

Constituent concentration

Interval 1 (bottom of 

core)

Interval 2 Interval 3 (top of 

core)

Percentage of silt and clay >99 >99 >99

Nutrients

Total nitrogen, mg/kg 2,000 2,000 2,000

Total phosphorus, mg/kg 780 800 850

Carbon

Carbon (total organic), % 1.6 1.6 1.7

Carbon (total), % 2.2 2.2 2.4

Trace elements

Aluminum, % 9.3 9.3 9.2

Antimony, mg/kg .7 .7 .7

Arsenic, mg/kg 12 12 12

Barium, mg/kg 610 600 610

Beryllium, mg/kg 2.8 2.9 2.9

Cadmium, mg/kg .4 .4 .4

Chromium, mg/kg 94 95 95

Cobalt, mg/kg 16 17 18

Copper, mg/kg 25 25 25

Iron, % 4.6 4.6 4.6

Lead, mg/kg 30 29 28

Lithium, mg/kg 66 66 65

Manganese, mg/kg 1,000 1,000 1,200

Molybdenum, mg/kg <1 <1 <1

Nickel, mg/kg 40 42 41

Selenium, mg/kg .6 .6 .6

Silver, mg/kg <.5 <.5 <.5

Strontium, mg/kg 200 190 190

Sulfur, % .05 .06 .06

Thallium, mg/kg <50 <50 <50

Tin, mg/kg 3 5 3

Titanium, % .47 .48 .48

Uranium, mg/kg <50 <50 <50

Vanadium, mg/kg 120 120 120

Zinc, mg/kg 130 120 130
Supplemental Information 27

Table A5. Percentage of silt and clay and constituent concentrations for bottomsediment samples collected from coring site F–5 (fig. 2) in Fall River Lake, southeast 

Kansas, October 2006. 

[Shading indicates concentration greater than threshold-effects guideline listed in table 3. >, greater 

than; mg/kg, milligrams per kilogram; %, percent dry weight; <, less than]

Constituent and unit of 

measurement

Constituent concentration

Interval 1 (bottom 

of core)

Interval 2 Interval 3 (top of 

core)

Percentage of silt and clay >99 >99 >99

Nutrients

Total nitrogen, mg/kg 2,000 2,000 2,000

Total phosphorus, mg/kg 740 750 730

Carbon

Carbon (total organic), % 1.5 1.6 1.5

Carbon (total), % 2.3 2.5 2.5

Trace elements

Aluminum, % 8.2 8.2 7.6

Antimony, mg/kg .6 .7 .6

Arsenic, mg/kg 9.6 9.5 8.4

Barium, mg/kg 590 580 560

Beryllium, mg/kg 2.6 2.6 2.4

Cadmium, mg/kg .4 .4 .4

Chromium, mg/kg 85 85 79

Cobalt, mg/kg 16 16 15

Copper, mg/kg 23 23 22

Iron, % 4.0 4.0 3.8

Lead, mg/kg 29 27 25

Lithium, mg/kg 56 57 54

Manganese, mg/kg 890 850 800

Molybdenum, mg/kg <1 <1 <1

Nickel, mg/kg 37 37 34

Selenium, mg/kg .6 .6 .5

Silver, mg/kg <.5 <.5 <.5

Strontium, mg/kg 190 190 190

Sulfur, % .05 .06 .07

Thallium, mg/kg <50 <50 <50

Tin, mg/kg 4 4 2

Titanium, % .50 .48 .47

Uranium, mg/kg <50 <50 <50

Vanadium, mg/kg 110 110 100

Zinc, mg/kg 110 110 100
28 Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006

Table A6. Diatom species, number of valves counted, and relative percentage abundance in bottomsediment samples collected from core F–2B at coring site F–2 (fig. 2) in Fall River Lake, southeast 

Kansas, October 2006. 

Depth of sample 

(inches)

Species Number of valves 

counted

Relative percentage 

abundance

0–6.3 Aulacoseira alpigena 96 16.0

Aulacoseira ambigua 101 16.8

Aulacoseira granulata 362 60.3

Cyclotella meneghiniana 2 .3

Cyclotella stelligera 6 1.0

Diploneis oblongella 2 .3

Fragilaria vaucheriae 1 .2

Gomphonema drutelingense 2 .3

Navicula capitatoradiata 1 .2

Navicula reichardtiana 1 .2

Navicula rostellata 3 .5

Nitzschia gracilis 2 .3

Nitzschia modesta 2 .3

Nitzschia recta 2 .3

Stephanodiscus hantzschii 2 .3

Stephanodiscus medius 9 1.5

Stephanodiscus niagarae 5 .8

Synedra delicatissima var. 

angustissima

1 .2

Total 600 1100

6.3–12.7 Aulacoseira alpigena 12 46.2

Aulacoseira ambigua 2 7.7

Aulacoseira granulata 7 26.9

Gomphonema drutelingense 2 7.7

Gyrosigma acuminatum 2 7.7

Stephanodiscus niagarae 1 3.8

Total 26 1100

12.7–19.0 Aulacoseira granulata 1 100

Total 1 100

19.0–25.3 Aulacoseira granulata 1 100

Total 1 100
Supplemental Information 29

Table A6. Diatom species, number of valves counted, and relative percentage abundance in bottomsediment samples collected from core F–2B at coring site F–2 (fig. 2) in Fall River Lake, southeast 

Kansas, October 2006.—Continued

Depth of sample 

(inches)

Species Number of valves 

counted

Relative percentage 

abundance

25.3–31.7 Aulacoseira granulata 2 100

Total 2 100

31.7–38.0 No diatoms 0 0

Total 0 0

38.0–44.3 No diatoms 0 0

Total 0 0

44.3–50.7 No diatoms 0 0

Total 0 0

50.7–57.0 No diatoms 0 0

Total 0 0

57.0–63.3 No diatoms 0 0

Total 0 0

63.3–69.7 Aulacoseira granulata 1 100

Total 1 100

69.7–76.0 Aulacoseira alpigena 142 27.5

Aulacoseira ambigua 25 4.8

Aulacoseira granulata 302 58.5

Cyclotella meneghiniana 5 1.0

Cyclotella stelligera 10 1.9

Cymbella tumida 1 .2

Diploneis oblongella 1 .2

Fragilaria vaucheriae 2 .4

Gyrosigma acuminatum 2 .4

Navicula capitatoradiata 3 .6

Nitzschia recta 2 .4

Stephanodiscus medius 20 3.9

Synedra delicatissima var. 

angustissima

1 .2

Total 516 1100

1

Number rounded to account for rounding errors in the individual species percentages.
Publishing support provided by:

Rolla Publishing Service Center

For more information concerning this publication, contact:

Director, USGS Kansas Water Science Center

4821 Quail Crest Place

Lawrence, KS 66049

(785) 842-9909

Or visit the Kansas Water Science Center Web site at:

http://ks.water.usgs.gov
Back cover. Map showing land use within the Fall River Lake drainage basin (fig. 1 in this report). Land use data from Kansas 

 Applied Remote Sensing Program, Data Access and Support Center, 1993.
Otis Creek

Reservoir

West

Branch

Fall

River

Ivanpah

Creek

Hog

Cre

ek

Cat Creek Battle Creek

Otis Creek

Oleson

Creek

East Branch Fall River Swing

Creek

Silver Creek Spring Creek

Burnt

Creek

Kitty Creek

Spring Creek

Fall

River

Honey

Creek

Otter

Creek

North

Branch

Otter

Creek South

Branch

Otter

Creek

Watson Branch

Tadpole

Creek

Ca

s

n

e

r

Cre

e

k

Badger Creek

Van Horn Branch

Durham Creek

Fa

ll

River

Climax

Fall River

Coyville

Eureka

Hamilton

Virgil

Toronto

New Albany

Fredonia

Yates Center

Severy

Boundary of

Fall River Lake

drainage basin 

07167500

07167000

07169500

ELK COUNTY

WILSON COUNTY

BUTLER

COUNTY

GREENWOOD COUNTY

WOODSON COUNTY

 CHASE COUNTY

 COFFEY COUNTY

Fall River

Lake

Juracek—Sedimentation and Occurrence of Selected Chemical Constituents and Diatoms, Fall River Lake, Kansas, 1948–2006—Scientific Investigations Report 2008–5019

Printed on recycled paper