U.S. Department of the Interior

U.S. Geological Survey

Data Series 915

Prepared in cooperation with the City of Independence, Missouri, 

Water Pollution Control Department

Hydrological, Water-Quality, and Ecological Data for 

Streams in Independence, Missouri, June 2005 through 

September 2013
U.S. Geological Survey scientist 

conducting macroinvertebrate 

sampling at Rock Creek at Kentucky Road, September 12, 2012. 

Photograph by Shelley Niesen, U.S. 

Geological Survey.

Continuous water-quality monitor in use at Rock 

Creek at Kentucky Road, September 12, 2012. Photograph by Shelley Niesen, U.S. Geological Survey.

Front cover background photograph: Little Blue River at Lee’s 

Summit Road, September 11, 2012. Photograph by Heather Krempa, 

U.S. Geological Survey.

Back cover background photograph: Little Blue River at Lee’s 

Summit Road, September 11, 2012. Photograph by Heather Krempa, 

U.S. Geological Survey.
Hydrological, Water-Quality, and 

Ecological Data for Streams in 

Independence, Missouri, June 2005 

through September 2013

By Shelley L. Niesen and Eric D. Christensen

Prepared in cooperation with the City of Independence, Missouri, 

Water Pollution Control Department

Data Series 915

U.S. Department of the Interior

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

SALLY JEWELL, Secretary

U.S. Geological Survey

Suzette M. Kimball, Acting Director

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

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Suggested citation:

Niesen, S.L., and Christensen, E.D., 2015, Hydrological, water-quality, and ecological data for streams in Independence, Missouri, June 2005 through September 2013: U.S. Geological Survey Data Series 915, 80 p., http://dx.doi.

org/10.3133/ds915.

ISSN: 2327-638X (online)
iii

Acknowledgments

The authors would like to express their appreciation to Dick Champion, Director; Dorris Bender; 

and Larry White of the Independence Water Pollution Control Department for their ongoing 

cooperative support of the U.S. Geological Survey studies in Independence, Missouri. Assistance from Independence Water Pollution Control employees was essential for completion of 

dry-weather screening. Dr. Andrew Carson of the University of Missouri, Rebecca Bushon, Erin 

Stelzer, and Amie Brady of the U.S. Geological Survey Ohio Water Microbiology Laboratory 

provided helpful reviews and technical advice regarding microbial source tracking methods and 

results. 
iv

Contents

Acknowledgments........................................................................................................................................iii

Conversion Factors......................................................................................................................................vii

Abbreviations.................................................................................................................................................ix

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

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

Purpose and Scope ..............................................................................................................................1

Description of Study Area ...................................................................................................................2

Previous Investigations........................................................................................................................5

Methods ..........................................................................................................................................................9

Streamflow and Continuous Water-Quality Monitoring.................................................................9

Water-Quality Sample Collection and Procedures .......................................................................10

Laboratory and Data Analysis ..........................................................................................................13

Quality Control and Quality Assurance ...........................................................................................16

Water-Quality Data......................................................................................................................................25

Continuous Streamflow and Water-Quality Measurements .......................................................25

Instantaneous Base-Flow Water Quality........................................................................................28

Instantaneous Stormflow Water Quality.........................................................................................29

Select Inorganic Constituents ..........................................................................................................29

Nutrients...............................................................................................................................................31

Total Recoverable Metals..................................................................................................................38

Common Organic Micro-Constituents and Pesticides in Streambed Sediment and Surface 

Water.......................................................................................................................................39

Fecal Indicator Bacteria, Microbial Source Tracking, and Suspended Sediment .................40

Dry-Weather Screening.....................................................................................................................49

Ecological Data ............................................................................................................................................50

Macroinvertebrate Surveys..............................................................................................................50

Habitat Assessments..........................................................................................................................50

Summary........................................................................................................................................................70

References Cited..........................................................................................................................................72

Appendixes 1 and 2......................................................................................................................................79

Figures

1. Map showing the Little Blue River Basin, sampling sites, study area location, and 

political boundaries for Independence, Missouri, and surrounding cities.........................3

2. Map showing land use/land cover in the Little Blue River Basin and adjacent basins 

within Independence, Missouri..................................................................................................4

3. Graphs showing average monthly temperatures and precipitation at Independence, 

Missouri, for June 2005 through September 2013 compared to the 27-year average 

from October 1986 through September 2013............................................................................6

4. Graph showng annual precipitation for Independence, Missouri, water years 

(October 1 through September 30) 2005 through 2013............................................................7
v

5. Photograph showing continuous water-quality monitor with (clockwise from upper 

left) turbidity, optical dissolved oxygen, pH, and combined specific conductance and 

water temperature sensors ......................................................................................................10

6. Graphs showing quality-assurance data for nutrients and select constituents in 

field replicate or laboratory duplicate sample pairs.............................................................18

7. Graphs showing quality-assurance data for fecal indicator bacteria in field 

replicate or laboratory duplicate sample pairs .....................................................................21

8. Graphs showing quality-assurance data for dry-weather screening samples in field 

replicate or laboratory duplicate sample pairs .....................................................................24

9. Graph showing monthly average streamflow by site, June 2005 through September 

2013 ...............................................................................................................................................25

10. Graph showing percentage deviations from the 27-year monthly average 

streamflow at Little Blue River near Lake City, Missouri, compared with the 

27-year monthly average precipitation measured and recorded at Independence, 

Missouri, June 2005 through September 2013.......................................................................26

11. Boxplots showing computed daily average values of dissolved oxygen, pH, specific 

conductance, water temperature, and turbidity at continuous water-quality 

monitoring sites in Independence, Missouri..........................................................................27

12. Graphs showing frequency of exceedance of daily average dissolved oxygen, pH, specific conductance, water temperature, and turbidity at sampling sites equipped with 

continuous water-quality monitors in Independence, Missouri. Period of record 

at individual sites varies ............................................................................................................30

13. Maps showing dry-weather screening sampling sites and locations of constituent 

detections for selected stream basins in Independence, Missouri, water years 2006 

through 2013 ................................................................................................................................56

14. Boxplots showing dry-weather screening constituent concentrations in streams in 

Independence, Missouri, water years 2006 through 2013 ...................................................65

15. Boxplots showing macroinvertebrate taxa and individuals enumerated in samples from 

all sites, March 2007 through March 2013..............................................................................66

Tables

1. Land use in the City of Independence and basins wholly or partially within 

Independence city boundaries...................................................................................................5

2. Sampling sites in Independence, Missouri, biologic sampling reference sites, 

and type of hydrologic, water-quality, and ecologic data collected, June 2005 

through September 2013..............................................................................................................8

3. Criteria for aquatic-life support categories for riffle habitats for the Missouri 

tributaries between the Blue and Lamine Rivers ecological drainage unit......................13

4. Summary of quality-control (replicate and duplicate) sample results for selected 

constituents in base-flow and stormflow water-quality samples at all Independence 

sites, June 2006 through September 2013 ..............................................................................17

5. Summary of detections of selected water-quality constituents and common 

organic micro-constituents in blank water samples at all Independence sites, 

June 2005 through September 2013.........................................................................................20

6. Average blank sample concentrations for microbial source tracking samples by 

initial sample collection date and batch processing data group .......................................22

7. Microbial source tracking replicate sample pairs................................................................23
vi

8. Macroinvertebrate taxonomy, revised taxa names, and pollution tolerance values 

for taxa identified in samples, March 2007 through March 2013.................................... Link

9. Summary of physical properties, nutrients, fecal indicator bacteria, and selected 

inorganic-constituent concentrations in base-flow samples by site, June 2005 

through September 2013........................................................................................................ Link

10. Summary of physical properties, nutrients, fecal indicator bacteria, and selected 

inorganic constituent concentrations in stormflow samples by site, June 2005 

through September 2013........................................................................................................ Link

11. Regression models for estimating annual loads, flow-weighted concentrations, 

and densities of selected sampled water-quality constituents..........................................32

12. Categories of common organic micro-constituents detected in urban streams.............39

13. Summary of constituent concentrations by category of total common organic 

micro-constituents by site in base-flow samples, June 2006 through September 

2013 ...............................................................................................................................................41

14. Summary of constituent concentrations by category of total common organic 

micro-constituents by site in stormflow samples, June 2005 through September 

2013 ...............................................................................................................................................44

15. Pesticide constituents analyzed in streambed sediment and surface-water 

samples ........................................................................................................................................47

16. Summary of selected pesticides detected in streambed sediment samples during base 

flow at all Independence sites, July 2010 through July 2013 ..............................................48

17. Presumptive host sources of Escherichia coli in samples collected May through 

October 2007................................................................................................................................49

18. Microbial source tracking marker concentrations for human and animal fecal 

source samples...........................................................................................................................51

19. Microbial source tracking samples by site, season, and streamflow condition ......... Link

20. Summary of dry-weather screening constituent detections in streams in 

Independence, Missouri, water years 2006 through 2013 ..................................................54

21. Macroinvertebrate taxa and individuals enumerated in samples from all sites, 

March 2007 through March 2013 ......................................................................................... Link

22. Habitat scores, dissolved oxygen, pH, specific conductance, water temperature, 

macroinvertebrate metrics used in the stream condition index, and aquatic-life 

support status for samples collected March 2007 through March 2013...........................67

Appendix 1. Base-flow water-quality sample results for selected physical and chemical 

properties and constituents, June 2006 through September 2013 ................................. Link

Appendix 2. Stormflow water-quality sample results for selected physical and chemical 

properties and constituents, June 2005 through September 2013 ................................. Link
vii

Conversion Factors

Inch/Pound to SI

Multiply By To obtain

Length

inch (in.) 2.54 centimeter (cm)

mile (mi) 1.609 kilometer (km)

Area

square mile (mi2

) 2.590 square kilometer (km2) 

Volume

cubic foot (ft3

) 0.02832 cubic meter (m3) 

Flow rate

cubic foot per second (ft3

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

SI to Inch/Pound

Multiply By To obtain

Length

micron (μm) 0.0000394 inch (in.)

centimeter (cm) 0.3937 inch (in.)

meter (m) 3.281 foot (ft) 

kilometer (km) 0.6214 mile (mi)

Area

square kilometer (km2

) 247.1 acre

square kilometer (km2

) 0.3861 square mile (mi2)

Volume

milliliter (mL) 0.0338 ounce, fluid (oz)

liter (L) 0.2642 gallon (gal)

cubic meter (m3

) 35.31 cubic foot (ft3)

Flow rate

cubic meter per second (m3

/s) 35.31 cubic foot per second (ft3/s)

Mass

gram (g) 0.03527 ounce, avoirdupois (oz)

kilogram (kg) 2.205 pound avoirdupois (lb)

megagram (Mg) 1.102 ton, short (2,000 lb)
viii

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

A water year is the 12-month period from October 1 through September 30 of the following 

year.

Vertical coordinate information is referenced to the North American Vertical Datum of 1988 

(NAVD 88).

Horizontal coordinate information is referenced to the North American Datum of 1983 

(NAD 83).

Specific conductance is given in microsiemens per centimeter at 25 degrees Celsius (μS/cm 

at 25 °C).

Concentrations of chemical constituents in water are given either in milligrams per liter (mg/L) 

or micrograms per liter (μg/L).
ix

Abbreviations

ABS alkyl benzene sulfonate

AllBac general fecal contamination marker

ALS aquatic-life support 

AQL Protection of aquatic life

BacCan dog-associated marker

bdl below detection limit

BMP best management practice

BoBac ruminant-associated marker

BOD5 5-day biochemical oxygen demand

COD chemical oxygen demand

col colonies

CWQM continuous water-quality monitor

CY calendar year

DEET N,N-diethyl-meta-toluamide

DNA deoxyribonucleic acid

dnq detected not quantified

E. coli Escherichia coli

EDL estimated detection limit

EPA U.S. Environmental Protection Agency

EPT Ephemeroptera plus Plecoptera plus Trichoptera

EPTR Ephemeroptera plus Plecoptera plus Trichoptera richness

FIB fecal indicator bacteria

GPS global positioning system

IDAS Invertebrate Data Analysis System

ITIS Integrated Taxonomic Information System

LAS linear alkylate sulfonate

LoD level of detection

LoQ level of quantification

LRL laboratory reporting level

LT-MDL long term method detection limit 

MBI Macroinvertebrate Biotic Index

MDL method detection limit

MDNR Missouri Department of Natural Resources

MPN most probable number

MRL minimum reporting level

MS4 municipal separate storm sewer system

MSCI Missouri stream condition index

MST microbial source tracking

N nitrogen
x

NH3 ammonia

NO2 nitrite

NO3 nitrate

NOAA National Oceanic and Atmospheric Association

NPDES National Pollution Discharge Elimination System

NTU nephelometric turbidity units

NURP Nationwide Urban Runoff Program 

NWIS National Water Information System

NWQL National Water Quality Laboratory

NWS National Weather Service

OMC organic micro-constituent

OWML Ohio Water Microbiology Laboratory

P phosphorus

PAH polyaromatic hydrocarbon

ppm parts per million

PVC polyvinyl chloride

qHF183 human-associated marker

qPCR quantitative polymerase chain reaction

R2 coefficient of determination

rep-PCR repetitive extragenic palindromic polymerase chain reaction

RICH total taxa richness

RTH richest targeted habitat

SCI stream condition index

SHANDIV Shannon Diversity Index

SSC suspended sediment concentration

SWMP stormwater management program

TDS total dissolved solids

USGS U.S. Geological Survey

WPC Water Pollution Control

WWTP wastewater treatment plant

WY water year
Hydrological, Water-Quality, and Ecological Data for 

Streams in Independence, Missouri, June 2005 through 

September 2013

By Shelley L. Niesen and Eric D. Christensen

Abstract 

Water-quality, hydrological, and ecological data collected 

from June 2005 through September 2013 from the Little Blue 

River and smaller streams within the City of Independence, 

Missouri, are presented in this report. These data were collected as a part of an ongoing cooperative study between the 

U.S. Geological Survey and the City of Independence Water 

Pollution Control Department to characterize the water quality 

and ecological condition of Independence streams. The quantities, sources of selected constituents, and processes affecting 

water quality and aquatic life were evaluated to determine the 

resulting ecological condition of streams within Independence. 

Data collected for this study fulfill the municipal separate 

sewer system permit requirements for the City of Independence and can be used to provide a baseline with which city 

managers can determine the effectiveness of current (2014) 

and future best management practices within Independence. 

Continuous streamflow and water-quality data, collected during base flow and stormflow, included physical and chemical 

properties, inorganic constituents, common organic microconstituents, pesticides in streambed sediment and surface 

water, fecal indicator bacteria and microbial source tracking 

data, and suspended sediment. Dissolved oxygen, pH, specific conductance, water temperature, and turbidity data were 

measured continuously at seven sites within Independence. 

Base-flow and stormflow samples were collected at eight 

gaged and two ungaged sites. Fecal sources samples were collected for reference for microbial source tracking, and sewage 

influent samples were collected as additional source samples. 

Dry-weather screening was done on 11 basins within Independence to identify potential contaminant sources to the streams. 

Benthic macroinvertebrate community surveys and habitat 

assessments were done on 10 stream sites and 2 comparison 

sites outside the city. Sampling and laboratory procedures and 

quality-assurance and quality-control methods used in data 

collection for this study are described in this report. 

Introduction 

The U.S. Geological Survey (USGS) and the City of 

Independence, Missouri, Water Pollution Control (WPC) 

Department began a cooperative study in June 2005 to characterize and evaluate the water quality and ecological condition 

of streams within Independence. The quantities and sources of 

pollutants were determined to better understand the processes 

that affect water quality and its effect on aquatic life in Independence streams. Hydrological, water-quality, and ecological data were collected between June 2005 and September 

2013 and compiled and summarized for this report. The data 

collected will assist Independence in fulfilling its National 

Pollution Discharge Elimination System (NPDES) permit 

requirements for the municipal separate storm sewer system 

(MS4). According to the Electronic Code of Federal Regulations (2013), an MS4 is a system of conveyances that include 

man-made channels, pipes, tunnels, and storm drains, as well 

as surface streets, catch basins, curbs, gutters, and ditches 

that discharge into waters of the United States. In order for 

Independence to meet the conditions for its MS4 permit and to 

design effective strategies to reduce contaminant discharges to 

streams, information about the source and nature of contaminants detected in receiving streams is needed. The data presented in this report can be used by Independence to evaluate 

differences between base-flow and stormflow water quality in 

its urban streams, implement its stormwater management program (SWMP), evaluate best management practices (BMPs), 

and establish a baseline by which the effectiveness of current 

(2014) and future BMPs can be measured.

Purpose and Scope

This report presents hydrological, water-quality, and 

ecological data collected by USGS from June 2005 through 

September 2013 as part of an ongoing cooperative study with 

the Independence WPC Department to characterize the waterquality and ecological condition of streams in Independence. 

Summary data presented in this report are based on data collected from June 2005 through December 2008 (Christensen 
2 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

and others, 2010) and data collected from January 2009 

through September 2013. Continuous streamflow was measured at eight sites and dissolved oxygen, pH, specific conductance, water temperature, and turbidity data were collected 

at seven sites in the study area equipped with streamgages 

and continuous water-quality monitors (CWQMs). Total 

dissolved solids ([TDS]; referred to in previous publications 

as dissolved residue on evaporation at 180 degrees Celsius 

[°C]), selected major ions, nutrients, metals, common organic 

micro-constituents (OMCs), pesticides in streambed sediment 

and surface water, fecal indicator bacteria (FIB; Escherichia 

Coli [E. Coli], fecal coliform, total coliform), microbial source 

tracking (MST), and suspended sediment concentration (SSC) 

data for base-flow and stormflow samples are presented. 

Estimated annual loads and flow-weighted concentrations of 

selected constituents are listed. Results for analyses of samples 

collected during dry-weather screening are summarized. Benthic macroinvertebrate community survey results and habitat 

assessments also are presented. Sampling, analytical, and 

quality-control and quality-assurance methods used in data 

collection and processing are described.

Description of Study Area

Independence is located to the east of Kansas City in 

Jackson County (fig.1). The study area covers 203 square 

kilometers (km2) within the boundaries of the city limits of 

Independence. The population of Independence in 2012 was 

117,270 (U.S. Census Bureau, 2014), yielding a population 

density of about 578 people per square kilometer. There were 

53,834 housing units within Independence in 2010, an increase 

of 7.1 percent from 2006 (U.S. Census Bureau, 2014). 

The streams in the twelve basins that cover most of 

Independence flow north to the Missouri River (fig. 1). About 

two-thirds of the city is drained by the Little Blue River and 

its tributaries. Of the total area of the Little Blue River Basin 

(585 km2, fig. 1), about 168 km2, or roughly 29 percent, is 

within Independence. Upstream conditions in the Little Blue 

River Basin affect downstream hydrologic and water-quality 

conditions in the city.

Streamflow in the Little Blue River is affected by reservoirs at Longview Lake on the main stem of the Little Blue 

River, and Prairie Lee Lake, Lake Jacomo, and Blue Springs 

Lake on the East Fork of the Little Blue River (fig. 1). Blue 

Springs Lake and Longview Lake reservoirs are upstream 

from Independence on the Little Blue River and affect base 

flow. Low-flow releases from Longview Lake are maintained 

at a minimum of about seven cubic feet per second (ft3

/s), but 

low-flow releases are not maintained for Blue Springs Lake. 

The dams on the East Fork of the Little Blue River were 

constructed in 1936 (Prairie Lee Lake; Heimann, 1995) and 

1986 (Blue Springs Lake; Rouse, 2004), whereas the dam on 

the Little Blue River (Longview Lake) was completed in 1985 

(U.S. Army Corps of Engineers, 2014). About one-half, or 

292 km2, of the drainage area of the Little Blue River Basin is 

regulated by these reservoirs. 

Some of the streams in Independence have stream classifications as designated by the State of Missouri. The Little 

Blue River is classified by the State of Missouri as a Class 

P (perennial) stream suitable for whole-body contact and 

secondary contact recreation (Missouri Department of Natural 

Resources, 2014a). The East Fork of the Little Blue River and 

Fire Prairie Creek are also Class P. Burr Oak Creek is a Class 

C stream, meaning it has perennial pools that may cease flow 

during periods of drought. The remaining streams in Independence are currently (2014) unclassified. Within Independence, 

the streams are mostly channelized. The Little Blue River also 

is listed in the Missouri Code of State Regulations (10 CSR 

20-7) as a metropolitan no discharge stream (Missouri Department of Natural Resources, 2014a).

Land use within the Independence city limits is a mix of 

developed (residential, commercial, industrial) and undeveloped (primarily agricultural, grassland, or forest, fig. 2). The 

western part of Independence is primarily urbanized, whereas 

the eastern and northern parts of the city are characterized by 

large tracts of undeveloped land, including forests, grasslands, 

and croplands, with some new residential construction on 

what had previously been vacant and agricultural-zoned land. 

Adair Creek (table 1; fig. 2) had the highest percentage 

(90.5 percent) of developed land (including open/low intensity 

and medium/high intensity land), whereas Fire Prairie Creek 

had the highest percentage (87.9 percent) of undeveloped land 

(including grassland/cultivated crops, mixed forest, water, 

wetlands, and barren land).

The 27-year monthly averages for temperature and 

precipitation in the study area indicate that July is typically 

the warmest month of the year and June is the wettest month 

(fig. 3). The 27-year comparison period was chosen because it 

represents the period since construction was completed for the 

last reservoir to regulate flow in the Little Blue River Basin. 

The average monthly temperatures during the study period 

from June 2005 to September 2013 were generally near or 

above the 27-year monthly averages (fig. 3). The late winter 

and spring months (February, March, April, and May) as well 

as September and December for the entire study period were 

wetter than the 27-year monthly averages for those months. 

The summer months of June, July, and August, and the fall 

months of October and November, as well as January, were 

drier than the 27-year monthly average precipitation for those 

months. 

The wettest water year (WY; 12-month period from 

October 1 to September 30, designated by the calendar year in 

which it ends) during the study period was WY 2008, followed 

by WY 2010 (fig. 4). The driest WY was 2006, followed by 

WY 2012. The 30-year average annual precipitation by calendar year (CY) for Independence, is 110.9 centimeters (cm; 

43.67 inches) (National Climatic Data Center, 2014b). 
Introduction 3

Kansas City

Grandview

Lee’s Summit

Raytown

Blue Springs

Lake Jacomo

Longview Lake

Blue Springs

Lake

Prairie Lee

Lake

MISSOURI

RIVER

Blue

River

Little

Blue

River

East Fork Little 

Blue River

Spring

Bundschu

Cr

Branch

Cr

Crackerneck Creek

Adair Creek

Prairie

Creek

W Fire

Burr OakCr eek

Rock Creek

Sugar Creek Creek

Mill

Fire Prairie Creek

Little Blue River Basin

Study area

!

! !

!

!

!

!

!

!

!

!

!

!

2

3

4

6

7 8

9 11

1

5

234158 10

WWTP

0 2.5 5 MILES

0 2.5 5 KILOMETERS

Base from U.S. Geological Survey digital data, 1:24,000, 1999

Transverse Mercator projection, Zone 15

Water-quality and biologic sampling site—Table 2

! Water-quality and biologic sampling site with streamgage and continuous water quality—Table 2 1

!8

Rural comparison biologic sampling site—Table 2 13

#

Water-quality and biologic sampling site with discontinued streamgage and continuous water quality—Table 2

Biologic sampling site—Table 2

!6

10

City of Independence—Study area

!234158 National Weather Service Cooperative Station 234158—From 2001 to present (2014)

!WWTP Wastewater treatment plant

EXPLANATION

94°35' 94°30' 94°25' 94°20' 94°15'

39°10'

39°05'

39°00'

38°55'

38°50’

#13

12#

RAY

JACKSON

CASS

Enlarged area

South Grand

River Basin

East Fork

Crooked River 

Basin

WWTP

Figure 1. The Little Blue River Basin, sampling sites, study area location, and political boundaries 

for Independence, Missouri, and surrounding cities.
4 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

Little Blue River Basin

Little Blue River

Little Blue River

Study area

EXPLANATION

Open water

Land use/land cover

Developed, medium/high intensity

Barren land—Rock/sand/clay

Mixed forest

Grassland/crop

Wetland

Developed, open space/low intensity

94°30’ 94°24’ 94°18’ 94°12’ 94°06’ 94°00’

39°00’

39°05’

39°10’

38°55’

38°50’

0 2 4 6 8 KILOMETERS

0 2 4 6 8 MILES

Base from U.S. Geological Survey digital data, 2000, 1:24,000

Universal Transverse Mercator projection, Zone 15

Land use modified from U.S. Geological Survey Land Cover National Land Cover Database, 2006

Fire Prairie Creek

West Fire

Prairie Creek

Mill Creek

Rock Creek Burr 

Oak 

Creek

Adair Creek

Crackerneck

Creek

Bundschu

Creek Sugar

Creek

Spring Branch

Creek

Fire Prairie Creek

West Fire

Prairie Creek

Mill Creek

Rock Creek Burr 

Oak 

Creek

Adair Creek

Crackerneck

Creek

Bundschu

Creek Sugar

Creek

Spring Branch

Creek

Independence

Figure 2. Land use/land cover in the Little Blue River Basin and adjacent basins within Independence, Missouri.
Introduction 5

Previous Investigations

In June 2005, the USGS began to collect and analyze 

base-flow and stormflow samples from selected streams within 

the city limits of Independence. The objective of waterquality monitoring was to characterize and assess contaminant 

sources, concentrations, loads, and yields of various constituents and their contributions to the water-quality and ecological 

condition of the Little Blue River from various basins and 

receiving streams. The first phase of the study (Christensen 

and others, 2010) collected data from June 2005 through 

December 2008 and included fewer sampling sites, less 

frequent base-flow sampling, and fewer analyzed constituents 

(pesticides, sulfate, and hardness were added in WY 2010) 

than the current phase of the study. The calculated loads 

published in Christensen and others (2010) may differ from 

those presented in this report because additional data from 

WYs 2009 to 2013 have been added to the calculations. Data 

used to evaluate the ecological health of Independence streams 

also were previously published in Christensen and Krempa 

(2012) and included data collected during WYs 2007 to 2011. 

The hydrologic monitoring network within Independence 

includes eight USGS streamgaging stations with varying 

periods of record. All sites except the Little Blue River near 

Lake City, Mo., were installed during this study. Streamflow 

measurements on the Little Blue River near Lake City, Mo. 

(site 9; fig. 1; table 2 have been maintained continuously and 

are available from 1948 to the present (2014; U.S. Geological Survey, 2009). Other streamgages have periodically been 

operated within Independence, through both the Nationwide 

Urban Runoff Program (NURP) study (U.S. Environmental 

Protection Agency, 1983) and the USGS in 1992 and 1993 

(Schalk, 1993). 

The U.S. Environmental Protection Agency (EPA) 

conducted the NURP research project between 1979 and 1983 

(U.S. Environmental Protection Agency, 1983). The NURP 

was the first comprehensive study of urban stormwater pollution in the United States. The current (2014) Rock Creek 

sampling site (site 1; table 2; fig. 1) was the previous location 

of NURP site RS3 (Mid-America Regional Council and F.X. 

Browne Associates, Incorporated, 1983). The NURP study 

Table 1. Land use in the City of Independence and basins wholly or partially within Independence city boundaries.

[km2, square kilometer; --, no data]

Location or 

basin name 

(fig. 2)

Drainage 

area1

(km2

)

Developed 

open/low 

intensity2

Developed 

medium/

high 

intensity3

Grassland/

cutivated 

crops4

Mixed 

forest5 Water Wetlands6 Barren

Total 

developed 

land7

Total 

undeveloped 

land8

City of Independence 203 45.0 9.4 30.3 13.9 0.33 1.1 0.05 54.4 45.6

Little Blue River9 585 38.9 7.4 32.2 17.9 2.8 0.76 0.06 46.3 53.7

Rock Creek9 24.3 75.5 12.4 4.0 6.9 0.31 0.94 -- 87.9 12.1

Sugar Creek 10.9 60.1 15.5 8.6 14.6 0.88 0.44 -- 75.5 24.5

Mill Creek 28.2 32.6 11.0 30.9 22.7 0.77 1.95 0.12 43.6 56.4

Adair Creek9 13.5 64.5 26.0 3.5 5.3 0.06 0.14 0.50 90.5 9.5

Crackerneck Creek9 12.9 73.0 15.8 6.3 4.4 0.05 0.42 -- 88.8 11.2

Spring Branch Creek9 23.6 51.3 8.8 25.1 13.4 0.20 1.2 0.04 60.1 39.9

Burr Oak Creek9 21.0 31.9 5.9 32.3 29.4 0.19 0.33 -- 37.9 62.2

Bundschu Creek9 13.7 34.7 3.8 44.0 16.2 0.76 0.61 -- 38.4 61.6

West Fire Prairie Creek 30.4 20.9 2.0 37.7 38.2 0.40 0.79 -- 22.9 77.1

Fire Prairie Creek 132 11.3 0.78 72.7 14.1 0.59 0.49 0.03 12.1 87.9

1

Drainage areas for sites with sampling locations are for the area upstream from the sampling location.

2

Includes the National Land Cover Database (U.S. Geological Survey, 2006) land cover categories: developed, open space; developed, low intensity.

3

Includes the National Land Cover Database (U.S. Geological Survey, 2006) land cover categories: developed, medium intensity; developed, high intensity.

4

Includes the National Land Cover Database (U.S. Geological Survey, 2006) land cover categories: shrub/scrub; grassland/herbaceous; sedge/herbaceous; 

pasture/hay; cultivated crops.

5

Includes the National Land Cover Database (U.S. Geological Survey, 2006) land cover categories: deciduous forest; evergreen forest; mixed forest.

6

Includes the National Land Cover Database (U.S. Geological Survey, 2006) land cover categories: woody wetlands; emergent herbaceous wetlands.

7

Total of developed open/low intensity and developed medium/high intensity land.

8

Total of grassland/cultivated crops, mixed forest, water, wetlands, and barren land.

9

Sampling site located in basin.
6 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

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Data from the National Climatic Data Center, 2014a

Data from the National Climatic Data Center, 2014a

EXPLANATION

Average 1986−2013

Average 2005−13

Temperature

EXPLANATION

Precipitation

Average 1986−2013

Average 2005−13

January February March April May June July August September October November December

Figure 3. Average monthly temperatures and precipitation at Independence, Missouri, for June 2005 through September 2013 

compared to the 27-year average from October 1986 through September 2013.
Introduction 7

concluded that urban runoff was the cause of much pollution and the goals of the Clean Water Act would not be met if 

action was not taken (U.S. Environmental Protection Agency, 

1983). The NPDES permit program was founded on the results 

of the NURP study. 

During the initial phase of the NPDES permit process, 

the USGS, in cooperation with Independence, did a study 

from 1991 to 1992 to evaluate the water quality of base flow 

and stormflow in Independence streams from five basins 

within Independence (Schalk, 1993). A total of 226 base-flow 

samples were collected and analyzed for four indicators of 

point-source discharges: chlorine, copper, phenols, and total 

detergents. Fifty-two samples (23 percent) had detections of 

chlorine, there was a single detection of total detergents, and 

there were no detections of copper or phenols that were higher 

than the existing method detection limits (MDL) from that 

study period; however, current (2014) MDLs used for this 

report are lower. Stormflow samples collected during three 

storms were analyzed for physical properties, nutrients, trace 

elements, pesticides, volatile and semivolatile organic compounds, and FIB. 

Point and non-point source illicit discharges of pollutants 

to streams can be detected through the measurement of OMCs 

(Kolpin and others, 2002; Zaugg and others, 2006). Previous 

studies have used OMCs when evaluating streams affected 

by wastewater and wastewater treatment plant discharges, 

including studies on the adjacent Blue River Basin in Missouri 

and Kansas (Wilkison and others, 2002, 2006, 2009; Lee and 

others, 2005). OMCs can originate, however, from sources 

other than wastewater discharges, such as runoff from chemically treated or impervious surfaces, organic plant matter, 

landfills and garbage, construction materials, groundwater, and 

atmospheric deposition (Adolphson and others, 2001; Peck 

and Hornbuckle, 2006; Ternes and Joss, 2006; Senior and 

Cinotto, 2007; Musolff and others, 2009). Although OMCs 

have traditionally been referred to in the literature as wastewater contaminants or wastewater indicator compounds (Kolpin 

and others, 2002; Wilkison and others, 2002, 2006, 2009; 

Zaugg and others, 2002, 2006; Lee and others, 2004; Lee and 

others, 2005), in this report these compounds will be referred 

to by the generic term of common organic micro-constituents, 

or OMCs. 

Figure 4. Annual precipitation for Independence, Missouri, water years (October 1 through September 30) 2005 through 2013.

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Table 2. Sampling sites in Independence, Missouri, biologic sampling reference sites, and type of hydrologic, water-quality, and ecologic data colleSeptember 2013. [USGS, U.S. Geological Survey; ID, identification number; ddmmss, degrees/minutes/seconds; km2, square kilometers; mi2, square miles; QC, continuous streamflow; PCP, prec

quality; SQW, stormflow water quality; CWQM, continuous water-quality monitor; IQW, benthic macroinvertebrates; HAB, habitat assessment; DWS, dry-weather screening; X, sampled; NA, not applicable; --, not sampled] Site number (fig. 1) Station name or basin Short station name USGS station ID Latitude (ddmmss) Longitude (ddmmss) Drainage area1 (km2) Drainage area1 (mi2) QC PCP BQW S

1 Rock Creek at Kentucky Road in Independence, Mo. Rock Creek 06893620 390643 0942820 24.3 9.4 X X X 

NA Sugar Creek NA NA NA NA 10.9 4.2 -- -- -- 

NA Mill Creek NA NA NA NA 28.2 10.9 -- -- -- 

2 Little Blue River at Lee’s Summit Road in Independence, Mo. Lee’s Summit Road 06893820 390102 0942314 255 98.4 X X X 

3 Adair Creek at Independence, Mo. Adair Creek 06893830 390216 0942148 13.5 5.2 X X X 

4 East Fork Little Blue River near Blue Springs, Mo. East Fork 06893890 390132 0942037 89.1 34.4 X X X 

5 Little Blue River at 39th Street in Independence, Mo.2 39th Street 06893910 390250 0942015 409 158 X X X 

6 Crackerneck Creek at Selsa Road in Independence, Mo.3 Crackerneck Creek 06893940 390322 0942041 12.9 5.0 X X X 

7 Spring Branch Creek at Holke Road in Independence, Mo.4 Spring Branch 06893970 390518 0942036 24.1 9.3 X X X 

8 Burr Oak Creek at Independence, Mo. Burr Oak 06893990 390510 0941832 21.0 8.1 -- -- X 

9 Little Blue River near Lake City, Mo. Lake City 06894000 390602 0941801 505 195 X X X 

10 Cut-off Meander near Lake City, Mo. Cut-off Meander 390259094201201 390259 0942012 NA NA -- -- -- 

11 Bundschu Creek at North Little Blue Parkway in Independence, Mo. Bundschu Creek 390617094190201 390617 0941902 13.7 5.3 -- -- X 

NA West Fire Priarie Creek NA NA NA NA 30.4 11.7 -- -- -- 

12 East Fork Crooked River near Richmond, 

Mo.

Crooked River Richmond 06895090 392222 0945432 249 96 -- -- -- 

13 South Grand River below Freeman, Mo. South Grand Freeman 06921582 383520 0942630 388 150 -- -- -- 

1Drainage areas for sites with station IDs are for the area upstream from the streamgage and sampling location.2Streamgage discontinued October 2009.3Streamgage discontinued October 2008.4Spring Branch streamgage moved downstream to Missouri State Highway 78 bridge on August 15, 2007, due to sedimentation at the original location on Holke Road. The dr

was 23.6 km2/9.1 mi2.
Methods 9

Methods 

Samples were collected from June 2005 through September 2013 at 13 sites; eight streamgages, two ungaged sites, a 

cut-off meander, and two biological reference sites. The locations of sampled sites and type of hydrologic, water quality, 

and ecologic data collected are listed in table 2 and figure 1. 

Sites will be referred to by site number (1 through 13) for the 

remainder of the report. The numerical reference will follow 

the same downstream order as the USGS station identifiers 

(table 2; fig. 1). Sites will be referred to as the following: 

site 1, Rock Creek at Kentucky Road in Independence, Mo. 

(hereafter referred to as “Rock Creek”); site 2, Little Blue 

River at Lee’s Summit Road in Independence, Mo. (hereafter 

referred to as “Little Blue River at Lee’s Summit Road”); 

site 3, Adair Creek at Independence, Mo. (hereafter referred 

to as “Adair Creek”); site 4, East Fork Little Blue River near 

Blue Springs. Mo. (hereafter referred to as “East Fork Little 

Blue River”); site 5, Little Blue River at 39th Street in Independence, Mo. (hereafter referred to as “Little Blue River at 

39th Street”); site 6, Crackerneck Creek at Selsa Road in Independence, Mo. (hereafter referred to as “Crackerneck Creek”); 

site 7, Spring Branch Creek at Holke Road in Independence, 

Mo. ( hereafter referred to as “Spring Branch Creek”); 

site 8, Burr Oak Creek at Independence, Mo. (hereafter 

referred to as “Burr Oak Creek”); site 9, Little Blue River near 

Lake City, Mo. (hereafter referred to as “Little Blue River near 

Lake City”); site 10, Cut-off meander near Lake City, Mo. 

(hereafter referred to as “Cut-off meander near Lake City” ); 

site 11, Bundschu Creek at North Little Blue Parkway in Independence, Mo. (hereafter referred to as “Bundschu Creek”); 

site 12, East Fork Crooked River near Richmond, Mo. (hereafter referred to as “East Fork Crooked River”); and site 13, 

South Grand River below Freeman, Mo. (hereafter referred to 

as “South Grand River”). 

Continuous streamflow and water-quality, and discrete 

base-flow and stormflow data were collected from sites 1 

through 5, 7, and 9 (site 5 discontinued in WY 2009). All data 

except continuous water-quality were collected at site 6 until 

the discontinuation of that site in WY 2008. Two ungaged sites 

(sites 8 and 11) were sampled for base-flow and stormflow 

water quality. Sites 12 and 13 were selected as comparison 

control sites for habitat assessment and benthic macroinvertebrate samples because they are relatively undeveloped 

compared to the Independence sites and are within the same 

ecoregions as Independence; these sites were located outside 

of the study area (fig. 1). One additional ungaged site within 

Independence (site 10) also was selected for benthic macroinvertebrate sampling and habitat assessment because it was 

in an undeveloped area closer to the other sampling sites and 

within the city limits. Additional sampling sites were selected 

during dry-weather screening based on conditions at the sites 

at the time of sampling.

 Stream sampling sites were selected because they are 

representative of Independence’s contribution to the water 

quality of the Little Blue River, and streams that drain 

developed areas of Independence that receive discharge 

from the MS4. The types of data collected at each sampling 

site included streamflow, physical and chemical properties, 

TDS, sodium, chloride, nutrients, metals, OMCs, pesticides 

in streambed sediment and surface water, FIB, and SSC. 

Low-flow (dry-weather) screening was also conducted at 

sampling sites and along the length of the streams draining 

Independence to monitor for point-source discharges and 

stream degradation such as garbage dumping. Water-quality 

samples also were collected and analyzed on a regular basis 

at three ungaged sites, Crackerneck Creek (site 6; subsequent 

to the removal of the gage in October 2008), Burr Oak Creek 

(site 8), and Bundschu Creek (site 11; table 2; fig. 1). Benthic 

macroinvertebrate community surveys and habitat assessments 

also were done. 

Streamflow and Continuous Water-Quality 

Monitoring

Streamflow measurements were made on all sites at regular intervals using standard USGS methods (Rantz and others, 

1982; U.S. Geological Survey, 2004; Oberg and others, 2005; 

Turnipseed and Sauer, 2010; Mueller and others, 2013), and 

were used to determine and maintain stage-discharge relations 

for each site. Streamflow at each individual site during base 

flow and stormflow was determined using the stage-discharge 

relationship (Rantz and others, 1982), or was measured or estimated at the time of sampling. Water surface elevation (stage) 

data were measured and recorded at eight sites using noncontact radar stage sensors and pressure transducers. Sites 2, 

5, and 9—all located on the Little Blue River—were equipped 

with non-contact radar stage sensors, and sites 1, 3, 4, 6, and 

7 used pressure transducers. Sites 1, 3, 6, and 7 are “flashy” 

in nature with rapid increases and decreases of flow, so that 

these sites measured, but did not record, stage data in 5-minute 

intervals. Stage data were recorded in 15-minute increments 

and transmitted by way of satellite telemetry to the National 

Water Information System (NWIS) for streamflow computation and records archival. Data are available for public display 

through NWISWeb (http://waterdata.usgs.gov) and updated 

hourly. 

Streamgages were equipped with unheated tipping-bucket 

rain gages to collect a cumulative total of precipitation every 

15 minutes. The rain gages were checked, cleaned, and maintained as necessary and were calibrated annually to ensure 

an accuracy of 0.025 cm of precipitation. National Weather 

Service (NWS) cooperative station data (station 234158 

fig. 1) were used to supplement tipping-bucket rain gage 

data during times of snowfall or other freezing precipitation 

because unheated tipping buckets are not able to accurately 

measure precipitation during freezing conditions. Climatic 

data, including precipitation, have been measured at a NWS 

cooperative station in Independence since 1973 (National 

Climatic Data Center, 2014a).
10 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

Six sites (sites 1 through 4, 7, and 9) are currently (2014) 

equipped with CWQMs (table 2; fig. 1) and operated and 

maintained according to standard USGS procedures (Wagner 

and others, 2006). An additional little Blue River site, site 5, 

was equipped with a CWQM, but was discontinued in 

October 2009. The CWQMs record water-quality values 

every 15 minutes. All sites with CWQMs are currently (2014) 

equipped with sensors to record specific conductance, water 

temperature, turbidity, and, at different periods during the 

study, dissolved oxygen and pH (fig. 5). The two Little Blue 

River sites (sites 2 and 9) are currently (2014) equipped with 

dissolved oxygen sensors, and site 9 also is equipped with a 

pH sensor. All real-time and daily data recorded from July 

2005 through September 2013 are stored and made available 

from the USGS NWIS at http://waterdata.usgs.gov/mo/nwis/

qw.

Continuous water-quality monitors were installed at 

a total of seven sites. Three sites (sites 5, 7, and 9; table 2; 

fig. 1) were the first to be equipped with CWQMs installed 

inside 46-cm diameter corrugated metal pipe cut to 1-meter 

(m) lengths and secured to the bottom of the stream. The 

pipes were positioned within the main channel such that 

water velocity could be maintained during periods of low 

flow, and repositioned as necessary to ensure adequate flow 

around the sensors. Frequent shallow water depths and severe 

sediment deposition at site 7 later forced the relocation of the 

streamgage and CWQM to a site downstream. The CWQM 

at the new site was installed in a 10.2-cm diameter polyvinyl 

chloride (PVC) conduit attached to the bank and positioned 

near the center of flow. This installation was slightly repositioned closer to the bank and then later replaced with a 46-cm 

diameter metal corrugated conduit to prevent damage from 

storm events. The CWQMs installed at site 1 and site 2 also 

were installed in metal conduits attached to the streambed, 

and the CWQMs installed at site 3 and site 4 were installed 

in 10.2-cm PVC pipes attached to the concrete culvert walls 

at the sites. Cross-section measurements were made with a 

CWQM designated as a field meter to ensure that the placement of the CWQM adequately represented parameter 

readings across the stream (Wagner and others, 2006). The 

CWQMs at all sites are subject to biofouling, sedimentation, 

and calibration drift, and were cleaned and calibrated on a 

regular basis. Sites were visited monthly on average, but site 

visits ranged from 1 to 214 days between visits, depending on 

sensor performance, season, and site conditions. Flooding on 

occasion greatly increased the amount of time between some 

site visits. The measured CWQM data were corrected based 

on manufacturer’s specifications, site knowledge, and USGS 

methods and procedures as described in Wagner and others 

(2006).

Water-Quality Sample Collection and 

Procedures

Base-flow (defined as streamflow unaffected by runoff) 

and stormflow samples were collected at 10 sites in Independence (sites 1 through 9 and 11) at varying intervals during the 

study period from June 2005 through September 2013. The 

method of collection varied based on sample conditions and 

analyzed constituents varied only slightly between base-flow 

and stormflow samples.

Base-flow samples were collected annually from June 

2006 to May 2008, twice annually from the fourth quarter 

of WY 2008 through WY 2009, three times in WY 2010, 

and quarterly beginning in WY 2011, with additional snowmelt samples collected to characterize winter conditions. 

Grab samples were collected in the centroid of flow during 

base-flow conditions and analyzed for selected water-quality 

constituents. 

Stormflow water-quality samples were collected 

quarterly beginning in June 2005 at sites 1–9 and 11 (table 2; 

fig. 1), with additional samples collected to characterize water 

quality during winter conditions or to make up for any constituent analyses that may have been omitted during previous 

stormflow sampling periods as a result of insufficient sample 

volume. Stormflow samples were collected using automatic 

samplers, or as grab samples at the centroid of flow if there 

was not a streamgage installed at the site or if the automatic 

samplers malfunctioned. Two complete sets of stormflow 

samples were taken as grabs, one prior to the installation of 

the automatic samplers in June 2005 and one in October 2007 

when the automatic samplers failed to function. 

Figure 5. Continuous water-quality monitor with (clockwise 

from upper left) turbidity, optical dissolved oxygen, pH, and 

combined specific conductance and water temperature 

sensors.
Methods 11

Automatic samplers were programmed to collect a flowweighted sample at sites with a streamgage once a designated 

stage threshold was exceeded. The individual samples were 

pumped at a pre-programmed interval and combined into 

one composite sample in a 9.5-liter glass receiving vessel. 

Sampling intervals were programmed based on the interval 

of continuous streamflow data collection. Sites were typically 

sampled every 15 minutes except for the smaller streams 

(sites 1, 3, 6, and 7), which were sampled every 5 minutes. 

The samplers were programmed specifically for each storm 

for the expected streamflow at each site and to obtain the 

most representative sample over the rise, peak, and recession of streamflow; however, given the unpredictability of 

precipitation and runoff during storms, volume of stormflow, 

and the length of recession at each site for each storm, the rise 

of streamflow was sampled more frequently than the peak 

or recession. For storm events of prolonged duration, the 

samples were either preserved by placing them on ice in the 

sampler, or by removing and refrigerating the partial sample 

and compositing it at a later time with the additional sample 

from the remainder of the storm event. Detailed USGS storm 

sampling procedures can be obtained in the USGS “National 

Field Manual for the Collection of Water Quality Data” (U.S. 

Geological Survey, variously dated). 

For composite samples collected by automatic sampler, 

streamflow was calculated as an average of the calculated 

15-minute streamflow values, computed from the established 

stage-discharge relationship for each site, over the interval of 

sample collection. Streamflow for grab samples was either 

determined from an established stage-discharge relationship 

at each streamgage or measured at the time of sampling at the 

site. Streamflow values were used in the calculation of annual 

loads of selected constituents.

Physical and chemical properties and selected water-quality constituents were analyzed from samples collected during 

base flow and stormflow. Physical and chemical properties 

(dissolved oxygen, pH, specific conductance, water temperature, and turbidity) were measured at all sites (sites 1 through 

9 and 11; table 2; fig. 1) in the stream during base-flow and 

stormflow sampling with calibrated CWQMs or field meters 

during sampling, or in the collected sample in the laboratory. 

Base-flow and stormflow samples were analyzed for TDS, 

sodium, chloride, nutrients (nitrogen [N] and phosphorous 

[P] species), total metals (aluminum, cadmium, chromium, 

copper, lead, zinc, and arsenic), dissolved mercury, cyanide, 

OMCs, FIB, and SSC. Dissolved metals analysis was done on 

one set of stormflow samples to assess the bioavailability of 

metals during stormflow. Analyses for 5-day biologic oxygen 

demand (BOD5

), chemical oxygen demand (COD), and oil and 

grease in base-flow and stormflow samples were done by, and 

data are available on file with, the City of Independence WPC 

Environmental Compliance Testing Laboratory (L. White, oral 

commun., 2014). Chlorophyll samples were also collected 

during base-flow sampling, but the data were not used for the 

purposes of this report. Sulfate and hardness during base flow 

and stormflow were added beginning in September 2012 and 

November 2012. Results for these two constituents are not 

presented because of the small number of samples collected 

through September 2013. Fourteen base-flow samples were 

analyzed for pesticides in streambed sediment from July 2010 

to July 2013 and 17 stormflow and 2 base-flow samples were 

analyzed for pesticides in water from September 2010 to 

June 2013. 

After collection, base-flow and stormflow samples were 

taken to the USGS Water Science Center in Lee’s Summit, 

Mo., to prepare aliquots for chemical analyses. All constituents except cyanide, pesticides in streambed sediment, and 

chlorophyll were collected as either grab samples during base 

flow or from automatic samplers during stormflow, in clean 

and sterilized 9.5-liter glass bottles. Collection bottles received 

multiple sequential rinses with detergent, dilute hydrochloric 

acid, methanol, and de-ionized and organic free water before 

use. Upon arrival at the laboratory, samples were transferred 

to a churn splitter that was cleaned and sterilized using the 

same procedures as for the glass collection bottles. Aliquots 

were removed from the churn splitter and placed in individual 

bottles for each respective constituent or group of constituents (total nutrients, total metals, OMCs, and pesticides) to be 

analyzed as raw samples. Any samples that required filtration were filtered according to established USGS procedures 

(U.S. Geological Survey, variously dated) using 0.45 micron 

(μm) cartridge filters. Samples to be analyzed at the USGS 

National Water Quality Laboratory (NWQL), in Lakewood, 

Co. (including TDS, sodium, chloride, nutrients, metals, 

OMCs, pesticides in streambed sediment and surface water, 

and sulfate) were placed on ice and shipped within 24 hours of 

processing. 

Cyanide, pesticides in streambed sediment, and chlorophyll were collected in separate containers for direct shipment 

to the analytical laboratories. Samples collected for cyanide 

were refrigerated and shipped overnight the same day to the 

TestAmerica (Severn-Trent) Laboratory in Arvada, Colorado, 

for analysis. If cyanide samples could not be shipped the same 

day as collection, samples were preserved with concentrated 

5-normal sodium hydroxide and shipped within 1 week. 

Samples for pesticides in streambed sediment were collected 

using a stainless steel spoon and placed on ice and shipped to 

the NWQL. Chlorophyll samples collected in the stream were 

taken to the USGS laboratory in Lee’s Summit, filtered using 

0.7 μm glass-fiber filters, and frozen until shipment on dry ice 

to the NWQL. 

Three types of microbiological samples were collected, 

including FIB, MST, and influent samples, and were prepared 

for analysis and shipment at the USGS Lee’s Summit laboratory. Samples for FIB were collected from the churn splitter 

in sterilized 500 milliliter (mL) bacteria bottles. Samples 

for MST markers were collected from the churn splitter in 

500 mL sterile deoxyribonucleic acid (DNA)-free bottles. The 

samples were refrigerated for no more than 8 hours on the day 

of collection before overnight shipment on ice to the University of Missouri Veterinary Pathology Laboratory, Columbia, 

Mo. (May through October 2007), or the USGS Ohio Water 
12 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

Microbiology Laboratory (OWML), Columbus, Ohio (June 

2008 through September 2013). Samples of influent were 

collected from the Rock Creek wastewater treatment plant 

(WWTP) (fig. 1) as grab samples in sterile 500-mL DNA-free 

bottles. Samples were refrigerated before overnight shipment 

on ice to the OWML. 

Forty-eight fecal source samples were collected from 

human and several domestic and wild animal sources (cat, 

chicken, cow, deer, dog, goose, horse, mouse, rabbit, and wild 

turkey) between September 2011 and May 2013 for comparison with environmental samples. Fecal source samples were 

collected in Jackson and Cass Counties, Missouri (fig. 1) 

except for four individual human samples that were collected 

in Columbus, Ohio. Twelve mixed-human sewage influent samples also were collected from influent to the City of 

Independence Rock Creek WWTP between September 2011 

and May 2013. All fecal samples were collected with sterile 

equipment and placed in sterile 50 mL centrifuge tubes, individually sealed in ziplock bags, and immediately placed on ice 

for transport. Animal fecal samples (cat, chicken, cow, deer, 

dog, goose, horse, mouse, rabbit, and wild turkey) were collected at several locations in Jackson and Cass counties, Mo. 

Human fecal samples were collected in Jackson County, Mo., 

and Columbus, Ohio. Samples were from individual hosts, 

with the possible exception of the mouse samples. More than 

one mouse was observed at the two collection locations and 

multiple fecal pellets were collected for each mouse sample. 

Samples were refrigerated and shipped overnight on ice to the 

OWML. The SSC samples were collected in 350 mL glass 

sediment bottles from the churn splitter and shipped to the 

USGS Missouri Sediment Laboratory in Rolla, Mo. 

 Beginning in WY 2006, dry-weather screening was 

done during base-flow conditions on selected Independence 

streams (table 2). Personnel from the USGS and Independence 

WPC walked the streams from the mouth to either the source 

of the stream where flow was no longer evident or until the 

city limits were reached. All measurable inflows were identified visually (pipe, culvert, groundwater seep, tributary, pond 

outflow) and sampled with the exceptions of very low flow 

that could not be measured accurately or diffuse groundwater 

seeps. At each site, horizontal coordinates were obtained using 

a hand-held global positioning system (GPS), streamflow was 

estimated or measured, and physical properties (pH, specific 

conductance, and water temperature) were recorded using portable water-quality meters calibrated according to established 

USGS protocols (U.S. Geological Survey, variously dated). A 

total of 1,052 samples were collected and analyzed between 

June 2005 and September 2013, not including field replicates, 

laboratory duplicates, or blank samples. Water samples were 

analyzed for one or more of four constituents: total chlorine, 

free and complexed copper (total dissolved copper; discontinued in WY 2011), phenols, and anion surfactants, compounds 

commonly used in household and industrial cleaners and 

solvents including alkyl benzene sulfonate (ABS) and linear 

alkylate sulfonate (LAS). On occasion some constituents were 

not analyzed because of low sample volume. 

Dry-weather screening analytes that had a measured 

value exceeding a guideline or standard for that analyte were 

considered to be potential sources of contamination to the 

stream and were considered for further investigation. The 

State reportable/compliance level for total chlorine of 

0.13 milligrams per liter (mg/L) was used as a guideline for 

total chlorine (Missouri Department of Natural Resources, 

2006). Unfiltered samples were used for determining total 

dissolved copper, which includes both free and complexed 

copper. A standard for total dissolved copper was not determined because Federal and State standards include only 

dissolved copper from filtered samples rather than unfiltered. 

The phenols method used for dry-weather screening measures all ortho- and meta-substituted phenols (Hach, 2002). 

The only standard or guideline for phenol compounds for the 

State of Missouri is the chronic standard for protection of 

aquatic life (AQL) of 0.100 mg/L (Missouri Department of 

Natural Resources, 2014b); therefore, the concentrations of 

phenols were considered to be equivalent to the concentration of the individual compound phenol for comparison. The 

most commonly detected surfactant (detergent) in base-flow 

samples was nonylphenol, a nonionic surfactant (4-nonylphenol; appendix 1, http://pubs.usgs.gov/ds/0915/downloads/

ds915_Appendix01.xlsx). The EPA freshwater standard for 

acute exposure for aquatic communities to nonylphenol of 

0.028 mg/L (U.S. Environmental Protection Agency, 2014) 

was used as an arbitrary guideline for determining potentially 

reportable detections of anionic surfactants. This guideline is 

conservative because the measured concentration of a single 

surfactant can be expected to be less than that of all surfactants 

combined. 

Macroinvertebrate samples were collected at sites 1 

through 13 (table 2; fig. 1). The macroinvertebrate sampling 

protocol was based on procedures described by Barbour and 

others (1999) and Sarver (2003a) for the collection of qualitative samples. The richest-targeted habitat (RTH) method 

(Barbour and others, 1999) was used where riffle/run habitats 

were targeted. Samples collected from this habitat type are 

likely representative of the stream reach (Barbour and others, 

1999; Cuffney and others, 2010). For each sample, six collections were made from various riffle locations to incorporate a 

variety of substrate size, stream velocity, and water depth, and 

samples were processed and composited in the field according to Sarver (2003a). Coarse substrate habitat was limited or 

unavailable at sites 4 and 12, so some subsamples were collected from fine-grained substrate or accumulated wood/leaf 

debris on the stream bottom. Site 12 was discontinued after 

the fall 2009 sampling because of a lack of an adequate single 

RTH to sample. After collection, the composite sample was 

brought to the laboratory in Lee’s Summit for further processing and placed in a lighted white processing tray with enough 

water to cover the bottom of the tray. A total of 600 individuals (or amount enumerated in 1 hour) were collected from the 

composite sample. Counting focused on maximizing sample 

biodiversity based on visually identified morphological differences of individuals selected during collection (Barbour and 
Methods 13

others, 2009). Finished samples were preserved with 90-percent ethanol until shipment to the NWQL for analysis.

Stream habitat assessments were completed in the fall 

of 2008, 2010, and 2012 and in the spring of 2010 at each 

sampling site to relate physical characteristics to biological 

variables. Ten physical-habitat characteristics (epifaunal substrate, embeddedness, velocity-depth regime, sediment deposition, channel flow status, channel alteration, riffle quality, bank 

stability, vegetative protection, and riparian vegetation) 

were measured and assigned a standardized score on a scale 

of 0 to 20 according to procedures described in Sarver 

(2003b). The scores were then summed to provide an overall 

assessment of stream physical-habitat quality with a total possible score of 200 indicating ideal habitat.

The Invertebrate Data Analysis System (IDAS) version 

5.0 was used for processing macroinvertebrate sample data 

and calculating taxa richness, abundance, and diversity metrics 

(Cuffney and Brightbill, 2011). Because of their proximity, 

urban character, and potential macroinvertebrate populations, 

data from sites 1 through 10 were combined for the purpose of 

resolving taxonomic ambiguities. Rural comparison streams 

(sites 12 and 13) were processed together, but separately from 

the urban sites. About 16 percent of sample taxonomic levels 

and about 5 percent of abundances were assigned tolerance 

values because of ambiguous taxonomy. Pollution tolerance 

values for taxa that were used to calculate the Macroinvertebrate Biotic Index (MBI) were assigned from the Missouri 

taxa listings (Sarver, 2005) or, if unavailable, assigned from 

established regional tolerance values (Cuffney and Brightbill, 

2011). Taxa were defined as intolerant if the tolerance value 

was less than or equal to 4, moderately tolerant if values were 

greater than 4 and less than 7, and tolerant if values were 

greater than or equal to 7. All metrics were calculated separately for urban and rural sites and for spring and fall seasons.

Four metrics are used by the Missouri Department of 

Natural Resources (MDNR) (Sarver, 2003a) in the calculation of the Missouri stream condition index (MSCI): total 

taxa richness (RICH), Ephemeroptera plus Plecoptera plus 

Trichoptera (EPT) richness (EPTR), Shannon Diversity Index 

(SHANDIV), and the MBI. These metrics were used to calculate the aquatic-life support (ALS) status for samples collected 

only from a stream’s RTH, which was usually coarse-substrate 

riffle habitat. The MSCI is calculated from samples collected 

from multiple habitats within a stream reach. This study’s 

stream condition index is noted simply as SCI because of 

this difference in calculation of the MSCI and the SCI. Other 

lesser differences in the calculation of individual metrics are 

noted below. Differences are not substantial and the MSCI and 

SCI are considered equivalent. Differences in the calculated 

SCI and component metrics for individual samples from previously published values (Christensen and Krempa, 2012) result 

from differences in resolving taxonomic ambiguities with the 

addition of more samples.

The RICH is the total number of distinct taxa present in 

a sample. The EPTR is the total richness of Ephemeroptera, 

Plecoptera, and Trichoptera taxa in a sample. The SHANDIV 

is a measure of taxa diversity in a community that takes into 

consideration taxa richness and evenness of the relative abundance of community (Shannon and Weaver, 1949). The MBI 

is a measure of the overall pollution tolerance of a macroinvertebrate community expressed on a scale of 0 to 10 with less 

tolerant individuals having a lower tolerance value and more 

tolerant individuals having a higher tolerance value (Sarver, 

2003a) and is comparable to the Hilsenhoff Biotic Index 

(Hilsenhoff, 1977, 1988). The MDNR uses only the Missouri 

taxa listings (Sarver, 2005) when calculating the MSCI.

Breakpoints for categories used to score the ALS status 

of streams (table 3) are determined and updated frequently 

by MDNR. Breakpoints for the ALS of individual habitats, 

including riffle habitat, were obtained from the MDNR for 

reference streams in the Central Irregular Plains ecoregion 

(not shown; Omernik, 1987) and Missouri tributaries between 

the Blue and Lamine Rivers ecological drainage unit (not 

shown; Sarver and others, 2002) that includes the study area. 

Reference site samples were collected between April 1998 and 

September 2008 (David Michaelson, Missouri Department of 

Natural Resources, written commun., 2011).

Laboratory and Data Analysis

Samples analyzed by the USGS NWQL, including TDS, 

sodium, chloride, nutrients (N and P species), total metals, 

dissolved mercury, cyanide, OMCs, pesticides in streambed 

Table 3. Criteria for aquatic-life support categories for riffle habitats for the Missouri tributaries between the Blue and Lamine Rivers 

ecological drainage unit.

[ >, greater than; <, less than]

Riffle aquatic-life support 

category

Total taxa 

richness

EphemeropteraPlecopteraTrichoptera richness

Macroinvertebrate 

biotic index

Shannon diversity 

index

Stream 

condition 

index

Spring Fall Spring Fall Spring Fall Spring Fall

Fully biologically supporting >36 >37 >9 >9 <5.5 <6.5 >2.27 >2.39 16–20

Partially biologically supporting 18–36 19–37 5–9 5–9 5.5–7.7 6.5–8.3 1.13–2.27 1.19–2.39 10–14

Nonbiologically supporting <18 <19 <5 <5 >7.7 >8.3 <1.13 <1.19 4–8
14 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

sediment and surface water, SSC, and sulfate were analyzed 

using established USGS procedures (Fishman and Friedman, 

1989; Fishman, 1993; Garbarino and Damrau, 2001; Garbarino and others, 2006; Garbarino and Struzeski, 1998; Hoffman 

and others, 1996; Noriega and others, 2004; Patton and Kryskalla, 2011; Patton and Truitt, 1992, 2000; Zaugg and others, 

2006). Grab samples collected for cyanide were analyzed by 

the TestAmerica (Severn-Trent) Laboratory in Arvada, Colo., 

using EPA approved methods (U.S. Environmental Protection 

Agency, 2013). Samples for SSC concentration were analyzed 

by the USGS sediment laboratory in Rolla, Mo., according 

to procedures described in Guy (1969). Samples for chlorophyll, after being filtered in the USGS Lee’s Summit laboratory, were analyzed at the NWQL according to EPA Method 

445.0 (Arar and Collins, 1997). Simple summary statistics 

were computed based on the constituent results received from 

the laboratories. Any results that were less than the MRL for 

a constituent were not included in the summary statistical 

analysis.

Colorimetric analysis was used to analyze the dryweather screening samples for total chlorine, total dissolved 

copper, phenols, and anionic surfactants using Hach reagents 

and a DR/2400® portable spectrophotometer at the USGS laboratory in Lee’s Summit, Mo. The Hach method for total chlorine oxidizes iodide in the reagent with chlorine in the sample 

that forms a pink color proportionate to the total chlorine 

concentration (Hach Company, 2004). The analysis method for 

total chlorine is equivalent to accepted EPA method 330.5 for 

analysis of total chlorine in water or wastewater (Hach Company, 2004). The Hach method for analysis of total dissolved 

copper utilizes AccuVac® vials which contains a reagent that 

reacts with copper in the sample to form a purple-colored 

complex proportionate to the copper concentration (Hach 

Company, 2004). There is not an equivalent EPA method for 

analysis of total dissolved copper. The analysis method initially used for phenols was a Hach colorimetric analysis (Hach 

Company, 2004), but was later changed (beginning in WY 

2013) to a colorimetric analysis method using a CHEMetrics 

VACUette kit for analysis of phenols in water (CHEMetrics, 

Incorporated, 2013). The Hach method for phenols analysis 

creates a reaction to form a dye, which is then extracted into 

chloroform and the color measured (Hach Company, 2004). 

Both the Hach and CHEMetrics methods are equivalent to 

accepted EPA method 420.1 for phenols in water and wastes 

(Hach Company, 2004; CHEMetrics, Incorporated, 2013; U.S. 

Environmental Protection Agency, 1978). Although the Hach 

method has a detection limit of 0.002 mg/L and the CHEMetrics method has a detection limit of 0.10 parts per million 

(ppm), or 0.10 mg/L, since the analyses were being used as a 

screening procedure only and not a quantitative method, the 

higher detection limit was acceptable. The anionic surfactant 

method extracts the surfactants from the sample contained in 

a glass separatory funnel and combines them with a violet dye 

in solution with benzene. The benzene is then separated and 

analyzed for imparted color (Hach Company, 2004). There is 

not an equivalent EPA method for anionic surfactants.

A limitation of all colorimetric methods is that suspended material and sediment (turbidity) and certain interfering compounds may cause positive or negative bias in the 

sample results through decreased light transmission or poor 

color development; however, recommended pre-treatment 

of samples to remove turbidity and any interfering constituents (Hach Company, 2004) was not done on dry-weather 

screening samples because the analyses were intended to be a 

screening procedure. All samples were collected as unfiltered 

samples. For those samples that were observed to be highly 

turbid, an aliquot of the sample was poured into a 50-mL 

glass beaker and allowed to settle for 2 minutes or longer to 

decrease the suspended material before being transferred to a 

sample cell or ampule for analysis. This less rigorous approach 

sometimes resulted in false positives, but detection levels were 

low. Laboratory procedures were put in place to reanalyze 

suspect samples and if high level detections were confirmed, 

to send the sample to the NWQL for further analysis. However, no high-level detections with suspected interference were 

confirmed. Samples that still had measurable results despite 

not having any visually observed turbidity or color were 

deleted and the results omitted from the statistical analyses. 

All deleted results were low and were at or near the detection 

limit. 

The estimated detection limit (EDL) for the colorimetric 

analysis of dry-weather screening samples was determined by 

the manufacturer of each analysis method (Hach Company, 

2004; CHEMetrics, Incorporated, 2013). A provisional MDL 

was determined for each dry-weather screening analyte by 

averaging the differences between an environmental sample 

result and the replicate or duplicate sample result and then 

rounding to the nearest 0.05 or 0.005 mg/L, depending on 

the analyte. An MDL is the lowest concentration at which 

an analyte can be expected to be measured with 99-percent 

confidence that the concentration is above zero (U.S. Environmental Protection Agency, 1997). The dry-weather screening 

analyte MDL values are considered provisional because more 

spike samples (samples with a known concentration of analyte 

added) are needed than have been currently (2014) analyzed to 

determine an MDL value that is within the 99-percent confidence level. Analyte concentrations between the EDL and 

the provisional MDL for a given analyte are reported as “M” 

values, or concentrations that are identified but not quantified; 

however, for purposes of this report, numerical values for samples reported as “M” were included in the statistical analyses 

and summary statistics to better indicate the large number of 

low level detections for dry-weather screening analytes. Any 

analyte concentrations below the EDL were not included in the 

statistical analysis.

All analyses for FIB were done at the USGS laboratory 

in Lee’s Summit, Mo. Fecal coliform samples were analyzed 

using standard plate methods according to established USGS 

procedures (U.S. Geological Survey, variously dated). Samples for E. coli and total coliform were analyzed using IDEXX 

Quanti-Tray® kits, which are a semiautomated quantification 

method (IDEXX Laboratories, 2009). Samples are diluted and 
Methods 15

placed into a Quanti-Tray® that contains 97 wells or reservoirs, then incubated for 24 hours at 37 °C. After incubation 

is completed, the number of cells that have turned yellow are 

counted to determine the most probable number (MPN) of 

total coliform colonies, and the number of cells that fluoresce 

under ultraviolet light are counted to determine the MPN of 

E. Coli. The MPN is determined by using a probability table 

to convert the number of cells to an MPN of bacteria colonies 

that could be expected to be counted in a water sample. The 

IDEXX method is considered to be a semiautomated quantification method because the bacteria colonies cannot be directly 

counted, but the change in color or fluorescence is used as an 

indicator of the approximate quantity of bacteria colonies 

the sample contains. Sample results are reported as the 

most probable number of colonies per 100 mL of sample 

(MPN/100 mL). For the purposes of this report the number 

of colonies per 100 mL (col/100 mL) reported for traditional 

plate methods for bacteria enumeration is considered to be 

equivalent to the MPN/100 mL.

Sources of E. coli bacteria in streams were evaluated to 

identify host sources using library-dependent MST methods 

(Carson and others, 2001; Dombek and others, 2000). MST 

samples were analyzed in WY 2007 at the University of Missouri Veterinary Pathology Laboratory in Columbia, Mo., 

using repetitive extragenic palindromic polymerase chain reaction (rep-PCR) methods (Dombek and others, 2000; Carson 

and others, 2001, 2003, 2005). Rep-PCR was used to produce 

the isolate DNA “fingerprints” of samples and to confirm that 

isolates were verifiably strains of E. coli using geographically 

specific, genotypic library-based methods (Carson and others, 

2003). E. coli isolated from water samples for MST analysis 

were compared to a host-source library of E. coli DNA patterns from three hosts: dogs, geese, and humans. A presumptive source of sampled bacteria is assigned through a statistical 

comparison of genetic markers obtained from environmental 

E. coli samples to genetic markers in the host-source library. 

The development of a host-source library specific to the Little 

Blue River Basin was beyond the scope of this study. A library 

of patterns developed for other studies in the local area (Wilkison and others, 2005, 2006) was used instead. Data were classified as human, non-human (dog and geese), and unknown. 

Fingerprint patterns of E. coli from collected water samples 

were compared with patterns from the host-source library for 

similarity using BioNumerics software, version 3.0 (Applied 

Maths NV, 2014). The source was designated as unknown if 

the sample did not have at least an 80-percent similarity to a 

known host group (A.C. Carson, University of Missouri Veterinary Pathology Laboratory, oral commun., 2009).

The MST samples for WY 2008 through 2013 were 

analyzed at the USGS OWML. Samples were received on ice 

at the OWML and processed in duplicate on the day of receipt 

using the following steps:

• the sample was logged in and assigned an identification 

number

• a 10- to 100-mL aliquot of the sample was amended 

with an E. coli carrying plasmid for spike and recovery procedures and filtered by vacuum through a 

0.4-micrometer pore-size polycarbonate filter

• the filter was transferred to a vial containing acid 

washed glass beads and held at -80 °C for further 

analysis.

Preserved filters were extracted by use of the GeneRite 

DNA-EZ extraction kit according to manufacturer’s instructions, with minor modifications. Extracted DNA was stored at 

-20 °C until analysis by quantitative polymerase chain reaction 

(qPCR). The qPCR analysis steps were as follows:

• Exogenous DNA (E. coli plasmid) was measured for 

spike-and-recovery efficiency. If recovery efficiency 

was less than 50 percent, the duplicate filter was 

extracted and used for analysis. Matrix inhibition was 

measured by spiking a known quantity of plasmidborne target sequence into the reaction mixture that 

also contained sample DNA extract. If the detection 

of spiked target was less than 95 percent, the sample 

was considered to exert matrix inhibition on the qPCR 

reaction. The sample was subsequently diluted and the 

highest-concentration dilution that did not exert matrix 

inhibition on the qPCR reaction was used for test reactions. 

• Host-associated markers by qPCR were analyzed by 

using the appropriate dilution as indicated by matrix 

inhibition tests:

• General fecal contamination marker (AllBac; Layton 

and others, 2006)

• Human-associated marker (qHF183; Seurinck and 

others, 2005)

• Ruminant-associated marker (BoBac; Layton and 

others, 2006)

• Dog-associated marker (BacCan; Kildare and others, 

2007)

Full analytical methods are available on request from 

the OWML. Contact information can be accessed at http://

oh.water.usgs.gov/micro_contact.htm.

Preserved macroinvertebrate samples were sent to the 

USGS NWQL for enumeration and taxonomic identification according to USGS protocols (Moulton and others, 

2000, 2002). Generally, taxa were identified by the NWQL 

to genus or species; however, some taxa were identified to 

a higher taxonomic level, typically family. Ambiguous taxa 

were resolved by removing the higher taxonomic level (parent) or merging the lower taxonomic level (children) with the 

parent. If the abundance of the ambiguous parent was higher 

than the sum of the children’s abundances, the children were 

deleted and their abundances were added to the parent. If the 

sum of the ambiguous children’s abundances was higher, the 
16 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

children were retained and the parent was deleted (Cuffney 

and Brightbill, 2011). This method of resolving ambiguities is 

conservative and may result in reduced sample richness and 

abundance but retains sensitivity of the data to differences in 

urban intensity (Cuffney and others, 2007).

Quality Control and Quality Assurance

Quality-control samples, designed to ensure the integrity of the data collected by testing all aspects of the sample 

collection and analysis process (U.S. Geological Survey, 

variously dated), consisted of about 10 percent of all waterquality samples collected during this study. Quality-assurance 

procedures were utilized to ensure the precision and accuracy 

of the water-quality data included in this report. Qualitycontrol and quality-assurance results for data collected during 

previous studies are included in this report and are presented 

in previous reports (Christensen and others, 2010; Christensen 

and Krempa, 2012). 

Various types of quality-control samples were collected 

for this study, and the type of quality-control sample chosen 

was dependent on the type of environmental sample being collected. Field replicate samples were collected to measure the 

amount of variability introduced during the sample collection 

and analysis process. Field blanks were used to determine if 

any contamination was introduced by sample collection and 

processing. Laboratory duplicates were analyzed to determine the amount of variability introduced during laboratory 

processing and analysis. Laboratory blanks were analyzed to 

determine if laboratory processing and analysis introduced any 

contamination to the samples. Laboratory spikes and accuracy 

checks were used to measure potential bias in the sampling 

analysis process for OMC, MST, and dry-weather screening samples. Field and laboratory replicates and blanks were 

collected and analyzed for base-flow and stormflow samples. 

Dry-weather screening samples utilized field replicates, 

laboratory duplicates and blanks, and laboratory spikes and 

accuracy checks to test sample collection, processing, and 

analysis. USGS standard water-quality sampling protocols 

(U.S. Geological Survey, variously dated) were followed when 

collecting and processing field and laboratory quality-control 

samples.

A total of 97 constituents were analyzed as environmental 

and replicate or duplicate samples for quality-control analysis 

in base-flow and stormflow samples. All constituents with 

at least four matching pairs of environmental and replicate 

or duplicate samples, with results greater than the minimum 

reporting level (MRL) for each constituent, are presented in 

table 4. The MRL is the lowest measured concentration of a 

constituent that may be reliably reported (Childress and others, 

1999). The MRL for each constituent analyzed by the USGS 

NWQL was determined by the USGS NWQL and varied with 

time during the study period (U.S. Geological Survey Nation 

Water Quality Laboratory, 2014). The average relative percent 

difference between the environmental sample and replicate or 

duplicate sample concentration for most constituents (dryweather screening samples are discussed separately) was 

less than 10 percent (table 4). There were 8 constituents with 

differences between 10 and 20 percent, and 3 constituents with 

differences greater than 20 percent. E. Coli, total coliform, 

and SSC had differences ranging from 22.8 to 29.2 percent 

(table 4). For all constituents, the highest relative percentage 

differences of sample pairs typically occurred at or near the 

MRL for a constituent.

Simple linear regression analysis was used to compare 

the base-flow and stormflow environmental and replicate or 

duplicate quality-control samples (fig. 6). Any constituent 

results that were less than the MRL were not included in the 

linear regression analysis. All measured constituents compared well with most coefficients of determination (R2

) values 

greater than 0.85; however, total mercury had an R2 value 

of 0.77. Although OMCs also compared well with R2 values 

greater than 0.85, because there were less than 10 paired values above the MRL for each OMC constituent, they have been 

excluded from figure 6. 

Generally, concentrations for most constituents analyzed 

in blank samples were at or below the MRL, indicating that 

sample collection and processing procedures were not a source 

of bias. Many values were reported as estimated values that 

were between the laboratory reporting limit (LRL) and the 

long term method detection limit (LT-MDL; Childress and 

others, 1999; Zaugg and others, 2002). The NWQL LRL for a 

constituent is calculated as twice the LT-MDL (Childress and 

others, 1999); however, there were 12 detections (9 estimated) 

of OMCs in 5 field blank samples, and 9 detections 

(5 estimated) of constituents other than OMCs in 7 field blank 

samples (table 5). The pesticides N,N-diethyl-meta-toluamide 

(DEET) and benzophenone were reported at low median 

concentrations of 0.287 and 0.170 micrograms per liter (μg/L), 

respectively. The detergent 4-nonylphenol and the flame retardant tris (2-butoxyethyl) phosphate also were detected at low 

median concentrations of 0.720 and 0.267 μg/L, respectively. 

The other OMCs with detections in blank samples (bisphenol A, naphthalene, and tributyl phosphate) were reported as 

estimated concentrations. One field blank sample had detections for chloride and ammonia, and two others had detections 

for total coliform; however, the detections were only slightly 

above the MRL for chloride and ammonia, and low for total 

coliform. Four field blank samples had detections for four 

other constituents (total sodium, ammonia, arsenic, and cyanide), which were reported as estimated concentrations. 

Additional quality-assurance procedures for water-quality 

samples are used at the USGS NWQL to quantify and assess 

all aspects of sample analysis, including bias, variability, 

method performance, and instrument sensitivity and calibration (Maloney, 2005). Deviations from the standard procedures of the laboratory (values less than the MRL or suspected 

interferences, for example) are reported as estimated values by 

all laboratories doing analyses for this study. 

Multiple dilutions of bacteria samples from Independence 

streams were used to ensure a count was obtained within the 
Table 4. Summary of quality-control (replicate and duplicate) sample results for selected constituents in base-flow and stormflow water-quality samsites, June 2006 through September 2013.[All Independence sites from table 2, fig. 1. mg/L, milligrams per liter; N, nitrogen; P, phosphorus; E. coli, Escherichia coli; MPN, most probable number; mL, milliliter; col, co

liter; E, environmental sample; Q, replicate or duplicate sample]

Statistic

Total 

dissolved 

solids

Sodium, 

dissolved

Sodium, 

total 

Chloride, 

dissolved

Ammonia 

plus organic 

nitrogen, total

Ammonia, 

dissolved

Nitrate plus 

nitrite, 

dissolved

Nitrate, 

dissolved 

Nitrite, 

dissolved 

Standard error 13.3 1.05 0.87 1.38 0.24 0.03 0.02 0.03 0.00 

Average relative percentage 

difference3

3.2 2.0 1.5 1.1 5.1 15.8 2.8 3.1 11.3 

Median relative percentage 

difference3

2.5 1.0 0.9 0.3 2.8 5.7 0.6 0.7 0.7 

Number of matched pairs 29 29 29 29 29 18 28 28 29 

Statistic Phosphorus, dissolved Phosphorus, total Total nitrogen1 E. coli (MPN/100 mL)2 Fecal coliform (col/100 mL) Total coliform (MPN/100 mL)2 Aluminum, total Cadmium, total Chromium

total 

Standard error 0.02 0.13 0.29 3,619 2,372 241,982 1,542 0.03 2.18 

Average relative percentage 

difference3

12.7 5.0 3.1 29.2 19.6 25.9 5.5 4.9 5.0 

Median relative percentage 

difference3

4.0 1.9 1.1 26.1 16.7 22.2 2.1 4.3 2.9 

Number of matched pairs 25 27 28 25 16 25 29 16 22 

Statistic Mercury, total Zinc, total Arsenic, total Suspended sediment Atrazine, total Carbazole, total

Total 

N,N-diethylm-toluamide 

(DEET)

Caffeine, 

total

Pyrene, 

total

Standard error 0.02 15.3 0.40 100.0 0.03 0.01 0.07 0.03 0.07

Average relative percentage 

difference3

13.0 5.7 5.0 22.8 17.1 7.0 13.1 9.7 19.0

Median relative percentage 

difference3

6.6 2.2 2.9 17.3 18.1 6.5 7.7 9.0 20.8

Number of matched pairs 13 25 29 37 4 3 9 4 4

1Total nitrogen equals ammonia plus nitrite plus nitrate plus organic nitrogen.2For the purposes of this report, most probable number per 100 milliliters is considered to be comparable to colonies per 100 milliliters.3Relative percentage differences are calculated from data that may contain values that are estimated. Values less than the minimum reporting level were not included in the sta

difference = [(E-Q)*100]/[(E+Q)/2].
18 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri Environmental sample concentration, in milligrams per liter

0

2

4

6

8

10

0

0.1

0.2

0.3

0.4

0.5

0

0.2

0.4

0.6

0.8

1.0

1.2

1.4

1.6

1.8

2.0

0

0.2

0.4

0.6

0.8

1.0

1.2

1.4

1.6

1.8

2.0

0

0.01

0.02

0.03

0.04

0.05

0

1

2

3

4

5

6

7

8

9

10

0

0.05

0.10

0.15

0.20

0.25

0.30

0.35

0

0.05

0.10

0.15

0.20

0.25

0.30

0.35

0

100

200

300

400

500

0 2 4 6 8 10 0 0.1 0.2 0.3 0.4 0.5

0 0.2 0.4 0.6 0.8 1.0 1.2 1.4 1.6 1.8 2.0 0 0.2 0.4 0.6 0.8 1.0 1.2 1.4 1.6 1.8 2.0 0 0.01 0.02 0.03 0.04 0.05

0 1 2 3 4 5 6 7 8 9 10 0 0.05 0.10 0.15 0.20 0.25 0.30 0.35 0 0.05 0.10 0.15 0.20 0.25 0.30 0.35

0 100 200 300 400 500

Total ammonia plus organic nitrogen Dissolved ammonia

Dissolved nitrate plus nitrite Dissolved nitrate Dissolved nitrite

Total organic nitrogen Dissolved orthophosphate Dissolved phosphorus

Dissolved chloride

Total dissolved solids Dissolved sodium Total sodium

0

50

100

150

200

250

300

0 50 100 150 200 250 300

0

50

100

150

200

250

300

0 50 100 150 200 250 300

0

200

400

600

800

1,000

0 200 400 600 800 1,000

R2=0.9849

n=29

R2=0.8792

n=18

R2=0.9973

n=28

R2=0.9971

n=28

R2=0.8376

n=29

R2=0.9835

n=18

R2=0.9953

n=24

R2=0.9341

n=25

R2=0.9997

n=29

R2=0.9998

n=29

R2=0.9996

n=29

R2=0.9954

n=29

Replicate or duplicate sample concentration, in milligrams per liter

EXPLANATION

R2 Coefficient of determination

n Number of replicate and duplicate 

pairs—Values may overlap

Figure 6. Quality-assurance data for nutrients and select constituents in field replicate or laboratory duplicate sample pairs.
Methods 19

R2=0.9692

n=22

R2=0.8868

n=21

R2=0.9474

n=29

R2=0.7681

n=13

R2=0.9613

n=25

R2=0.9824

n=29

R2=0.9701

n=29

R2=0.9978

n=16

R2=0.9805

n=28

R2=0.9721

n=27

EXPLANATION

R2 Coefficient of determination

n Number of replicate and duplicate 

pairs—Values may overlap

Environmental sample concentration, in micrograms per liter

Replicate or duplicate sample concentration, in micrograms per liter

0

0.5

1.0

1.5

2.0

2.5

3.0

3.5

0 0.5 1.0 1.5 2.0 2.5 3.0 3.5

0

2

4

6

8

10

12

0 2 4 6 8 10 12

Environmental sample concentration,

in milligrams per liter

Replicate or duplicate sample concentration, in milligrams per liter

0

10,000

20,000

30,000

40,000

0 10,000 20,000 30,000 40,000

0

0.2

0.4

0.6

0.8

1.0

1.2

1.4

1.6

1.8

2.0

0 0.2 0.4 0.6 0.8 1.0 1.2 1.4 1.6 1.8 2.0

0

10

20

30

40

50

0 10 20 30 40 50

0

10

20

30

40

50

60

70

80

90

100

0 10 20 30 40 50 60 70 80 90 100 0 10 20 30 40 50 60 70 80 90 100

0

10

20

30

40

50

60

70

80

90

100

0

0.1

0.2

0.3

0.4

0.5

0 0.1 0.2 0.3 0.4 0.5

0

50

100

150

200

250

300

350

0 50 100 150 200 250 300 350

0

2

4

6

8

10

12

14

0 2 4 6 8 10 12 14

Total aluminum Total cadmium Total chromium

Total copper Total lead Total mercury

Total zinc Total arsenic

R2=0.9881

n=37

0

1,000

2,000

3,000

4,000

5,000

6,000

0 1,000 2,000 3,000 4,000 5,000 6,000

Total phosphorus Total nitrogen Suspended sediment

Figure 6. Quality-assurance data for nutrients and select constituents in field replicate or laboratory duplicate sample pairs. 

—Continued
Table 5. Summary of detections of selected water-quality constituents and common organic micro-constituents in blank water samples at all Indepethrough September 2013. [All Independence sites from table 2, fig. 1. mg/L, milligrams per liter; N, nitrogen; MPN, most probable number; mL, milliliters; μg/L, micrograms per liter; --, not sampled; LT

tion level; na, not available] Statistic Other selected constituents Common organic micro-constituents Total sodium (mg/L) Chloride, dissolved (mg/L) Ammonia, dissolved (mg/L as N) Total coliform (MPN/100 mL)1 Arsenic, total (μg/L) Cyanide, (mg/L) Total N,N-diethyl- m-toluamide (DEET) (μg/L) Total 4-nonyl- phenol (μg/L) Total benzo- phenone (μg/L) Total bisphenol A (μg/L) Total naphthalen

(μg/L) 

Samples2 8 8 8 6 8 7 5 5 5 5 5 

Detections3 1 1 2 2 1 2 3 1 3 1 2 

Minimum4 0.06 0.141 0.01 3 0.10 0.003 0.020 0.720 0.090 0.007 0.063 

Maximum4 -- -- 0.02 7 -- 0.005 0.359 -- 0.300 -- 0.100 

Average4 -- -- 0.01 5 -- 0.004 0.222 -- 0.187 -- 0.082 

Median4 -- -- 0.01 5 -- 0.004 0.287 -- 0.170 -- 0.082 

LT-MDL 0.12 0.04 0.02 1 0.40 na 0.04 1.6 0.08 0.04 0.220 

1For the purposes of this report, most probable number per 100 milliliters is considered to be comparable to colonies per 100 milliliters. 2Number of samples analyzed for each selected constituent or common organic micro-constituent. 3Number of samples with detections of each selected constituent or common organic micro-constituent. 4Minimum, maximum, average, and median values are calculated from data that may contain values that are estimated. Values less than the minimum reporting level were not 

analysis.
Methods 21

optimal range for reporting bacteria densities. Standard USGS 

procedures were used to estimate any bacteria concentrations 

outside the optimal range (U.S. Geological Survey, variously 

dated). Replicate samples also were collected and enumerated 

for FIB. Bacteria replicates compared well with R2 values of 

0.86 for E. Coli, 0.97 for fecal coliform, and 0.88 for total 

coliform (fig. 7). 

Samples for MST collected in WY 2007 were quality 

assured by comparing E. coli samples originating from dogs, 

geese, and humans to those in the geographically specific 

genotype library. Samples from known sources in the geographically specific genotype library were updated biannually. If the samples were correctly identified, then the library 

was considered to still be valid (A.C. Carson, oral commun., 

2009).

Laboratory quality-control samples for MST samples 

collected from WY 2008 through WY 2013 included filtration 

blanks, extraction blanks, and no-template controls. Low-level 

detections of MST markers less than the laboratory determined 

level of quantification were present in a small number of blank 

samples. These detections were used to determine the lower 

detection limits for each marker. Average blank concentrations 

by laboratory sample run and method are presented in table 6.

Quality assurance for each sample run included the following processes or procedures:

1. All analyses were done in duplicate.

2. Each analytical run included a 6-point standard curve and 

an analysis blank (no-template control). 

3. Each filtration run included a procedure blank with the 

addition of spike-and-recovery control. 

4. Each extraction run included an extraction blank to test 

for cross contamination.

To guard against false-positive results, a detection threshold was established for each qPCR method. The level of detection (LoD) was defined as the 95-percent confidence interval 

around the detections on blank samples. Results for samples 

that register the presence of a constituent lower than the 

upper range observed for blank samples are reported as below 

detection limit (bdl); however, low-level quantification can be 

unreliable. To guard against interpretation of unreliable results, 

a level of quantification (LoQ) was established based on the 

lowest concentration that is reliably detected for each qPCR 

method. Results for samples that register the presence of 

bacterial DNA higher than the upper range observed for blank 

samples, but lower than the quantification limit, are reported 

as detected not quantified (dnq) and the estimated concentration value is provided. In addition, eight quality-control field 

sample replicates were collected (table 7).

Simple linear regression analysis was used to compare 

the dry-weather screening environmental and quality-control 

samples (fig. 8). Any sample results below the MRL for a 

constituent were not included in the statistical analysis. Three 

of the four constituents analyzed (total chlorine, phenols, and 

anionic surfactants) show high correlation, with R2

 values 

of 0.99, 0.90, and 0.98, respectively. All three, however, had 

one outlying sample pair with a higher concentration than the 

other sample pairs. When these outlying pairs are removed 

from the regression data, anionic surfactants still exhibit high 

correlation (R2=0.90) and chlorine shows moderate correlation 

(R2=0.48), but phenols show low correlation (R2=0.02). These 

lower correlations indicate that the reproducibility of chlorine 

and phenols analyses decreases at low concentrations. Most 

(67 percent) of the total dissolved copper analyses were at or 

below the provisional MRL (0.04 mg/L) and total dissolved 

copper analyses showed poor correlation, with an R2

 value of 

0.02 The recovery values for spike samples of total dissolved 

copper were generally less than 10 percent of full recovery 

EXPLANATION

R2 Coefficient of determination

n Number of replicate and duplicate 

pairs—Values may overlap

0

10,000

20,000

30,000

40,000

50,000

60,000

0

10,000

20,000

30,000

40,000

0 10,000 20,000 30,000 40,000 0 10,000 20,000 30,000 40,000 50,000 60,000 0 500,000 1,000,000 1,500,000 2,000,000 2,500,000 3,000,000

Escherichia coli Fecal coliform Total coliform

Environmental sample density,

in colonies per 100 milliliters

Replicate or duplicate sample density, in colonies per 100 milliliters (equivalent to MPN/100 mL)

R2=0.9736

n=16

R2=0.8811

n=25

R2=0.8622

n=25

3,000,000

0

500,000

1,000,000

1,500,000

2,000,000

2,500,000

Figure 7. Quality-assurance data for fecal indicator bacteria in field replicate or laboratory duplicate sample pairs.
22 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

(data on file at the USGS Water Science Center office in 

Lee’s Summit). Total dissolved copper analyses were discontinued during the 2011 WY. Spike sample analyses for each 

dry-weather screening analyte (total chlorine, total dissolved 

copper, phenols, and anionic surfactants) were done before 

and at the conclusion of each annual sampling period by the 

same technicians who analyzed the environmental samples. 

Dry-weather screening results in this report are considered to 

be semiquantitative.

Given collection, identification, and enumeration constraints, replicates for macroinvertebrate samples were not 

collected. Macroinvertebrate sample collection and enumeration are expensive, labor intensive, and time consuming. The 

MDNR determined that collection of an additional macroinvertebrate sample from a different reach of the same stream 

improved impairment detection by only 9.3 percent (Rabeni 

and others, 1997) and when duplicate samples were analyzed 

Table 6. Average blank sample concentrations for microbial source tracking samples by initial sample collection date and batch 

processing data group.

[copies/100 mL, copies per 100 milliliters; B. Theta, Bacteroides thetaiotaomicron; NTC, no-template control qPCR blank; --, no data; Filtration, filtration 

blank; Extraction, extraction blank; LoD, level of detection; LoQ, level of quantification]

Blank type

AllBac1

copies/100 mL 

(number of blanks)

HF1832

copies/100 mL 

(number of blanks)

B. Theta3

copies/100 mL 

(number of blanks)

BacCan4

copies/100 mL 

(number of blanks)

BoBac5

copies/100 mL 

(number of blanks)

6/13/2008–9/23/2008

NTC 60(2) 1(2) 1(1) 9(2) --

Filtration 134(9) 1(9) 1(9) 9(9) --

Extraction 113(4) 1(11) 1(4) 9(2) --

10/22/2008–8/19/2009

NTC 44(2) 1(2) 1(2) 9(2) --

Filtration 336(14) 5(14) 1(14) 18(14) --

Extraction 239(4) 2(4) 1(4) 14(4) --

3/4/2010–9/1/2010

NTC 44(2) 9(2) 1(4) 9(2) --

Filtration 610(12) 53(7) 1(12) 27(12) --

Extraction 261(3) 222(2) 1(3) 65(3) --

11/3/2010–8/19/2011

NTC 50(2) 1(2) -- 9(2) 51(2)

Filtration 115(12) 2(12) -- 10(12) 92(12)

Extraction 109(3) 1(3) -- 9(3) 51(3)

9/15/2011–6/11/2012

NTC 44(3) 1(3) -- 9(2) 53(3)

Filtration 70(11) 71(9) -- 20(8) 68(11)

Extraction 70(4) 102(4) -- 11(3) 57(4)

11/29/2012–9/19/2013

NTC 50(4) 1(3) -- 9(3) 51(3)

Filtration 265(7) 1(3) -- 9(3) 52(2)

Extraction 95(8) 1(10) -- 9(10) 51(10)

Total blanks 106 96 53 102 50

LoD 1,360 560 760 780 420

LoQ 2,600 1,320 800 1,700 840

1

AllBac, assay for general fecal contamination (Layton and others, 2006).

2

qHF183, assay for human-associated fecal contamination (Seurinck and others, 2005).

3

B. Theta, assay for human-associated fecal contamination (Carson and others, 2005).

4

BacCan, assay for canine-associated fecal contamination (Kildare and others, 2007).

5

BoBac, assay for ruminant-associated fecal contamination (Layton and others, 2006).
Table 7. Microbial source tracking replicate sample pairs.[Sample ID, laboratory identification number; E. coli, Escherichia coli; MPN/100 mL, most probable number per 100 milliliters; copies/100 mL, copies per 100 milliters; B. Th

cron; S, stormflow; --, no data; nd, not detected; na, not available (sample not collected); <, less than; bdl, below detection limit; B, base flow; dnq, concentration is below the lithe limit of detection; E, estimated; ~, duplicate qPCR results do not agree]

Sample 

ID Date

Site number 

(table 2, 

fig. 1)

Flow

E. coli

(MPN/

100 mL) 

E. coli

remarks

AllBac1

(copies/ 

100 mL)

AllBac 

remarks

HF1832

(copies/ 

100 mL)

HF183 

remarks

B. Theta3

(copies/ 

100 mL)

B. Theta

remarks

BacCan4

(copies/ 

100 mL)

BacCa

remar

1330-02 11/6/2008 7 S 30,000 -- 23,100,000 -- 11,200 -- -- nd 48,100 -- 

1330-03 11/6/2008 7 S -- -- 19,400,000 -- 19,800 -- <5,070 bdl 56,700 -- 

1521-04 6/30/2009 5 B na na 949,000 -- <2,240 bdl -- nd <3,120 bdl 

1521-05 6/30/2009 5 B na na 637,000 -- <2,240 bdl -- nd <3,120 bdl 

1538-05 7/12/2009 9 S 13,000 -- 9,280,000 -- 37,300 dnq -- nd <31,200 bdl 

1538-06 7/12/2009 9 S -- -- 10,700,000 -- <22,400 bdl <30,400 bdl 139,000 E~ 

1712-06 4/20/2010 2 B 140 -- 8,500,000 -- <5,600 bdl -- nd <15,600 bdl 

1712-07 4/20/2010 2 B -- -- 7,900,000 -- 3,730 -- -- nd <1,560 bdl 1726-06 5/19/2010 3 S 1,200 -- 2,990,000 -- 6,920 dnq -- nd 6,880 -- 

1726-07 5/19/2010 3 S -- -- 5,250,000 -- 9,380 -- -- nd 21,700 -- 

1760-07 7/20/2010 7 B 650 -- 8,870,000 -- <2,800 bdl -- nd <3,900 bdl 

1760-08 7/20/2010 7 B -- -- 11,300,000 -- <2,800 bdl -- nd <3,900 bdl 

1789-01 9/1/2010 9 S 20,000 -- 14,100,000 -- 152,000 dnq -- nd <62,400 bdl 

1789-02 9/1/2010 9 S -- -- 13,600,000 -- <112,000 bdl -- nd <156,000 bdl 

1948-01 8/19/2011 3 S 16,000 -- 27,300,000 -- 27,600 -- na na 7,280 dnq 

1948-02 8/19/2011 3 S 8,100 -- 10,300,000 -- 27,600 -- na na <3,900 bdl 

1AllBac, assay for general fecal contamination (Layton and others, 2006).2qHF183, assay for human-associated fecal contamination (Seurinck and others, 2005).3B. Theta, assay for human-associated fecal contamination (Carson and others, 2005).4BacCan, assay for canine-associated fecal contamination (Kildare and others, 2005).5BoBac, assay for ruminant-associated fecal contamination (Layton and others, 2006).
24 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

they were identified to the same impairment category 

95 percent of the time (Sarver and others, 2002). Therefore, 

a taxon-based approach to quality control and quality assurance was used at the USGS NWQL (Grotheer and others, 

2000; Moulton and others, 2000, 2002). Quality-assurance 

measures included repeat identification of new specimens by a 

different taxonomist and random reviews for a minimum of 

10 percent of all identifications. 

Taxonomic identifications at the NWQL laboratory were 

compared to the Integrated Taxonomic Information System 

(ITIS) database. Taxa listed as invalid or not found in the IT 

IS database were either corrected or flagged and alternative 

authority noted. Taxonomic keys and specimens are maintained at the USGS NWQL in Lakewood, Colo. Additional 

information on quality-control and quality-assurance procedures for data presented in this report can be found in Christensen and Krempa (2012), and for the USGS NWQL at http://

nwql.usgs.gov/Public/quality.shtml.

The accuracy and comparability of biotic indices and 

other tolerance-based metrics rely on the assigned tolerance 

values. Tolerance values from published sources generally 

are used, including Hilsenhoff (1977, 1988), Huggins and 

Moffet (1988), Lenat (1993), Bode and others (2002), and 

Klemm and others (2002). State and national listings may 

vary because some tolerance values are regionally adjusted 

to better represent local tolerance. Tolerance values are less 

accurate when applied to streams outside of the geographic 

area from which the values were established (Blocksom and 

Winters, 2006). Missouri’s taxa tolerance listing uses values 

that are representative and applicable to the study area and 

continues to be refined (Sarver, 2005); therefore, tolerance 

values from the Missouri taxa listings (Sarver, 2005) were 

used, or if unavailable, assigned from established regional 

tolerance values (Cuffney and Brightbill, 2011). Greater than 

93 percent of identified taxa in samples were assigned tolerance values (table 8, http://pubs.usgs.gov/ds/0915/downloads/

ds915_table08.xlsx).

Figure 8. Quality-assurance data for dry-weather screening samples in field replicate or laboratory duplicate 

sample pairs.

EXPLANATION

R2 Coefficient of determination

n Number of replicate and duplicate 

pairs—Values may overlap

R2=0.02

n=12

R2=0.98

n=45

R2=0.99

n=46

R2=0.48

R2=0.02

R2=0.90

R2=0.90

n=12

Excluding large value

Excluding large value

Excluding large value

0

0.02

0.04

0.06

0.08

0.10

0.12

0.14

0.16

0

0.500

1.000

1.500

2.000

2.500

0

0.50

1.00

1.50

2.00

2.50

0

0.020

0.040

0.060

0.080

0.100

0 0.50 1.00 1.50 2.00 2.50 0 0.02 0.04 0.06 0.08 0.10 0.12 0.14 0.16

0 0.020 0.040 0.060 0.080 0.100 0 0.500 1.000 1.500 2.000 2.500

Total chlorine Total dissolved copper

Phenols Anionic surfactants

Replicate or duplicate sample concentration, in milligrams per liter

Environmental sample concentration, in milligrams per liter

Table 8. Macroinvertebrate taxonomy, revised taxa names, and pollution tolerance values for taxa 

identified in samples, March 2007 through March 2013.
Water-Quality Data 25

Water-Quality Data

Water-quality data for Independence streams were 

collected from base-flow and stormflow samples at eight 

streamgage sites (sites 1 through 7 and 9; table 2; fig. 1) and 

from two ungaged sites (sites 8 and 11). Physical and chemical 

properties, TDS, sodium, chloride, nutrients, metals, OMCs, 

pesticides in streambed sediment and surface water, FIB, 

MST, and SSC data were collected. Dry-weather screening 

was done within the boundaries of each of the stream basins 

in Independence to identify possible contamination from point 

source discharges.

Continuous Streamflow and Water-Quality 

Measurements

Continuous water-quality data were collected at eight 

streamgage sites (sites 1 through 7 and 9; table 2; fig. 1) over 

various time periods during the study. From July 2005 through 

September 2013, continuous streamflow data were collected 

at sites 1, 7, and 9. Continuous streamflow data were collected 

at sites 5 and 6 beginning in July 2005, but were discontinued 

in WY 2009 at site 5 and in WY 2008 at site 6. Continuous 

streamflow data were collected at site 2 from October 2009 

through September 2013, at site 3 from October 2008 through 

September 2013, and at site 4 from November 2009 through 

September 2013. 

Monthly average streamflow was calculated for the eight 

streamgages (sites 1 through 7 and 9; table 2; fig. 1), and 

varied from 0.02 ft3

/s at site 4 in October 2011 to 1,055 ft3/s at 

site 9 in May 2007 (fig. 9). Streamflow at all sites was lowest 

during the fall (August through November) of 2011 and summer (July through August) of 2012.

Annual and monthly precipitation for WY 2006 were 

lower than in any other year from 2005 to 2013. The precipitation measured at NWS cooperative station 234158 (fig. 1) in 

Independence during CY 2006 was 66.6 cm. All other years 

from CY 2005 to CY 2013 measured from 75.5 cm to 

145.9 cm (National Climatic Data Center, 2014a). The percentage deviations of precipitation and streamflow at Lake City 

(site 9; table 2; fig. 1) during the study period as compared 

with the 27-year average indicate there is a strong positive correlation between local precipitation and streamflow (fig. 10). 

The CYs 2005, 2006, 2011, and 2012 had less than average 

precipitation and streamflow than the 27-year average (with 

Figure 9. Monthly average streamflow by site, June 2005 through September 2013.

0.001

0.01

1.00

10.0

100

1,000

10,000

June

Sept.

Dec.

Mar.

June

Sept.

Dec.

Mar.

June

Sept.

Dec.

Mar.

June

Sept.

Dec.

Mar.

June

Sept.

Dec.

Mar.

June

Sept.

Dec.

Mar.

June

Sept.

Dec.

Mar.

June

Sept.

Dec.

Mar.

June

Sept.

2005 2006 2007 2008 2009 2010 2011 2012 2013

Month and year

Site 1 (06893620)

Site 2 (06893820)

Site 3 (06893830)

Site 4 (06893890)

Site 5 (06893910)

Site 6 (06893940)

Site 7 (06893970)

Site 9 (06894000)

Site number and U.S. Geological Survey 

streamgage number

EXPLANATION

Monthly average streamflow, in cubic feet per second
26 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

the exception of August 2005 and November 2011), whereas 

most months from CYs 2008 through 2010 had greater than 

average precipitation and streamflow. The CYs 2007 and 

2013 were divided between months of lower than average and 

higher than average precipitation and streamflow. 

Seven sites (sites 1 through 5, 7 and 9; table 2; fig. 1) 

were equipped with CWQMs either for part or all of the study 

period. Sites 5, 7, and 9 were installed at the beginning of 

the study period in July 2005. Site 5 was discontinued and 

the CWQM removed in October 2009. Site 7 suffered from 

frequent shallow water depths and severe sediment deposition, 

July

Oct.

Jan.

Apr.

July

Oct.

Jan.

Apr.

July

Oct.

Jan.

Apr.

July

Oct.

Jan.

Apr.

July

Oct.

Jan.

Apr.

July

Oct.

Jan.

Apr.

July

Oct.

Jan.

Apr.

July

Oct.

Jan.

Apr.

July

2005 2006 2007 2008 2009 2010 2011 2012 2013

Month and year

-100 0 100 200 300 400

Percentage deviation from 27-year average 

Streamflow

Precipitation—Data from the 

 National Climatic Data Center 

 (2014a), years 1986–2013

EXPLANATION

Figure 10. Percentage deviations from the 27-year monthly average streamflow at Little Blue River near Lake 

City, Missouri, compared with the 27-year monthly average precipitation measured and recorded at Independence, 

Missouri, June 2005 through September 2013.
Water-Quality Data 27

forcing the relocation of the streamgage and CWQM downstream in August 2007. The CWQM was repositioned closer 

to the bank in November 2009, and the culvert was replaced 

in November 2010. The CWQM at site 7 was also temporarily 

discontinued from June to November 2010. Sites 1 through 

4 were installed in December 2011 (site 1), October 2009 

(site 2), October 2008 (site 3), and December 2009 (site 4). 

Dissolved oxygen, pH, specific conductance, water temperature, and turbidity were recorded in 15-minute intervals. The 

sensors installed at each site varied during the course of the 

study period. Beginning with CWQM installation and through 

the end of the study period in September 2013, sites 1, 2, and 

4 had all sensors installed (dissolved oxygen, pH, specific 

conductance, water temperature, and turbidity). The sensors 

for dissolved oxygen, pH, and turbidity were removed from 

site 3 in January 2012 and turbidity was reinstated in December 2012 (WY 2013). Site 7 recorded all values until November 2008, only specific conductance and water temperature 

Figure 11. Boxplots of computed daily average values of dissolved oxygen, pH, specific conductance, water temperature, and 

turbidity at continuous water-quality monitoring sites in Independence, Missouri.

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Dissolved oxygen pH

Specific conductance

Turbidity

Water temperature

Dissolved oxygen, in milligrams per liter

0

5

10

15

20

25

618 1,423 1,181 1,287 1,376 1,430 2,898

10-2

10-1

100

101

102

103

104

0

1,000

2,000

3,000

4,000

5,000

Turbidity, in nephelometric turbidity units Specific conductance, in microsiemens per 

centimeter at 25 degrees Celsius

6.5

7.0

7.5

8.0

8.5

9.0

9.5

-10

0

10

20

30

40

pH, in standard units Water temperature, in degrees Celsius

Site 1 Site 2 Site 3 Site 4 Site 5 Site 7 Site 9

Site 1 Site 2 Site 3 Site 4 Site 5 Site 7 Site 9

623 1,433 1,183 1,306 1,381 1,441 2,875

620 1,432 1,816 1,332 1,487 2,711 2,951 623 1,425 1,817 1,365 1,512 2,716 2,952

604 1,346 1,399 1,285 1,331 1,409 2,776

x

x

o

o

EXPLANATION

620 Number of values

Upper detached

Upper outside

Upper adjacent

75th percentile

Median

25th percentile

Lower adjacent

Lower outside

Lower detached
28 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

from November 2008 until January 2010 and from November 

2010 to September 2012, and then all sensors were reinstated 

from October 2012 to September 2013. Daily values were 

computed from the measured data and the summarized data 

are presented by site in the boxplots in figure 11.

For streams such as the Little Blue River that are designated as warm-water fisheries in Missouri, the MDNR 

standard for AQL for dissolved oxygen is 5 mg/L or greater 

(Missouri Department of Natural Resources, 2014b). This 

standard was used to determine compliance of dissolved 

oxygen on streams equipped with CWQMs. Daily average 

dissolved oxygen concentrations were at or below 5 mg/L less 

than 1 percent of the time for the Little Blue River sites 

(sites 2, 5, and 9; fig. 12) and nearly 10 percent of the time for 

site 4. Daily average dissolved oxygen values ranged from a 

minimum of 0.9 mg/L to a maximum of 18.6 mg/L (fig. 11, 

12), both recorded at site 7.

The pH of surface water typically ranges from 6.5 to 

8.5 standard units (Hem, 1992). The pH standards for AQL as 

set forth by the MDNR require that the pH of surface waters 

not be outside a range of 6.5 to 9.0 standard units (Missouri 

Department of Natural Resources, 2014b). No daily values for 

pH in Independence streams were outside the Missouri AQL 

range of 6.5 to 9.0 (fig. 11, 12), although a few continuous values for site 3 (table 2; fig. 1) were recorded above 9.0 standard 

units. Daily pH values ranged from 6.9 standard units at site 3 

to 8.4 standard units at sites 4 and 7. 

Specific conductance of streamflow is a surrogate measurement for ionized constituent concentration and can be 

affected by several factors, including amount of precipitation 

and runoff, point-source contamination, and underlying soil 

and rock composition. The State of Missouri does not have a 

designated guideline or standard for specific conductance of 

stream waters. The duration curve of recorded daily specific 

conductance values is shown in figure 12. The daily average 

values of specific conductance ranged from a minimum of 

221 microsiemens per centimeter at 25 °C (μS/cm at 

25 °C; hereafter referred to as μS/cm) at site 3 (table 2; fig. 1) 

to a maximum of 3,680 μS/cm at site 7 (fig. 11). The range of 

recorded specific conductance daily average values was generally higher for the smaller streams in Independence (sites 1, 3, 

and 7) than for the larger stream sites on the Little Blue River 

and the East Fork of the Little Blue River (sites 2, 4, and 9).

For warm-water streams in the State of Missouri, the 

AQL standard for water temperature is 32.2 °C (90 degrees 

Fahrenheit [°F]; Missouri Department of Natural Resources, 

2014b). Daily average values of water temperature ranged 

from -0.2 °C at site 7 (fig. 11) to 32.4°C at site 9 (table 2; 

fig. 1). The duration curve shown on figure 12 for daily 

average water temperatures recorded from the CWQMs in 

Independence streams indicates that the Missouri AQL was 

only exceeded less than 1 percent of the time. The continuous 

water-quality data, however, indicate more frequent exceedance, but only of short duration (less than 10 hours) at site 7 

during the summer of WY 2006 and sites 3 and 4 during summer WY 2010.

Turbidity in water can have a variety of sources, such as 

fine sediment, suspended organic matter, plankton or other 

microscopic organisms, organic acids, and dyes (American 

Society of Testing Materials International, 2002). Turbidity 

was measured to determine the clarity of the water and to be 

used as an indicator of the stream ecological condition and 

health. The study area in Independence is covered by EPA 

level III ecoregion 40 guidelines (U.S. Environmental Protection Agency, 2000). The recommended guideline for turbidity 

is 15.5 nephelometric turbidity units (NTU). The 15.5-NTU 

guideline is considered a reference only and was used merely 

for comparison to the measured data to determine if the data 

were considered to be high. Daily average turbidity exceeded 

the U.S. Environmental Protection Agency (EPA) recommended guideline between 15 and 60 percent of the time 

(fig. 12). Most measured turbidity values that exceeded the 

recommended 15.5-NTU guideline for turbidity of stream 

water were recorded during periods of high flow. Both the 

maximum (1,054 NTU) and minimum (0.0 NTU) daily average turbidity values for sites with CWQMs installed during 

the study period were recorded at Lee’s Summit Road (site 2; 

fig. 11). The maximum turbidity sensor range reported by the 

sensor manufacturer is 1,000 NTU; however, individual sensors used in this study recorded maximum values ranging from 

about 1,200 to 1,500 NTU that were considered valid, depending on the individual sensor. On occasion during this study, the 

maximum individual turbidity sensor values were exceeded so 

that daily average turbidity values may have been higher than 

reported on some days. 

Instantaneous Base-Flow Water Quality

From June 2006 to September 2013, 175 base-flow waterquality samples were collected at 10 sites (sites 1 through 

9 and 11; table 9, http://pubs.usgs.gov/ds/0915/downloads/

ds915_table09.xlsx). Base-flow samples were collected at five 

sites (sites 1, 5, 6, 7, and 9) beginning in June of 2006. Site 5 

was discontinued in WY 2009, and site 6 was discontinued in 

WY 2008 when the gage was removed, but was reinstated as 

a sample site in WY 2010. Five other current (2014) sample 

sites began collection in WY 2008 (site 3), WY 2009 (site 4), 

WY 2010 (sites 2 and 8), and WY 2012 (site 11). Site 8 was 

subsequently discontinued in WY 2011. Most of the samples 

were split between the spring and early summer season 

(73 samples) and the winter season (71 samples), with the 

remainder (31 samples) collected during the fall transitional 

season. Streamflow, physical and chemical properties, TDS, 

sodium, chloride, nutrients, metals, cyanide, dissolved mercury, OMCs, pesticides in streambed sediment and surface 

water, FIB, and SSC data were collected. FIB results are 

discussed in the Fecal Indicator Bacteria, Microbial Source 

Tracking, and Suspended Sediment section later in this report. 

Results from individual base-flow samples are presented in 

appendix 1.

Table 9. Summary of physical properties, nutrients, fecal indicator bacteria, and selected inorganicconstituent concentrations in base-flow samples by site, June 2006 through September 2013.
Water-Quality Data 29

Instantaneous measurements of physical and chemical 

properties taken at the time of base-flow sampling in Independence streams varied within the normal range for environmental waters (Hem, 1992; table 9). Dissolved oxygen varied 

from 3.1 mg/L to 17.2 mg/L. The range of pH was narrow and 

varied from slightly acidic at 6.3 standard units to a slightly 

alkaline value of 8.4 standard units. Specific conductance 

values for all base-flow samples ranged between 319 μS/cm 

and 2,100 μS/cm. Water samples taken during the warmer 

months of May to September typically had low specific conductance values that did not exceed 1,000 μS/cm. Two sets 

of samples taken during the winter season had higher specific 

conductance values than most of the other samples. One set 

of samples collected on December 5, 2006, had a specific 

conductance range of between 873 μS/cm and 1,720 μS/cm 

and another set of base-flow samples taken on March 3, 2013, 

had a range of 438 μS/cm to 1,900 μS/cm. All but one sample 

during the March 3, 2013, sampling had specific conductance 

values between 1,320 μS/cm and 1,900 μS/cm. Water temperature for all base-flow samples ranged from -0.1 °C to 31.1 °C 

and turbidity from 0.3 NTU to 300 NTU (table 9). 

Instantaneous Stormflow Water Quality

From June 2005 through September 2013, 205 stormflow water-quality samples were collected at 10 sites (sites 

1 through 9 and 11; table 10, http://pubs.usgs.gov/ds/0915/

downloads/ds915_table10.xlsx). Sites 1, 5, 6, 7, and 9 were 

collected beginning in June of 2005. Site 5 was discontinued 

in WY 2009, and site 6 was discontinued in WY 2008 when 

the gage was removed but was reinstated as a sample site in 

WY 2010. Five other sample sites began collection later in the 

study, in WY 2008 (site 3), WY 2009 (site 2), WY 2010 (sites 

4 and 8), and WY 2012 (site 11). During the summer months, 

80 stormflow samples were collected, 66 during winter 

months, and 59 during the fall transitional season. Streamflow, 

physical and chemical properties, TDS, sodium, chloride, 

nutrients, total metals, cyanide, dissolved mercury, OMCs, 

pesticides in surface water, FIB, and SSC data were collected. 

FIB results are discussed in the Fecal Indicator Bacteria, 

Microbial Source Tracking, and Suspended Sediment section 

later in this report. Results from individual stormflow samples 

are presented in appendix 2 (http://pubs.usgs.gov/ds/0915/

downloads/ds915_Appendix02.xlsx).

Instantaneous measurements of physical and chemical 

properties in Independence streams taken at the time of stormflow sampling, either in situ or from the collected sample in 

the laboratory, varied within the normal range for environmental waters (Hem, 1992; table 10). Dissolved oxygen ranged 

from 5.9 mg/L to 15.7 mg/L (table 10). The pH ranged from 

near neutral at 6.6 standard units to slightly alkaline at 8.3 

standard units. Specific conductance ranged from 101 μS/cm 

to 2,160 μS/cm. Water temperatures that were either measured 

in the stream at the time of sampling or a calculated average from measured CWQM data for the time period during 

sampling ranged from 0.1 °C to 28.3 °C (table 10). Turbidity 

in stormflow samples ranged from 5 NTU to 4,840 NTU.

Select Inorganic Constituents

Total dissolved solids measured in base-flow samples 

ranged from 187 mg/L to 1,190 mg/L (table 9). The median 

TDS value for most sites was close to the median for all sites 

of 441 mg/L, and ranged from 250 mg/L at site 4 (table 2; 

fig. 1) to 531 mg/L at site 7. The Little Blue River sites 

(sites 2, 5, and 9) typically had lower median TDS values than 

the smaller Independence streams (sites 1, 3, 6, 7, 8, and 11), 

although site 4 had a lower median value than that of the main 

stem Little Blue River sites. 

Minimum (61 mg/L) and maximum (1,200 mg/L) 

measured TDS values in stormflow were similar to values 

collected during base-flow conditions (table 10). The median 

TDS value for stormflow (211 mg/L; table 10) was less than 

that of base flow (441 mg/L; table 9), and the median TDS values for stormflow at each site (sites 1 through 9) were lower 

than base-flow values and ranged from 153 mg/L to 241 mg/L 

(table 10). The Little Blue River sites (sites 2, 5, and 9) had 

comparable values to those measured on the smaller streams in 

Independence (sites 1, 3, 4, 6, 7, and 8).

Daily average streamflow, estimated annual load, and 

estimated annual flow-weighted concentrations of select constituents measured at sites 1 through 9, along with the regression models used to calculate each value, are listed in table 

11. The highest estimated annual load of TDS was 72,600 

megagrams (Mg) at site 9 in WY 2010. The estimated annual 

load of TDS and annual average streamflow was highest at site 

9 for all years from WY 2006 to 2013. The estimated annual 

flow-weighted concentration of TDS ranged from 134 mg/L at 

site 2 in WY 2013 to 1,123 mg/L at site 1 in WY 2006. Site 1 

had the highest estimated annual flow-weighted concentration 

of TDS in all WYs except 2009, when it was highest at site 3 

(table 11). 

Chloride concentrations in base-flow samples ranged 

from 16.9 mg/L to 459 mg/L (table 9). Fifteen chloride 

concentrations measured in Independence streams at sites 

1 through 9 and 11 during individual sampling events in 

December 2006, January 2010 and 2011, and March 2013 

(appendix 1) were higher than the chronic standard for AQL 

of 230 mg/L previously established for Missouri streams. 

The recently updated (January 2014) Missouri AQL standard 

for chloride (Missouri Department of Natural Resources, 

2014b) is based on the hardness of the water sampled. The 

latest standard will not be used for this study because it was 

updated more recently than the study period and no hardness 

data were collected for any samples prior to November 2012. 

Site 3 also had measured chloride concentrations more than 

230 mg/L during February 2009 and 2011, and March 2010. 

No measured chloride concentrations exceeded the Missouri 

acute standard for AQL of 860 mg/L (Missouri Department of 

Natural Resources, 2014b).

Table 10. Summary of physical properties, nutrients, fecal indicator bacteria, and selected inorganic 

constituent concentrations in stormflow samples by site, June 2005 through September 2013.
30 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

Figure 12. Frequency of exceedance of daily average dissolved oxygen, pH, specific conductance, water temperature, and 

turbidity at sampling sites equipped with continuous water-quality monitors in Independence, Missouri. Period of record at individual 

sites varies.

0

5

10

15

20

Dissolved oxygen

pH

Specific conductance

0 20 40 60 80 100

0

1,000

2,000

3,000

4,000

6.5

7.0

7.5

8.0

8.5

pH, in standard units Dissolved oxygen, in milligrams per liter Specific conductance, in microsiemens per 

centimeter at 25 degrees Celsius

Frequency of exceedance, in percent

Missouri Department of Natural Resources protection

of aquatic life for warm-water fisheries minimum

standard (5 milligrams per liter)

Missouri Department of Natural Resources protection of 

aquatic life minimum standard (6.5 standard units)

Missouri Department of Natural Resources protection of 

aquatic life maximum standard (9.0 standard units)

Site 1 (06893620)

Site 2 (06893820)

Site 3 (06893830)

Site 4 (06893890)

Site 5 (06893910)

Site 7 (06893970)

Site 9 (06894000)

Site number and U.S. Geological Survey 

streamgage number—Table 2; fig. 1

EXPLANATION
Water-Quality Data 31

Measured chloride concentrations in stormflow ranged 

from 3.4 mg/L to 508 mg/L (table 10). The highest concentration of chloride measured in stormflow samples occurred in 

February 2011 at site 3 (appendix 2). No measured chloride 

concentrations exceeded the Missouri acute AQL standard 

of 860 mg/L (Missouri Department of Natural Resources, 

2014b). There were 11 measured chloride concentrations in 

stormflow that exceeded the Missouri chronic standard for 

AQL of 230 mg/L for chloride. Five of the highest chloride 

values were recorded at site 7 (appendix 2). 

The estimated annual load of chloride was highest at 

downstream site 9 for all WYs from 2006 to 2013 (table 11). 

The highest estimated annual chloride load was 14,100 Mg 

at site 9 in WY 2010. The estimated annual flow-weighted 

chloride concentrations were highest at site 7 for the first three 

years of record (WYs 2006 to 2008), but were highest at 

site 3 when the site was installed in WY 2009 to WY 2013. 

The highest estimated annual flow-weighted concentration for 

chloride was 152 mg/L in WY 2013 at site 3. Site 7 had the 

second highest annual flow-weighted chloride concentrations 

for all years after the installation of site 3. 

Nutrients

Concentrations of nutrients in base-flow samples, including total N and P, are summarized in table 9. Site 11 (table 2; 

fig. 1) had the highest median concentrations for total N 

(2.2 mg/L) and P (0.152 mg/L). All other sites ranged from 

0.5 to 1.5 mg/L for total N and 0.045 to 0.131 mg/L for total P. 

Median total organic N and dissolved nitrate account for 

84 percent of the median total N concentration in all base-flow 

Figure 12. Frequency of exceedance of daily average dissolved oxygen, pH, specific conductance, water temperature, and 

turbidity at sampling sites equipped with continuous water-quality monitors in Independence, Missouri. Period of record at individual 

sites varies.—Continued

Water temperature

Turbidity

35

0

5

10

15

20

25

30

U.S. Environmental Protection Agency

recommended ecoregion 40 guideline

(15.5 nephelometric turbidity units)

Missouri Department of Natural Resources protection 

of aquatic life standard (32.2 degrees Celsius 

[90 degrees Fahrenheit])

0

100

101

102

103

Water temperature, in degrees Celsius Turbidity, in nephelometric turbidity units

0 20 40 60 80 100

Frequency of exceedance, in percent

Site 1 (06893620)

Site 2 (06893820)

Site 3 (06893830)

Site 4 (06893890)

Site 5 (06893910)

Site 7 (06893970)

Site 9 (06894000)

Site number and U.S. Geological Survey 

streamgage number—Table 2; fig. 1

EXPLANATION
Table 11. Regression models for estimating annual loads, flow-weighted concentrations, and densities of selected sampled water-quality constituen[n, number of samples; R2, coefficient of determination; RMSE, root mean squared error; ft3/s, cubic feet per second; ln, natural logarithm; L, instantaneous (daily) load; ln(Q), l

ln(streamflow); ln(Q2), ln of streamflow squared; T, decimal time minus center of decimal time; T2, decimal time squared; sin, sine; cos, cosine; --, no data; E. coli, Escherichia c

of load calculation, recorded zero average daily streamflows were assigned a minimal value of 0.01 ft3/s] Site number (table 2; fig. 1) Regression model n R2 RMSE1 Sample average daily streamflow (ft3/s) Study period of record average daily streamflow (ft3/s) Average annual

2006 2007 2008 2009 

Total dissolved solids 1 ln(L)=0.773ln(Q)-0.016ln(Q2)-0.019T-0.16T2+0.166sin(2πT)+0.139cos(2πT)+9.36 55 0.978 0.278 77.0 6.33 2.16 6.32 9.56 9.19 

2 ln(L)=0.917ln(Q)+0.266sin(2πT)+0.200cos(2πT)+3.83 28 0.977 0.240 198 88.7 -- -- -- -- 

3 ln(L)=0.939ln(Q)-0.012ln(Q2)+0.421sin(2πT)+0.242cos(2πT)+1.69 34 0.992 0.245 62.2 5.53 -- -- -- 6.78 

54 ln(L)=0.948ln(Q)+0.263 26 0.993 0.179 22.8 27.2 -- -- -- -- 

5 ln(L)=0.882ln(Q)+0.152sin(2πT)+0.242cos(2πT)+4.61 26 0.979 0.222 533 130 28.6 146 184 151 

6 ln(L)=0.796ln(Q)-0.018ln(Q2)+0.203sin(2πT)+0.388cos(2πT)+2.13 38 0.972 0.358 97.6 4.44 1.48 5.14 6.39 -- 

57 ln(L)=0.805ln(Q)-0.020ln(Q2)-0.052T+0.252sin(2πT)+0.377cos(2πT)+2.32 53 0.976 0.342 81.0 8.14 3.22 10.6 10.5 9.44 

9 ln(L)=0.907ln(Q)-0.024ln(Q2)+0.169sin(2πT)+0.150cos(2πT)+4.825 54 0.980 0.227 541 178 41.3 202 259 226 

Chloride 1 ln(L)=0.738ln(Q)-0.031ln(Q2)+0.405sin(2πT)+0.460cos(2πT)+0.434 71 0.930 0.469 61.6 6.33 2.16 6.32 9.56 9.19 

52 ln(L)=1.02ln(Q)-0.059ln(Q2)+0.075T+0.129T2+0.524sin(2πT)+0.332cos(2πT)+1.93 33 0.934 0.455 176 88.7 -- -- -- -- 

3 ln(L)=0.942ln(Q)-0.017ln(Q2)+0.797sin(2πT)+0.311cos(2πT)+0.386 45 0.972 0.433 47.5 5.53 -- -- -- 6.78 

54 ln(L)=0.972ln(Q)+0.001ln(Q2)+0.044T+0.077T2+0.114sin(2πT)+0.044cos(2πT)-1.37 34 0.987 0.263 28.3 27.2 -- -- -- -- 

5 ln(L)=0.841ln(Q)+0.356sin(2πT)+0.522cos(2πT)+2.855 27 0.927 0.430 504 130 28.6 146 184 151 

56 ln(L)=0.735ln(Q)-0.025ln(Q2)+0.555sin(2πT)+0.502cos(2πT)+0.071 39 0.916 0.625 90.8 4.44 1.48 5.14 6.39 -- 

7 ln(L)=0.763ln(Q)-0.028ln(Q2)+0.449sin(2πT)+0.742cos(2πT)+0.256 60 0.924 0.600 74.1 8.14 3.22 10.6 10.5 9.44 

59 ln(L)=0.875ln(Q)-0.046ln(Q2)+0.396sin(2πT)+0.292cos(2πT)+2.94 61 0.915 0.480 553 178 41.3 202 259 226 

Ammonia 1 ln(L)=1.15ln(Q)+0.050ln(Q2)-0.033T+0.434T2+0.762sin(2πT)-0.321cos(2πT)+9.36 68 0.924 0.799 79.8 6.33 2.16 6.32 9.56 9.19 

72 ln(L)=1.10ln(Q)-0.173ln(Q2)+0.642T-5.01 28 0.781 0.983 198 88.7 -- -- -- -- 73 ln(L)=1.03ln(Q)+0.283T-7.987 34 0.878 1.11 62.2 5.53 -- -- -- 6.78 

4 ln(L)=0.886ln(Q)-7.97 27 0.888 0.722 22.7 27.2 -- -- -- -- 5 ln(L)=1.03ln(Q)-0.201T+0.696sin(2πT)+0.301cos(2πT)-3.99 27 0.884 0.732 539 130 28.6 146 184 151 

76 ln(L)=1.06ln(Q)+0.727sin(2πT)+0.107cos(2πT)-6.42 38 0.880 1.05 97.6 4.44 1.48 5.14 6.39 -- 77 ln(L)=1.14ln(Q)+0.646sin(2πT)+0.211cos(2πT)-8.02 53 0.835 1.34 81.0 8.14 3.22 10.6 10.5 9.44 79 ln(L)=1.26ln(Q)+0.033ln(Q2)-0.098T+0.076T2+0.497sin(2πT)+0.039cos(2πT)-5.02 55 0.856 0.981 555 178 41.3 202 259 226 
Site number 

(table 2; 

fig. 1)

Regression model n R2 RMSE1

Sample average 

daily 

streamflow 

(ft3/s)

Study period of 

record average 

daily streamflow 

(ft3/s)

Average annual

2006 2007 2008 2009 

Nitrate plus nitrite

1 ln(L)=0.853ln(Q)+0.22ln(Q2)-0.023sin(2πT)-0.178cos(2πT)-3.93 68 0.978 0.295 79.8 6.33 2.16 6.32 9.56 9.19 

2 ln(L)=1.28ln(Q)-0.063ln(Q2)+0.256T-2.69 28 0.918 0.631 198 88.7 -- -- -- -- 

3 ln(L)=0.998ln(Q)-6.34 34 0.917 0.863 62.2 5.53 -- -- -- 6.78 

84 ln(L)=1.05ln(Q)-6.92 27 0.865 0.958 22.7 27.2 -- -- -- -- 

5 ln(L)=1.24ln(Q)-0.135T+0.222sin(2πT)+0.141cos(2πT)-2.17 27 0.955 0.469 539 130 28.6 146 184 151 

6 ln(L)=0.999ln(Q)-4.10 38 0.968 0.453 97.6 4.44 1.48 5.14 6.39 -- 

87 ln(L)=1.01ln(Q)-4.74 53 0.947 0.631 81.0 8.14 3.22 10.6 10.5 9.44 

9 ln(L)=1.20ln(Q)-1.97 55 0.922 0.593 555 178 41.3 202 259 226 

Organic nitrogen

1 ln(L)=1.50ln(Q)-0.041ln(Q2)-0.039T+0.019T2+0.122sin(2πT)-0.092cos(2πT)-3.93 68 0.988 0.399 79.8 6.33 2.16 6.32 9.56 9.19 

2 ln(L)=1.47ln(Q)+0.111T-0.302sin(2πT)-0.119cos(2πT)-2.05 28 0.983 0.331 198 88.7 -- -- -- -- 

3 ln(L)=1.14ln(Q)+0.019ln(Q2)+0.057T-5.13 34 0.995 0.242 62.2 5.53 -- -- -- 6.78 

54 ln(L)=1.10ln(Q)-0.368sin(2πT)-0.119cos(2πT)-6.08 27 0.965 0.484 22.7 27.2 -- -- -- -- 

5 ln(L)=1.43ln(Q)+0.048ln(Q2)-1.26 27 0.976 0.369 539 130 28.6 146 184 151 

6 ln(L)=1.35ln(Q)+0.051ln(Q2)-0.133T-3.97 38 0.985 0.442 97.6 4.44 1.48 5.14 6.39 -- 7 ln(L)=1.43ln(Q)+0.054ln(Q2)-4.84 53 0.986 0.439 81.0 8.14 3.22 10.6 10.5 9.44 

9 ln(L)=1.46ln(Q)+0.055ln(Q2)-0.095sin(2πT)-0.171cos(2πT)-1.17 55 0.981 0.361 555 178 41.3 202 259 226 

Total phosphorous

1 ln(L)=1.41ln(Q)+0.061ln(Q2)-0.033T+0.171T2 -0.112sin(2πT)-0.174cos(2πT)-4.92 68 0.986 0.408 79.8 6.33 2.16 6.32 9.56 9.19 

2 ln(L)=1.74ln(Q)+0.269T-0.684sin(2πT)-0.164cos(2πT)-3.48 28 0.965 0.560 198 88.7 -- -- -- -- 

3 ln(L)=1.22ln(Q)+0.046ln(Q2)-0.044T+0.070T2 -0.184sin(2πT)-0.105cos(2πT)-4.92 34 0.995 0.313 62.2 5.53 -- -- -- 6.78 

4 ln(L)=1.18ln(Q)+0.018ln(Q2)-0.434T-0.420T2 -1.02sin(2πT)+0.039cos(2πT)-7.44 27 0.881 0.907 22.7 27.2 -- -- -- -- 

5 ln(L)=1.56n(Q)+0.059ln(Q2)-2.60 27 0.957 0.541 539 130 28.6 146 184 151 

6 ln(L)=1.41ln(Q)-0.057ln(Q2)-0.128T-5.04 38 0.980 0.534 97.6 4.44 1.48 5.14 6.39 -- 

7 ln(L)=1.46ln(Q)+0.051ln(Q2)-0.197sin(2πT)-0.278cos(2πT)-5.44 53 0.974 0.634 81.0 8.14 3.22 10.6 10.5 9.44 

9 ln(L)=1.68ln(Q)+0.071ln(Q2)-0.355sin(2πT)-0.289cos(2πT)-2.54 55 0.967 0.549 555 178 41.3 202 259 226 

Table 11. Regression models for estimating annual loads, flow-weighted concentrations, and densities of selected sampled water-quality constituen[n, number of samples; R2, coefficient of determination; RMSE, root mean squared error; ft3/s, cubic feet per second; ln, natural logarithm; L, instantaneous (daily) load; ln(Q), l

ln(streamflow); ln(Q2), ln of streamflow squared; T, decimal time minus center of decimal time; T2, decimal time squared; sin, sine; cos, cosine; --, no data; E. coli, Escherichia c

of load calculation, recorded zero average daily streamflows were assigned a minimal value of 0.01 ft3/s]
Table 11. Regression models for estimating annual loads, flow-weighted concentrations, and densities of selected sampled water-quality constituen[n, number of samples; R2, coefficient of determination; RMSE, root mean squared error; ft3/s, cubic feet per second; ln, natural logarithm; L, instantaneous (daily) load; ln(Q), l

ln(streamflow); ln(Q2), ln of streamflow squared; T, decimal time minus center of decimal time; T2, decimal time squared; sin, sine; cos, cosine; --, no data; E. coli, Escherichia c

of load calculation, recorded zero average daily streamflows were assigned a minimal value of 0.01 ft3/s] Site number (table 2; fig. 1) Regression model n R2 RMSE1 Sample average daily streamflow (ft3/s) Study period of record average daily streamflow (ft3/s) Average annual

2006 2007 2008 2009 

Total nitrogen 1 ln(L)=1.18ln(Q)-0.057ln(Q2)-0.035T+0.066sin(2πT)-0.150cos(2πT)-2.91 68 0.989 0.291 79.8 6.33 2.16 6.32 9.56 9.19 

2 ln(L)=1.40ln(Q)+0.176T-1.61 28 0.979 0.332 198 88.7 -- -- -- -- 

3 ln(L)=1.12ln(Q)+0.012ln(Q2)+0.083T-4.71 34 0.995 0.227 62.2 5.53 -- -- -- 6.78 

4 ln(L)=1.09ln(Q)-0.367sin(2πT)-0.005cos(2πT)-5.57 27 0.957 0.528 22.7 27.2 -- -- -- -- 

55 ln(L)=1.34ln(Q)-0.722 27 0.974 0.357 539 130 28.6 146 184 151 

6 ln(L)=1.22ln(Q)+0.026ln(Q2)-0.075T-3.09 38 0.986 0.382 97.6 4.44 1.48 5.14 6.39 -- 

7 ln(L)=1.29ln(Q)+0.028ln(Q2)+0.088sin(2πT)-0.173cos(2πT)-3.65 53 0.984 0.429 81.0 8.14 3.22 10.6 10.5 9.44 

9 ln(L)=1.38ln(Q)+0.043ln(Q2)-0.708 55 0.975 0.38 555 178 41.3 202 259 226 

E. coli (colonies/100 mL)9 1 ln(L)=1.89ln(Q)-0.182sin(2πT)-0.898cos(2πT)+13.8 48 0.964 0.905 81.1 6.33 2.16 6.32 9.56 9.19 

2 ln(L)=2.52ln(Q)-1.66sin(2πT)-0.263cos(2πT)+14.1 25 0.907 1.31 188 88.7 -- -- -- -- 

3 ln(L)=1.54ln(Q)+0.072ln(Q2)+0.476T+0.070T2 -1.19sin(2πT)-1.16cos(2πT)+8.70 30 0.897 1.74 55.5 5.53 -- -- -- 6.78 

4 ln(L)=0.872ln(Q)-0.125ln(Q2)-2.11sin(2πT)-0.655cos(2πT)+10.6 24 0.673 1.55 21.9 27.2 -- -- -- -- 

5 ln(L)=2.25ln(Q)-0.1q5ln(Q2)-0.733sin(2πT)-0.326cos(2πT)+15.9 25 0.936 1.01 547 130 28.6 146 184 151 

6 ln(L)=1.73ln(Q)-0.105T -0.773sin(2πT)-1.06cos(2πT)+13.3 35 0.964 0.930 91.9 4.44 1.48 5.14 6.39 -- 

7 ln(L)=1.82ln(Q)-0.616sin(2πT)-1.02cos(2πT)+13.1 45 0.958 1.00 89.9 8.14 3.22 10.6 10.5 9.44 

9 ln(L)=2.35ln(Q)-1.16sin(2πT)-0.757cos(2πT)+15.1 50 0.918 1.26 618 178 41.3 202 259 226 

Suspended sediment 1 ln(L)=1.62n(Q)+0.054ln(Q2)-0.072T+1.36 58 0.961 0.742 71.3 6.33 2.16 6.32 9.56 9.19 

2 ln(L)=2.04ln(Q)-0.604sin(2πT)-0.123cos(2πT)+2.65 28 0.948 0.807 198 88.7 -- -- -- -- 

3 ln(L)=1.24ln(Q)-0.798 33 0.945 0.861 64.1 5.53 -- -- -- 6.78 

4 ln(L)=1.25ln(Q)-0.0003(Q2)+0.480T-0.582T2 -0.972sin(2πT)+0.0358cos(2πT)-1.34 26 0.811 1.28 22.8 27.2 -- -- -- -- 

5 ln(L)=1.77ln(Q)+0.078ln(Q2)-0.150T+3.81 26 0.965 0.569 533 130 28.6 146 184 151 

6 ln(L)=1.56ln(Q)+0.057ln(Q2)-0.137T+1.62 36 0.964 0.812 95.6 4.44 1.48 5.14 6.39 -- 7 ln(L)=1.65ln(Q)+0.170sin(2πT)-0.400cos(2πT)+1.39 51 0.957 0.910 82.4 8.14 3.22 10.6 10.5 9.44 

9 ln(L)=2.00ln(Q)+0.055ln(Q2)-0.194sin(2πT)-0.406cos(2πT)+3.98 53 0.947 0.852 614 178 41.3 202 259 226 
Table 11. Regression models for estimating annual loads, flow-weighted concentrations, and densities of selected sampled water-quality constituen[n, number of samples; R2, coefficient of determination; RMSE, root mean squared error; ft3/s, cubic feet per second; ln, natural logarithm; L, instantaneous (daily) load; ln(Q), l

ln(streamflow); ln(Q2), ln of streamflow squared; T, decimal time minus center of decimal time; T2, decimal time squared; sin, sine; cos, cosine; --, no data; E. coli, Escherichia c

of load calculation, recorded zero average daily streamflows were assigned a minimal value of 0.01 ft3/s]

Site number 

(table 2; 

fig. 1)

Estimated annual2 load3 Estimated annual2 flow-weighted c

2006 2007 2008 2009 2010 2011 2012 2013 2006 2007 2008 2009 2010 

Total dissolved solids

1 2,166 3,041 3,790 3,421 3,553 2,402 2,607 2,647 1,123 539 444 417 409 

2 -- -- -- -- 22,400 9,320 8,340 11,600 -- -- -- -- 148 

3 -- -- -- 2,570 2,900 1,550 1,550 2,150 -- -- -- 424 406 

54 -- -- -- -- -- 3,140 2,090 5,570 -- -- -- -- -- 

5 8,130 31,700 40,400 36,100 -- -- -- -- 318 242 245 268 -- 

6 523 1,410 1,640 -- -- -- -- -- 395 307 287 -- -- 

57 1,410 4,270 3,640 3,440 4,190 1,830 -- 1,810 490 452 387 408 363 

9 11,700 46,800 61,000 56,700 72,600 29,500 23,400 40,600 317 259 264 281 259 

Chloride

1 130 300 361 410 459 257 201 265 67.4 53.2 42.2 50.0 52.8 

52 -- -- -- -- 7,360 2,460 2,570 7,070 -- -- -- -- 48.5 

3 -- -- -- 799 865 479 472 699 -- -- -- 132.0 121.2 

54 -- -- -- -- -- 542 378 1,310 -- -- -- -- -- 

5 1,650 5,950 7,560 7,020 -- -- -- -- 64.6 45.5 45.8 52.0 -- 

56 108 296 328 -- -- -- -- -- 81.7 64.5 57.3 -- -- 

7 239 851 727 729 950 450 -- 503 83.1 90.1 77.0 86.5 82.4 

59 2,370 9,300 12,100 11,600 14,100 6,460 5,170 8,360 64.3 51.6 52.2 57.5 50.3 

Ammonia

1 0.160 0.792 0.721 0.566 0.518 0.317 0.140 0.424 0.083 0.140 0.084 0.069 0.06

72 -- -- -- -- 1.84 1.48 2.51 8.42 -- -- -- -- 0.073 -- -- -- 0.189 0.304 0.197 0.245 0.427 -- -- -- 0.031 0.04

4 -- -- -- -- -- 0.880 0.601 1.47 -- -- -- -- -- 

5 2.20 12.2 11.4 7.95 -- -- -- -- 0.086 0.093 0.069 0.059 -- 

76 0.131 0.681 0.663 -- -- -- -- -- 0.099 0.148 0.116 -- -- 77 0.123 0.784 0.583 0.589 0.698 0.277 -- 0.399 0.043 0.083 0.062 0.070 0.0679 2.28 19.4 12.5 8.98 12.0 3.53 2.96 12.8 0.062 0.108 0.054 0.044 0.04
Site number (table 2; fig. 1) Estimated annual2 load3 Estimated annual2 flow-weighted c

2006 2007 2008 2009 2010 2011 2012 2013 2006 2007 2008 2009 2010 

Nitrate plus nitrite 1 1.35 3.81 5.67 5.65 6.08 3.34 1.94 2.96 0.700 0.675 0.664 0.688 0.70

2 -- -- -- -- 58.7 18.2 23.2 71.4 -- -- -- -- 0.3

3 -- -- -- 1.21 1.42 0.698 0.682 0.915 -- -- -- 0.200 0.19

84 -- -- -- -- -- 3.38 2.15 6.63 -- -- -- -- -- 

5 7.59 67.7 64.4 43.6 -- -- -- -- 0.297 0.518 0.391 0.323 -- 

6 0.874 3.03 3.77 -- -- -- -- -- 0.661 0.660 0.661 -- -- 

87 1.37 4.95 4.94 4.40 6.03 2.30 -- 2.72 0.476 0.524 0.525 0.522 0.52

9 11.8 94.6 115 93.8 140.0 37.6 28.1 68.1 0.320 0.524 0.497 0.465 0.49

Organic nitrogen 1 1.99 14.2 22.8 10.9 10.4 6.41 1.90 4.96 1.03 2.52 2.67 1.33 1.20 

2 -- -- -- -- 299 37.6 47.9 178 -- -- -- -- 1.97 

3 -- -- -- 3.65 4.59 2.15 2.32 3.41 -- -- -- 0.603 0.64

54 -- -- -- -- -- 8.47 5.20 18.3 -- -- -- -- -- 

5 14.2 300 251 156 -- -- -- -- 0.556 2.29 1.52 1.16 -- 

6 1.28 8.76 8.67 -- -- -- -- -- 0.968 1.91 1.52 -- -- 

7 2.80 22.8 22.5 12.2 19.6 4.50 -- 7.32 0.97 2.41 2.39 1.45 -- 

9 24.30 601 521 328 646 92.7 68.8 262 0.659 3.33 2.25 1.63 2.30 

Total phosphorous 1 0.81 4.26 8.84 3.71 3.77 2.34 0.76 1.67 0.420 0.755 1.035 0.452 0.43

2 -- -- -- -- 132 10.7 22.1 100 -- -- -- -- 0.87

3 -- -- -- 0.625 0.704 0.285 0.364 0.643 -- -- -- 0.103 0.09

4 -- -- -- -- -- 1.55 1.57 3.35 -- -- -- -- -- 

5 3.67 130 91.0 51.4 -- -- -- -- 0.144 0.993 0.552 0.381 -- 6 0.444 3.56 3.39 -- -- -- -- -- 0.336 0.776 0.594 -- -- 

7 1.49 9.45 12.0 5.40 9.88 2.13 3.17 0.518 1.000 1.274 0.641 0.85

9 7.70 359 305 135 348 28.7 25.2 115 0.209 1.990 1.319 0.669 1.24

Table 11. Regression models for estimating annual loads, flow-weighted concentrations, and densities of selected sampled water-quality constituen[n, number of samples; R2, coefficient of determination; RMSE, root mean squared error; ft3/s, cubic feet per second; ln, natural logarithm; L, instantaneous (daily) load; ln(Q), l

ln(streamflow); ln(Q2), ln of streamflow squared; T, decimal time minus center of decimal time; T2, decimal time squared; sin, sine; cos, cosine; --, no data; E. coli, Escherichia c

of load calculation, recorded zero average daily streamflows were assigned a minimal value of 0.01 ft3/s]
Table 11. Regression models for estimating annual loads, flow-weighted concentrations, and densities of selected sampled water-quality constituen[n, number of samples; R2, coefficient of determination; RMSE, root mean squared error; ft3/s, cubic feet per second; ln, natural logarithm; L, instantaneous (daily) load; ln(Q), l

ln(streamflow); ln(Q2), ln of streamflow squared; T, decimal time minus center of decimal time; T2, decimal time squared; sin, sine; cos, cosine; --, no data; E. coli, Escherichia c

of load calculation, recorded zero average daily streamflows were assigned a minimal value of 0.01 ft3/s]

Site number 

(table 2; 

fig. 1)

Estimated annual2 load3 Estimated annual2 flow-weighted c

2006 2007 2008 2009 2010 2011 2012 2013 2006 2007 2008 2009 2010 

Total nitrogen

1 6.65 19.2 37.7 21.5 22.6 14.4 8.2 12.0 3.45 3.40 4.42 2.62 2.60 

2 -- -- -- -- 360 62.2 75.9 294 -- -- -- -- 2.37 

3 -- -- -- 4.93 6.34 3.12 3.41 5.12 -- -- -- 0.814 0.8

4 -- -- -- -- -- 12.3 7.86 25.2 -- -- -- -- -- 

55 22.9 296 318 221 -- -- -- -- 0.897 2.26 1.93 1.64 -- 

6 2.57 12.8 14.1 -- -- -- -- -- 1.94 2.79 2.47 -- -- 

7 5.01 30.4 29.4 20.8 30.5 8.82 -- 12.9 1.74 3.22 3.12 2.47 2.65 

9 36.7 659 611 440 757 142 104 331 1.00 3.65 2.64 2.18 2.70 

E. coli (colonies/100 mL)9

1 254,000 1,960,000 6,530,000 1,880,000 2,230,000 1,680,000 282,000 738,000 13,168 34,729 76,490 22,908 25,665 

2 -- -- -- -- 146,000,000 2,060,000 12,400,000 31,900,000 -- -- -- -- 96,303 

3 -- -- -- 38,700 110,000 55,400 123,000 105,000 -- -- -- 639 1,542 

4 -- -- -- -- -- 85,800 29,900 112,000 -- -- -- -- -- 

5 597,000 17,800,000 26,800,000 10,000,000 -- -- -- -- 2,338 13,615 16,275 7,411 -- 6 103,000 567,000 1,350,000 -- -- -- -- -- 7,793 12,353 23,658 -- -- 

7 483,000 1,910,000 4,490,000 1,240,000 2,970,000 560,000 -- 659,000 16,797 20,216 47,704 14,710 25,762 

9 1,940,000 86,700,000 168,000,000 29,300,000 126,000,000 4,000,000 8,670,000 27,000,000 5,261 48,064 72,637 14,518 44,935 

Suspended sediment

1 471 4,030 8,060 2,980 2,820 1,700 411 905 244 714 944 363 325 

2 -- -- -- -- 250,000 10,300 16,700 80,900 -- -- -- -- 1,649 

3 -- -- -- 470 555 240 248 348 -- -- -- 77.6 77.8 

4 -- -- -- -- -- 998 960 922 -- -- -- -- -- 

5 2,560 194,000 80,800 33,700 -- -- -- -- 100 1,484 491 250 -- 6 390 4,470 4,020 -- -- -- -- -- 295 974 704 -- -- 

7 1,650 14,500 13,600 8,260 12,900 2,970 -- 5,170 574 1,535 1,445 980 1,119 

9 7,010 808,000 523,000 219,000 635,000 35,100 30,000 206,000 190 4,479 2,261 1,085 2,265 

1RMSE is calculated from the estimated residual variance of the model.2Water year, October 1 of previous year through September 30.3Estimated loads are given in metric tons (megagram) except for E. coli loads, which are in billions of colonies.4Estimated flow-weighted concentrations are given in milligrams per liter (mg/L) except for E. coli concentrations that are in colonies per 100 milliliters.5Model does not meet the Turnbull-Weiss normality test criteria for Adjusted Maximum Likelihood Estimation (AMLE) method. Least Absolute Deviation (LAD) method used to estimate loads.6Streamflow measurements begin on November 20, 2009.7Model does not meet the Turnbull-Weiss normality test criteria due to the large proportion of censored values. Visual inspection indicates acceptable distribution of the residuals.8Model does not meet the Turnbull-Weiss normality test criteria for the AMLE method. Less than values were assigned concentration values equal to the detection limit of 0.04 mg/L before applying the LAD method.9For purposes of this report, colonies per 100 mL is considered equivalent to most probable number per 100 mL.
38 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

samples, with total organic N accounting for 37 percent and 

dissolved nitrate for 46 percent (table 9). Median dissolved P 

accounted for 68 percent of median total P for base-flow samples (table 9). Sites 1 and 11 had the highest measured values 

for nitrate plus nitrite, nitrate, nitrite, total N, orthophosphate, 

and dissolved and total P in base-flow samples (appendix 1). 

Median dissolved P was 68 percent of median total P for baseflow samples.

Concentrations of nutrients, including total N and P, 

in stormflow are summarized in table 10. Sites 1 and 7 had 

the highest median concentrations (3.2 mg/L) of total N in 

stormflow, and median total N concentrations at all other sites 

ranged between 1.2 mg/L and 2.8 mg/L. During the study 

period, total organic N and dissolved nitrate accounted for 

98 percent of the median total N in stormflow samples, with 

78 percent being total organic N and 20 percent being dissolved nitrate. Although the highest total P concentration 

(1.29 mg/L as P) in stormflow samples was measured at site 

11, there was only one sample collected at that site during the 

study period so no median value was calculated. Site 7 had the 

highest median total P concentration (1.19 mg/L) in stormflow 

samples and median total P at all other sites ranged from 0.188 

to 0.851 mg/L (table 10). Median dissolved P accounted for 

only about 13 percent of median total P in stormflow samples 

(table 10). Site 7 had the highest measured concentrations for 

total N and total P, ammonia plus organic N, and total organic 

N (appendix 2). These concentrations were all recorded 

from one May 2006 sample that also had a high SSC 

(71,600 mg/L). The lowest median concentration of total N 

(1.2 mg/L) in stormflow samples was measured at sites 3 and 

4, and site 3 also had the lowest median concentration of total 

P (0.188 mg/L). 

The EPA proposed provisional nutrient standards for level 

III ecoregion 40 streams, including those in Independence are 

0.86 mg/L for total N and 0.09 mg/L for total P (U.S. Environmental Protection Agency, 2000). Nutrient concentrations in 

base-flow samples from the smaller streams in Independence 

(sites 1, 3, 4, 6, 7, 8, and 11) exceeded the EPA standards for 

total N in 52 percent of samples and total P in 48 percent of 

samples (appendix 1). Base-flow nutrient concentrations at the 

Little Blue River sites (Lee’s Summit Road, site 2; 39th Street, 

site 5; and Lake City, site 9) exceeded the EPA standards for 

total N in 24 percent of samples and total P in 30 percent of 

samples. 

Nutrient concentrations in stormflow on the smaller 

streams (sites 1, 3, 4, 6, 7, 8, and 11) exceeded the EPA provisional standards for total N (0.86 mg/L; U.S. Environmental 

Protection Agency, 2000) in about 93 percent of samples 

and total P (0.09 mg/L) in about 94 percent of samples 

(appendix 2). Nutrient concentrations in stormflow at the 

Little Blue River sites (sites 2, 5, and 9) exceeded the EPA 

provisional standards for total N in about 92 percent of 

samples and total P in about 97 percent of samples. 

Site 9 had the highest estimated annual loads during most 

years for nutrient constituents (total N, total organic N, nitrate 

plus nitrite, ammonia, and total P) and the highest annual 

average daily streamflow (table 11). The only exception was 

the estimated annual load of nitrate plus nitrite, which was 

higher at site 2 in 2013. The estimated annual load of all nutrient constituents consistently increased each year from 2011 to 

2013 at site 2, but decreased at site 9 from 2011 to 2012 and 

then increased in 2013.

The estimated annual flow-weighted concentrations for 

most nutrient constituents were highest at sites 1 or 9 for the 

period of WYs 2006 to 2011, and highest at sites 1 or 2 from 

WYs 2012 to 2013. Exceptions to this were estimated annual 

flow-weighted concentrations for ammonia during all years 

except WYs 2011 and 2013, and total P during WY 2006. 

Site 6 had the highest estimated annual flow-weighted concentration of ammonia for all years of operation of the site (WYs 

2006 to 2008). From WYs 2012 to 2013, the estimated annual 

flow-weighted concentrations of nutrient constituents (total N, 

total organic N, nitrate plus nitrite, ammonia, and total P) were 

higher on the Little Blue River at site 2 than downstream at 

site 9. Site 1 had the highest estimated annual flow-weighted 

concentration for at least one nutrient constituent nearly onehalf the time from WYs 2006 to 2013. In WY 2011, all estimated annual flow-weighted concentrations for nutrients were 

highest at site 1. Nitrate plus nitrite was consistently higher 

at site 1, except in WY 2013. The highest estimated annual 

flow-weighted concentrations for the study period from WYs 

2006 to 2013 for most nutrient constituents were highest during WYs 2007 and 2008. The only exception was nitrate plus 

nitrite, which was highest during WYs 2012 and 2013. Sites 3 

and 4, beginning with their installment in WYs 2009 and 2011, 

had the lowest estimated annual flow-weighted concentrations 

during most years and for most nutrient constituents, except 

ammonia in WYs 2012 and 2013.

Total Recoverable Metals

Total recoverable aluminum, cadmium, chromium, copper, lead, zinc, arsenic, and dissolved mercury were analyzed 

in base-flow and stormflow samples from sites 1 through 9 and 

11. Total recoverable metals are determined from an unfiltered 

sample that includes both dissolved and suspended material. 

The Missouri AQL standards are only for dissolved metals 

rather than total recoverable metals (except for mercury, which 

is a dissolved metals standard), and are pH and hardness 

dependent and therefore vary by sample (Missouri Department 

of Natural Resources, 2014b). Hardness was not analyzed in 

base-flow or stormflow samples collected for the project during WYs 2005 to 2013. The total recoverable metals results 

were therefore unable to be compared to the Missouri AQL 

standards. Concentrations for most total recoverable metals, 

except aluminum, in base-flow samples were generally low 

and were less than 5 μg/L (appendix 1). Concentrations for 

most total recoverable metals, except aluminum, in stormflow 

generally were higher but were less than 80 μg/L (appendix 2). 

Among trace elements analyzed in base-flow and stormflow samples, total recoverable aluminum concentrations were 
Water-Quality Data 39

highest. Total recoverable aluminum concentrations ranged 

from 7 μg/L to 1,420 μg/L in base flow (table 9), and 8.5 μg/L 

to 170,000 μg/L in stormflow (table 10), at least two orders of 

magnitude greater than the combined total of all other metals. The highest concentration of total recoverable aluminum 

(170,000 μg/L) was measured in a stormflow sample from 

site 7 in March 2006, which also had the highest SSC (appendix 2). In October 2007, dissolved metals were analyzed in 

one set of stormflow samples in addition to total recoverable 

metals. The dissolved metals concentrations were lower than 

the total recoverable metals concentrations, and did not exceed 

Missouri standards for AQL (Missouri Department of Natural 

Resources, 2014b).

Common Organic Micro-Constituents and 

Pesticides in Streambed Sediment and Surface 

Water

At sites 1 through 9 and 11 (table 2; fig. 1), 71 base-flow 

samples were analyzed between June 2006 and July 2013 for 

11 categories of OMCs (table 12). Four categories of OMCs 

were detected in 50 percent or more of base-flow samples; 

Table 12. Categories of common organic micro-constituents detected in urban streams.

[PAH, polycyclic aromatic hydrocarbon; categories adopted from Zaugg and others, 2002; Lee and others, 2005; Wilkison and others, 2006]

Antioxidant Detergent Disinfectant Fire retardant

5-Methyl-1H-benzotriazole 4-Cumylphenol Phenol BDE congener 47

3-tert-Butyl-4-hydroxyanisole 

(BHA)

4-Nonylphenol Tribromomethane Tributyl phosphate

4-n-Octylphenol Triclosan Tris(2-chloroethyl) phosphate

4-tert-Octylphenol Tris(dichloroisopropyl) phosphate

Ethoxy-nonylphenol

Diethoxy-nonylphenol

Ethoxy-octylphenol

Diethoxy-octylphenol

Flavoring or fragrance PAH or combustion by-product Pesticide Plastics

3-Methyl-1H-indole (skatol) 1-Methylnaphthalene 1,4-Dichlorobenzene Bis(2-ethylhexyl) phthalate

Acetophenone 2,6-Dimethylnaphthalene 3,4-Dichlorophenyl isocyanate Bisphenol A

Acetyl hexamethyl tetrahydro 

naphthalene (AHTN)

2-Methylnaphthalene 9,10-Anthraquinone Diethyl phthalate

Camphor Anthracene Atrazine Triethyl citrate

D-Limonene Benzo[a]pyrene Benzophenone Triphenyl phosphate

Hexahydro-hexamethyl cyclopenta-benzopyran (HHCB)Fluoranthene Bromacil Tris(2-butoxyethyl) phosphate

Indole Naphthalene Carbaryl

Isoborneol p-Cresol Carbazole

Isoquinoline Phenanthrene Chlorpyrifos

Menthol Pyrene Diazinon

Methyl salicylate Dichlorvos

Metalaxyl

Metolachlor

N,N-Diethyl-m-toluamide 

(DEET)

Pentachlorophenol

Prometon

Solvent Sterol or stanol Stimulant

Isophorone 3-β-Coprostanol Caffeine

Isopropylbenzene (cumene) Cholesterol Cotinine

Tetrachloroethene β-Sitosterol

β-Stigmastanol
40 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

polyaromatic hydrocarbons (PAHs) and combustion products 

(66 percent), pesticides (100 percent), plastics (52 percent), 

and sterols and stanols (72 percent; table 13). Most detections 

of OMCs were not quantified because they were at or near 

the NWQL LRL (appendix 1). Pesticides detected in at least 

one-half of all base-flow samples were atrazine (76 percent), 

DEET (76 percent) and prometon (59 percent); 3,4-dichlorophenyl isocyanate also was detected about one-half of the time 

(49 percent; appendix 1). The sterol or stanol cholesterol also 

was detected in low concentrations in 72 percent of base-flow 

samples. All other OMCs were detected less than one-half 

of the time. The median concentration of total OMCs of all 

base-flow samples was 0.06 μg/L, with a minimum combined 

concentration of 0.003 μg/L and a maximum of 53.3 μg/L 

(table 13).

Common organic microconstituents were analyzed in 

130 stormflow samples collected from Independence 

streams from June 2005 to September 2013 (table 14). The 

median total OMC concentration for all stormflow samples 

(0.13 μg/L) was higher than that of base-flow (0.06 μg/L; 

table 13). Five categories of OMCs had detections more than 

90 percent of the time; PAHs and combustion products 

(97 percent), pesticides (100 percent), plastics (95 percent), 

sterols or stanols (90 percent), and stimulants (94 percent). 

Most detections of OMCs in stormflow were less than 2 μg/L 

or less than the NWQL LRL for the constituent and not quantified (appendix 2). The most commonly detected pesticides 

were DEET (95 percent) and 9,10-anthraquinone (96 percent), 

and the most commonly detected PAHs or combustion products were fluoranthene (94 percent) and pyrene (92 percent; 

data on file at the USGS Water Science Center in Lee’s Summit). The stimulant caffeine was also detected 93 percent of 

the time. The pesticide 3,4-dichlorophenyl isocyanate had the 

highest median concentration (0.48 μg/L) and was detected 

73 percent of the time. The PAH or combustion product fluoranthene had the highest median concentration (0.26 μg/L) 

and was the most frequently detected. The detergent diethoxynonylphenol (all isomers) had the highest median concentration (1.12 μg/L) of all OMCs, and was detected in 28 percent 

of samples (appendix 2). Sites 1and 6 had the highest median 

detections of total OMCs in stormflow (0.16 μg/L, table 14). 

The combined minimum concentration of all OMCs in stormflow was 0.002 μg/L and the combined maximum was 

26.4 μg/L. All stormflow samples had at least one quantified 

detection of at least one OMC compound (appendix 2). 

Fourteen base-flow samples were analyzed for pesticides 

(table 15) in streambed sediment at all sites in July 2010, two 

sites (sites 2 and 9) in April 2011, and two sites (sites 1 and 9) 

in September 2012 and July 2013. One-half of the constituents 

analyzed (11 of 22) had detections in one or more samples and 

trans-chlordane had the most detections (table 16). Of the sites 

sampled in July 2010, sites 3 and 4 had no pesticide detections 

(appendix 1). 

Two base-flow samples and 17 stormflow samples were 

analyzed for pesticides in water. Base-flow samples were 

analyzed for two sites on the Little Blue River (sites 2 and 

9) in April 2011. Stormflow samples were analyzed for all 

sites (sites 1 through 9 and 11) in September 2010; sites 3 and 

9 in June 2011, and sites 1 and 9 in August and November 

2011 and June 2012 and 2013. Twenty-six constituents were 

analyzed (table 15), and none had measureable detections in 

either base flow or stormflow because all results were less than 

the NWQL LRL of the compound (appendix 2). 

Fecal Indicator Bacteria, Microbial Source 

Tracking, and Suspended Sediment 

Fecal indicator bacteria were analyzed in 159 base-flow 

and 168 stormflow samples collected from June 2005 to 

September 2013. E. coli, fecal coliform, and total coliform 

bacteria were analyzed at sites 1 through 9 and 11 between 

June 2005 and September 2013. Fecal coliform analysis was 

discontinued at the end of July 2010. Median E. Coli densities 

measured in base-flow samples ranged from 19 MPN/100 mL 

at site 3 to 410 MPN/100 mL at site 7 (table 9). Median fecal 

coliform densities in base-flow samples collected in June 2006 

through July 2010 at sites 1 through 11 ranged from 4 col/100 

mL at site 3 to 530 col/100 mL at site 1, and median total coliform densities ranged from 2,950 MPN/100 mL at site 2 

to 33,000 MPN/100 mL at site 11. The Little Blue River 

sites (sites 2, 5, and 9) had lower median FIB densities, including E. Coli, than sites 1, 6, 7, 8, and 11 (table 9), except 

site 3, which is directly downstream from the spillway of a 

small lake, and site 4, located about 1.5 kilometers downstream from Blue Springs Lake.

Median E. Coli densities measured in stormflow 

samples at sites with multiple samples (sites 1 through 9) 

in August 2005 through September 2013 ranged from 

1,200 MPN/100 mL at site 3 to 31,000 MPN/100 mL at 

site 1 (table 10). Median fecal coliform densities measured 

from August 2005 through July 2010 at sites 1 through 9 during stormflow ranged from 960 col/100 mL at site 3 to 

42,000 col/100 mL at site 1. Median total coliform 

densities ranged from 57,000 MPN/100 mL at site 3 to 

1,190,000 MPN/100 mL at site 1. Although site 11 had lower 

median measured E. Coli and total coliform concentrations 

than the lowest median concentrations given above, site 11 

was not used for comparison because only one stormflow sample was collected during the study. The Little Blue River sites 

(sites 2, 5 and 9) had lower median FIB densities in stormflow 

than the smaller Independence streams (sites 1, 6 through 8, 

and 11) except sites 3 and 4 (table 10). 

Estimated annual loads of E. Coli ranged from 

29,900 billion colonies at site 4 during WY 2012 to 

168,000,000 billion colonies at site 9 during WY 2008 

(table 11). The estimated annual load of E. Coli was highest at 

site 9 during WYs 2006 through 2009 and 2011, and highest at 

site 2, located upstream from site 9 during WYs 2010, 2012, 

and 2013. Sites 2 and 9 both had higher annual daily average 

streamflow than the other Independence sites. Site 7 had the 

highest estimated annual flow-weighted concentration of 
Table 13. Summary of constituent concentrations by category of total common organic micro-constituents by site in base-flow samples, June 2006 t[μg/L, micrograms per liter; PAHs, polyaromatic hydrocarbons; OMC, common organic micro-constituents; ft3/s, cubic feet per second; --, no data]

Site number 

and number 

of samples 

(table 2; 

fig. 1)

Statistic

Total 

antioxidants 

(μg/L)

Total 

detergents 

(μg/L)

Total 

disinfectants 

(μg/L)

Total

 fire 

retardants 

(μg/L)

Total

flavorings 

and 

fragrances 

(μg/L)

Total 

PAHs and 

combustion 

products 

(μg/L)

Total 

pesticides 

(μg/L)

Total 

plastics 

(μg/L)

Total 

solvents 

(μg/L)

Total 

sterols and 

stanols 

(μg/L)

T

stim

(μ

All (71) Detections2 6 30 7 33 26 47 71 37 20 51 3

Total individual 

constituents detected3

6 40 7 45 32 135 303 57 20 107 4

Minimum4 0.06 0.04 0.02 0.01 0.003 0.004 0.004 0.01 0.004 0.11 

Maximum4 0.60 2.26 0.14 0.10 0.14 0.52 53.30 2.24 0.02 2.61 

Average4 0.21 0.37 0.08 0.05 0.02 0.04 0.35 0.29 0.01 0.59 

Median4 0.08 0.22 0.08 0.05 0.02 0.02 0.06 0.11 0.01 0.43 

1 (12) Detections2 2 8 2 4 5 10 12 9 2 9 

Minimum4 0.07 0.04 0.02 0.02 0.003 0.004 0.004 0.02 0.004 0.17 

Maximum4 0.08 1.18 0.14 0.10 0.14 0.52 2.30 2.24 0.01 1.62 

Average4 0.07 0.38 0.08 0.05 0.03 0.07 0.16 0.35 0.01 0.56 Median4 0.07 0.24 0.08 0.04 0.02 0.03 0.06 0.13 0.01 0.42 

2 (5) Detections2 0 2 0 2 1 5 5 0 2 2 

Minimum4 -- 0.06 -- 0.04 0.02 0.01 0.01 -- 0.01 0.11 

Maximum4 -- 0.12 -- 0.06 0.02 0.13 1.42 -- 0.01 0.37 

Average4 -- 0.09 -- 0.05 0.02 0.03 0.12 -- 0.01 0.20 Median4 -- 0.09 -- 0.04 0.02 0.01 0.04 -- 0.01 0.15 

3 (7) Detections2 1 3 2 5 1 5 7 5 3 7 

Minimum4 0.08 0.23 0.07 0.01 0.09 0.01 0.01 0.01 0.01 0.23 

Maximum4 0.08 1.08 0.11 0.07 0.09 0.03 2.84 1.05 0.02 2.61 

Average4 0.08 0.66 0.09 0.05 0.09 0.02 0.15 0.27 0.02 0.86 Median4 0.08 0.66 0.09 0.06 0.09 0.02 0.05 0.17 0.02 0.60 

4 (5) Detections2 0 2 0 2 3 3 5 1 3 4 

Minimum4 -- 0.11 -- 0.03 0.01 0.01 0.02 0.05 0.01 0.13 

Maximum4 -- 0.16 -- 0.09 0.02 0.10 0.66 0.17 0.01 0.82 

Average4 -- 0.13 -- 0.05 0.01 0.03 0.11 0.11 0.01 0.38 Median4 -- 0.13 -- 0.03 0.01 0.01 0.06 0.11 0.01 0.32 
Table 13. Summary of constituent concentrations by category of total common organic micro-constituents by site in base-flow samples, June 2006 tContinued [μg/L, micrograms per liter; PAHs, polyaromatic hydrocarbons; OMC, common organic micro-constituents; ft3/s, cubic feet per second; --, no data] Site number and number of samples (table 2; fig. 1) Statistic Total antioxidants (μg/L) Total detergents (μg/L) Total disinfectants (μg/L) Total fire retardants (μg/L) Total flavorings and fragrances (μg/L) Total PAHs and combustion products (μg/L) Total pesticides (μg/L) Total plastics (μg/L) Total solvents (μg/L) Total sterols and stanols (μg/L) T

stim

(μ

5 (7) Detections2 0 2 0 2 2 3 7 5 2 3 

Minimum4 -- 0.13 -- 0.02 0.01 0.01 0.01 0.01 0.01 0.32 

Maximum4 -- 0.37 -- 0.06 0.05 0.05 4.33 1.80 0.01 1.24 

Average4 -- 0.25 -- 0.04 0.02 0.03 0.29 0.40 0.01 0.88 

Median4 -- 0.25 -- 0.05 0.01 0.03 0.08 0.08 0.01 0.94 

6 (9) Detections2 1 4 2 6 5 7 9 7 2 5 

Minimum4 0.38 0.09 0.08 0.02 0.003 0.004 0.01 0.01 0.01 0.14 

Maximum4 0.38 1.44 0.09 0.07 0.07 0.15 53.30 1.29 0.02 2.56 

Average4 0.38 0.40 0.08 0.05 0.03 0.03 1.59 0.32 0.01 0.81 Median4 0.38 0.21 0.08 0.05 0.02 0.02 0.07 0.08 0.01 0.50 

7 (11) Detections2 1 5 1 4 5 6 11 3 2 10 

Minimum4 0.06 0.05 0.03 0.02 0.003 0.004 0.01 0.04 0.01 0.16 

Maximum4 0.06 2.26 0.03 0.06 0.03 0.11 2.91 0.49 0.01 2.35 

Average4 0.06 0.60 0.03 0.04 0.01 0.02 0.16 0.20 0.01 0.60 

Median4 0.06 0.20 0.03 0.04 0.01 0.01 0.05 0.13 0.01 0.46 

8 (2) Detections2 0 0 0 1 2 1 2 2 0 2 

Minimum4 -- -- -- 0.04 0.02 0.09 0.02 0.02 -- 0.12 

Maximum4 -- -- -- 0.04 0.02 0.09 0.08 0.62 -- 0.46 

Average4 -- -- -- 0.04 0.02 0.09 0.05 0.32 -- 0.24 Median4 -- -- -- 0.04 0.02 0.09 0.05 0.32 -- 0.19 

9 (12) Detections2 1 3 0 7 2 6 12 5 4 9 

Minimum4 0.60 0.09 -- 0.01 0.02 0.01 0.01 0.01 0.01 0.17 

Maximum4 0.60 0.37 -- 0.10 0.02 0.05 4.21 0.44 0.01 0.87 

Average4 0.60 0.24 -- 0.05 0.02 0.02 0.21 0.15 0.01 0.41 Median4 0.60 0.25 -- 0.05 0.02 0.02 0.07 0.13 0.01 0.32 
Table 13. Summary of constituent concentrations by category of total common organic micro-constituents by site in base-flow samples, June 2006 tContinued[μg/L, micrograms per liter; PAHs, polyaromatic hydrocarbons; OMC, common organic micro-constituents; ft3/s, cubic feet per second; --, no data]

Site number 

and number 

of samples 

(table 2; 

fig. 1)

Statistic

Total 

antioxidants 

(μg/L)

Total 

detergents 

(μg/L)

Total 

disinfectants 

(μg/L)

Total

 fire 

retardants 

(μg/L)

Total

flavorings 

and 

fragrances 

(μg/L)

Total 

PAHs and 

combustion 

products 

(μg/L)

Total 

pesticides 

(μg/L)

Total 

plastics 

(μg/L)

Total 

solvents 

(μg/L)

Total 

sterols and 

stanols 

(μg/L)

T

stim

(μ

11 (1) Detections2 0 1 0 0 0 1 1 0 0 0 

Minimum4 -- 0.10 -- -- -- 0.01 0.03 -- -- -- 

Maximum4 -- 0.10 -- -- -- 0.01 0.11 -- -- -- 

Average4 -- 0.10 -- -- -- 0.01 0.07 -- -- -- 

Median4 -- 0.10 -- -- -- 0.01 0.07 -- -- -- 

1Streamflow calculated from an established stage-discharge relation for the site at the time of sampling.2Number of samples with one or more detections of OMC greater than the method detection level. OMC categories may have more than one OMC detected per sample.3Total number of individual OMCs detected. Detections of individual OMCs are presented in the appendixes.4Minimum, maximum, average, and median values are calculated from data that may contain estimated values. Values less than the minimum reporting level were not include
Table 14. Summary of constituent concentrations by category of total common organic micro-constituents by site in stormflow samples, June 2005 t[μg/L, micrograms per liter; PAHs, polyaromatic hydrocarbons; OMC, common organic micro-constituents; ft3/s, cubic feet per second; --, no data] Site number and number of samples (table 2; fig. 1) Statistic Total antioxidants (μg/L) Total detergents (μg/L) Total disinfectants (μg/L) Total fire retardants (μg/L) Total flavorings and fragrances (μg/L) Total PAHs and combustion products (μg/L) Total pesticides (μg/L) Total plastics (μg/L) Total solvents (μg/L) Total sterols and stanols (μg/L) Tot

stimu

(μg

All (130) Detections2 45 92 47 101 79 126 130 123 59 117 122 

Total individual constituents detected3 45 187 53 177 165 795 981 352 62 271 147 

Minimum4 0.08 0.02 0.02 0.02 0.003 0.004 0.002 0.01 0.01 0.06 0

Maximum4 1.10 3.27 0.54 2.07 1.10 4.68 20.40 6.21 0.13 26.40 3

Average4 0.28 0.51 0.12 0.09 0.12 0.20 0.37 0.28 0.03 1.26 0Median4 0.22 0.33 0.09 0.07 0.07 0.07 0.13 0.16 0.02 0.78 0

1 (24) Detections2 14 21 13 20 21 24 24 23 14 24 22 

Minimum4 0.13 0.04 0.04 0.02 0.01 0.01 0.01 0.01 0.01 0.06 0

Maximum4 1.10 3.27 0.50 0.19 1.10 4.62 19.00 6.21 0.13 13.00 3

Average4 0.36 0.71 0.14 0.09 0.15 0.30 0.59 0.35 0.03 1.99 0Median4 0.28 0.50 0.09 0.08 0.09 0.10 0.15 0.17 0.03 1.16 0

2 (6) Detections2 2 3 3 5 5 6 6 6 4 6 6 

Minimum4 0.17 0.04 0.04 0.02 0.01 0.01 0.02 0.02 0.01 0.19 0

Maximum4 0.19 1.05 0.09 0.34 0.26 0.36 0.56 2.52 0.04 1.34 0

Average4 0.18 0.30 0.07 0.08 0.09 0.10 0.13 0.38 0.02 0.61 0Median4 0.18 0.18 0.08 0.05 0.06 0.08 0.11 0.14 0.02 0.56 0

3 (11) Detections2 7 7 3 9 6 11 11 11 5 11 11 

Minimum4 0.08 0.03 0.04 0.02 0.02 0.004 0.01 0.01 0.01 0.06 0

Maximum4 0.30 1.17 0.10 0.11 0.04 0.31 0.49 0.85 0.03 4.27 0

Average4 0.20 0.33 0.07 0.06 0.03 0.05 0.12 0.23 0.02 1.22 0Median4 0.22 0.28 0.05 0.05 0.03 0.02 0.09 0.15 0.02 1.06 0
Table 14. Summary of constituent concentrations by category of total common organic micro-constituents by site in stormflow samples, June 2005 tContinued[μg/L, micrograms per liter; PAHs, polyaromatic hydrocarbons; OMC, common organic micro-constituents; ft3/s, cubic feet per second; --, no data]

Site number 

and number 

of samples 

(table 2; 

fig. 1)

Statistic

Total 

antioxidants 

(μg/L)

Total 

detergents 

(μg/L)

Total 

disinfectants 

(μg/L)

Total 

fire 

retardants 

(μg/L)

Total 

flavorings 

and 

fragrances 

(μg/L)

Total 

PAHs and 

combustion 

products 

(μg/L)

Total 

pesticides 

(μg/L)

Total 

plastics 

(μg/L)

Total 

solvents 

(μg/L)

Total 

sterols and 

stanols 

(μg/L)

Tot

stimu

(μg

4 (5) Detections2 0 3 2 2 2 3 5 3 3 5 3 

Minimum4 -- 0.04 0.03 0.03 0.01 0.01 0.02 0.03 0.01 0.28 0

Maximum4 -- 0.87 0.05 0.07 0.03 0.02 0.76 0.55 0.02 1.87 0

Average4 -- 0.34 0.04 0.05 0.02 0.01 0.14 0.20 0.01 0.71 0Median4 -- 0.23 0.04 0.05 0.02 0.01 0.07 0.13 0.02 0.62 0

5 (19) Detections2 2 14 4 13 11 18 19 17 5 15 18 

Minimum4 0.20 0.04 0.05 0.04 0.004 0.004 0.01 0.01 0.01 0.20 0

Maximum4 0.23 1.74 0.48 0.25 0.33 1.03 2.60 0.75 0.03 1.70 0

Average4 0.21 0.46 0.16 0.08 0.09 0.13 0.31 0.22 0.02 0.78 0Median4 0.21 0.32 0.06 0.08 0.06 0.07 0.14 0.15 0.02 0.75 0

6 (16) Detections2 5 12 6 14 10 16 16 16 7 14 15 

Minimum4 0.21 0.02 0.04 0.02 0.01 0.004 0.01 0.01 0.01 0.15 0

Maximum4 0.48 1.44 0.54 0.32 0.58 4.65 20.40 1.90 0.04 3.44 0

Average4 0.31 0.46 0.19 0.11 0.09 0.37 0.63 0.36 0.02 0.98 0

Median4 0.24 0.34 0.14 0.08 0.04 0.14 0.16 0.20 0.03 0.84 0

7 (24) Detections2 10 17 9 18 14 24 24 23 13 21 23 

Minimum4 0.16 0.04 0.02 0.02 0.003 0.01 0.002 0.01 0.01 0.14 0

Maximum4 0.81 1.95 0.28 2.07 0.50 1.87 6.20 2.20 0.05 26.40 0

Average4 0.33 0.58 0.11 0.13 0.13 0.18 0.38 0.27 0.03 1.61 0Median4 0.23 0.38 0.09 0.07 0.09 0.09 0.15 0.20 0.03 0.78 0

8 (2) Detections2 1 1 0 1 1 2 2 1 0 2 2 

Minimum4 0.09 0.19 -- 0.02 0.02 0.01 0.01 0.01 -- 0.08 0

Maximum4 0.09 0.19 -- 0.11 0.02 0.04 1.19 1.48 -- 0.54 0

Average4 0.09 0.19 -- 0.07 0.02 0.02 0.17 0.41 -- 0.29 0Median4 0.09 0.19 -- 0.07 0.02 0.01 0.06 0.03 -- 0.20 0
Table 14. Summary of constituent concentrations by category of total common organic micro-constituents by site in stormflow samples, June 2005 tContinued [μg/L, micrograms per liter; PAHs, polyaromatic hydrocarbons; OMC, common organic micro-constituents; ft3/s, cubic feet per second; --, no data] Site number and number of samples (table 2; fig. 1) Statistic Total antioxidants (μg/L) Total detergents (μg/L) Total disinfectants (μg/L) Total fire retardants (μg/L) Total flavorings and fragrances (μg/L) Total PAHs and combustion products (μg/L) Total pesticides (μg/L) Total plastics (μg/L) Total solvents (μg/L) Total sterols and stanols (μg/L) Tot

stimu

(μg

9 (23) Detections2 4 14 7 19 9 22 23 23 8 19 22 

Minimum4 0.09 0.03 0.03 0.02 0.01 0.01 0.01 0.01 0.01 0.11 0

Maximum4 0.14 1.31 0.19 0.22 0.45 1.39 8.10 0.54 0.05 1.30 0

Average4 0.12 0.32 0.09 0.07 0.14 0.14 0.28 0.17 0.02 0.56 0Median4 0.12 0.26 0.07 0.06 0.12 0.06 0.11 0.15 0.02 0.53 0

1Average streamflow for the sampled storm interval. 2Number of samples with one or more detections of OMC greater than the method detection level. OMC categories may have more than one OMC detected per sample. 3Total number of individual OMCs detected. Detections of individual OMCs are presented in the appendixes. 4Minimum, maximum, average, and median values are calculated from data that may contain estimated values. Values less than the minimum reporting level were not include
Water-Quality Data 47

E. coli during WY 2006, and site 9 had the highest flowweighted concentration during WY 2007. Site 1 had the 

highest flow-weighted concentrations in WYs 2008, 2009, and 

2011, and site 2 had the highest flow-weighted concentrations 

in WYs 2010, 2012, and 2013. The lowest estimated annual 

flow-weighted concentrations of E. Coli were measured at 

site 5 in WYs 2006 and 2008, site 6 in WY 2007, and site 3 in 

WYs 2009 and 2010. Site 4 had the lowest estimated annual 

flow-weighted concentrations of E. Coli of all the sites for 

all three years of collection there (WYs 2011 to 2013). The 

estimated annual flow-weighted concentrations of E. Coli

measured on the Little Blue River at site 2 in WY 2011, 

site 5 in WY 2006, and at site 9 during WYs 2006 and 2011 

were less than one-half of the lowest concentration measured 

in any other year at those sites.

The MST results for WY 2007 collected at two Little 

Blue River sites (sites 5 and 9) were combined to compare 

with the smaller Independence streams. Samples from sites 6 

and 7, and the Little Blue River sites (5 and 9) were analyzed 

for host sources of E. coli bacteria during one base-flow and 

stormflow samplings in August and October 2007 (table 17). 

Additional stormflow samples were collected at sites 5 and 

9 in May 2007 and at site 1 in October 2007. Site 6 had the 

highest percentage of human sources of E. coli (26.7 percent) 

for base-flow samples. Percentages of E. coli from human 

sources in stormflow samples in the three smaller streams 

(sites 1, 6, and 7) were higher (20.0 to 27.8 percent) than for 

sites 5 and 9. 

E. coli and MST markers were analyzed using libraryindependent methods in 119 base-flow, 89 stormflow, and 4 

snowmelt samples collected from June 2008 through September 2013. MST samples were collected at sites 1 through 

9 and 11. In addition, 48 fecal source samples were collected 

between September 2011 and May 2013 from human, ruminant, dog, and several domestic and wild animal sources. 

Twelve sewage influent samples also were collected from 

September 2011 through May 2013 (table 18).

E. coli was detected in 112 of 119 base-flow samples 

(E. coli was not analyzed in 5 samples), all 89 stormflow 

samples, and all 4 snowmelt samples for which MST markers 

also were analyzed (table 19, http://pubs.usgs.gov/ds/0915/

downloads/ds915_table19.xlsx). AllBac, a general marker 

used to indicate the presence of fecal material in bacterial 

sources, was detected in all samples. B.theta, a human marker, 

was detected and quantifiable in 4 base-flow and 9 stormflow 

samples out of 45 analyzed. HF183, a human marker, was 

detected in 60 of 119 samples and quantifiable in 37 samples; 

BacCan, a canine marker, was detected in 22 of 119 samples 

and quantifiable in 12 samples; and BoBac, a ruminant 

marker, was detected in 41 of 71 samples and quantifiable in 

37 samples. For stormflow samples, HF183 was detected in 

73 of 89 samples and quantifiable in 57 samples; BacCan was 

detected in 57 of 89 samples and quantifiable in 39 samples; 

and BoBac was detected in 41 of 46 samples and quantifiable in 31 samples. HF183 was detected, but not quantified, 

in two of four snowmelt samples; BacCan was detected, but 

not quantified, in two samples; and BoBac was detected and 

quantified in all four snowmelt samples. 

During the recreation season, about 45 percent of baseflow samples and about 98 percent of stormflow samples 

exceeded the Missouri standard (Missouri Department of 

Natural Resources, 2014b) for whole-body contact recreation 

for E. coli of 206 colony forming units per 100 milliliters 

(CFU/100 mL) (table 19). E. coli and host-associated genetic 

markers (human, canine, and ruminant) were detected more 

frequently and at higher concentrations during stormflow than 

Table 15. Pesticide constituents analyzed in streambed sediment and surface-water samples.

[DDT, dichlorodiphenyltrichloroethane; HCH, hexachlorocyclohexane; DDD, dichlorodiphenyl dichloroethane; DDE, dichlorodiphenyldichloroethylene]

Pesticides analyzed in streambed sediment samples (dry weight, in micrograms per kilogram)

Aldrin Heptachlor epoxide p,p’-DDT Aroclor 1260

α-Endosulfan Heptachlor p,p’-Methoxychlor

α-HCH Hexachlorobenzene Toxaphene

β-HCH Lindane trans-Chlordane

cis-Chlordane Mirex trans-Nonachlor

Dieldrin p,p’-DDD Aroclor 1016 plus Aroclor 1242

Endrin p,p’-DDE Aroclor 1254

Pesticides analyzed in unfiltered surface-water samples (in micrograms per liter)

Aldrin δ-HCH Lindane Aroclor 1221

α-Endosulfan Dieldrin p,p’-DDD Aroclor 1232

α-HCH Endosulfan sulfate p,p’-DDE Aroclor 1248

β-Endosulfan Endrin aldehyde p,p’-DDT Aroclor 1254

β-HCH Endrin Toxaphene Aroclor 1260

Chlordane (technical) Heptachlor epoxide trans-Chlordane

cis-Chlordane Heptachlor Aroclor 1016 plus Aroclor 1242

Table 19. Microbial source tracking samples by site, season, and streamflow condition.
Table 16. Summary of selected pesticides detected in streambed sediment samples during base flow at all Independence sites, July 2010 through J[μg/kg, micrograms per kilogram; p,p’-DDD, p,p’-dichlorodiphenyl dichloroethane; p,p’-DDE, p,p’-dichlorodiphenyldichloroethylene; p,p’-DDT, p,p’-dichlorodiphenyltrichlorofrom table 2, fig. 1] Statistic cis- Chlordane (μg/kg) Dieldrin (μg/kg) Heptachlor epoxide (μg/kg) p,p’-DDD (μg/kg) p,p’-DDE (μg/kg) p,p’-DDT (μg/kg) trans- Chlordane (μg/kg) trans- Nonachlor (μg/kg) Aroclor 1016 plus Aroclor 1242 (μg/kg) Ar

Samples 14 14 14 14 14 14 14 14 14 

Detections1 6 7 1 4 4 4 10 8 4 

Minimum2 0.80 0.270 4.20 2 1.00 0.560 0.280 0.430 4.700 

Maximum2 17.00 1.900 4.20 8 3.70 14.000 9.800 7.100 76.000 

Average2 6.00 1.057 4.20 4 1.80 4.478 2.984 2.711 24.175 Median2 4.10 0.83 4.20 3.60 1.40 2.600 0.640 0.910 8.700 

1Number of samples with one or more detections of selected pesticide constituents. 2Minimum, maximum, average, and median values are calculated from data that may contain estimated values or less than the minimum reporting level.
Water-Quality Data 49

in base-flow conditions. Most of the estimated E. coli loads 

occurred during stormflow (table 11).

Median SSC for base-flow samples collected at sites 1 

through 9 and 11 from WYs 2006 through 2013 ranged from 

13 mg/L at site 2 to 63 mg/L at site 6 (table 9). The Little Blue 

River sites (sites 2, 5, and 9) had lower SSC concentrations 

than most of the smaller Independence streams (sites 1, 6, 7, 8, 

and 11) except for sites 3 and 4 located just downstream from 

lake spillways.

Median SSC measured at sites with multiple stormflow 

samples (sites 1 through 9) for WYs 2005 through 2013 

ranged from 66 mg/L at site 3 to 1,130 mg/L at site 7 

(table 10). Although site 11 had a higher measured SSC than 

site 7, site 11 was not used for comparison because only one 

stormflow sample was collected there during the study period. 

The Little Blue River sites 2 and 9 had concentrations in the 

mid-range compared to those of the smaller streams draining 

Independence (sites 1, 3, 6, and 7). Site 5 had a median SSC of 

211 mg/L but was discontinued in October 2009. Sites 1, 3, 4, 

and 8 had lower SSCs than sites 2 and 9, and sites 6 and 7 had 

higher median SSCs. The median SSC for site 2 (732 mg/L) 

was higher than downstream at site 9 (643 mg/L).

Estimated SSC annual loads ranged from 240 Mg at 

site 3 in WY 2011 to 808,000 Mg at site 9 in WY 2007 

(table 11). Site 9 also had the highest annual daily average 

streamflow and estimated annual load of SSC during all years 

in the study period. The SSC estimated annual flow-weighted 

concentrations varied from 35 mg/L at site 4 in WY 2013 to 

4,479 mg/L at site 9 in WY 2007. The highest estimated 

annual flow-weighted concentrations were at site 7 in WYs 

2006 and 2011, and site 9 in WYs 2007 through 2010 and 

2013. Lee’s Summit Road (site 2) had the highest estimated 

SSC annual flow-weighted concentration in WY 2012. Most 

sites measured during WY 2007, except for site 1, had the 

highest estimated annual flow-weighted SSC that WY among 

all WYs of measurement. Site 1 had the highest estimated 

annual flow-weighted SSC in WY 2008, sites 2 and 3 in 

WY 2010, and site 4 in WY 2012. Most sites measured during 

WY 2006, except for site 1, had the lowest estimated annual 

flow-weighted SSC that WY among all WYs of measurement. 

Site 1 had the lowest estimated annual flow-weighted SSC in 

WY 2012, sites 2 and 3 in WY 2011, and site 4 in WY 2013. 

Dry-Weather Screening

 Dry-weather screening was done by the USGS and 

Independence WPC Department personnel during WYs 2006 

through 2013 in most basins within Independence except Fire 

Prairie Creek (table 2; fig. 2). Any measureable inflow, discharge, or tributary flow to the selected stream was sampled. 

Two basins, Rock Creek (table 20; fig. 13) and Spring Branch 

Creek, were sampled four times from WYs 2006 to 2013. 

Adair Creek was sampled three times, and all remaining basins 

(Crackerneck, Mill, Sugar, Bundschu, Burr Oak, and West Fire 

Prairie Creeks, and East Fork Little Blue and Little Blue 

Rivers) were sampled one or two times. A total of 

1,052 samples (table 20) were collected from area stream 

basins for analysis of total chlorine, total dissolved copper, 

phenols, and anionic surfactants. Total chlorine was analyzed 

in 1,049 samples; phenols in 1,035 samples; and anionic 

surfactants in 1,048 samples (table 20; fig. 14). Total dissolved 

copper was discontinued as an analyte after WY 2010 and was 

analyzed in 803 samples; however, 39 sample results were 

not included in any statistical analysis because the presence 

of total dissolved copper was detected above the MDL but the 

samples had no visual color. 

Sources for most dry-weather screening analyte detections that exceeded a guideline or standard could not be determined, and when determined were considered to be 

de minimus (minimal) from a source such as car washing or 

lawn watering. Eight detections were determined to have a 

source such as a straight pipe discharge or broken water/septic 

line and corrective action was taken by Independence WPC. 

About 207 samples (19.7 percent) were at or above a defined 

standard or guideline for each constituent. A total of 

Table 17. Presumptive host sources of Escherichia coli in samples collected May through October 2007.

[Christensen and others, 2010. E. coli, Escherichia coli; B, base flow; S, stormflow]

Site number 

(table 2; fig. 1) Date Streamflow condition

E. coli

(number of colonies)

Presumptive host source (percentage of total colonies)

Dog and goose Human Unknown

Base-flow samples

6 8/7/2007 B 190 40.0 26.7 33.0

7 8/7/2007 B 470 25.0 0.0 75.0

5 and 9 8/7/2007 B 140 69.2 15.4 15.4

Stormflow samples

5 and 9 5/8/2007 S 77,000 50.7 12.0 37.3

1 10/18/2007 S 35,800 50.0 20.0 30.0

6 10/18/2007 S 18,000 33.3 27.8 38.9

7 10/18/2007 S 21,000 50.0 22.2 28.0

5 and 9 10/18/2007 S 40,000 38.2 14.5 47.3
50 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

73 samples (6.9 percent) were over the State reportable/compliance level for total chlorine of 0.13 mg/L (table 20; Missouri Department of Natural Resources, 2006), which 

was used as a guideline in this report; nearly one-half 

(35 samples) of these samples were detected in the Spring 

Branch Creek basin. No Federal or State standard has been 

determined for dissolved copper in unfiltered (total) samples. 

There were, however, 226 detections (21.5 percent) that were 

higher than the EDL for total dissolved copper. For purposes 

of comparison in this report, the concentrations of phenols 

were considered to be equivalent to the concentration of the 

individual compound phenol, for which there is a Missouri 

State AQL chronic standard of 0.100 mg/L (Missouri Department of Natural Resources, 2014b). The Missouri State AQL 

chronic standard for phenol was recently updated (January 

2014) to a standard of 0.256 (Missouri Department of Natural 

Resources, 2014b), but for purposes of this report the previous standard of 0.100 mg/L will be used. Only one sample 

(less than 1 percent) was measured at a level greater than the 

Missouri AQL of 0.100 mg/L, from the Rock Creek basin in 

WY 2006. The most commonly detected surfactant (detergent) 

in base-flow samples was nonylphenol, a nonionic surfactant 

(appendix 1). There were 133 samples (12.6 percent) that were 

detected above the EPA freshwater standard for acute exposure 

for aquatic communities to nonylphenol of 0.028 mg/L, which 

was used as guideline in this report; more than one-half of 

these samples were measured in the Rock Creek (44 samples) 

and Spring Branch Creek (41 samples) basins (table 20). 

Ecological Data

Benthic macroinvertebrate samples were collected and 

habitat assessments were done at the nine base-flow and 

stormflow measuring sites in Independence (sites 1 through 

9), one additional site in Independence (site 10), and two 

comparison sites (sites 12 and 13). Benthic macroinvertebrate 

samples were collected in March during WY 2007 through 

2009, 2011, and 2013 for spring representation, and September 

during WY 2008, 2009, 2011, and 2012, and October 2010 for 

fall representation. Habitat assessments were done every other 

year beginning in WY 2008 (WYs 2008, 2010, and 2012). 

Macroinvertebrate Surveys

Macroinvertebrate samples were processed, taxa enumerated, and taxa richness, abundance, and diversity metrics 

for macroinvertebrate samples were calculated using IDAS 

version 5.0 (Cuffney and Brightbill, 2011). Taxa by site and 

sampling date, as listed at the USGS NWQL, are presented 

in table 21 (http://pubs.usgs.gov/ds/0915/downloads/ds915_

table21.xlsx). 

Four metrics are used by the MDNR (Sarver, 2003a) 

in the calculation of the MSCI: RICH, EPTR, MBI, and 

SHANDIV (Sarver, 2003a). The range in the four metrics and 

the SCI for spring and fall samples for streams in Independence (sites 1 through 11) are shown in figure 15. Differences 

in the calculated SCI and component metrics for individual 

samples from previously published values (Christensen and 

Krempa, 2012) are not substantial and result from differences in resolving taxonomic ambiguities with the addition of 

more samples. Samples were collected during the spring and 

fall to account for seasonal variability in macroinvertebrate 

communities. Calculating SCI from a single season may not 

capture the range of ALS status of streams. The RICH and 

SHANDIV metrics values are noticeably higher during the 

spring, whereas the EPTR metric has higher values during the 

fall. The MBI metric seems similar in fall and spring. The total 

number of distinct taxa is higher and more diverse during the 

spring season. The number of Ephemeroptera, Plecoptera, and 

Trichoptera is higher and the overall condition of the streams, 

taking into account all metrics, is better during the fall season 

(table 22). The median tolerance of stream taxa is similar 

between the two seasons, with an MBI value of about 6 even 

though the tolerance of the taxa in the streams is somewhat 

broader in the fall than in the spring, with a greater abundance 

of lesser and greater-tolerant taxa (fig. 15; table 22).

Individual macroinvertebrate metric values and the SCI 

indices for samples by season along with selected field parameters are presented in table 22. Individual macroinvertebrate 

metric values varied substantially by site and year; however, 

seasonal median SCI scores for all Independence sites combined were the same despite some variability in component 

metrics (fig. 15). SCI scores indicated that 20 percent of spring 

Independence stream site samples met the criteria for full support of aquatic life and 80 percent were considered partially 

supportive, whereas fall samples for Independence sites indicated that 42 percent scored fully biologically supporting and 

58 percent partially biologically supporting. No Independence 

stream sample had a non-supporting score using the criteria 

provided in table 3.

Habitat Assessments

Stream habitat assessments were completed in the fall 

of 2008, 2010, and 2012, and in the spring of 2010 at each 

macroinvertebrate sampling site. A total possible score of 200 

indicated ideal habitat. Habitat scores ranged from 65 

(table 22) at site 7 in the spring of 2010 to 139 at the rural 

comparison site (site 13) in the spring of 2007, or between 

about 33 and 70 percent of the ideal score of 200.

Table 21. Macroinvertebrate taxa and individuals enumerated in samples from all sites, March 2007 through 
Table 18. Microbial source tracking marker concentrations for human and animal fecal source samples.[ID, laboratory identification number; E. coli, Escherichia coli; MPN/gDW, most probable number per gram dry weight; copies/gDW, copies per gram dry weight; Human, indivOH, Ohio; e, exponent; --, no data; nd, not detected; bdl, below detection limit; <, less than; MO, Missouri; Livestock, livestock fecal source group; dnq, concentration is below above the limit of detection; ~, duplicate qPCR results do not agree; E, estimated; Wildlife, wildlife fecal source group; Pet, pet fecal source group; MPN/100 mL, most probablies/100 mL, copies per 100 milliliters; Mixed human, influent source sample group; >, greater than; na, not available (sample not collected)]

Laboratory 

ID Date Source Group

E. coli

(MPN/ 

gDW)

E. coli

remark

AllBac1

(copies/ 

gDW)

AllBac 

remark

HF1832

(copies/ 

gDW)

HF183 

remark

BacCan3

(copies/ 

gDW)

Bac

rem

Human fecal samples

2299-01 4/15/2013 Human OH Female 36 Human 6.00e+09 -- 3.23e+11 -- 1.51e+08 -- -- n

2299-02 4/15/2013 Human OH Female 28 Human 1.00e+08 -- 4.17e+11 -- -- bdl -- n

2299-03 4/15/2013 Human OH Male 58 Human 8.80e+07 -- 6.63e+11 -- 5.19e+10 -- -- n

2299-04 4/15/2013 Human OH Male 17 Human 9.40e+03 < 8.72e+11 -- 3.05e+07 -- -- n

2299-05 4/15/2013 Human MO Male 46 Human 1.40e+04 -- 2.14e+12 -- 3.12e+07 -- -- n

2299-06 4/15/2013 Human MO Male 21 Human 4.50e+07 -- 5.46e+11 -- 8.93e+10 -- -- n

2299-07 4/15/2013 Human MO Male 56 Human 3.70e+06 -- 8.07e+11 -- 1.38e+08 -- -- n

2299-08 4/15/2013 Human MO Male 52 Human 1.40e+04 < 3.18e+11 -- -- bdl -- n

2299-09 4/15/2013 Human MO Male 50 Human 2.70e+08 -- 1.29e+12 -- 8.96e+07 -- -- n

2300-01 4/16/2013 Human MO Male 24 Human 1.60e+04 -- 1.01e+12 -- 8.68e+08 -- -- n

2300-02 4/16/2013 Human MO Male 35 Human 6.70e+08 -- 5.62e+11 -- 5.29e+07 -- 2.17e+10 -

2300-03 4/16/2013 Human MO Male 50–55 Human 9.30e+07 -- 2.79e+12 -- 1.42e+11 -- -- n

2300-04 4/16/2013 Human MO Male 57 Human 3.20e+08 -- 2.60e+12 -- 1.08e+11 -- -- n

Ruminant fecal samples

1998-03 10/24/2011 Cow number 1 Livestock 3.46e+04 -- 4.03e+11 -- 1.42e+06 -- 2.33e+07 -

1998-04 10/24/2011 Cow number 2 Livestock 4.85e+03 -- 3.68e+11 -- 1.83e+06 -- 6.13e+06 -

1998-05 10/24/2011 Cow number 3 Livestock 5.62e+04 -- 2.99e+11 -- 1.09e+06 -- 1.72e+07 -

1998-06 10/24/2011 Cow number 4 Livestock 1.20e+08 -- 1.81e+11 -- 7.36e+05 -- 2.13e+06 -

1998-07 10/24/2011 Cow number 5 Livestock 2.26e+08 -- 1.25e+11 -- -- bdl 4.08e+06 -

1998-08 10/24/2011 Cow number 6 Livestock 5.97e+06 -- 2.80e+11 -- 2.72e+05 dnq~ 1.07e+06 E1998-09 10/24/2011 Cow number 7 Livestock 3.02e+03 -- 2.45e+11 -- -- bdl 9.29e+06 -

1998-10 10/24/2011 Cow number 8 Livestock 9.67e+04 -- 2.55e+11 -- 8.65e+05 E~ 3.14e+06 -

1985-06 9/22/2011 Deer number 1 Wildlife 4.13e+08 -- 1.45e+10 -- -- bdl 4.09e+06 -

1985-15 9/22/2011 Deer number 10 Wildlife 5.33e+06 -- 3.15e+11 -- 1.25e+06 -- 2.14e+07 -

1985-16 9/22/2011 Deer number 11 Wildlife 7.06e+06 -- 5.98e+10 -- 4.40e+05 -- 3.26e+05 dn

1985-10 9/22/2011 Deer number 5 Wildlife 3.32e+06 -- 1.78e+11 -- 3.46e+08 -- 7.71e+07 -

1985-11 9/22/2011 Deer number 6 Wildlife 3.02e+06 -- 1.15e+11 -- 3.83e+06 -- 4.74e+07 -

1985-14 9/22/2011 Deer number 9 Wildlife 1.10e+06 -- 2.38e+10 -- 4.07e+05 -- 4.48e+05 -
Table 18. Microbial source tracking marker concentrations for human and animal fecal source samples.—Continued [ID, laboratory identification number; E. coli, Escherichia coli; MPN/gDW, most probable number per gram dry weight; copies/gDW, copies per gram dry weight; Human, indivOH, Ohio; e, exponent; --, no data; nd, not detected; bdl, below detection limit; <, less than; MO, Missouri; Livestock, livestock fecal source group; dnq, concentration is below above the limit of detection; ~, duplicate qPCR results do not agree; E, estimated; Wildlife, wildlife fecal source group; Pet, pet fecal source group; MPN/100 mL, most probablies/100 mL, copies per 100 milliliters; Mixed human, influent source sample group; >, greater than; na, not available (sample not collected)] Laboratory ID Date Source Group E. coli (MPN/ gDW) E. coli remark AllBac1 (copies/ gDW) AllBac remark HF1832 (copies/ gDW) HF183 remark BacCan3 (copies/ gDW) Bac

rem

Canine fecal samples 1985-01 9/22/2011 Dog number 1 Pet 1.47e+07 -- 1.17e+11 -- 2.58e+06 -- -- n

2110-01 7/10/2012 Dog number 1 Pet 7.87e+07 -- 1.81e+11 -- 7.67e+05 E~ 2.71e+08 -

1985-02 9/22/2011 Dog number 2 Pet 9.96e+09 -- 4.97e+11 -- 1.01e+07 -- 8.63e+10 -

2110-02 7/10/2012 Dog number 2 Pet 9.24e+06 -- 8.55e+11 -- 3.03e+07 -- 2.05e+11 -

1985-03 9/22/2011 Dog number 3 Pet 2.66e+09 -- 3.40e+11 -- 2.43e+07 -- 4.01e+09 -

2110-03 7/10/2012 Dog number 3 Pet 5.57e+00 -- 8.88e+09 -- -- bdl 5.47e+07 -

1985-04 9/22/2011 Dog number 4 Pet 8.43e+00 -- 2.60e+11 -- 2.01e+06 -- 5.46e+09 -

2110-04 7/10/2012 Dog number 4 Pet 1.06e+10 -- 8.00e+11 -- 8.93e+06 -- -- b

Other fecal samples 2310-01 5/8/2013 Chicken Livestock 1.60e+09 -- 3.18e+07 -- -- bdl -- n

2310-02 5/8/2013 Chicken Livestock 1.30e+08 -- 1.98e+06 -- -- nd -- n

2310-03 5/8/2013 Cat Pet 5.60e+05 -- 1.22e+11 -- -- nd -- n

2310-04 5/8/2013 Turkey Wildlife 1.00e+02 -- -- bdl -- nd -- n

2310-05 5/8/2013 Mouse Wildlife 1.40e+05 -- 1.56e+10 -- -- nd 4.50e+05 -

2310-06 5/8/2013 Mouse Wildlife 1.40e+04 -- 2.41e+10 -- -- nd 3.88e+05 -

1985-05 9/22/2011 Goose Wildlife 1.50e+03 -- 2.65e+07 -- 4.01e+05 E~ -- b

1998-01 10/24/2011 Goose number 1 Wildlife 9.45e+00 < -- bdl 2.06e+06 -- -- n

1998-02 10/24/2011 Goose number 2 Wildlife 1.14e+01 < 2.57e+07 -- -- nd -- n

2310-07 5/8/2013 Goose Wildlife 2.80e+01 < 7.79e+05 E~ -- nd -- n

2310-08 5/8/2013 Rabbit Wildlife 9.60e+09 -- 1.68e+08 -- -- nd -- n

2313-01 5/14/2013 Horse Livestock 8.10e+08 -- 3.18e+09 -- -- bdl 4.19e+03 -

2313-02 5/14/2013 Horse Livestock 5.40e+06 -- 1.29e+10 -- -- bdl -- b
Table 18. Microbial source tracking marker concentrations for human and animal fecal source samples.—Continued[ID, laboratory identification number; E. coli, Escherichia coli; MPN/gDW, most probable number per gram dry weight; copies/gDW, copies per gram dry weight; Human, indivOH, Ohio; e, exponent; --, no data; nd, not detected; bdl, below detection limit; <, less than; MO, Missouri; Livestock, livestock fecal source group; dnq, concentration is below above the limit of detection; ~, duplicate qPCR results do not agree; E, estimated; Wildlife, wildlife fecal source group; Pet, pet fecal source group; MPN/100 mL, most probablies/100 mL, copies per 100 milliliters; Mixed human, influent source sample group; >, greater than; na, not available (sample not collected)]

Laboratory 

ID Date Source Group

E. coli

(MPN/ 

100 mL)

E. coli

remark

AllBac1

(copies/ 

100 mL)

AllBac 

remark

HF1832

(copies/ 

100 mL)

HF183 

remark

BacCan3

(copies/ 

100 mL)

Bac

rem

Influent samples

1976-05 9/15/2011 Human influent Mixed human 2.40e+06 > 3.76e+09 -- 1.27e+08 -- 3.56e+06 -

2022-02 12/1/2011 Human influent Mixed human na na 1.42e+09 -- 7.06e+07 -- 8.80e+05 -

2033-07 1/19/2012 Human influent Mixed human na na 5.84e+09 -- 1.77e+08 -- 5.37e+06 -

2060-01 5/22/2012 Human influent Mixed human 5.50e+05 -- 1.28e+10 -- 4.13e+08 -- 1.23e+07 -

2223-02 9/18/2012 Human influent Mixed human 6.10e+06 -- 1.24e+10 -- 1.09e+09 -- 1.06e+07 -

2266-01 11/29/2012 Human influent Mixed human 2.60e+07 -- 5.83e+09 -- 2.45e+08 -- 6.95e+06 -

2281-07 2/6/2013 Human influent Mixed human 5.00e+06 -- 7.17e+09 -- 2.48e+08 -- 9.40e+06 -

2286-02 3/5/2013 Human influent Mixed human 1.00e+06 -- 3.20e+09 -- 1.31e+08 -- 4.32e+06 -

2297-01 4/9/2013 Human influent Mixed human 1.30e+06 -- 4.10e+09 -- 1.31e+08 -- 4.16e+06 -

2299-10 4/15/2013 Human influent Mixed human 1.10e+06 -- 2.19e+09 -- 1.05e+08 -- 1.39e+06 -

2306-01 4/23/2013 Human influent Mixed human 1.40e+06 -- 6.62e+09 -- 3.44e+08 -- 4.83e+06 -

2319-01 5/29/2013 Human influent Mixed human 1.30e+06 -- 3.83e+09 -- 2.40e+08 -- 4.34e+06 -

1AllBac, assay for general fecal contamination (Layton and others, 2006).2HF183, assay for human-associated fecal contamination (Seurinck and others, 2005).3BacCan, assay for canine-associated fecal contamination (Kildare and others, 2005).4BoBac, assay for ruminant-associated fecal contamination (Layton and others, 2006).
54 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

Table 20. Summary of dry-weather screening constituent detections in streams in Independence, Missouri, water years 2006 through 

2013.

[Water year, from October 1 of previous year to September 30; mg/L, milligrams per liter; All basins, combination of all data for all streams; EDL, estimated 

detection limit; MDL, method detection limit; results are semiquantitative]

Sample 

water year Statistic

Total 

chlorine 

(mg/L)

Total 

dissolved 

copper 

(mg/L)

Phenols 

(mg/L)

Anionic 

surfactant 

(mg/L)

Sample 

water year Statistic

Total 

chlorine 

(mg/L)

Total 

dissolved 

copper 

(mg/L)

Phenols 

(mg/L)

Anionic 

surfactant 

(mg/L)

All basins (table 2; fig. 2)—1,052 samples collected Rock Creek Basin (table 2; fig. 2)

2006–2013 Analyses 1,049 803 1,035 1,048 2006, 2008, 

2009, 

2013

Analyses 260 260 260 260

Detections1 983 226 601 726 Detections1 243 77 145 256

Percent deleted2 0.38 4.98 1.62 0.38 Minimum3 0.02 0.04 0.002 0.002

Minimum3 0.02 0.04 0.002 0.002 Maximum3 2.06 0.49 0.200 0.490

Maximum3 7.00 0.49 0.200 12.100 Average3 0.08 0.07 0.008 0.023

Average3 0.08 0.07 0.007 0.043 Median3 0.05 0.06 0.002 0.013

Median3 0.06 0.06 0.004 0.011 Number above 

guideline6

14 0 1 44

EDL4 0.02 0.04 0.002 0.002

MDL5 0.05 0.05 0.005 0.010

Number above 

guideline6

73 0 1 133

Adair Creek Basin (table 2; fig. 2) East Fork Little Blue River Basin (table 2; fig. 2)

2007, 2008, 

2010

Analyses 197 197 197 197 2009 Analyses 4 4 4 4

Detections1 176 53 121 182 Detections1 4 2 1 4

Minimum3 0.02 0.04 0.002 0.002 Minimum3 0.08 0.04 0.02 0.01

Maximum3 1.89 0.22 0.019 0.278 Maximum3 0.11 0.06 0.02 0.02

Average3 0.07 0.06 0.005 0.019 Average3 0.10 0.05 0.02 0.02

Median3 0.05 0.05 0.003 0.012 Median3 0.10 0.05 0.02 0.02

Number above 

guideline6

7 0 0 14 Number above 

guideline6

0 0 0 0

Crackerneck Creek Basin (table 2; fig. 2) Spring Branch Creek Basin (table 2; fig. 2)

2006, 2013 Analyses 49 49 49 49 2006, 2009, 

2011, 

2012

Analyses 258 258 258 258

Detections1 45 1 18 41 Detections1 245 39 146 233

Minimum3 0.02 0.05 0.002 0.002 Minimum3 0.02 0.04 0.002 0.002

Maximum3 0.15 0.05 0.045 0.218 Maximum3 0.43 0.18 0.033 1.940

Average3 0.05 0.05 0.010 0.023 Average3 0.08 0.07 0.008 0.027

Median3 0.05 0.05 0.008 0.015 Median3 0.07 0.06 0.006 0.011

Number above 

guideline6

1 0 0 12 Number above 

guideline6

35 0 0 41
Ecological Data 55

Table 20. Summary of dry-weather screening constituent detections in streams in Independence, Missouri, water years 2006 through 

2013.—Continued

[Water year, from October 1 of previous year to September 30; mg/L, milligrams per liter; All basins, combination of all data for all streams; EDL, estimated 

detection limit; MDL, method detection limit; results are semiquantitative]

Sample 

water year Statistic

Total 

chlorine 

(mg/L)

Total 

dissolved 

copper 

(mg/L)

Phenols 

(mg/L)

Anionic 

surfactant 

(mg/L)

Sample 

water year Statistic

Total 

chlorine 

(mg/L)

Total 

dissolved 

copper 

(mg/L)

Phenols 

(mg/L)

Anionic 

surfactant 

(mg/L)

Little Blue River Basin (table 2; fig. 2) Mill Creek Basin (table 2; fig. 2)

2006, 2009 Analyses 45 45 45 45 2007, 2011 Analyses 100 100 100 100

Detections1 43 15 19 43 Detections1 94 12 50 94

Minimum3 0.03 0.04 0.002 0.003 Minimum3 0.02 0.04 0.002 0.002

Maximum3 0.13 0.14 0.080 0.079 Maximum3 7.00 0.08 0.048 12.100

Average3 0.07 0.06 0.015 0.017 Average3 0.15 0.05 0.007 0.199

Median3 0.07 0.05 0.009 0.013 Median3 0.07 0.05 0.005 0.011

Number above 

guideline6

1 0 0 7 Number above 

guideline6

11 0 0 12

Sugar Creek Basin (table 2; fig. 2) Bundschu Creek Basin (table 2; fig. 2)

2007, 2011 Analyses 25 25 25 25 2008, 2012 Analyses 68 68 68 68

Detections1 25 2 16 25 Detections1 63 10 61 67

Minimum3 0.03 0.04 0.002 0.003 Minimum3 0.02 0.05 0.002 0.002

Maximum3 1.55 0.04 0.015 0.068 Maximum3 0.11 0.07 0.031 0.047

Average3 0.13 0.04 0.006 0.018 Average3 0.05 0.06 0.005 0.011

Median3 0.06 0.04 0.005 0.015 Median3 0.04 0.06 0.003 0.009

Number above 

guideline6

1 0 0 3 Number above 

guideline6

0 0 0 3

Burr Oak Creek Basin (table 2; fig. 2) West Fire Prairie Creek Basin (table 2; fig. 2)

2008 Analyses 24 24 24 24 2009 Analyses 22 22 22 22

Detections1 24 3 22 18 Detections1 21 12 2 19

Minimum3 0.02 0.04 0.002 0.003 Minimum3 0.03 0.05 0.003 0.002

Maximum3 0.15 0.06 0.010 0.018 Maximum3 0.15 0.11 0.003 0.021

Average3 0.06 0.05 0.004 0.007 Average3 0.08 0.07 0.003 0.008

Median3 0.05 0.06 0.002 0.006 Median3 0.08 0.07 0.003 0.007

Number above 

guideline6

1 0 0 0 Number above 

guideline6

2 0 0 0

1

Number of detections is the number of samples for each analyte with concentrations greater than the EDL.

2

Percent of values deleted due to suspected interferences.

3

Minimum, maximum, average, and median values are calculated from data that may contain estimated values. Values less than the provisional method detection limit were not included in the stastical analysis.

4

The EDL is determine by Hach Company©, the manufacturer of the analyte tests.

5

The provisional MDL is determined by a comparison of the results of the environmental samples with the replicate and duplicate samples.

6

Number of detections greater than a specific Federal or Missouri State standard or guideline.
56 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

INTERSTATE 70

23RD

NOLAND

STERLING

TRUMAN

39TH

BLUE RIDGE

CRYSLER

WINNER

KENTUCKY

U.S. HIGHWAY 40

WESTPORT

OSAGE

BLUE RIDGE CUTOFF

LEXINGTON

32ND

SPRING

CRYSLER

INDEPENDENCE

Independence

#

(!

(!

!(

Rock Creek Basin

Stream

Sampling site

Phenol detection greater than 0.1 milligram per liter

Anionic surfactant detection greater than 0.028 milligram per liter

Chlorine detection greater than 0.13 milligram per liter

EXPLANATION

0 0.5 1 MILE

0 0.5 1 KILOMETER

Base from U.S. Geological Survey digital data, 1:50,000

Universal Transverse Mercator projection, Zone 15

94°28'30" 94°27' 94°25'30"

39°07'30"

39°06'

39°04'30"

39°03'

!(

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MISSOURI RIVER

Figure 13. Dry-weather screening sampling sites and locations of constituent 

detections for selected stream basins in Independence, Missouri, water years 2006 

through 2013.
Ecological Data 57

!(

!(

!(

!(

#

## # #

#

#

##

#

##

#

#

#

#

#

## # # TRUMAN

KENTUCKY

INTERSTATE 435

WINNER

NOLAND

STERLING

BLUE RIDGE

LEXINGTON

Independence

CRYSLER

INDEPENDENCE

CRYSLER

94°28'30" 94°27' 94°25'30" 94°24'

39°07'30"

39°06'

Base from U.S. Geological Survey digital data, 1:50,000

Universal Transverse Mercator projection, Zone 15

0 0.5 1 KILOMETER

0 0.5 1 MILE

EXPLANATION

Sugar Creek Basin

Stream

# Sampling site

! Anionic surfactant detection greater than 0.028 milligram per liter

! Chlorine detection greater than 0.13 milligram per liter

MISSOURI RIVER

Figure 13. Dry-weather screening sampling sites and locations of constituent detections for selected stream 

basins in Independence, Missouri, water years 2006 through 2013.—Continued
58 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

!(

!( !(

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Independence

#

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##

TRUMAN

KENTUCKY

NOLAND

U.S. HIGHWAY 24

STATE ROUTE 291

INDEPENDENCE

LEE'S SUMMIT

STATE HIGHWAY 291

UNION

CRYSLER

94°25'30" 94°24' 94°22'30"

39°07'30"

39°06'

Base from U.S. Geological Survey digital data, 1:50,000

Universal Transverse Mercator projection, Zone 15

Mill Creek Basin

Stream

# Sampling site

!( Anionic surfactant detection greater than 0.028 milligram per liter

!( Chlorine detection greater than 0.13 milligram per liter

0 0.5 1 KILOMETER

0 0.5 1 MILE

EXPLANATION

MISSOURI RIVER

Figure 13. Dry-weather screening sampling sites and locations of constituent detections for selected stream 

basins in Independence, Missouri, water years 2006 through 2013.—Continued
Ecological Data 59

Independence

Little Blue River

West

Fire

Prarie 

Creek

Little

E.

Fork

Little

Blue

Blue

River

River

")

")

")

")

")

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INTERSTATE 70

39TH

TRUMAN

R D MIZE

POWELL

LEE'S SUMMIT

23RD

BUNDSCHU

HOLKE

SELSA

KENTUCKY

INTERSTATE 470

BLY

STATE HIGHWAY 78

CRENSHAW

STATE HIGHWAY 291

STATE ROUTE 291

U.S. HIGHWAY 40

35TH

U.S. HIGHWAY 24 NECESSARY

33RD

WOODS CHAPEL

LEE’S SUMMIT

JONES

94°20' 94°15'

39°05'

39°00'

Base from U.S. Geological Survey digital data, 1:50,000

Universal Transverse Mercator projection, Zone 15

0 1 2 MILES

0 1 2 KILOMETERS

Little Blue River, East Fork Little Blue River, and 

West Fire Prairie Creek Basins

Stream

# Sampling site

!( Anionic surfactant detection greater than 0.028 milligram per liter

!( Chlorine detection greater than 0.13 milligram per liter

EXPLANATION

") Streamgage sample site

Figure 13. Dry-weather screening sampling sites and locations of constituent detections for selected stream 

basins in Independence, Missouri, water years 2006 through 2013.—Continued
60 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

Little Blue River

")

")

!(

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INTERSTATE 70

39TH

NOLAND

CRYSLER

LEE'S SUMMIT

U.S. HIGHWAY 40

INTERSTATE 470

BLUE RIDGE

R D MIZE

33RD

35TH

STATE HIGHWAY 291

OSAGE

32ND

SELSA

BLUE PARKWAY

LITTLE 

94°25'30" 94°24' 94°22'30" 94°21'

39°03'

39°01'30"

Base from U.S. Geological Survey digital data, 1:50,000

Universal Transverse Mercator projection, Zone 15

Adair Creek Basin

Stream

0 0.5 1 KILOMETER

0 0.5 1 MILE

EXPLANATION

# Sampling site

!( Anionic surfactant detection greater than 0.028 milligram per liter

!( Chlorine detection greater than 0.13 milligram per liter

") Streamgage sample site

Figure 13. Dry-weather screening sampling sites and locations of constituent detections for selected stream basins in 

Independence, Missouri, water years 2006 through 2013.—Continued
Ecological Data 61

Little Blue River

!(

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39TH

INTERSTATE 70

23RD

NOLAND

HOLKE

R D MIZE SELSA

LEE'S SUMMIT

STATE HIGHWAY 291

33RD

35TH

OSAGE

NECESSARY

STATE HIGHWAY 78

32ND

INTERSTATE 470

94°24' 94°22'30" 94°21'

39°04'30"

39°03'

Base from U.S. Geological Survey digital data, 1:50,000

Universal Transverse Mercator projection, Zone 15

Crackerneck Creek Basin

Stream

# Sampling site

!( Anionic surfactant detection greater that 0.028 milligram per liter

!( Chlorine detection greater than 0.13 milligram per liter

0 0.5 1 KILOMETER

0 0.5 1 MILE

EXPLANATION

Figure 13. Dry-weather screening sampling sites and locations of constituent detections for selected stream basins 

in Independence, Missouri, water years 2006 through 2013.—Continued
62 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

Little Blue River

Independence

0 0.5 1 KILOMETER

0 0.5 1 MILE

")

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TRUMAN

23RD

NOLAND

POWELL

HOLKE

BUNDSCHU

LEE'S SUMMIT

STATE HIGHWAY 78

JONES

STATE HIGHWAY 291

OSAGE

R D MIZE

U.S. HIGHWAY 24

NECESSARY

STATE ROUTE 291

CRENSHAW

JONES

EXPLANATION

94°25'30" 94°24' 94°22'30" 94°21' 94°19'30"

39°06'

39°04'30"

Base from U.S. Geological Survey digital data, 1:50,000

Universal Transverse Mercator projection, Zone 15

Spring Branch Basin

Stream

# Sampling site

!( Anionic surfactant detection greater than 0.028 milligram per liter

!( Chlorine detection greater than 0.13 milligram per liter

") Streamgage sampling site

Figure 13. Dry-weather screening sampling sites and locations of constituent detections for selected stream basins in 

Independence, Missouri, water years 2006 through 2013.—Continued
Ecological Data 63

EXPLANATION

!(

# #

#

#

#

#

#

#

#

# #

#

##

#

# #

#

#

Independence

39TH

CRENSHAW

R D MIZE

NECESSARY

94°19'30" 94°18' 94°16'30"

39°04'30"

39°03'

Little Blue River

Base from U.S. Geological Survey digital data, 1:50,000

Universal Transverse Mercator projection, Zone 15

0 0.5 1 KILOMETER

0 0.5 1 MILE

Burr Oak Basin

Stream

# Sampling site

!( Chlorine detection greater than 0.13 milligram per liter

Figure 13. Dry-weather screening sampling sites and locations of constituent detections for selected stream basins in 

Independence, Missouri, water years 2006 through 2013.—Continued
64 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

Independence

!(

!(

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Little Blue River

POWELL

TRUMAN

BUNDSCHU U.S. HIGHWAY 24

KENTUCKY

STATE HIGHWAY 78

OLD LEXINGTON BLY

TRUMAN

JONES

0 0.5 1 KILOMETER

0 0.5 1 MILE

94°22'30" 94°21' 94°19'30" 94°18'

39°07'30"

39°06'

Base from U.S. Geological Survey digital data, 1:50,000

Universal Transverse Mercator projection, Zone 15

Bundschu Creek Basin

EXPLANATION

Stream

# Sampling site

!( Anionic surfactant detection greater than 0.028 milligram per liter

Figure 13. Dry-weather screening sampling sites and locations of constituent detections for selected stream basins 

in Independence, Missouri, water years 2006 through 2013.—Continued
Ecological Data 65

Figure 14. Boxplots of dry-weather screening constituent concentrations in streams in Independence, Missouri, water years 2006 

through 2013.

xxxx

xx

xx

xx

o

ooo

o

x

xxxxx

xxx

x

x

xx

xx

x x

x

xx

x

xx

o

o

o

Total chlorine Total dissolved copper Phenols Anionic surfactants

1,049 764 1,035 1,048

0.00001

0.0001

0.001

0.01

0.1

1

10

100

Analyte concentration, in milligrams per liter

MDNR

permitting

level for

chlorine

(0.13 mg/L)

MDNR chronic standard for

protection of aquatic life

for phenol (0.100 mg/L)

EXPLANATION

Number of samples

Upper detached

Upper outside

Upper adjacent

75th percentile

Median

25th percentile

Lower adjacent

Lower outside

Missouri Department

of Natural Resources

Milligrams per liter

Provisional method

detection limit (MDL)

Estimated detection

limit (EDL)

Estimated concentrations

below MDL for each

analyte

1,048

x

o

MDNR

mg/L
66 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

x

30 26

26

30 26 30 26

30 26 30 26

Total taxa richness

15

18

21

24

27

30

33

36

39

42

45

Macroinvertebrate biotic index

4

5

6

7

8

9

Stream condition index

10

12

14

16

18

8

20

Ephemeroptera-Plecoptera-Trichoptera

richness

0

1

2

3

4

5

6

7

8

9

10

11

12

13

14

1.0

1.2

1.4

1.6

1.8

2.0

2.2

2.4

2.6

2.8

3.0

3.2

Shannon diversity index

Season

Season

Spring Fall

Spring Fall

x

EXPLANATION

Number of values

Upper outside

Upper adjacent

75th percentile

Median

25th percentile

Lower adjacent

Figure 15. Macroinvertebrate taxa and individuals enumerated in samples from all sites, March 2007 through March 2013.
Table 22. Habitat scores, dissolved oxygen, pH, specific conductance, water temperature, macroinvertebrate metrics used in the stream condition isupport status for samples collected March 2007 through March 2013.[STAID, station identification number; mg/L, milligrams per liter; μS at 25 °C, microsiemens per centimeter at 25 degrees Celsius; RICH, total taxa richness; EPTR, Ephemeroprichness; MBI, Macroinvertebrate Biotic Index; SHANDIV, Shannon Diversity Index; SCI, stream condition index; ALS, aquatic-life support status; --, no data; PBS, partially bfully biologically supporting; NBS, nonbiologically supporting]

Site 

number 

(table 2; 

fig. 1)

STAID

Sample 

collection 

date

Habitat 

score

Dissolved 

oxygen 

(mg/L)

pH 

(standard 

units)

Specific 

conductance 

(μS at 25 °C)

Water 

temperature 

(°C)

RICH EPTR MBI SHANDIV RICH Score EPTR Score MBI Score SH

S

Spring samples

1 06893620 3/20/2007 -- 12.5 7.7 879 11.0 27 5 6.49 2.27 3 3 3 

1 06893620 3/26/2008 -- 12.6 7.7 797 8.2 26 4 6.57 2.37 3 1 3 

1 06893620 3/17/2009 -- 10.8 7.7 850 12.4 30 7 6.61 2.79 3 3 3 

1 06893620 4/19/2010 110 11.2 7.8 794 14.6 -- -- -- -- -- -- -- 

1 06893620 3/15/2011 -- 10.7 6.9 815 5.1 27 6 5.88 2.61 3 3 3 

1 06893620 3/20/2013 -- 13.2 8.0 763 4.5 31 5 5.80 2.62 3 3 3 

1 06893620 3/21/2013 -- 13.2 8.0 725 4.0 35 7 5.94 2.75 3 3 3 

2 06893820 4/14/2010 90 12.3 7.6 620 18.3 -- -- -- -- -- -- -- 

2 06893820 3/15/2011 -- 12.4 8.0 868 5.0 37 10 6.13 2.62 5 5 3 

2 06893820 3/18/2013 -- 11.8 8.2 562 5.3 36 10 5.99 2.96 3 5 3 

3 06893830 3/18/2009 14.4 7.6 855 10.5 31 5 6.88 2.69 3 3 3 

3 06893830 4/16/2010 73 9.0 8.2 961 20.1 -- -- -- -- -- -- -- 

3 06893830 3/10/2011 13.0 7.7 1,240 5.4 28 2 6.05 2.57 3 1 3 

3 06893830 3/19/2013 -- -- -- 1,190 7.1 26 2 5.17 2.10 3 1 5 

4 06893890 3/16/2011 -- 13.0 7.2 401 6.4 37 4 7.00 2.70 5 1 3 

4 06893890 3/20/2013 -- 13.0 8.4 446 5.8 22 0 6.07 1.37 3 1 3 

5 06893910 3/21/2007 11.2 7.9 538 11.2 34 5 6.31 2.38 3 3 3 

5 06893910 3/27/2008 12.4 7.9 485 7.7 36 7 6.30 2.43 3 3 3 

5 06893910 3/19/2009 15.8 7.8 489 9.3 41 7 6.30 2.65 5 3 3 

6 06893940 3/22/2007 -- 8.9 7.1 807 13.8 31 5 6.66 2.66 3 3 3 

6 06893940 3/25/2008 -- 14.2 7.8 820 8.0 30 4 6.00 2.37 3 1 3 

6 06893940 3/11/2011 -- 11.4 7.4 808 4.9 31 4 6.40 2.54 3 1 3 

7 06893970 3/21/2007 11.0 8.0 873 11.6 26 4 7.26 2.37 3 1 3 

7 06893970 3/25/2008 15.1 7.9 846 7.4 28 4 6.85 2.30 3 1 3 

7 06893970 3/17/2009 -- 7.8 832 10.2 32 7 6.29 2.51 3 3 3 

7 06893970 4/8/2010 65 11.2 7.9 758 10.4 -- -- -- -- -- -- -- 

7 06893970 3/10/2011 0.0 7.6 810 3.9 29 5 5.91 2.39 3 3 3 

7 06893970 3/19/2013 -- 12.1 8.4 896 5.0 32 5 6.16 2.43 3 3 3 
Table 22. Habitat scores, dissolved oxygen, pH, specific conductance, water temperature, macroinvertebrate metrics used in the stream condition isupport status for samples collected March 2007 through March 2013.—Continued [STAID, station identification number; mg/L, milligrams per liter; μS at 25 °C, microsiemens per centimeter at 25 degrees Celsius; RICH, total taxa richness; EPTR, Ephemeroptaxa richness; MBI, Macroinvertebrate Biotic Index; SHANDIV, Shannon Diversity Index; SCI, stream condition index; ALS, aquatic-life support status; --, no data; PBS, partiaFBS, fully biologically supporting; NBS, nonbiologically supporting] Site number (table 2; fig. 1) STAID Sample collection date Habitat score Dissolved oxygen (mg/L) pH (standard units) Specific conductance (μS at 25 °C) Water temperature (°C) RICH EPTR MBI SHANDIV RICH Score EPTR Score MBI Score SH

S

Spring samples—Continued 8 06893990 4/16/2010 75 9.1 8.0 544 16.3 -- -- -- -- -- -- -- 

8 06893990 3/11/2011 -- 12.2 7.6 685 5.3 40 9 5.98 2.51 5 3 3 

9 06894000 3/20/2007 10.0 8.0 535 11.3 34 10 6.19 2.16 3 5 3 

9 06894000 3/27/2008 12.4 7.8 523 7.7 32 9 5.89 2.55 3 3 3 

9 06894000 3/19/2009 15.3 7.7 543 10.2 29 10 5.82 2.70 3 5 3 

9 06894000 4/20/2010 84 8.8 8.1 587 16.4 -- -- -- -- -- -- -- 

9 06894000 3/16/2011 11.2 6.7 708 6.7 37 8 5.81 2.31 5 3 3 

9 06894000 3/18/2013 -- 12.3 7.9 508 5.8 32 7 5.30 2.78 3 3 5 

12 06895090 3/22/2007 -- 8.7 7.9 500 13.0 34 4 6.55 2.28 3 1 3 

12 06895090 3/26/2008 -- 12.1 7.8 495 7.7 40 10 7.30 2.63 5 5 3 

12 06895090 4/13/2010 89 8.6 7.8 514 17.1 -- -- -- -- -- -- -- 

13 06921582 3/14/2007 139 11.1 8.2 519 14.8 33 8 6.26 2.24 3 3 3 

13 06921582 3/14/2008 11.3 8.0 744 8.0 28 8 6.44 2.10 3 3 3 

13 06921582 3/23/2009 10.3 8.0 665 14.5 38 12 5.90 2.96 5 5 3 

13 06921582 4/14/2010 132 11.3 7.8 531 17.5 -- -- -- -- -- -- -- 

13 06921582 3/18/2011 -- 9.1 7.7 456 12.3 32 8 6.28 2.53 3 3 3 

Fall samples 1 06893620 8/27/2008 96 10.2 7.9 880 22.7 -- -- -- -- -- -- -- 

1 06893620 9/23/2008 8.2 7.7 846 19.3 26 6 6.35 2.60 3 3 5 

1 06893620 9/17/2009 7.9 7.6 812 19.1 28 7 6.02 2.54 3 3 5 

1 06893620 10/4/2010 110 8.6 7.9 808 11.9 24 6 6.30 2.51 3 3 5 

1 06893620 9/12/2012 112 6.3 7.4 628 19.7 26 6 6.32 2.42 3 3 5 

2 06893820 10/6/2010 90 9.3 7.9 438 13.3 32 10 5.76 2.42 3 5 5 

2 06893820 9/13/2012 87 6.9 -- 457 20.7 33 13 5.50 2.34 3 5 5 

3 06893830 9/17/2009 7.0 7.5 469 22.5 23 3 5.66 1.81 3 1 5 

3 06893830 10/7/2010 73 7.5 7.6 657 17.1 29 5 6.02 2.44 3 3 5 

3 06893830 9/18/2012 94 5.8 7.5 616 17.0 32 8 5.25 2.31 3 3 5 

4 06893890 10/5/2010 -- 6.8 7.8 365 19.3 28 6 7.63 2.50 3 3 3 
Table 22. Habitat scores, dissolved oxygen, pH, specific conductance, water temperature, macroinvertebrate metrics used in the stream condition isupport status for samples collected March 2007 through March 2013.—Continued[STAID, station identification number; mg/L, milligrams per liter; μS at 25 °C, microsiemens per centimeter at 25 degrees Celsius; RICH, total taxa richness; EPTR, Ephemeroptaxa richness; MBI, Macroinvertebrate Biotic Index; SHANDIV, Shannon Diversity Index; SCI, stream condition index; ALS, aquatic-life support status; --, no data; PBS, partiaFBS, fully biologically supporting; NBS, nonbiologically supporting]

Site 

number 

(table 2; 

fig. 1)

STAID

Sample 

collection 

date

Habitat 

score

Dissolved 

oxygen 

(mg/L)

pH 

(standard 

units)

Specific 

conductance 

(μS at 25 °C)

Water 

temperature 

(°C)

RICH EPTR MBI SHANDIV RICH Score EPTR Score MBI Score SH

S

Fall samples—Continued

4 06893890 9/13/2012 66 5.4 7.2 479 18.2 30 5 6.96 2.21 3 3 3 

5 06893910 9/2/2008 88 6.2 7.9 465 25.6 -- -- -- -- -- -- -- 

5 06893910 9/26/2008 -- 6.8 7.7 413 21.6 24 8 5.93 2.21 3 3 5 

5 06893910 9/15/2009 -- 9.4 7.6 395 22.1 22 9 5.05 2.03 3 3 5 

5 06893910 10/6/2010 88 8.3 7.8 427 15.7 27 9 5.58 2.02 3 3 5 

6 06893940 9/25/2008 -- 7.3 7.6 743 19.6 25 5 6.56 2.63 3 3 3 

6 06893940 9/18/2012 77 6.4 8.0 791 17.1 33 6 5.35 1.91 3 3 5 

7 06893970 8/26/2008 97 9.1 8.1 789 21.9 -- -- -- -- -- -- -- 

7 06893970 9/23/2008 -- 8.0 7.6 833 18.7 29 7 6.69 2.46 3 3 3 

7 06893970 9/16/2009 -- 11.8 7.8 814 20.2 24 5 6.98 2.16 3 3 3 

7 06893970 10/7/2010 65 8.4 8.0 787 13.7 29 8 6.29 2.41 3 3 5 

7 06893970 9/17/2012 108 7.6 7.5 597 17.7 32 4 7.82 2.44 3 1 3 

8 06893990 10/4/2010 -- 9.2 7.9 638 11.3 22 6 6.68 1.89 3 3 3 

9 06894000 9/2/2008 90 5.8 7.8 492 25.6 -- -- -- -- -- -- -- 

9 06894000 9/26/2008 -- 7.7 7.7 452 21.3 29 10 6.18 1.76 3 5 5 

9 06894000 9/15/2009 -- 8.1 7.7 431 22.3 19 7 5.67 1.98 3 3 5 

9 06894000 10/5/2010 84 9.0 8.0 466 15.4 36 11 5.90 2.67 3 5 5 

9 06894000 9/12/2012 95 7.0 7.7 551 22.6 26 9 5.89 1.91 3 3 5 

10 390259094201201 9/19/2012 77 8.6 7.4 528 18.2 33 10 6.37 2.75 3 5 5 

12 06895090 8/28/2008 86 6.0 7.6 565 25.2 -- -- -- -- -- -- -- 

12 06895090 9/24/2008 -- 7.6 7.8 551 19.4 16 4 7.89 1.86 1 1 3 

12 06895090 9/16/2009 -- 9.3 7.5 550 20.2 24 5 6.80 2.14 3 3 3 

13 06921582 9/3/2008 116 5.5 -- 948 22.3 -- -- -- -- -- -- -- 

13 06921582 9/25/2008 -- 7.8 7.9 710 19.8 30 11 6.22 2.20 3 5 5 

13 06921582 9/18/2009 -- 8.5 7.7 601 19.6 33 12 6.08 2.03 3 5 5 

13 06921582 10/1/2010 132 7.2 7.9 546 17.3 22 7 6.03 1.77 3 3 5 

13 06921582 9/14/2012 123 6.8 8.1 481 18.1 31 6 6.35 2.58 3 3 5 

1The SCI is the sum of the RICH, EPTR, MBI, and SHANDIV scores.2The ALS rating is based on the SCI. A score of 8 or less is NBS, a score of 10 to 14 is PBS, and a score of 16 to 20 is FBS.
70 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

Summary

The U.S. Geological Survey (USGS) and the City of 

Independence, Missouri, Water Pollution Control (WPC) 

Department began a cooperative study in June 2005 to characterize and evaluate the water quality and ecological condition 

of urban streams within Independence. Continuous streamflow, physical and chemical properties, total dissolved solids 

(TDS), sodium, chloride, nutrients, total recoverable metals, dissolved mercury, common organic micro-constituents 

(OMCs), pesticides in streambed sediment and surface water, 

fecal indicator bacteria (FIB; Escherichia coli, fecal coliform, total coliform), microbial source tracking (MST), and 

suspended sediment concentration (SSC) data were collected 

and analyzed in base-flow and stormflow samples. Annual 

loads were calculated using these data to characterize contaminant sources to Independence receiving streams and their 

contributions to the Little Blue River, beginning June 2005 

through September 2013. Annual loads were estimated for 

TDS, chloride, total nitrogen and select other nitrogen species, 

total phosphorus, Escherichia coli (E. coli), and SSC by using 

regression models. Annual dry-weather screenings were done 

beginning in water year (WY; time period from October 1 of 

the previous year to September 30 of the current year) 2006 

in most basins in Independence to identify any point source 

discharges containing possible contaminants. 

Continuous streamflow data were collected and automatic 

samplers were installed at eight sites; three sites on the Little 

Blue River (site 2, Little Blue River at Lee’s Summit Road; 

site 5, Little Blue River at 39th Street; and site 9, Little Blue 

River near Lake City) and five smaller streams in Independence (site 1, Rock Creek; site 3, Adair Creek; site 4, East 

Fork Little Blue River; site 6, Crackerneck Creek; and site 7, 

Spring Branch Creek). Two ungaged sites on smaller streams 

also were sampled for base-flow and stormflow water quality: site 8, Burr Oak Creek; and site 11, Bundschu Creek. Two 

comparison sites were selected as control sites for habitat 

assessment and benthic macroinvertebrate samples: site 12, 

East Fork Crooked River; and site 13, South Grand River. One 

additional ungaged site within Independence (site 10, Cut-off 

meander near Lake City) also was selected for benthic macroinvertebrate sampling and habitat assessment. The summary 

sites will hereafter be referred to by site number (1 through 

13). Water-surface elevation (stage) data were measured in 

15-minute intervals and used to compute streamflow records. 

Streamflow measurements were made at all sampling sites at 

regular intervals. 

Seven sites (sites 1 through 5, 7, and 9) were equipped 

with continuous water-quality monitors (CWQMs) either for 

part or all of the study period. Dissolved oxygen, pH, specific 

conductance, water temperature, and turbidity were recorded 

in 15-minute intervals. Daily average dissolved oxygen values 

were at or below the Missouri standard for protection of 

aquatic life (AQL) less than 1 percent of the time on the Little 

Blue River (sites 2, 5, and 9) to as much as 10 percent of the 

time at site 4. No daily values of pH recorded in Independence 

streams were outside the Missouri AQL range. Daily pH 

values ranged between 6.9 standard units to 8.4 standard units. 

The daily average specific conductance values for Independence streams ranged between 221 microsiemens per centimeter (μS/cm) to 3,680 μS/cm, and were generally higher on 

the smaller streams (sites 1, 3, and 7) than on the Little Blue 

River (sites 2, 5, and 9). The Missouri AQL standard for water 

temperature in streams was exceeded less than 1 percent of 

the time in Independence streams. The daily average water 

temperature values recorded at sites with CWQMs ranged 

from -0.2 degrees Celsius (°C) to 32.4 °C. Daily average 

turbidity exceeded the U.S. Environmental Protection Agency 

(EPA) recommended guideline between 15 and 60 percent 

of the time, and site 2 had both the minimum (0.0 NTU) and 

maximum (1,054 NTU) recorded daily turbidity value of all 

the sites.

From June 2005 to September 2013, there were a total of 

175 base-flow and 205 stormflow water-quality samples collected at 10 sites in Independence (sites 1 through 9, and 11). 

Most of the base-flow samples were split between the spring 

and early summer season (73 samples) and the winter season 

(71 samples), with the remainder (31 samples) collected during the fall transitional season. The stormflow samples 

were primarily collected during the early summer season 

(80 samples), with the remaining samples split between the 

winter season (66 samples) and the fall transitional season 

(59 samples). 

Base-flow and stormflow measurements of physical and 

chemical properties in Independence streams varied within 

the normal range for environmental waters. The minimum and 

maximum measured TDS in base flow (187 milligrams per 

liter [mg/L] to 1,190 mg/L) was similar to that of stormflow 

(61 mg/L to 1,200 mg/L). Most of the smaller streams (sites 1, 

3, and 6 through 8) had higher median base-flow TDS concentrations than the Little Blue River sites (sites 2, 5, and 9), but 

median stormflow TDS concentrations were similar among 

all sites. The median TDS value for all stormflow samples 

(221 mg/L) was less than that of all base-flow samples 

(441 mg/L). Measured chloride concentrations in base flow 

ranged from 16.9 mg/L to 459 mg/L, and stormflow ranged 

from 3.4 mg/L to 508 mg/L. Fifteen base-flow samples and 

11 stormflow samples had measured chloride concentrations 

greater than the Missouri chronic standard for AQL, but none 

exceeded the Missouri acute standard for AQL. There were 

eight total recoverable metals (unfiltered sample that includes 

dissolved and suspended material) analyzed in base-flow and 

stormflow samples: aluminum, cadmium, chromium, copper, 

lead, zinc, arsenic, and dissolved mercury. Concentrations 

of aluminum were highest in both base-flow and stormflow 

samples, and ranged from 7 micrograms per liter (μg/L) 

to 1,420 μg/L in base-flow samples and from 8.5 μg/L to 

170,000 μg/L in stormflow samples. Most total recoverable 

metals concentrations were generally less than the Missouri 

AQL for dissolved metals. 

Daily average streamflow, estimated annual load, and 

estimated annual flow-weighted concentrations were computed 
Summary 71

for select constituents (TDS, chloride, select nutrient constituents, E. coli, and SSC) measured at each Independence site 

(sites 1 through 9). The highest estimated annual load of TDS 

was 72,600 megagrams (Mg) in WY 2010 and the highest 

estimated annual flow-weighted concentration of TDS was 

1,123 mg/L in WY 2006. The highest estimated annual chloride load was 14,100 Mg in WY 2010 and the highest estimated annual flow-weighted concentration for chloride was 

152 mg/L in WY 2013.The median total nitrogen (N) concentrations measured in base flow ranged from 0.5 mg/L to 

2.2 mg/L, and from 1.2 mg/L to 3.2 mg/L in stormflow. 

Median total phosphorus (P) concentrations ranged from 

0.045 mg/L to 0.152 mg/L in base flow, and from 0.04 mg/L 

to 1.29 mg/L in stormflow. The median total organic N and 

nitrate concentrations accounted for 84 percent of the median 

total N concentration in base-flow samples and 98 percent in 

stormflow samples. Median dissolved P accounted for 68 percent of the median total P concentration in base-flow samples 

and 13 percent in stormflow samples. Total N concentrations 

exceeded the EPA provisional nutrient standard in 52 percent of base flow and 93 percent of stormflow samples in the 

smaller streams (sites 1, 3, 4, 6 through 8), and 24 percent 

of base-flow and 92 percent of stormflow samples at the 

Little Blue River sites (sites 2, 5, and 9). Total P concentrations exceeded the EPA provisional nutrient standard in 

48 percent of base-flow and 94 percent of stormflow samples 

on the smaller streams, and in 30 percent of base-flow and 

97 percent of stormflow samples on the Little Blue River 

(sites 2, 5 and 9).

There were 71 base-flow samples and 130 stormflow 

samples from June 2005 to September 2013 that were analyzed for 11 categories of OMCs. Four categories (polyaromatic hydrocarbons [PAHs] and combustion products, 

pesticides, plastics, and sterols and stanols) were detected in 

at least 50 percent of base-flow samples, and the same four 

categories along with stimulants were detected in greater than 

90 percent of stormflow samples. The overall median concentration of OMCs in all base-flow samples was 0.06 μg/L, and 

in all stormflow samples was 0.13 μg/L. The highest maximum concentration of OMCs in base flow measured at each 

site (53.3 μg/L) was higher than that of stormflow (26.4 μg/L). 

All stormflow samples had at least one quantified detection of 

at least one OMC compound.

Fourteen base-flow samples were analyzed for pesticides 

in streambed sediment. One-half of the analyzed constituents 

(11 of 22) had detections in one or more samples. Two baseflow samples and 17 stormflow samples were also analyzed 

for pesticides in surface water. Twenty-six constituents were 

analyzed, but none were detected in any base-flow or stormflow samples. 

FIB were analyzed in 159 base-flow samples and 168 

stormflow samples collected from June 2005 to September 

2013. Median E. coli densities in base flow ranged from 19 

most probable number per 100 milliliters (MPN/100 mL) to 

410 MPN/100 mL, and in stormflow from 1,200 MPN/100 mL 

to 31,000 MPN/100 mL. Median fecal coliform densities in 

base flow ranged from 4 colonies per 100 milliliters (col/100 

mL) to 530 col/100 mL, and in stormflow from 960 col/100 

mL to 42,000 col/100 mL. Median total coliform densities 

in base flow ranged from 2,950 MPN/100 mL to 

33,000 MPN/100 mL, and in stormflow from 57,000 

MPN/100 mL to 1,190,000 MPN/100 mL. The Little Blue 

River sites (sites 2, 5, and 9) tended to have lower median FIB 

densities in both base-flow and stormflow than those measured 

on most of the smaller streams (sites 1, 6 through 8, and 11). 

The median SSC concentration for base-flow samples ranged 

from 13 mg/L to 63 mg/L and for stormflow from 66 mg/L to 

1,130 mg/L, and was generally lower on the Little Blue River 

sites than on most of the smaller streams (sites 1, 6 through 

8, and 11) during base flow, and mid-range for the Little Blue 

River sites between those measured in sites 1, 3, 6, and 7 during stormflow.

The highest estimated annual load of E. coli was 

168,000,000 billion colonies and the highest estimated annual 

flow-weighted concentration of E. coli was 96,303 billion 

colonies.. The highest estimated annual SSC load was 

808,000 Mg, and the highest estimated annual flow-weighted 

concentration of SSC was 4,479 mg/L. 

E. coli and MST markers were analyzed using libraryindependent methods in 119 base-flow, 89 stormflow, and 4 

snowmelt samples from June 2008 through September 2013. 

MST samples were collected at 10 sites (sites 1 through 9 

and 11). In addition, 48 fecal source samples were collected 

between September 2011 and May 2013 from human, ruminant, dog, and several domestic and wild animal sources (cat, 

chicken, cow, deer, goose, horse, mouse, rabbit, and wild 

turkey). Twelve sewage influent samples also were collected 

from September 2011 through May 2013.

E. coli were detected in 112 of 119 base-flow samples (E. 

coli was not analyzed in 5 samples), all 89 stormflow samples, 

and all 4 snowmelt samples, for which MST markers also were 

analyzed. During the recreation season, about 45 percent of 

base-flow samples and about 98 percent of stormflow samples 

exceeded the Missouri standard for E. coli. E. coli and hostsource bacteria (human, canine, and ruminant) as determined 

by MST were detected more frequently and at higher concentrations during stormflow. Most of the estimated E. coli loads 

occur during stormflow.

Dry-weather screening was done by the USGS and 

Independence WPC Department personnel during WYs 

2006 through 2013 in most basins within the city limits. Any 

measureable inflow, discharge, or tributary flow to the selected 

stream was sampled. Two basins (Rock Creek and Spring 

Branch Creek) were sampled four times, one (Adair Creek) 

was sampled three times, and the remaining eight basins 

(Crackerneck, Mill, Sugar, Bundschu, Burr Oak, and West Fire 

Prairie Creeks, and East Fork Little Blue and Little Blue Rivers) were sampled one or two times. A total of 1,052 samples 

were collected from area stream basins for analysis of total 

chlorine, total dissolved copper, phenols, and anionic surfactants. Eight detections were determined to have a source such 

as a straight pipe discharge or broken water/septic line and 
72 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

corrective action was taken by Independence WPC. About 207 

(19.7 percent) of samples were at or above a defined standard 

or guideline for each of the constituents. A total of 73 samples 

were above the standard for total chlorine, 1 sample was above 

the standard for phenols, and 133 samples were above the 

guideline for anionic surfactants. No Federal or State standard 

has been determined for dissolved copper in unfiltered (total) 

samples. 

Individual macroinvertebrate metric values varied 

substantially by site and year; however, seasonal median 

stream condition index (SCI) scores for all Independence sites 

combined were the same despite some variability in component metrics. SCI scores indicated that 20 percent of spring 

Independence stream site samples met the criteria for full support of aquatic life and 80 percent were considered partially 

supportive, whereas 42 percent of fall samples were considered fully biologically supporting and 58 percent partially 

biologically supporting. No Independence stream sample had 

a non-supporting score.

This report presents all publishable data collected from 

June 2005 to September 2013 in streams and basins within the 

city limits of Independence, Missouri. The streamflow, waterquality, and ecological data collected during this study fulfill 

the municipal separate sewer system permit requirements 

for Independence and can be used to provide a baseline to 

determine the effectiveness of current (2014) and future best 

management practices within Independence. 

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Appendixes 1 and 2
80 Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri

Appendix 1. Base-flow water-quality sample results for 

selected physical and chemical properties and constituents, June 

2006 through September 2013 (http://pubs.usgs.gov/ds/0915/

downloads/ds915_Appendix01.xlsx).

Appendix 2. Stormflow water-quality sample results for 

selected physical and chemical properties and constituents, June 

2005 through September 2013 (http://pubs.usgs.gov/ds/0915/

downloads/ds915_Appendix02.xlsx).

Publishing support provided by:

Rolla Publishing Service Center

For more information concerning this publication, contact:

Director, Missouri Water Science Center

U.S. Geological Survey

1400 Independence Road, MS-100

Rolla, MO 65401

(573) 308–3667

Or visit the Missouri Water Science Center Web site at:

http://mo.water.usgs.gov/

Niesen and Christensen—Hydrological, Water-Quality, and Ecological Data for Streams in Independence, Missouri—Data Series 915

ISSN: 2327-638X (online)

http://dx.doi.org/10.3133/ds915