Distribution and Sources of Polychlorinated 

Biphenyls in Woods Inlet, Lake Worth, 

Fort Worth, Texas, 2003

By Richard E. Besse, Peter C. Van Metre, and Jennifer T. Wilson

U.S. Department of the Interior

U.S. Geological Survey

In cooperation with the U.S. Air Force

Scientific Investigations Report 2005–5064
U.S. Department of the Interior

Gale A. Norton, Secretary

U.S. Geological Survey

Charles G. Groat, Director

U.S. Geological Survey, Reston, Virginia: 2005

For sale by U.S. Geological Survey, Information Services

Box 25286, Denver Federal Center

Denver, CO 80225

For more information about the USGS and its products:

Telephone: 1-888-ASK-USGS

World Wide Web: http://www.usgs.gov/

Any use of trade, product, or firm names in this publication is for descriptive purposes only and does not imply

endorsement by the U.S. Government.

Although this report is in the public domain, permission must be secured from the individual copyright owners to

reproduce any copyrighted materials contained within this report.

Suggested citation:

Besse, R.E., Van Metre, P.C., and Wilson, J.T., 2005, Distribution and sources of polychlorinated biphenyls in Woods

Inlet, Lake Worth, Fort Worth, Texas, 2003: U.S. Geological Survey Scientific Investigations Report 2005–5064, 40 p.
iii

Contents

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

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

Approach . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 3

Watershed Characteristics . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 3

Collection and Processing of Bottom Sediment Samples . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5

Collection and Processing of Suspended Sediment Samples . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5

Collection and Processing of Streambed Sediment Samples . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 7

Analytical Methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 7

Quality Control . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 8

Age-Dating Cores . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 10

Distribution and Sources of Polychlorinated Biphenyls in Woods Inlet . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 10

Polychlorinated Biphenyls in Bottom Sediment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 10

Polychlorinated Biphenyls in Suspended and Streambed Sediment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 13

Source Identification Using Polychlorinated Biphenyl Congener Assemblages . . . . . . . . . . . . . . . . . . . . . . . 14

Summary . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 17

References . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 18

Appendixes

1. Core-specific and analytical polychlorinated biphenyl data from core, surficial bottom, 

suspended, and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, 

Fort Worth, Texas . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 21

1.1 Porosity, cesium-137 (137Cs) activity, mass accumulation rate (MAR), and deposition 

dates for gravity core samples, Woods Inlet, Lake Worth, Fort Worth, Texas, 2003 . . . . . . . . . . . 23

1.2 Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations 

in core, surficial bottom, suspended, and streambed sediment samples, Woods Inlet 

and tributaries, Lake Worth, Fort Worth, Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 24

2. Analytical data for major and trace elements, selected polycyclic aromatic hydrocarbons, 

and selected organochlorine pesticides from core, surficial bottom, suspended, and 

streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas . . . . . . . 33

2.1 Selected major and trace element concentrations in surficial bottom, suspended, and 

streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, 

Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 36

2.2 Selected polycyclic aromatic hydrocarbon concentrations in surficial bottom, 

suspended, and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, 

Fort Worth, Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 38

2.3 Selected organochlorine pesticide concentrations in surficial bottom, suspended, and 

streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, 

Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 40
iv

Figures

1–3. Maps showing:

1. Location of study area and polychlorinated biphenyl (PCB) concentrations in surficial 

bottom sediment, Lake Worth, Fort Worth, Texas, 2000–2001 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2

2. Sediment sampling sites for this study in Woods Inlet and tributaries, Lake Worth, 

Fort Worth, Texas . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 4

3. Watersheds of tributary streams to Woods Inlet, Lake Worth, Fort Worth, Texas . . . . . . . . . 6

4. Photograph showing passive suspended sediment sampler, Gruggs Park Creek (a tributary 

to Woods Inlet), Lake Worth, Fort Worth, Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 7

5. Graphs showing cesium-137 profiles in gravity cores used for age-dating, Woods Inlet, Lake 

Worth, Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 10

6. Graphs showing detection frequency by polychlorinated biphenyl (PCB) congener and 

sample type, Woods Inlet, Lake Worth, Fort Worth, Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 11

7. Map showing total polychlorinated biphenyl (PCB) concentrations (sum of PCB congeners) 

in surficial bottom sediment, Woods Inlet, Fort Worth, Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 12

8. Graphs showing trends in total polychlorinated biphenyl (PCB) concentrations (sum of PCB 

congeners) in sediment cores relative to (a) sediment depth and (b) date of sediment 

deposition, Woods Inlet, Lake Worth, Fort Worth, Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 13

9. Map showing total polychlorinated biphenyl (PCB) concentrations (sum of PCB congeners) 

in suspended and streambed sediment from tributary streams to Woods Inlet, Lake Worth, 

Fort Worth, Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14

10. Graphs showing selected polychlorinated biphenyl (PCB) congener assemblages normalized 

(divided) by total PCB (sum of PCB congeners) for surficial bottom sediment in areas of 

Woods inlet and suspended and streambed sediment in tributary streams to Woods Inlet, 

Lake Worth, Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 16

11. Map showing results of cluster analysis using selected polychlorinated biphenyl (PCB) 

congeners, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003 . . . . . . . . . . . . . . . . . . . . 17

Tables

1. Sampling site descriptive information, Woods Inlet and tributaries, Lake Worth, Fort Worth, 

Texas, 2003 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 3

2. Polychlorinated biphenyl congeners analyzed for this report . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 8

3. Summary of median relative percent differences (RPDs) of duplicate samples from this 

study and other coring and suspended sediment studies done by the U.S. Geological Survey 

(USGS) in Texas . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9

4. Root mean squared difference (RMSD), from smallest to largest, between normalized 

concentrations of 17 polychlorinated biphenyl congeners in suspended and streambed 

sediment samples in tributaries and mean of all surficial bottom sediment sample 

concentrations of those congeners in Woods Inlet, Lake Worth, Fort Worth, Texas, 2003 . . . . . . . . . 15
Distribution and Sources of Polychlorinated 

Biphenyls in Woods Inlet, Lake Worth, 

Fort Worth, Texas, 2003

By Richard E. Besse, Peter C. Van Metre, and Jennifer T. Wilson

Abstract

Woods Inlet is a flooded stream channel on the southern 

shore of Lake Worth along the western boundary of Air Force 

Plant 4 in Fort Worth, Texas, where elevated polychlorinated 

biphenyl (PCB) concentrations in sediment were detected in a 

previous study. In response, the U.S. Geological Survey, in 

cooperation with the U.S. Air Force, conducted a study in 2003 

to map the extent of elevated PCB concentrations in Woods 

Inlet and to identify possible sources (or more specifically, 

source areas) of PCBs in the watershed of Woods Inlet. Three 

gravity cores (penetration to pre-reservoir sediment at three 

sites) and 17 box cores (surficial bottom sediment samples) 

were collected in Woods Inlet. Suspended sediment in stormwater runoff and streambed sediment were sampled in tributaries to Woods Inlet following storms. Assemblages of PCB 

congeners in surficial inlet sediments and suspended and 

streambed sediments were analyzed to indicate sources of PCBs 

in the inlet sediments on the basis of chemical signatures of 

PCBs. Woods Inlet receives runoff primarily from three tributaries: (1) Gruggs Park Creek, (2) the small unnamed creek that 

drains a Texas National Guard maintenance facility, called 

TNG Creek for this report, and (3) Meandering Road Creek. 

Twenty-seven of 209 possible PCB congeners were analyzed. 

The sum of the congeners was used as a measure of total PCB. 

The spatial distribution of total PCB concentrations in the inlet 

indicates that most PCBs are originating in the Meandering 

Road Creek watershed. Peak total PCB concentrations in the 

three gravity cores occurred at depths corresponding to sediment deposition dates of about 1960 for two of the cores and 

about 1980 for the third core. The magnitudes of peak total PCB 

concentrations in the gravity cores followed a spatial distribution generally similar to that of surficial bottom sediment 

concentrations. Total PCB concentrations in suspended and 

streambed sediment varied greatly between sites and indicated 

a likely source of PCBs associated with a sampling site that 

receives runoff from Air Force Plant 4. Three approaches to the 

analyses of congener assemblages indicate that PCBs in surficial bottom sediment of Woods Inlet primarily enter Lake 

Worth from Meandering Road Creek and that runoff from Air 

Force Plant 4 is a source of the PCBs in Meandering Road 

Creek. Although current (2003) transport of PCBs from Air 

Force Plant 4 to the creek is occurring, large decreases in PCB 

concentrations with decreasing age in two cores indicate that 

PCB loading to the inlet has decreased greatly since the 1960s. 

Because runoff entering Meandering Road Creek from some 

parts of Air Force Plant 4 was not measured or sampled in this 

study, it cannot be said with certainty that the Air Force Plant 4 

site sampled is the only source of PCBs to Meandering Road 

Creek.

Introduction

Lake Worth is a reservoir on the West Fork Trinity River 

on the western edge of Fort Worth, Tex. (fig. 1). Air Force Plant 

4 (AFP4) and Naval Air Station-Joint Reserve Base Carswell 

Field (NAS–JRB) are on the southern shore of Lake Worth. In 

spring 2000, following fish sampling by the U.S. Geological 

Survey (USGS) (Moring, 2002), the Texas Department of 

Health (TDH) issued a fish-consumption advisory because high 

levels of polychlorinated biphenyls (PCBs) detected in fish 

samples posed a “significant health risk” (Texas Department of 

Health, 2004). The occurrence of PCBs in fish prompted an 

investigation by the USGS, in cooperation with the U.S. Air 

Force (USAF), to sample and analyze Lake Worth bottom sediment for sediment-bound contaminants, including PCBs. The 

findings of that study (Harwell and others, 2003) reported elevated PCB concentrations in surficial sediment in Woods Inlet 

relative to those in surficial sediment in other parts of the lake 

(fig. 1). This finding indicated that a source of PCBs likely was 

in the watershed of Woods Inlet. Woods Inlet is on the southern 

shore of Lake Worth along the western boundary of AFP4 and 

downstream from urban development in the cities of Fort Worth 
Figure 1. Location of study area and polychlorinated biphenyl (PCB) concentrations in surficial bottom sediment, Lake Worth, Fort Worth, Texas, 200Harwell and others, 2003, fig. 10).

Figure 1 Location of study area and concentrations of polychlorinated biphenyls (PCB) in surficial sediment Lake Worth Fort Worth Texa

Base modified froDigital orthophoto Universal TransveDatum NAD 83, 1-

EXPLANA

NABotottiopeNois llevSitIndcolWoLa

12

97o27' 97o26'

32o47'

97o29' 97o28' 97o25'

32o48'

32o49'

32o46'

0 

0 

ND

ND

ND

ND

ND

9

ND

20

15

140

ND

10 12

ND

ND

ND

12

9 ND 3

ND

F

LOC

IH–820

Air Force

Plant 4

Woods

Inlet

Meandering

Road Creek

Lake Worth

White

Settlement

Naval Air

StationJoint

Reserve

Base

Carswell

Field

(NAS–JRB)

West Fork

Trinity River
Approach 3

and White Settlement. Harwell and others (2003) also detected 

higher concentrations of selected trace elements (metals) and 

polycyclic aromatic hydrocarbons (PAHs) in Woods Inlet than 

in other parts of the lake.

In response to the elevated PCB concentrations in sediment in Woods Inlet, the USGS, again in cooperation with the 

USAF, conducted a study in 2003 to map the distribution of elevated PCB concentrations in Woods Inlet and to identify possible sources (or more specifically, source areas) of PCBs in the 

watershed of Woods Inlet. This report describes the methods 

and findings of that study. Gravity cores and surficial inlet bottom sediment samples were collected and analyzed to map the 

distribution of PCB concentrations in Woods Inlet. Suspended 

sediment in stormwater runoff and streambed sediment in tributaries to Woods Inlet were sampled following storms to identify current (2003) sources of PCBs. Assemblages of PCB congeners (groups of individual PCB compounds) in bottom 

sediments and suspended and streambed sediments were analyzed to indicate sources of PCBs in the bottom sediments in the 

inlet on the basis of chemical signatures of PCBs. Sediment 

samples also were analyzed for major and trace elements, 

selected PAHs, and selected organochlorine pesticides. 

Although those results are insufficient to describe distribution 

in Woods Inlet or to identify potential sources of trace elements, 

PAHs, and pesticides, those data are included in an appendix of 

this report.

The authors thank NAS–JRB and Lockheed Martin Corporation for access to the inlet and tributary sampling sites and for 

providing maps of watersheds on AFP4. Also, the authors thank 

the cities of Fort Worth and White Settlement for allowing the 

USGS to install suspended sediment samplers on streams.

Approach

The distribution of PCBs in Woods Inlet was determined 

using a combination of surficial bottom sediment samples (top 

5 centimeters [cm] at 20 sites) and bottom sediments from gravity cores that penetrated the lacustrine sediment sequence that 

was deposited since 1914, when Lake Worth was constructed 

(three sites) (fig. 2; table 1). Sources of PCBs in current (2003) 

storm runoff were investigated by sampling suspended sediment at five sites on tributary streams (fig. 2) during three 

storms and by sampling streambed sediment at four of those 

five sites after each of the three storms. Historical and presentday sources of PCBs also were investigated by evaluating the 

relative distributions of PCB congeners in the stream and inlet 

sediment samples. Congener assemblages can be indicative of 

different PCB sources (Cacela and others, 2002; Colman, 2000; 

Johnson and others, 2000).

Watershed Characteristics

Woods Inlet receives runoff primarily from three tributaries: (1) Gruggs Park Creek, (2) the small unnamed creek that 

drains a Texas National Guard maintenance facility (hereinafter, TNG Creek), and (3) Meandering Road Creek (fig. 2). Suspended and streambed sampling sites were established on each 

of these three creeks. One site near the mouth of Gruggs Park 

Creek (GRUGGS) receives runoff from urban and agricultural 

areas and from an interstate highway, but it does not receive 

runoff from AFP4. A second site near the mouth of TNG Creek 

(TNG) receives runoff from the Texas National Guard maintenance facility and urban areas but not from AFP4. A third site 

near the mouth of Meandering Road Creek (LMRC) receives 

runoff from three stormwater outfalls that drain areas of AFP4, 

Table 1. Sampling site descriptive information, Woods Inlet 

and tributaries, Lake Worth, Fort Worth, Texas, 2003. 

[--, not recorded] 

Site

identifier

(fig. 2)

Latitude

(degrees,

minutes)

Longitude

(degrees,

minutes)

Sample

date

Water

depth

(meters)

Surficial bottom sediment

B1 97°27.551' 32°46.968' 04/22/03 1.5

B2 97°27.498' 32°46.962' 04/22/03 2.5

B3 97°27.377' 32°46.941' 04/22/03 3.6

B4 97°27.354' 32°46.783' 04/22/03 1.2

B5 97°27.319' 32°46.822' 04/22/03 2.7

B6 97°27.255' 32°46.721' 04/22/03 .9

B7 97°27.268' 32°46.772' 04/22/03 1.5

B8 97°27.271' 32°46.859' 04/22/03 3.3

B9 97°27.273' 32°46.895' 04/22/03 3.4

B10 97°27.266' 32°46.980' 04/22/03 3.8

B11 97°27.288' 32°46.999' 04/22/03 4.2

B12 97°27.322' 32°47.006' 04/22/03 4.3

B13 97°27.240' 32°47.058' 04/22/03 4.6

B14 97°27.273' 32°47.074' 04/22/03 4.4

B15 97°27.282' 32°47.088' 04/22/03 4.0

B16 97°27.156' 32°47.055' 04/22/03 4.0

B17 97°27.201' 32°47.150' 04/22/03 4.8

Core sediment

WWD1 97°27.309' 32°46.950' 04/21/03 3.8

WWD2 97°27.422' 32°46.967' 04/21/03 3.4

WWD3 97°27.267' 32°46.811' 04/21/03 2.7

Suspended and streambed sediment

GRUGGS 97°27.877' 32°46.732' Multiple --

TNG 97°27.424' 32°46.679' Multiple --

LMRC 97°27.212' 32°46.637' Multiple --

OF4 97°27.215' 32°46.572' Multiple --

UMRC 97°27.809' 32°46.003' Multiple --
4 Distribution and Sources of Polychlorinated Biphenyls in Woods Inlet, Lake Worth, Fort Worth, Texas, 2003

Figure 2. Sediment sampling sites for this study in Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas.

97 ̊28' 97 ̊27'

32 ̊46'

32 ̊47'

Base modified from U.S. Geological Survey

Digital orthophoto quarter-quadrangle,

Universal Transverse Mercator projection, Zone 14,

Datum NAD 83, 1-foot resolution

0 0.25 0.5 MILE

0 0.5 KILOMETER

Sediment sampling

site and site

identifier—Site

identifier referenced

in table 1

Box core (surficial)

Gravity core (core)

Suspended and

streambed

WWD1

WWD2 WWD1

WWD3

WWD1

WWD2 WWD1

WWD3

B3

B3

B1 B2

B5

B4

B7

B10 B11 B12

B13

B14 B15

B16

B17

B6

B9

B8

B3

B3

B1 B2

B5

B4

B7

B10 B11 B12

B13

B14 B15

B16

B17

B6

B9

B8

TNG

TNG

OF4

LMRC

GRUGGS

UMRC TNG

TNG

OF4

LMRC

GRUGGS

UMRC

Air Force Air Force

Plant 4 Plant 4

Woods

Inlet

Meandering Meandering

Road Creek Road Creek

Texas National Texas National

Guard (TNG) facility Guard (TNG) facility Landfill 1 Landfill 1

Landfill 3 Landfill 3

Outfall 4 Outfall 4

Gruggs

Park Creek Park Creek

Gruggs arm of Gruggs arm of

Woods

Inlet

Air Force

Plant 4

Woods

Inlet

Meandering

Road Creek

Texas National

Guard (TNG) facility Landfill 1

Landfill 3

Outfall 4

Gruggs

Park Creek

Gruggs arm of

Woods

Inlet
Approach 5

from two historical landfills (1 and 3) on AFP4, and from urban 

areas south and west of AFP4. A fourth site at outfall 4 about 

200 meters (m) upstream from LMRC on Meandering Road 

Creek (OF4) receives runoff from buildings, parking areas, and 

one historical landfill on AFP4. A fifth site on Meandering 

Road Creek upstream from AFP4 (UMRC) receives runoff 

from urban areas but not from AFP4. GRUGGS and UMRC are 

considered urban reference sites because the sites receive runoff 

from urban areas but not from AFP4 or the Texas National 

Guard facility. The watershed areas (fig. 3) upstream from 

LMRC (4.1 square kilometers [km2]), GRUGGS (2.0 km2), and 

TNG (0.4 km2) are 46, 55 and 71 percent urban (including 

industrial and transportation categories), respectively. The 

watershed area upstream from LMRC includes the watershed 

areas upstream from UMRC (2.8 km2

) and OF4 (0.2 km2), 

which are 38 and 96 percent urban, respectively. 

Suspended sediment samples were collected during three 

storms at each of the five sites. Streambed sediment samples 

were collected at all of the sites except OF4 following each of 

the three storms in which suspended sediment samples were 

collected. 

Collection and Processing of Bottom Sediment 

Samples

Of the 20 sediment sampling sites in Woods Inlet, 17 were 

sampled for surficial bottom sediment only (fig. 2) using a 14- 

by 14- by 20-cm Wildco box corer. The box-core samples (top 

5 cm) were removed from the box by vertical extrusion and sectioning following the methods of Van Metre and others (2004). 

Each sample was homogenized and split. A subsample for analysis of organic compounds was transferred to a baked-glass jar 

and chilled pending shipment to the USGS National Water 

Quality Laboratory (NWQL) in Denver, Colo. A subsample for 

analysis of major and trace elements (selected sites only), 

organic carbon, and grain size was transferred to a polypropylene jar, chilled, and returned to the USGS office in Austin, Tex. 

There, samples for analysis of major and trace elements and 

organic carbon were frozen, freeze-dried, and ground to a fine 

powder before shipment to the NWQL. Samples for analysis of 

grain size were stored in jars and shipped wet to the NWQL.

At three sampling sites, gravity cores were collected to 

investigate historical trends of sediment-associated contaminants in bottom sediment (fig. 2) following the sampling methods of Van Metre and others (2004). These sites were selected 

to represent historical trends in contaminants in the main body 

of Woods Inlet (WWD1) and in the two tributary arms, Gruggs 

Park Creek arm (WWD2) and Meandering Road Creek arm 

(WWD3). The cores were collected using a Benthos gravity 

corer with a diameter of 6.3 cm, a barrel length of as much as 

3.1 m, and a polycarbonate core liner. Cores were subsampled 

on site by vertical extrusion of the sediment in measured increments using a piston fit into the bottom of the liner. All three 

gravity cores were subsampled at 5-cm intervals from the top 

of the core to a depth of 10 cm (two samples) and thereafter in 

10-cm intervals to the bottom of the core. Each subsample was 

homogenized and split. Samples for analysis of organic compounds were transferred to a baked-glass jar, and samples for 

analysis of major and trace elements (one sample only), cesium137 (137Cs) for age-dating, and grain size were transferred to a 

polypropylene jar. Samples were chilled pending shipment to 

the NWQL or freeze-drying. Sampling tools were washed 

between each sample using phosphate-free detergent and native 

water. 

Collection and Processing of Suspended Sediment 

Samples

Suspended sediment samples were collected at five sites 

during three storms using passive samplers (fig. 4). A passive 

sampler consists of a 36-cm diameter, capped steel pipe holding 

a 25-liter (L) Nalgene carboy with a water intake that is submerged during stormflow and an air exhaust tube. The sampler 

will obtain a 25-L sample of runoff from the “first flush” (initial 

rise in flow) during a storm. The streams are ephemeral and 

only flow in response to precipitation. During a storm, the water 

level rises above the level of the intake and fills the carboy. The 

air exhaust is constructed to block the flow of air or water once 

the carboy is filled, which prevents continual circulation 

through the sampler. Additional stormwater samples were collected during storms at some sites to provide a sufficient mass 

of suspended sediment for chemical analyses. The 25-L carboys 

were retrieved after the water level had fallen below the intakes 

of the samplers after a storm and transported to the USGS office 

in Fort Worth. The water was stored on ice until processing. 

Processing each sample took several hours, so processing all of 

the samples from a storm typically took from 1 to 2 days after 

the storm. In all, 15 environmental samples and one environmental duplicate sample were obtained for analysis.

Sediment was isolated from the water samples by in-line 

filtration following the methods of Mahler and Van Metre 

(2003). The 25-L carboy was agitated to suspend the sediment 

in the water column and immediately poured into a 25-L churn. 

The churn has a paddle that, with steady motion, keeps the sediment suspended and the sample well mixed during processing. 

As the original 25 L was filtered, additional water was poured 

into the churn from other bottles if available. Sediment for the 

inorganic analyses (major and trace elements) was collected on 

a 142-millimeter (mm) diameter, 0.45-micron (μm) pore size 

polytetrafluoroethylene (PTFE) filter in an acrylic filter holder. 

Sediment for the analysis of organic compounds was collected 

on a 293-mm diameter, 0.45-μm pore size PTFE filter in a stainless steel filter holder. Water was pumped from the churn with 

a peristaltic pump through the filter until the filter was clogged. 

The volume of water that was passed though the filter was 

noted. The filter was removed from the holder and placed in a 

locking plastic bag with 10 to 20 milliliters (mL) of deionized 

water. The filter was gently massaged in the bag to release the 

sediment from the filter. This process was repeated, usually 

three to six times, until enough sediment was collected for 
Figure 3. Watersheds of tributary streams to Woods Inlet, Lake Worth, Fort Worth, Texas.

97o30'

32o45'

97o27'30"

32o46'15"

Gruggs Park Creek

watershed

Meandering Road Creek

watershed

Texas National

Guard facility

watershed

Landfill 1

Landfill 3

Meand ering Road Creek

Gruggs Park Creek

Woods Inlet

0 0.2 0.4 0.6 

Base from U.S. Geological Survey digital raster graph 0 0.2 0.4 0.6 0.8 1 KILOME1:24,000 Lake Worth topographic quadrangle

TNG

OF4

LMRC

GRUGGS

UMRC

TNG

TNG

OF4

LMRC

GRUGGS

UMRC

TNG

Boundary of watershedBoundary of subwatershedSuspended andstreambed sedimentsampling site andidentifier
Approach 7

analysis. The sediment slurry was then poured into a 125-mL 

glass or 125-mL Nalgene jar for organic and inorganic analysis, 

respectively. The samples for organic analysis were allowed to 

settle for approximately 4 days under refrigeration at which 

point the overlying water was decanted with a sterile glass 

pipette, and the samples were sent chilled to the NWQL. The 

samples for inorganic analysis were freeze-dried at the USGS 

office in Austin and then sent to the NWQL.

Collection and Processing of Streambed Sediment 

Samples

Streambed sediment samples were collected within 5 days 

of each storm runoff at four of the five sampling sites. No 

streambed sediment samples were collected at OF4 because the 

passive sampler is located at the end of a cement culvert, and 

therefore no streambed is upstream from the sampler. Twelve 

environmental samples and three environmental duplicate samples were collected. The environmental duplicates were collected independently by a second sampling team on the same 

day as the environmental samples were taken for each site. The 

objective in doing environmental duplicates this way was to test 

the repeatability of the streambed sediment sampling protocol, 

including environmental variability, sampling variability, and 

analytical uncertainty. Three laboratory duplicates (a single 

environmental sample split at the laboratory) of streambed sediment also were analyzed.

Streambed sediment samples were collected using a precleaned nylon spoon to scoop 10 subsamples from the streambed in depositional areas with relatively fine-grained sediment, 

upstream from each of the four passive samplers (Shelton and 

Capel, 1994). The 10 subsamples from each site were put into 

wide-mouth glass jars to make a composite sample and taken to 

the USGS laboratory in Fort Worth for processing. Two liters of 

native water was collected from each site for sieving the samples. In the laboratory, the sediment from each site was poured 

into a large pre-cleaned Pyrex mixing bowl and homogenized 

with a Teflon spatula. Approximately one-half of the material 

was passed through a 2-mm mesh stainless steel sieve and the 

fraction less than 2 mm was collected in a 250-mL baked-glass 

jar for analysis of organic compounds. This sample was then put 

in a refrigerator and allowed to settle. The other half of the sample was processed for analysis of inorganic elements. Approximately 400 mL of native water was poured into a 1,000-mL 

glass beaker. An aliquot (two to three tablespoons) of the composite sample was placed into the center of a 63-μm nylon sieve 

cloth. The corners of the cloth were then drawn up to form a 

bag. This bag was dipped repeatedly into the beaker containing 

the native water separating out the particles of less than 63−μm 

diameter. This process was repeated until all of the composite 

sample was sieved, after which the slurry in the 1,000-mL beaker was transferred to a 500-mL plastic bottle and stored in a 

refrigerator and allowed to settle. After settling, the overlying 

liquid was decanted with a sterile glass pipette. Samples for 

analysis of organic compounds were shipped chilled to the 

NWQL. Samples for elemental analysis were freeze-dried, 

ground to a fine powder, and shipped to the NWQL.

Analytical Methods

Samples for analysis of major and trace elements were 

completely digested using a mixture of hydrochloric-nitricperchloric-hydrofluoric acids and analyzed by inductively coupled plasma/mass spectrometry (ICP/MS) (Briggs and Meier, 

2003). Mercury was analyzed by cold vapor atomic absorption 

spectrometry (Arbogast, 1996). 137Cs activity was measured by 

counting freeze-dried sediments in fixed-geometry containers 

with a high-resolution, intrinsic germanium detector gammaspectrometer (Robbins and Edgington, 1976). 

Organochlorine pesticides, PCBs, PAHs, and alkylsubstituted PAHs (alkyl-PAHs) were extracted, isolated, and 

analyzed using the procedures of Noriega and others (2003) and 

Olson and others (2004). Briefly, wet bottom sediment was 

extracted overnight with dichloromethane in a Soxhlet apparatus. The extract was reduced in volume and filtered. Two 

Figure 4. Passive suspended sediment sampler, Gruggs Park 

Creek (a tributary to Woods Inlet), Lake Worth, Fort Worth, Texas, 

2003.
8 Distribution and Sources of Polychlorinated Biphenyls in Woods Inlet, Lake Worth, Fort Worth, Texas, 2003

aliquots of the sample extract were quantitatively injected into 

a polystyrene-divinylbenzene gel permeation column (GPC) 

and eluted with dichloromethane to remove sulfur and partially 

isolate the target analytes from coextracted high-molecularweight interferents such as humic substances. The first aliquot 

was passed through a silica column cleanup step and then analyzed for PAHs and alkyl-PAHs by capillary-column gas chromatography (GC) with detection by mass spectrometry (MS). 

Parent PAHs were identified and quantified by comparison to 

authentic standards. Individual alkyl-PAHs were quantified 

when authentic alkyl-substituted standards were available. 

When authentic alkyl-substituted standards were unavailable, a 

parent PAH was used as the standard for quantitation. The multiple isomeric alkyl-PAHs were quantified from mass chromatograms as the sum of all isomers at each alkylation level 

(C1-naphthalenes, C2-naphthalenes, and so forth). Nineteen 

parent PAHs, 10 specific alkyl-PAHs, and the homologous 

series of alkyl-PAHs were determined. The second aliquot was 

further split into two fractions by combined alumina/silica 

adsorption chromatography followed by a micro Florisil column cleanup step prior to determination of the organochlorine 

pesticides and PCBs by dual capillary-column gas chromatography with electron capture detection (GC-ECD) (Olson and 

others, 2004). The organochlorine pesticides were reported as 

individual compounds. Technical chlordane was estimated 

from trans-nonachlor, cis-chlordane, and trans-chlordane concentrations. PCBs were reported as individual Aroclor 

(1016/1242, 1254, or 1260) equivalents (Noriega and others, 

2003). 

For this study, Fraction 1 (PCB fraction) of the organiccompound analysis was analyzed for 27 (of 209 possible) 

selected PCB congeners (table 2) along with the other Fraction 

1 analytes during GC–ECD analysis. The congeners chosen for 

this analysis were some of the more dominant congeners in the 

most widely used Aroclors (1016, 1242, 1254, and 1260). In 

addition to the dominance of these congeners, potential coelution issues and signal response for this analytical method 

were considered. A series of dilutions of a custom mixture containing the 27 selected PCB congeners was used to make the 

calibration standards. Calibration standards were prepared at 

four levels, and a minimum of three points were used for the 

calibration curves. An additional congener solution, prepared at 

a concentration that was mid-range on the curve, was used as a 

check standard to verify the calibration curve. 

The laboratory reporting level for PCB Aroclors was 5 

micrograms per kilogram (μg/kg); however, variations in sample mass, sample matrix, and analytical interferences raised 

reporting levels for some environmental samples to 20 μg/kg or 

more. A laboratory reporting level has not been established for 

individual congeners because the method is relatively new 

(W.T. Foreman, U.S. Geological Survey, written commun., 

2001); however, it is believed to be conservatively about 1 

μg/kg (M.C. Noriega, U.S. Geological Survey, oral commun., 

2003). Concentrations well below that level were reported when 

the analyst was confident in the detection; those values were 

identified in the data tables in appendix 1.2 as estimated (E). 

Because the quantification of individual congeners is believed 

to be more precise than the Aroclor equivalents, the sum of the 

congeners was used as a measure of total PCB rather than the 

sum of the Aroclors. A comparison of all suspended, streambed, 

and bottom sediment samples indicated that the sum of the congeners accounted for 57 percent (mean, ± 6 percent [one standard deviation]) of the sum of the Aroclors.

Quality Control 

Quality control for organic compound (PCB, PAH, 

organochlorine pesticide) analyses consisted of analyzing an 

Table 2. Polychlorinated biphenyl congeners analyzed for this report.

Congener

number

International Union of Pure and

Applied Chemistry (IUPAC) name

Congener

number

International Union of Pure and

Applied Chemistry (IUPAC) name

8 2,4'-Dichlorobiphenyl 118 2,3',4,4',5-Pentachlorobiphenyl 

18 2,2',5-Trichlorobiphenyl 138 2,2',3,4,4',5'-Hexachlorobiphenyl

22 2,3,4'-Trichlorobiphenyl 146 2,2',3,4',5,5'-Hexachlorobiphenyl

26 2,3',5-Trichlorobiphenyl 149 2,2',3,4’,5',6-Hexachlorobiphenyl

28 2,4,4'-Trichlorobiphenyl 151 2,2',3,5,5',6-Hexachlorobiphenyl

31 2,4',5-Trichlorobiphenyl 170 2,2',3,3',4,4',5-Heptachlorobiphenyl

33 2,3',4'-Trichlorobiphenyl 174 2,2',3,3',4,5,6'-Heptachlorobiphenyl

44 2,2',3,5'-Tetrachlorobiphenyl 177 2,2',3,3',4,5',6'-Heptachlorobiphenyl

49 2,2',4,5'-Tetrachlorobiphenyl 180 2,2',3,4,4',5,5'-Heptachlorobiphenyl

52 2,2',5,5'-Tetrachlorobiphenyl 183 2,2',3,4,4',5',6-Heptachlorobiphenyl

70 2,3',4',5-Tetrachlorobiphenyl 187 2,2',3,4',5,5',6-Heptachlorobiphenyl

95 2,2',3,5',6-Pentachlorobiphenyl 194 2,2',3,3',4,4',5,5'-Octachlorobiphenyl

101 2,2',4,5,5'-Pentachlorobiphenyl 206 2,2',3,3',4,4',5,5',6-Nonochlorobiphenyl

110 2,3,3',4',6-Pentachlorobiphenyl
Approach 9

analytical blank sample, a spiked sample, a certified reference 

material (CRM), and a duplicate, and monitoring recovery of 

surrogate compounds with each set of 12 environmental samples (Noriega and others, 2003; Olson and others, 2004). PCB 

and organochlorine pesticide blank samples had no detections. 

PAH blank samples had detections for eight of the 11 compounds, with concentrations ranging from an estimated 0.18 to 

1.4 μg/kg. The typical minimum reporting level for PAH compounds is 5 μg/kg. Median spike recoveries were 68 percent for 

PCBs and organochlorine pesticides and 69 percent for PAHs. 

PCB and organochlorine pesticide spike recoveries were within 

control limits for 93 percent of the spike results. No spike recovery control limits for the PAHs were established by the NWQL. 

CRM concentrations were within acceptable concentration 

ranges for 94 percent of the PCB and organochlorine pesticide 

CRM results and 88 percent of the PAH CRM results. All CRM 

concentrations that were outside an acceptable range were 

lower than the minimum value of the range. Recovery corrections were not applied. Quality control for major and trace element analyses consisted of analyzing several standard reference 

materials (SRMs) and one or more duplicates with each batch 

of as many as 20 samples. Median relative percent difference 

(RPD) for all elements for all SRMs was 4.2 percent. 

Analytical results from two types of duplicate samples are 

included in this report—environmental duplicates and laboratory duplicates (appendixes 1 and 2). An environmental duplicate is a sample that is split into two jars at the time of collection; both jars are submitted to the laboratory for analysis. A 

laboratory duplicate is a single sample that is split by the laboratory during preparation and analyzed in duplicate. Although 

the analytical methods of PCB analysis were the same for core, 

surficial, suspended, and streambed sediment, sample mass was 

small enough for suspended sediment samples that reporting 

levels and precision were affected, and the number of duplicates 

analyzed was limited. Twelve duplicate samples were analyzed 

for PCBs (table 3). The median RPD of the duplicate PCB analyses ranged from 12.0 to 74.8 percent. Fifteen duplicate samples were analyzed for major and trace elements. The median 

RPD of the duplicate major and trace element analyses ranged 

from 1.6 to 2.1. Eight duplicate samples were analyzed for 

PAHs. The median RPD of the duplicate PAH analyses ranged 

from 19.3 to 30.4 percent. Eight duplicate samples were analyzed for organochlorine pesticides. The median RPD of the 

duplicate organochlorine pesticide analyses ranged from 16.3 to 

40.3 percent. Generally, the median RPDs for PCBs were 

greater for the suspended and streambed sediment samples than 

for the core and surficial sediment samples. 

In addition to the median RPDs of duplicate samples for 

this report, table 3 shows the median RPDs of duplicate samples 

from other USGS sediment coring studies using the same collection and analytical methods. Generally, the median RPDs of 

organic compounds for the suspended and streambed sediment 

samples in this report are greater than the median RPDs for the 

suspended and streambed sediment samples in other sediment 

coring studies. Few duplicate samples have been analyzed 

for PCB congeners in other sediment coring studies because 

the analytical method used by the NWQL is relatively new 

(W.T. Foreman, U.S. Geological Survey, written commun., 

2001). Median RPDs for core sediment samples analyzed for 

PCBs and for all types of sediment samples analyzed for major 

and trace elements for this report are similar in magnitude to 

median RPDs for those constituents from other sediment coring 

studies.

Table 3. Summary of median relative percent differences (RPDs) of duplicate samples from this study and other coring and suspended 

sediment studies done by the U.S. Geological Survey (USGS) in Texas. 

[Number of samples in parentheses; PCBs, polychlorinated biphenyls; PAHs, polycyclic aromatic hydrocarbons] 

Constituent Core sediment

samples

Surficial bottom

sediment samples

Suspended sediment

samples

Streambed sediment

samples

Median RPDs from this study

PCBs

Aroclors 12.2 (4) 27.5 (1) 74.8 (1) 13.0 (6)

Congeners 12.0 (4) 21.2 (1) 35.5 (1) 25.0 (6)

Major and trace elements No duplicate 2.0 (1) 1.6 (3) 2.1 (11)

PAHs No duplicate 19.3 (1) 30.4 (1) 29.0 (6)

Organochlorine pesticides No duplicate 16.3 (1) No detections (1) 40.3 (6)

Median RPDs from other USGS studies using the same methods (Van Metre and others, 2004)

PCBs

Aroclors 11.2 (57) 8.3 (5) 24.7 (5) No duplicate

Congeners 15.1 (1) No duplicate No duplicate No duplicate

Major and trace elements 2.3 (66) 2.6 (4) 2.2 (49) 4.4 (6)

PAHs 11.2 (63) 14.9 (8) 19.8 (5) 6.6 (2)

Organochlorine pesticides 15.6 (57) 7.7 (5) 18.6 (5) No duplicate
10 Distribution and Sources of Polychlorinated Biphenyls in Woods Inlet, Lake Worth, Fort Worth, Texas, 2003

Figure 5. Cesium-137 profiles in gravity cores used for age-dating, Woods Inlet, Lake Worth, Texas, 2003.

Gravity core WWD1 Gravity core WWD2 Gravity core WWD3

0 0.50 1.00 1.50 0 0.50 1.00 1.50 -0.01 0.49 0.99

CESIUM-137 ACTIVITY,

IN PICOCURIES PER GRAM

CESIUM-137 ACTIVITY,

IN PICOCURIES PER GRAM

CESIUM-137 ACTIVITY,

IN PICOCURIES PER GRAM

0

20

40

60

80

100

120

140

160

180

200

CORE DEPTH, IN CENTIMETERS

0

20

40

60

80

100

120

140

0

20

40

60

80

100

120

140

160

180

200

CORE DEPTH, IN CENTIMETERS

CORE DEPTH, IN CENTIMETERS

Age-Dating Cores

The methods for age-dating reservoir and inlet cores used 

in this study are described in Harwell and others (2003) and 

Van Metre and others (2004). Briefly, a sediment core from an 

undisturbed depositional zone in a reservoir penetrates through 

layers of sediment deposited over the history of the reservoir. 

Several date markers are recorded in the core that allow for estimation of deposition dates for the core, usually assuming a constant sediment mass accumulation rate (MAR, in grams per centimeter squared per year) between the markers. Three date 

markers were used in cores from Lake Worth: the pre-reservoir 

land surface (the boundary between soil and lacustrine bottom 

sediment in the core) dated as 1914, the year construction of the 

dam was completed; the peak in 137Cs, dated as 1964, when 

137Cs fallout from atmospheric testing of nuclear weapons 

peaked; and the top of the core matched with the sampling date 

(fig. 5). Between each of these depth-date markers, MARs were 

used to assign dates on the basis of the mass of each sample and 

of the cumulative mass between the mid-point of the sample and 

a date marker. Mass was estimated by accurately weighing measured volumes of wet and dry sediment to determine bulk density and density of solids, each in grams per cubic centimeter.

Sedimentation rates in reservoirs commonly decrease 

over time as the shoreline gradually stabilizes. Callender and 

Robbins (1993) found that an exponentially decreasing model 

of MAR fit the pattern of decreasing sedimentation rates in 

48 of 83 reservoirs they studied. Sedimentation rates in all 

three Woods Inlet gravity cores decreased over time as indicated by comparison of MAR before and after the 137Cs peak in 

1964. An exponential model was applied to these three cores to 

assign deposition dates to samples following the approach of 

Van Metre and others (2004). Porosity, activity of 137Cs, MAR, 

and deposition dates are listed in appendix 1.1. 

Distribution and Sources of Polychlorinated 

Biphenyls in Woods Inlet

Detection frequencies for the 27 PCB congeners varied by 

the degree of chlorination and by sample type. In general, detection frequency increased with increasing degree of chlorination 

and was higher in surficial bottom sediment than in suspended 

and streambed sediment (fig. 6). Detection frequencies for PCB 

8, for example, with two chlorine atoms, were 20 and 8 percent 

for inlet and stream sediments, respectively. Average detection 

frequency for the heptachlorobiphenyls (seven chlorine atoms) 

were 100 and 78 percent for surficial bottom sediments and suspended and streambed sediments, respectively. 

Polychlorinated Biphenyls in Bottom Sediment

Total PCB concentrations in 20 samples of surficial bottom sediment from Woods Inlet ranged from 4.75 to 73.8 μg/kg 

(fig. 7; appendix 1.2). Total PCB concentrations were highest 

near the mouth of Meandering Road Creek and decreased 
Distribution and Sources of Polychlorinated Biphenyls in Woods Inlet 11

consistently toward the main lake. Total PCB concentrations at 

the mouth of the other two tributary streams, Gruggs Park Creek 

and TNG Creek, were lower than at the mouth of Meandering 

Road Creek and were similar to the surficial bottom sediment 

concentrations in the middle of Woods Inlet. The spatial distribution of surficial total PCB concentrations indicates that PCBs 

are originating in the Meandering Road Creek watershed.

Peak total PCB concentrations occurred in the 70–80-cm 

sample at WWD1, the 30–40-cm sample at WWD2, and the 50–

60-cm sample at WWD3 (fig. 8; appendix 1.2). These peak total 

PCB concentration depths correspond to about 1960 for WWD1 

and WWD3 and about 1980 for WWD2. PCB concentrations 

increased greatly from those of the early 1940s to the peaks in 

the three gravity cores. The magnitudes of peak total PCB concentrations in the gravity cores followed a spatial distribution 

generally similar to that of surficial bottom sediment concentrations (fig. 7). The highest concentration at WWD3 (349 μg/kg) 

was near the mouth of Meandering Road Creek (and at the 

mouth of TNG Creek), the next highest at WWD1 (128 μg/kg), 

near the confluence of the three tributary creeks, and the lowest 

peak concentration at WWD2 (47.6 μg/kg), near the mouth of 

Gruggs Park Creek. The 1960 peaks at WWD1 and WWD3 are 

Figure 6. Detection frequency by polychlorinated biphenyl (PCB) congener and sample type, Woods Inlet, Lake Worth, Fort Worth, 

Texas, 2003 (**PCB used in graphical and cluster analysis).

0 25 50 75 100 0 25 50 75 100

DETECTION FREQUENCY, IN PERCENT

PCB 8

PCB 18

PCB 22

PCB 26

PCB 28

PCB 31

PCB 33

PCB 44

PCB 49

**PCB 52

 PCB 70

 PCB 95

 PCB 101

**PCB 110

**PCB 118

 PCB 138

 PCB 146

 PCB 149 

**PCB 151

**PCB 170

 PCB 174

 PCB 177

 PCB 180

 PCB 183

**PCB 187

 PCB 194

PCB 206

PCB CONGENER

Surficial bottom sediment samples

Suspended and streambed 

sediment samples

Number of 

chlorine atoms

2

3

4

5

6

7

8

9
12 Distribution and Sources of Polychlorinated Biphenyls in Woods Inlet, Lake Worth, Fort Worth, Texas, 2003

Figure 7. Total polychlorinated biphenyl (PCB) concentrations (sum of PCB congeners) in surficial bottom sediment, Woods Inlet, Fort 

Worth, Texas, 2003.

97 ̊28' 97 ̊27'

32 ̊46'

32 ̊47'

Base modified from U.S. Geological Survey

Digital orthophoto quarter-quadrangle,

Universal Transverse Mercator projection, Zone 14,

Datum NAD 83, 1-foot resolution 0 0.25 0.5 MILE

0 0.5 KILOMETER

Sediment sampling

site and total PCB

concentration, in

micrograms

per kilogram

Box core (surficial)

Gravity core (surficial

20 subsample) .7

14.7

4.75

6.54

8.509.00

10.0

36.7

73.8

8.09

10.9

8.06

34.0

15.9 14.9

13.216.9

14.7

14.7 13.9

20.7

22.9

14.7

4.75

6.54

8.509.00

10.0

36.7

73.8

8.09

10.9

8.06

34.0

15.9 14.9

13.216.914.7

22.9

20.7

14.7 13.9

20.7 Air Force Air Force

Plant 4 Plant 4

Woods

Inlet

Meandering Meandering

Road Creek Road Creek

Texas National Texas National

Guard (TNG) facility Guard (TNG) facility Landfill 1 Landfill 1

Landfill 3 Landfill 3

Outfall 4 Outfall 4

Gruggs

Park Creek Park Creek

Air Force

Plant 4

Woods

Inlet

Meandering

Road Creek

Texas National

Guard (TNG) facility Landfill 1

Landfill 3

Outfall 4

Gruggs

Park Creek
Distribution and Sources of Polychlorinated Biphenyls in Woods Inlet 13

consistent in age with the peak in a gravity core from near the 

mouth of Woods Inlet collected in 2002 (Harwell and others, 

2003). 

PCB concentrations in surficial bottom sediment were 

much lower than peak concentrations. The surficial bottom sediment concentration of total PCB at WWD1, for example, is 

13.9 μg/kg, about one-ninth the peak concentration. Van Metre 

and others (1998) reported that PCB concentrations in reservoir 

sediment cores tended to follow an exponential decrease after 

they were banned, with a half-life of about 10 years. The halflife for total PCB (number of years to degrade to one-half the 

peak concentration) in the two cores with pronounced 1960 

peaks, estimated from a regression line fit to the natural logarithms of total PCB concentrations, was 10.2 years at WWD3 

and 14 years at WWD1. These rates were consistent with those 

in PCB concentrations in sediment cores nationally (Van Metre 

and others, 1998). 

PCBs were not detected in sediment deposited before the 

1940s from two of the three Woods Inlet cores (WWD1 and 

WWD2); however, some PCB congeners were detected at low 

(estimated) concentrations near the bottom of core WWD3 

(appendix 1.2). Commercial manufacturing of PCBs, which 

have no natural sources, began in 1929, and PCBs usually are 

not detected in cores of lake sediment deposited before the 

1940s (Van Metre and others, 1998). The bottom two samples 

from core WWD3, dated as 1917 and 1927, predate use of 

PCBs, which indicates either sample contamination or mixing 

of sediment containing PCBs in the core. Large, relatively narrow peaks in 137Cs activity and PCB concentrations and a high 

sedimentation rate in Lake Worth indicate that mixing extensive enough to move PCBs 30 to 50 cm down core is unlikely. 

Cross-contamination of samples is possible during collection 

and subsampling of a core by smearing of sediment along the 

inside walls of the core liner. Total PCB concentrations in the 

bottom three samples from core WWD3 (80–130 cm, 1938 and 

earlier) ranged from 0.77 to 1.91 μg/kg, about 200 times smaller 

than the peak concentration of 349 μg/kg dated as 1957 (fig. 8; 

appendix 1.2). Cross-contamination of the samples during subsampling was the likely cause of these low-level detections. 

This low-level contamination does not affect interpretations of 

the PCB data in the core. 

Polychlorinated Biphenyls in Suspended and 

Streambed Sediment

PCBs could reach Woods Inlet from several sources and 

by several pathways. Potential sources of PCBs include one of 

the historical landfills or historically contaminated soils on 

AFP4 and point or nonpoint sources in the surrounding urban 

area. Because PCBs are very hydrophobic, the primary pathway 

for them to enter urban creeks and lakes is erosion and fluvial 

transport attached to sediment. The most likely pathway for 

them to enter Woods Inlet is attached to suspended sediment 

transported by runoff during storms.

Total PCB concentrations in suspended and streambed 

sediment varied greatly among sites and indicated a likely 

source of PCBs associated with site OF4, which receives runoff 

from AFP4 (fig. 9; appendix 1.2). The three sites not influenced 

by AFP4 (GRUGGS, TNG, and UMRC) had five samples in 

which no PCB congeners were detected and 13 samples in 

which one or more congeners were detected; total PCB for those 

13 samples ranged from 0.54 to 14.8 μg/kg. In contrast, the 

Figure 8. Trends in total polychlorinated biphenyl (PCB) 

concentrations (sum of PCBcongeners) in sediment cores relative 

to (a) sediment depth and (b) date of sediment deposition, Woods 

Inlet, Lake Worth, Fort Worth, Texas, 2003.

WWD1

WWD2

WWD3

EXPLANATION

Gravity core site

(a)

(b)

1910

1920

1930

1940

1950

1960

1970

1980

1990

2000

2010

0 100 200 300 400

TOTAL PCB CONCENTRATION,

IN MICROGRAMS PER KILOGRAM

DATE

0

20

40

60

80

100

120

140

160

180

0 100 200 300 400

DEPTH, IN CENTIMETERS

TOTAL PCB CONCENTRATION,

IN MICROGRAMS PER KILOGRAM
14 Distribution and Sources of Polychlorinated Biphenyls in Woods Inlet, Lake Worth, Fort Worth, Texas, 2003

three suspended sediment samples from OF4 contained total 

PCB concentrations of 81.3, 99.2, and 166 μg/kg, with a mean 

of 116 μg/kg. The six samples from LMRC, influenced by flow 

at UMRC (no AFP4 runoff) and OF4 (AFP4 runoff), reflected 

intermediate concentrations that ranged from 17.8 to 103 μg/kg. 

One or more PCB congeners were detected in both 

media in eight of the 12 paired suspended and streambed 

sediment samples (fig. 9). Total PCB was greater for suspended 

sediment in seven of the eight pairs and the ratio of suspended to 

streambed sediment concentration ranged from 1.1 to 6.0, with 

a median of 2.0. Large concentrations in suspended sediment 

compared to those in streambed sediments could reflect finer 

grain size or higher organic carbon concentrations, or both.

The one sample where streambed sediment concentration 

was greater than suspended sediment concentration was the 

LMRC sample from August 30, 2003. Total PCB concentration 

was much less in the August 30 suspended sediment sample 

than in the two subsequent suspended sediment samples from 

this site. Differences in major element concentrations between 

this sample and the two subsequent samples, including higher 

calcium, lower organic carbon, and slightly lower aluminum 

and iron, indicate a different source of sediment for the August 

30 sample than the two subsequent samples. Grain size was not 

analyzed for the August 30 sample, but the differences in major 

element and contaminant concentrations could indicate a 

coarser, sandier material, possibly material mobilized from the 

bed of Meandering Road Creek. 

Source Identification Using Polychlorinated Biphenyl 

Congener Assemblages 

Three approaches were applied to identify sources of 

PCBs in surficial bottom sediment using congener assemblages: 

(1) graphical comparisons, (2) a simple measure of differences 

among congener patterns, and (3) cluster analysis. All samples 

deeper than 5 cm in the gravity cores, and suspended and 

streambed sediment samples with frequent nondetections were 

excluded from these analyses. Concentrations were first normalized by dividing by total PCB to convert each congener 

Figure 9. Total polychlorinated biphenyl (PCB) concentrations (sum of PCB congeners) in suspended and streambed sediment from 

tributary streams to Woods Inlet, Lake Worth, Fort Worth, Texas, 2003.

97 ̊28' 97 ̊27'

32 ̊46'

32 ̊47'

Base modified from U.S. Geological Survey

Digital orthophoto quarter-quadrangle,

Universal Transverse Mercator projection, Zone 14,

Datum NAD 1983, 1-foot resolution

0 0.25 0.5 MILE

0 0.5 KILOMETER

TNG

OF4

LMRC

GRUGGS

UMRC

 99.2

 81.3

166

17.8 (103)

 57.0 (47.5)

 44.5 (41.7) 12.6 (4.89)

14.8 (4.80)

 0 (2.28)

6.23 (1.03)

0 (0.54)

0 (0) 

 7.45 (4.58)

 4.48 (2.23)

 0 (1.10)

EXPLANATION

Sediment sampling

site and site

identifier—Site

identifier referenced

in table 1

Suspended sediment

(streambed sediment)—

Total PCB concentration,

in micrograms per

kilogram, for three

storms in order

earliest to latest;

see appendix 1.2

TNG

TNG

OF4

LMRC

GRUGGS

UMRC

TNG

12.6 (4.89)

Air Force Air Force

Plant 4 Plant 4

Woods

Inlet

Meandering Meandering

Road Creek Road Creek

Texas National Texas National

Guard (TNG) facility Guard (TNG) facility

Landfill 1 Landfill 1 Landfill 3 Landfill 3

Outfall 4 Outfall 4

Gruggs

Park Creek Park Creek

Air Force

Plant 4

Woods

Inlet

Meandering

Road Creek

Texas National

Guard (TNG) facility

Landfill 1 Landfill 3

Outfall 4

Gruggs

Park Creek
Distribution and Sources of Polychlorinated Biphenyls in Woods Inlet 15

concentration to a fraction of total PCBs. The assumption in 

these analyses is that the relative concentrations of congeners in 

a sediment sample in the inlet are not changed appreciably 

during transport and deposition from distinct sources, except 

by mixing, This assumption implies that processes such as 

degradation and desorption of selected congeners do not greatly 

alter relative concentrations. Source areas of PCBs that potentially could be identified through interpretation of data collected 

in this study are urban areas west of AFP4, the Texas National 

Guard facility, the part of AFP4 that contributes runoff to OF4, 

and AFP4 (by comparison of UMRC and LMRC results). 

The first approach to identify sources of PCBs to Woods 

Inlet involved graphical analysis of normalized concentrations 

of six selected congeners. Six congeners were selected that were 

detected frequently, covered a range in the level of chlorination, 

were at relatively high concentrations, and varied between 

samples from different sites. The lines representing normalized 

sample concentrations of the six congeners from areas of 

Woods Inlet and from tributary stream sites (fig. 10) generally 

form similar patterns within sample groups (within graphs). 

Some patterns on suspended and streambed sediment graphs 

(column 2 in fig. 10), which represent potential sources, are 

similar to patterns on surficial bottom sediment graphs (column 

1 in fig. 10). Normalized congener concentration patterns for 

suspended and streambed sediment samples from LMRC are 

similar to patterns for surficial sediment in the Meandering 

Road Creek arm of Woods Inlet and the middle of Woods Inlet. 

Patterns for two of the three samples from OF4 also are similar 

to those for samples from the Meandering Road Creek arm and 

middle of Woods Inlet. The TNG sample patterns are variable 

and distinctly different from any of the patterns of the surficial 

sediment samples in the inlet, with roughly increasing proportions of congeners with increasing chlorination. The GRUGGS 

and UMRC (urban reference) sample patterns also are variable 

and show some similarity to sample patterns of the Gruggs arm 

of Woods Inlet and to some sample patterns from the middle of 

Woods Inlet. The clearest visual match between a potential 

source, as indicated by suspended and streambed sediment 

graphs, and PCBs in Woods Inlet, as indicated by surficial 

bottom sediment graphs, is that between site LMRC and the 

Meandering Road Creek arm of Woods Inlet. A close second 

in terms of visual match is that between LMRC and the middle 

of Woods Inlet and that between OF4 (two of four samples) 

and the Meandering Road Creek arm and middle of Woods 

Inlet. 

The second approach to identify sources using congener 

assemblages, the measure of differences among congener patterns, was the root mean squared difference (RMSD) between 

normalized concentrations of the 17 most frequently detected 

congeners. Normalized concentrations of each of the suspended 

and streambed sediment samples (representing potential 

sources) were compared to the mean of all surficial bottom 

sediment sample concentrations (representing the end-point of 

interest). The RMSD is computed as the square root of the sum 

of squared differences between the normalized concentrations; 

the smaller it is, the more similar the data are. The LMRC suspended and streambed sediment samples, and two of the three 

OF4 samples, are more similar to the Woods Inlet surficial 

bottom sediment samples than samples from the other tributary 

sites (table 4), possibly indicating a common source. 

The third approach to source identification, cluster analysis (Davis, 2002), was carried out using the six congeners that 

were used for the graphical analysis. Cluster analysis involves 

grouping samples on the basis of similarity of a response variable or variables, which, as in the graphical analysis (fig. 10), 

was the ratio of individual PCB congeners to total PCB. Six 

clusters were indicated on the basis of interpretation of the data, 

the distribution of which is shown in figure 11. Cluster 1 contains middle of Woods Inlet and Meandering Road Creek arm 

samples (most surficial bottom sediment), three of four samples 

from LMRC, and two of three samples from OF4. None of the 

other tributary samples were grouped in this cluster. Cluster 2 

comprises three samples from Woods Inlet that were not in the 

probable path of discharge from Meandering Road Creek and 

two samples from the urban reference sites GRUGGS and 

UMRC. Cluster 3 accounts for the Gruggs arm of Woods Inlet 

samples, along with one sample each from the urban reference 

Table 4. Root mean squared difference (RMSD), from smallest to 

largest, between normalized concentrations of 17 polychlorinated 

biphenyl congeners in suspended and streambed sediment 

samples in tributaries and mean of all surficial bottom sediment 

sample concentrations of those congeners in Woods Inlet, Lake 

Worth, Fort Worth, Texas, 2003. 

Suspended or

streambed

sediment site

(fig. 2)

Sample

date

Sample

type RMSD

LMRC 8/30/2003 Suspended 0.046

LMRC 8/31/2003 Streambed .065

OF4 9/11/2003 Suspended .073

OF4 8/30/2003 Suspended .076

LMRC 9/16/2003 Streambed .095

LMRC 10/6/2003 Streambed .098

GRUGGS 8/31/2003 Streambed .110

UMRC 8/30/2003 Suspended .125

OF4 10/5/2003 Suspended .131

UMRC 8/31/2003 Streambed .140

TNG 8/31/2003 Streambed .141

GRUGGS 8/30/2003 Suspended .145

TNG 9/11/2003 Suspended .170

TNG 8/30/2003 Suspended .200

TNG 9/16/2003 Streambed .236
Figure 10. Selected polychlorinated biphenyl (PCB) congener assemblages normalized (divided) by total PCB (sum of PCB congeners) for surficial boWoods inlet and suspended and streambed sediment in tributary streams to Woods Inlet, Lake Worth, Texas, 2003.

RATIO OF INDIVIDUAL PCB CONGENER TO TOTAL PCB

PCB CONGENER

PCB CONGENER

RATIO OF INDIVIDUAL PCB CONGENER TO TOTAL PCB

(See figure 2 for location of sites. See table 2 for names of PCBcongeners identified here by number. Data are in appendix 1.2)

Suspended and streambed sediment

in tributary stream sites

Site OF4

Site LMRC

Sites GRUGGS and UMRC

Site TNG

Surficial bottom sediment

in areas of Woods Inlet

Middle of Woods Inlet

Meandering Road Creek

arm of Woods Inlet

Gruggs arm of Woods Inlet

00.040.08

0.120.16

00.040.08

0.120.16

00.040.08

0.120.16

00.040.08

0.120.16

00.040.08

0.120.16

00.040.08

0.120.16

00.040.08

0.120.16

PCB

52

PCB

110

PCB 

118

PCB

151

PCB

170

PCB

187

PCB

52

PCB

110

PCB 

118

PCB

151

PCB

170

PCB

187

Symbols and corresponding samples

EXPLANATION

WWD1.1WWD.B3WWD.B9WWD.B10WWD.B11WWD.B12WWD.B13WWD.B14WWD.B15WWD.B16WWD.B17

WWD3.1WWD.B6WWD.B7WWD.B8

Symbols and corresponding samples

EXPLANATION

WWD2.1WWD.B1WWD.B2

Symbols and corresponding samples

EXPLANATION

SuSuSu

Syco

EXPLANA

SSSS

Syco

EXPLANA

USSGSS

Sc

EXPLANA

SSSS

Sc

EXPLANA
Summary 17

sites GRUGGS and UMRC. Cluster 4 contains no inlet samples, 

only one sample each from OF4, LMRC, and TNG. Cluster 5 

consists of a single TNG sample, and cluster 6 comprises two 

TNG samples. The four samples from site TNG are in three 

different clusters, which indicates the most variability among 

tributary sites and inlet areas. 

The three approaches to the analyses of congener assemblages indicate that PCBs in surficial bottom sediment of 

Woods Inlet primarily enter Lake Worth from Meandering 

Road Creek and that runoff from AFP4 is a source of the PCBs 

in Meandering Road Creek. Although current (2003) transport 

of PCBs from AFP4 to the creek is occurring, as OF4 sample 

analyses indicate, the large decreases in PCB concentrations 

with decreasing depth in cores WWD1 and WWD3 (fig. 8) are 

evidence that PCB loading to the inlet has decreased greatly 

since the 1960s. Because runoff entering Meandering Road 

Creek from some parts of AFP4 was not measured or sampled 

in this study, it cannot be said with certainty that site OF4 is the 

only source of PCBs to Meandering Road Creek.

Summary

In response to the finding in a previous study of elevated 

polychlorinated biphenyl (PCB) concentrations in sediment in 

Woods Inlet, a feature on the southern shore of Lake Worth 

along the western boundary of Air Force Plant 4 (AFP4) in Fort 

Worth, Tex., the U.S. Geological Survey, in cooperation with 

the U.S. Air Force, conducted a study in 2003 to map the distribution of elevated PCB concentrations in Woods Inlet and to 

identify possible sources (or more specifically, source areas) of 

PCBs in the watershed of Woods Inlet. Gravity cores (penetration to pre-reservoir sediment at three sites) and surficial bottom 

sediment samples (top 5 cm at 20 sites) were collected and analyzed to map the distribution of PCB concentrations in Woods 

Inlet. Suspended sediment in stormwater runoff and streambed 

sediment were sampled in tributaries to Woods Inlet following 

storms to identify possible current (2003) sources of PCBs. In 

addition, assemblages of PCB congeners in surficial bottom 

sediments and suspended and streambed sediments were 

analyzed to indicate sources of PCBs in the surficial bottom 

Figure 11. Results of cluster analysis using selected polychlorinated biphenyl (PCB) congeners, Woods Inlet and tributaries, Lake 

Worth, Fort Worth, Texas, 2003.

97 ̊28' 97 ̊27'

32 ̊46'

32 ̊47'

Base modified from U.S. Geological Survey

Digital orthophoto quarter-quadrangle,

Universal Transverse Mercator projection, Zone 14,

Datum NAD 83, 1-foot resolution

0 0.25 0.5 MILE

0 0.5 KILOMETER

Cluster 1

Cluster 2

Cluster 3

Cluster 4

Cluster 5

Cluster 6

EXPLANATION

Air Force Air Force

Plant 4 Plant 4

Woods

Inlet

Meandering Meandering

Road Creek Road Creek

Texas National Texas National

Guard (TNG) facility Guard (TNG) facility

Landfill 3 Landfill 3 Landfill 1 Landfill 1

Outfall 4 Outfall 4

Gruggs

Park Creek Park Creek

Air Force

Plant 4

Woods

Inlet

Meandering

Road Creek

Texas National

Guard (TNG) facility

Landfill 3 Landfill 1

Outfall 4

Gruggs

Park Creek
18 Distribution and Sources of Polychlorinated Biphenyls in Woods Inlet, Lake Worth, Fort Worth, Texas, 2003

sediments on the basis of chemical signatures of PCBs. Sediment samples also were analyzed for major and trace elements, 

selected PAHs, and selected organochlorine pesticides. 

Woods Inlet receives runoff primarily from three tributaries: (1) Gruggs Park Creek, (2) the small unnamed creek that 

drains a Texas National Guard maintenance facility, called 

TNG Creek for this report, and (3) Meandering Road Creek. 

Three stormwater sampling sites were established near the 

mouths of each of these three creeks (GRUGGS, TNG, LMRC, 

respectively). GRUGGS and TNG receive urban runoff but not 

runoff from AFP4; LMRC receives urban runoff from AFP4 

and other areas. A fourth site (OF4) along Meandering Road 

Creek upstream from LMRC receives runoff exclusively from 

AFP4. A fifth site (UMRC) is on Meandering Road Creek 

upstream from AFP4 but downstream from urban areas; thus it 

receives urban runoff but none from AFP4. Suspended sediment samples were collected during three storms at each of the 

five sites. Streambed sediment samples were collected at all of 

the sites except OF4 following each of the three storms in which 

suspended sediment samples were collected. 

Twenty-seven of 209 possible PCB congeners were analyzed. The sum of the congeners was used as a measure of total 

PCB. Total PCB concentrations in 20 samples of surficial sediment from Woods Inlet ranged from 4.75 to 73.8 μg/kg. Total 

PCB concentrations were highest near the mouth of Meandering Road Creek and decreased consistently toward Lake Worth. 

Total PCB concentrations at the mouth of the other two tributary streams, Gruggs Park Creek and TNG Creek, were lower 

than at the mouth of Meandering Road Creek and were similar 

to the surficial bottom sediment concentrations in the middle of 

Woods Inlet. The spatial distribution of surficial total PCB concentrations indicates that PCBs are originating in the Meandering Road Creek watershed.

Peak total PCB concentrations in the three gravity cores 

occurred at depths corresponding to sediment deposition dates 

of about 1960 for two of the cores and about 1980 for the third 

core. The magnitudes of peak total PCB concentrations in the 

gravity cores followed a spatial distribution generally similar to 

that of surficial sediment concentrations. The highest concentration at WWD3 (349 μg/kg) was near the mouth of Meandering Road Creek (and at the mouth of TNG Creek), the next 

highest at WWD1 (128 μg/kg), near the confluence of the three 

tributary creeks, and the lowest peak concentration at WWD2 

(47.6 μg/kg), near the mouth of Gruggs Park Creek. 

Total PCB concentrations in suspended and streambed 

sediment varied greatly among sites and indicated a likely 

source of PCBs associated with site OF4, which receives runoff 

from AFP4. The three sites not influenced by AFP4 (GRUGGS, 

TNG, and UMRC) had five samples in which no PCB congeners were detected and 13 samples in which one or more congeners were detected; total PCB concentration for those 13 samples ranged from 0.54 to 14.8 μg/kg. In contrast, the three 

suspended sediment samples from OF4 contained total PCB 

concentrations of 81.3, 99.2, and 166 μg/kg, with a mean of 

116 μg/kg. The six samples from LMRC, influenced by flow at 

UMRC (no AFP4 runoff) and OF4 and other stormwater outfalls from AFP4 (AFP4 runoff), reflected intermediate concentrations that ranged from 17.8 to 103 μg/kg. 

Three approaches to the analyses of congener assemblages—graphical comparisons of normalized congener 

concentrations for pattern similarity, a simple measure of difference among congener patterns (root mean squared difference 

between normalized congener concentrations), and cluster analysis—indicate that PCBs in surficial sediment of Woods Inlet 

primarily enter Lake Worth from Meandering Road Creek and 

that runoff from AFP4 is a source of the PCBs in Meandering 

Road Creek. Although current (2003) transport of PCBs from 

AFP4 to the creek is occurring as OF4 sample analyses indicate, 

large decreases in PCB concentrations with decreasing depth in 

cores WWD3 and WWD1 are evidence that PCB loading to the 

inlet has decreased greatly since the 1960s. Because runoff 

entering Meandering Road Creek from some parts of AFP4 

was not measured or sampled in this study, it cannot be said 

with certainty that site OF4 is the only source of PCBs to 

Meandering Road Creek.

Trace element, PAH, and organochlorine pesticide concentration data from this study are included in the report. However, the data are insufficient to describe the distribution and 

sources of those constituents in Woods Inlet sediment.

References

Arbogast, B.F., ed., 1996, Analytical methods manual for the 

Mineral Resources Surveys Program: U.S. Geological 

Survey Open-File Report 96–525, 248 p. 

Briggs, P.H., and Meier, A.L., 2003, The determination of 

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coupled plasma-mass spectrometry, in Taggart, J.E., Jr., ed., 

Analytical methods for chemical analysis of geologic and 

other materials: U.S. Geological Survey Open-File Report 

02–223, chap. I, 14 p. 

Cacela, Dave, Beltman, D.J., and Lipton, Joshua, 2002, 

Polychlorinated biphenyl source attribution in Green Bay, 

Wisconsin, USA, using multivariate similarity among congener profiles in sediment samples: Environmental Toxicology 

and Chemistry, v. 21, no. 8, p. 1,591–1,599.

Callender, Edward, and Robbins, J.A., 1993, Transport and 

accumulation of radionuclides and stable elements in a 

Missouri River reservoir: Water Resources Research, v. 29, 

no. 6, p. 1,787–1,804.

Colman, J.A., 2000, Source identification and fish exposure 

for polychlorinated biphenyls using congener analysis 

from passive water samplers in the Millers River Basin, 

Massachusetts: U.S. Geological Survey Water-Resources 

Investigations Report 00–4250, 44 p.

Davis, J.C., 2002, Statistics and data analysis in geology 

(3d ed.): Wiley, New York, 638 p.
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Harwell, G.R., Van Metre, P.C., Wilson, J.T., and Mahler, B.J., 

2003, Spatial distribution and trends in trace elements, 

polycyclic aromatic hydrocarbons, organochlorine pesticides, and polychlorinated biphenyls in Lake Worth sediment, Fort Worth, Texas: U.S. Geological Survey WaterResources Investigations Report 03–4269, 56 p.

Johnson, G.W., Jarman, W.M., Bacon, C.E., Davis, J.A., 

Ehrlich, Robert, and Risebrough, R.W., 2000, Resolving 

polychlorinated biphenyl source fingerprints in suspended 

particulate matter of San Francisco Bay: Environmental 

Science and Technology, v. 34, no. 4, p. 552–559.

Mahler, B.J., and Van Metre, P.C., 2003, A simplified approach 

for monitoring hydrophobic organic contaminants associated 

with suspended sediments—Methodology and applications: 

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v. 44, no. 3, p. 288–297.

Moring, J.B., 2002, Data on occurrence of selected trace metals, 

organochlorines, and semivolatile organic compounds in 

edible fish tissues from Lake Worth, Fort Worth, Texas, 

1999: U.S. Geological Survey Open-File Report 02–016, 

23 p.

Noriega, M.C., Wydoski, D.S., and Foreman, W.T., 2003, 

Methods of analysis by the U.S. Geological Survey National 

Water Quality Laboratory—Determination of organochlorine pesticides and polychlorinated biphenyls in bottom and 

suspended sediment by gas chromatography with electroncapture detection: U.S. Geological Survey Water-Resources 

Investigations Report 03–4293, 46 p.

Olson, M.C., Iverson, J.L., Furlong, E.T., and Schroeder, M.P., 

2004, Methods of analysis by the U.S. Geological Survey 

National Water Quality Laboratory—Determination of polycyclic aromatic hydrocarbon compounds in sediment by gas 

chromatography/mass spectrometry: U.S. Geological Survey 

Water-Resources Investigations Report 03–4318, 45 p.

Robbins, J.A., and Edgington, D.N., 1976, Determination of 

recent sedimentation rates in Lake Michigan using 210Pb 

and 137Cs: Geochimica et Cosmochimica Acta, v. 39, 

p. 285–304.

Shelton, L.R., and Capel, P.D., 1994, Guidelines for collecting 

and processing samples of stream bed sediment for analysis 

of trace element and organic contaminants for the National 

Water-Quality Assessment Program: U.S. Geological Survey 

Open-File Report 94–0458, 20 p.

Texas Department of Health, 2004, Fish consumption advisories and bans: accessed March 9, 2004, at 

http://www.tdh.state.tx.us/bfds/ssd

Van Metre, P.C., Wilson, J.T., Callender, Edward, and Fuller, 

C.C., 1998, Similar rates of decrease of persistent, hydrophobic and particle-reactive contaminants in riverine systems: 

Environmental Science and Technology, v. 32, no. 21, 

p. 3,312–3,317.

Van Metre, P.C., Wilson, J.T., Fuller, C.C., Callender, Edward, 

and Mahler, B.J., 2004, Collection, analysis, and age-dating 

of sediment cores from 56 U.S. lakes and reservoirs sampled 

by the U.S. Geological Survey, 1992–2001: U.S. Geological 

Survey Scientific Investigations Report 2004–5184, 180 p.
20 Distribution and Sources of Polychlorinated Biphenyls in Woods Inlet, Lake Worth, Fort Worth, Texas, 2003

Blank Page
Appendix 1—Core-Specific and Analytical 

Polychlorinated Biphenyl Data From Core, 

Surficial Bottom, Suspended, and Streambed 

Sediment Samples, Woods Inlet and Tributaries, 

Lake Worth, Fort Worth, Texas
22

Blank Page
Appendix 1 23

Appendix 1

Appendix 1.1. Porosity, cesium-137 (137Cs) activity, mass accumulation rate (MAR), and deposition dates for gravity core samples, 

Woods Inlet, Lake Worth, Fort Worth, Texas, 2003. 

[cm, centimeter; pCi/g, picocurries per gram; --, not analyzed] 

Core site and

depth interval

(cm)

Middepth

(cm)

Thickness

(cm) Porosity

137Cs

activity

(pCi/g)

MAR

Deposition

date

(year)

Comments

WWD1 (0–5) 2.5 5 0.87 0.16 0.62 2002

WWD1( 5–10) 7.5 5 .79 .19 .64 1999

WWD1 (10–20) 12.5 10 .81 .19 .68 1994

WWD1 (20–30) 25 10 .80 .22 .72 1988

WWD1 (30–40) 35 10 .79 .33 .76 1982

WWD1 (40–50) 45 10 .77 .45 .81 1976

WWD1 (50–60) 55 10 .77 .73 .86 1970

WWD1 (60–70) 65 10 .78 1.36 .92 1964 137Cs peak

WWD1 (70–80) 75 10 .76 .74 .97 1959

WWD1 (80–90) 85 10 .75 .13 1.03 1953

WWD1 (90–100) 95 10 .75 .02 1.08 1948

WWD1 (100–110) 105 10 .73 .01 1.15 1942

WWD1 (110–120) 115 10 .75 -.02 1.21 1937

WWD1 (120–130) 125 10 .76 -.01 1.26 1933

WWD1 (130–140) 135 10 .77 0 1.33 1928

WWD1 (140–150) 145 10 .79 .01 1.38 1924

WWD1 (150–160) 155 10 .75 -.01 1.44 1920

WWD1 (160–166) 163 6 .63 -- 1.50 1916 Pre-reservoir surface at 160 cm (1914)

WWD2 (0–5) 2.5 5 .79 .12 .74 2002

WWD2 (5–10) 7.5 5 .80 .18 .77 1999

WWD2 (10–20) 15 10 .80 .20 .82 1994

WWD2 (20–30) 25 10 .75 .23 .88 1988

WWD2 (30–40) 35 10 .75 .34 .95 1982

WWD2 (40–50) 45 10 .71 .32 1.03 1976

WWD2 (50–60) 55 10 .73 .57 1.12 1969

WWD2 (60–70) 65 10 .74 1.04 1.19 1964 137Cs peak

WWD2 (70–80) 75 10 .73 1.01 1.27 1959

WWD2 (80–90) 85 10 .70 .41 1.35 1954

WWD2 (90–100) 95 10 .72 .04 1.43 1949

WWD2 (100–110) 105 10 .71 .02 1.53 1944

WWD2 (110–120) 115 10 .74 .01 1.60 1940

WWD2 (120–130) 125 10 .71 .02 1.69 1936

WWD2 (130–140) 135 10 .71 0 1.77 1932

WWD2 (140–150) 145 10 .75 -.03 1.84 1929

WWD2 (150–160) 155 10 .75 0 1.91 1926

WWD2 (160–170) 165 10 .74 -.01 1.98 1923

WWD2 170–180) 175 10 .76 -- 2.08 1919

WWD2 (180–190) 185 10 .70 .01 2.13 1917 Did not penetrate to pre-reservoir surface (1914)

WWD3 (0–5) 2.5 5 .76 .09 .67 2001

WWD3 (5–10) 7.5 5 .65 -- .71 1996

WWD3 (10–20) 15 10 .70 .09 .76 1988

WWD3 (20–30) 25 10 .71 .23 .83 1979

WWD3 (30–40) 35 10 .71 .37 .90 1971

WWD3 (40–50) 45 10 .69 .80 .97 1964 137Cs peak

WWD3 (50–60) 55 10 .68 .65 1.03 1957

WWD3 (60–70) 65 10 .73 .04 1.11 1950

WWD3 (70–80) 75 10 .69 .01 1.17 1944

WWD3 (80–90) 85 10 .68 -.01 1.25 1938

WWD3 (90–100) 95 10 .70 -- 1.32 1932

WWD3 (100–110) 105 10 .69 .01 1.39 1927

WWD3 (110–120) 115 10 .75 -- 1.46 1922

WWD3 (120–130) 125 10 .61 -.01 1.53 1917 Possible pre-reservoir surface at 124 cm
24

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 

Sample identifier and

depth interval

(cm)

Sample

type

Minimum 

depth

(cm)

Maximum 

depth

(cm)

Middepth

(cm)

Sample

date

Sample

used

in cluster

analysis

Aroclor

1242

Aroclor

1254

Aroclor

1260

Total

PCB

Aroclors

Gravity cores

WWD1 (0–5) core (surficial) 0 5 2.5 4/21/2003 Yes <15 E13 E9.2 E22

WWD1 (10–20) core 10 20 15 4/21/2003 E5.9 E24 17 E47

WWD1 (30–40) core 30 40 35 4/21/2003 E4.4 E13 E10 E27

WWD1 (50–60) core 50 60 55 4/21/2003 22 E45 21 E88

WWD1 (70–80) core 70 80 75 4/21/2003 E6.4 E110 E110 E226

WWD1 (80–90) core 80 90 85 4/21/2003 <5.0 E64 29 E93

WWD1 (90–100) core 90 100 95 4/21/2003 <5.0 E20 E3.3 E23

WWD1 (100–110) core 100 110 105 4/21/2003 <5.0 <5.0 <5.0 <15

WWD1 (120–130) core 120 130 125 4/21/2003 <5.0 <5.0 <5.0 <15

WWD1 (140–150) core 140 150 145 4/21/2003 <5.0 <5.0 <5.0 <15

WWD1 (160–166) core 160 166 163 4/21/2003 <5.0 <5.0 <5.0 <15

WWD1 (160–166) dup core 160 166 163 4/21/2003 <5.0 <5.0 <5.0 <15

WWD2 (0–5) core (surficial) 0 5 2.5 4/21/2003 Yes <5.0 E8.0 E14 E22

WWD2 (10–20) core 10 20 15.0 4/21/2003 <5.0 E7.0 E13 E20

WWD2 (30–40) core 30 40 35.0 4/21/2003 E11 E22 52 E85

WWD2 (50–60) core 50 60 55.0 4/21/2003 <11 18 17 E35

WWD2 (70–80) core 70 80 75.0 4/21/2003 <5.0 E12 19 E31

WWD2 (70–80) dup core 70 80 75.0 4/21/2003 <5.0 E12 17 E29

WWD2 (100–110) core 100 110 105.0 4/21/2003 <5.0 E2.8 E1.6 E4.4

WWD2 (100–110) dup core 100 110 105.0 4/21/2003 <5.0 E3.3 E1.4 E4.7

WWD2 (130–140) core 130 140 135.0 4/21/2003 <5.0 <5.0 <5.0 <15

WWD2 (160–170) core 160 170 165.0 4/21/2003 <5.0 <5.0 <5.0 <15

WWD3 (0–5) core (surficial) 0 5 2.5 4/21/2003 Yes <5.0 E20 13 E33

WWD3 (10–20) core 10 20 15.0 4/21/2003 E4.6 E28 23 E56

WWD3 (20–30) core 20 30 25.0 4/21/2003 18 E110 54 E182

WWD3 (30–40) core 30 40 35.0 4/21/2003 42 E110 54 E206

WWD3 (40–50) core 40 50 45.0 4/21/2003 83 260 130 473

WWD3 (50–60) core 50 60 55.0 4/21/2003 13 380 260 653

WWD3 (60–70) core 60 70 65.0 4/21/2003 E5.6 290 83 E379

WWD3 (70–80) core 70 80 75.0 4/21/2003 <5.0 E7.5 E3.9 E11

WWD3 (80–90) core 80 90 85.0 4/21/2003 <5.0 E2.2 E1.6 E3.8

WWD3 (100–110) core 100 110 105.0 4/21/2003 <5.0 <5.0 <5.0 <15

WWD3 (120–130) core 120 130 125.0 4/21/2003 <5.0 <5.0 <5.0 <15

WWD3 (120–130) dup core 120 130 125.0 4/21/2003 <5.0 <5.0 <5.0 <15

Box cores

WWD.B1 (0–5) surficial 0 5 2.5 4/22/2003 Yes E4.1 E7.9 18 E30

WWD.B2 (0–5) surficial 0 5 2.5 4/22/2003 Yes E4.3 E7.2 12 E24

WWD.B2 (0–5) dup surficial 0 5 2.5 4/22/2003 E5.6 E9.5 16 E31

WWD.B3 (0–5) surficial 0 5 2.5 4/22/2003 Yes <15 E6.1 E7.9 E14

WWD.B4 (0–5) surficial 0 5 2.5 4/22/2003 Yes <10 E6.8 E9.5 E16

WWD.B5 (0–5) surficial 0 5 2.5 4/22/2003 Yes <10 E11 E8.9 E20

WWD.B6 (0–5) surficial 0 5 2.5 4/22/2003 Yes E7.4 E60 49 E116

WWD.B7 (0–5) surficial 0 5 2.5 4/22/2003 Yes E8.0 34 23 E65

WWD.B8 (0–5) surficial 0 5 2.5 4/22/2003 Yes <10 21 E15 E36

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003. 

[Concentrations in micrograms per kilogram; cm, centimeters; <, nondetection at indicated concentration; E, estimated; dup, duplicate; na, not applicable; env 

dup, environmental duplicate; lab dup, laboratory duplicate]
Appendix 1 25

WWD.B9 (0–5) surficial 0 5 2.5 4/22/2003 Yes E6.2 32 21 E59

WWD.B10 (0–5) surficial 0 5 2.5 4/22/2003 Yes <5.0 13 10 E23

WWD.B11 (0–5) surficial 0 5 2.5 4/22/2003 Yes <10 E15 E12 E27

WWD.B12 (0–5) surficial 0 5 2.5 4/22/2003 Yes <5.0 E12 E9.3 E21

WWD.B13 (0–5) surficial 0 5 2.5 4/22/2003 Yes <10 E8.0 E5.9 E14

WWD.B14 (0–5) surficial 0 5 2.5 4/22/2003 Yes <5.0 E8.7 E6.7 E15

WWD.B15 (0–5) surficial 0 5 2.5 4/22/2003 Yes <5.0 E7.7 E7.4 E15

WWD.B16 (0–5) surficial 0 5 2.5 4/22/2003 Yes <10 E6.3 E6.4 E13

WWD.B17 (0–5) surficial 0 5 2.5 4/22/2003 Yes <5.0 E4.6 E4.4 E9.0

Suspended and streambed sediment

UMRC suspended na na na 8/30/2003 Yes <40 <40 <40 <120

UMRC streambed na na na 8/31/2003 Yes <5.0 <5.0 <5.0 <15

UMRC suspended na na na 9/11/2003 <105 <105 <105 <315

UMRC streambed na na na 9/16/2003 <5.0 <5.0 <5.0 <15

UMRC env dup streambed na na na 9/16/2003 <5.0 <5.0 <5.0 <15

UMRC suspended na na na 10/5/2003 <25 <25 <25 <75

UMRC streambed na na na 10/6/2003 <5.0 <5.0 <5.0 <15

GRUGGS suspended na na na 8/30/2003 Yes <70 <70 <70 <210

GRUGGS streambed na na na 8/31/2003 Yes <5.0 <5.0 E5.4 E5.4

GRUGGS lab dup streambed na na na 8/31/2003 <5.0 <5.0 E5.3 E5.3

GRUGGS suspended na na na 9/11/2003 <40 <40 E17 E17

GRUGGS streambed na na na 9/16/2003 <10 <10 <10 <30

GRUGGS env dup streambed na na na 9/16/2003 <5.0 <5.0 E6.4 E6.4

GRUGGS suspended na na na 10/5/2003 <25 <25 <25 <75

GRUGGS streambed na na na 10/6/2003 <5.0 <5.0 E3.2 E3.2

TNG suspended na na na 8/30/2003 Yes <50 <50 E20 E20

TNG streambed na na na 8/31/2003 Yes <5.0 E3.0 E7.6 E10.6

TNG suspended na na na 9/11/2003 Yes <60 <60 E17 E17

TNG streambed na na na 9/16/2003 Yes <5.0 <5.0 E10 E10

TNG suspended na na na 10/5/2003 <65 <65 <65 <195

TNG streambed na na na 10/6/2003 <5.0 E2.4 7.7 E10.1

OF4 suspended na na na 8/30/2003 Yes <45 88 92 E180

OF4 suspended na na na 9/11/2003 Yes <20 E77 E77 E154

OF4 suspended na na na 10/5/2003 Yes <75 216 280 E496

LMRC suspended na na na 8/30/2003 Yes <20 E18 E11 E29

LMRC streambed na na na 8/31/2003 Yes E4.3 92 50 E146

LMRC lab dup streambed na na na 8/31/2003 E1.7 45 35 E81.7

LMRC suspended na na na 9/11/2003 E57 E81 E170 E308

LMRC streambed na na na 9/16/2003 Yes <5.0 40 39 E79

LMRC env dup streambed na na na 9/16/2003 <5.0 45 45 E90

LMRC suspended na na na 10/5/2003 <25 47.8 38.6 E86.4

LMRC env dup suspended na na na 10/5/2003 <50 99 90 E189

LMRC streambed na na na 10/6/2003 Yes <20 52 33 E85

LMRC lab dup streambed na na na 10/6/2003 <10 52 34 E86

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 

Sample identifier and

depth interval

(cm)

Sample

type

Minimum 

depth

(cm)

Maximum 

depth

(cm)

Middepth

(cm)

Sample

date

Sample

used

in cluster

analysis

Aroclor

1242

Aroclor

1254

Aroclor

1260

Total

PCB

Aroclors
26

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 

Sample identifier and

depth interval

(cm)

Date

Sample used

in cluster

analysis

PCB 8 PCB 18 PCB 22 PCB 26 PCB 28 PCB 31 PCB 33 PCB 44

Gravity cores

WWD1 (0–5) 4/21/2003 Yes <3.0 <3.0 <3.0 <3.0 E0.18 E0.23 E0.21 E0.19

WWD1 (10–20) 4/21/2003 E.075 E.19 E.090 E.078 E.46 E.36 E.33 E.43

WWD1 (30–40) 4/21/2003 <1.0 <1.0 <1.0 <1.0 E.20 E.15 E.39 E.20

WWD1 (50–60) 4/21/2003 E.47 E.91 E.11 <1.0 1.4 1.3 1.5 1.5

WWD1 (70–80) 4/21/2003 <1.0 <1.0 <1.0 <1.0 E.23 E.47 E.61 1.2

WWD1 (80–90) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.55 E.94

WWD1 (90–100) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.25 E.30

WWD1 (100–110) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD1 (120–130) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD1 (140–150) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD1 (160–166) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD1 (160–166) dup 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD2 (0–5) 4/21/2003 Yes <1.0 <1.0 <1.0 <1.0 E.31 E.32 E.14 E.26

WWD2 (10–20) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.14

WWD2 (30–40) 4/21/2003 <1.0 <1.0 <1.0 <1.0 E.34 E.17 <1.0 E.40

WWD2 (50–60) 4/21/2003 <1.0 <1.0 <1.0 <1.0 E.40 E.33 E.62 E.46

WWD2 (70–80) 4/21/2003 <1.0 <1.0 <1.0 <1.0 E.11 E.10 E.021 E.16

WWD2 (70–80) dup 4/21/2003 <1.0 <1.0 <1.0 <1.0 E.90 E.11 E.0068 E.14

WWD2 (100–110) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 E.16 E.015 E.033

WWD2 (100–110) dup 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 E.18 E.015 E.039

WWD2 (130–140) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD2 (160–170) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD3 (0–5) 4/21/2003 Yes <1.0 <1.0 <1.0 <1.0 E.23 E.18 <1.0 E.25

WWD3 (10–20) 4/21/2003 <1.0 <1.0 <1.0 <1.0 E.30 E.28 E.71 E.44

WWD3 (20–30) 4/21/2003 E.74 E1.4 E.63 E.35 1.9 2.0 1.8 2.7

WWD3 (30–40) 4/21/2003 E.73 E1.8 E.75 <1.0 3.3 2.4 1.8 3.3

WWD3 (40–50) 4/21/2003 1.2 E5.3 2.2 E.99 7.0 7.0 E3.8 7.1

WWD3 (50–60) 4/21/2003 <1.0 <1.0 <1.0 <1.0 E.68 1.3 E.90 3.6

WWD3 (60–70) 4/21/2003 <1.0 <1.0 E.92 <1.0 <1.0 1.2 <1.0 2.8

WWD3 (70–80) 4/21/2003 <1.0 <1.0 E.17 <1.0 <1.0 E2.0 <1.0 E.099

WWD3 (80–90) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD3 (100–110) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD3 (120–130) 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.031

WWD3 (120–130) dup 4/21/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.024

Box cores

WWD.B1 (0–5) 4/22/2003 Yes <1.0 <1.0 <1.0 <1.0 E.33 E.23 <1.0 E.15

WWD.B2 (0–5) 4/22/2003 Yes <1.0 <1.0 <1.0 <1.0 E.34 E.29 E.23 E.68

WWD.B2 (0–5) dup 4/22/2003 <1.0 <1.0 <1.0 <1.0 E.44 E.37 E.32 E.33

WWD.B3 (0–5) 4/22/2003 Yes <3.0 <3.0 <3.0 <3.0 <3.0 <3.0 <3.0 E.055

WWD.B4 (0–5) 4/22/2003 Yes <2.0 <2.0 <2.0 <2.0 <2.0 <2.0 <2.0 <2.0

WWD.B5 (0–5) 4/22/2003 Yes <2.0 <2.0 <2.0 <2.0 <2.0 <2.0 <2.0 E.14

WWD.B6 (0–5) 4/22/2003 Yes <1.0 <1.0 <1.0 <1.0 E.55 E.52 E.66 1.0

WWD.B7 (0–5) 4/22/2003 Yes E1.1 <2.0 <2.0 <2.0 E.34 E.38 E.43 E.64

WWD.B8 (0–5) 4/22/2003 Yes <2.0 <2.0 <2.0 <2.0 E.29 E.36 E.23 E.43

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 
Appendix 1 27

WWD.B9 (0–5) 4/22/2003 Yes E0.21 E0.92 <1.0 <1.0 E0.59 E0.61 E0.30 E0.69

WWD.B10 (0–5) 4/22/2003 Yes <1.0 <1.0 <1.0 <1.0 E.20 E.25 E.21 E.30

WWD.B11 (0–5) 4/22/2003 Yes <2.0 <2.0 <2.0 <2.0 E.25 E.30 E.22 E.35

WWD.B12 (0–5) 4/22/2003 Yes <1.0 <1.0 <1.0 <1.0 E.28 E.28 E.077 E.27

WWD.B13 (0–5) 4/22/2003 Yes <2.0 <2.0 <2.0 <2.0 E.28 E.33 E.32 E.28

WWD.B14 (0–5) 4/22/2003 Yes <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.22

WWD.B15 (0–5) 4/22/2003 Yes <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.13

WWD.B16 (0–5) 4/22/2003 Yes <2.0 <2.0 <2.0 <2.0 <2.0 <2.0 <2.0 E.019

WWD.B17 (0–5) 4/22/2003 Yes <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.071

Suspended and streambed sediment

UMRC 8/30/2003 Yes <8.0 <8.0 <8.0 <8.0 <8.0 <8.0 <8.0 <8.0

UMRC 8/31/2003 Yes <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

UMRC 9/11/2003 <21 <21 <21 <21 <21 <21 <21 <21

UMRC 9/16/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

UMRC env dup 9/16/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

UMRC 10/5/2003 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0

UMRC 10/6/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

GRUGGS 8/30/2003 Yes <14 <14 <14 <14 <14 <14 <14 <14

GRUGGS 8/31/2003 Yes <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

GRUGGS lab dup 8/31/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

GRUGGS 9/11/2003 <8.0 <8.0 <8.0 <8.0 <8.0 <8.0 <8.0 <8.0

GRUGGS 9/16/2003 <2.0 <2.0 <2.0 <2.0 <2.0 <2.0 <2.0 <2.0

GRUGGS env dup 9/16/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

GRUGGS 10/5/2003 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0

GRUGGS 10/6/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

TNG 8/30/2003 Yes <10 <10 <10 <10 <10 <10 <10 <10

TNG 8/31/2003 Yes <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.02

TNG 9/11/2003 Yes <12 <12 <12 <12 <12 <12 <12 E.29

TNG 9/16/2003 Yes <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

TNG 10/5/2003 <13 <13 <13 <13 <13 <13 <13 <13

TNG 10/6/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

OF4 8/30/2003 Yes <9.0 <9.0 <9.0 <9.0 <9.0 <9.0 E1.4 E1.3

OF4 9/11/2003 Yes <4.0 E.23 <4.0 <4.0 E.58 E.76 E.60 E1.1

OF4 10/5/2003 Yes <11 <11 <11 <11 <11 <11 <11 <11

LMRC 8/30/2003 Yes <4.0 <4.0 <4.0 <4.0 <4.0 <4.0 <4.0 E.32

LMRC 8/31/2003 Yes E.82 E.19 <1.0 <1.0 E.26 E.48 E.30 1.5

LMRC lab dup 8/31/2003 <1.0 E.11 <1.0 <1.0 E.13 E.20 E.10 E.39

LMRC 9/11/2003 <10 <10 E1.3 E.48 <10 <10 E.48 <10

LMRC 9/16/2003 Yes <1.0 <1.0 <1.0 <1.0 E.12 E.20 E.10 E.36

LMRC env dup 9/16/2003 <1.0 <1.0 <1.0 <1.0 E.17 E.19 E.13 E.40

LMRC 10/5/2003 <10 <10 <10 <10 <10 <10 <10 <10

LMRC env dup 10/5/2003 <10 <10 <10 <10 <10 <10 <10 <10

LMRC 10/6/2003 Yes <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

LMRC lab dup 10/6/2003 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.33

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 

Sample identifier and

depth interval

(cm)

Date

Sample used

in cluster

analysis

PCB 8 PCB 18 PCB 22 PCB 26 PCB 28 PCB 31 PCB 33 PCB 44
28

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 

Sample identifier and

depth interval

(cm)

PCB 49 PCB 52 PCB 70 PCB 95 PCB 101 PCB 110 PCB 118 PCB 138 PCB 146 PCB 149

Gravity cores

WWD1 (0–5) <3.0 E0.70 E0.75 E0.80 E1.2 E1.6 E0.95 E1.8 E0.30 E1.4

WWD1 (10–20) E.45 E.90 1.1 1.0 1.4 2.5 2.7 3.2 E.47 1.9

WWD1 (30–40) E.67 E.58 E.54 E.72 1.0 1.5 E.89 1.5 E.26 1.4

WWD1 (50–60) 2 3.0 2.9 3.0 3.6 6.8 3.3 5.6 E.71 3.4

WWD1 (70–80) 2.1 3.5 3.9 5.4 9.3 14 E14 17 2.4 12

WWD1 (80–90) 1.4 3.0 2.3 3.5 8.3 9.6 E6.6 8.8 1.0 7.4

WWD1 (90–100) E.72 1.1 E.80 E1.0 1.7 2.1 1.6 1.6 E.15 1.2

WWD1 (100–110) E.036 E.061 E.11 E.064 E.17 E.23 E.12 E.14 E.035 E.082

WWD1 (120–130) <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD1 (140–150) <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD1 (160–166) <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD1 (160–166) dup <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD2 (0–5) E.20 E.54 E.71 E.69 1.1 1.1 E.59 1.8 E.16 1.4

WWD2 (10–20) E.14 E.32 E.38 E.44 E.88 E.89 E.55 1.6 E.16 1.1

WWD2 (30–40) E.74 1.1 E.85 1.6 2.9 2.8 1.6 7.0 1.0 7.2

WWD2 (50–60) E.62 1.1 1.1 1.2 1.6 2.2 1.2 2.7 E.45 2.2

WWD2 (70–80) E.31 E.51 E.62 E.78 1.1 1.7 E.74 2.3 E.47 2.1

WWD2 (70–80) dup E.26 E.49 E.55 E.70 1.2 1.6 E.64 2.1 E.42 1.9

WWD2 (100–110) E.15 E.16 E.23 E.18 E.30 E.37 E.17 E.37 E.070 E.26

WWD2 (100–110) dup E.11 E.17 E.21 E.19 E.28 E.44 E.18 E.40 E.074 E.27

WWD2 (130–140) <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD2 (160–170) <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

WWD3 (0–5) E.55 E.93 E.74 1.0 1.6 2.4 1.6 3.3 E.36 2.1

WWD3 (10–20) E.72 1.4 1.0 1.6 2.3 3.8 2.1 4.7 E.58 3.3

WWD3 (20–30) 3.4 8.7 E6.7 8.5 14 17 E12 16 1.8 13

WWD3 (30–40) 4.1 9.5 7.6 9.6 12 18 12 18 1.9 12

WWD3 (40–50) 7.4 16 E14 15 22 28 E19 27 3.4 21

WWD3 (50–60) 3.9 16 E12 18 32 42 29 50 6.6 39

WWD3 (60–70) 3.2 13 E9.4 14 24 32 E23 30 3.1 22

WWD3 (70–80) E.21 E.44 E.32 E.42 E.78 E.86 E.61 E.75 E.034 E.60

WWD3 (80–90) <1.0 E.097 E.085 E.065 E.22 E.27 E.17 E.31 <1.0 E.16

WWD3 (100–110) <1.0 E.048 <1.0 E.025 E.16 E.20 E.10 E.18 <1.0 E.12

WWD3 (120–130) E.030 E.26 <1.0 E.080 E.15 E.19 <1.0 <1.0 <1.0 E.025

WWD3 (120–130) dup E.029 E.21 <1.0 E.060 E.12 E.16 <1.0 <1.0 <1.0 E.021

Box cores

WWD.B1 (0–5) E.43 E.30 E.58 E.61 E.73 E.94 E.60 2.4 E.24 1.6

WWD.B2 (0–5) E.48 E.56 E.58 E.89 E.89 E.92 E.54 1.8 E.072 1.2

WWD.B2 (0–5) dup E1.0 E.75 E.72 E.82 E.90 1.3 E.69 2.2 E.14 1.5

WWD.B3 (0–5) <3.0 E.26 E.42 E.21 E.64 E.93 E.51 E1.2 E.23 E1.0

WWD.B4 (0–5) <2.0 E.24 <2.0 E.2 E.55 E1.1 E.48 E1.2 <2.0 E.95

WWD.B5 (0–5) <2.0 E.48 E.55 E.62 E.90 E1.3 E.71 E1.6 E.087 E1.0

WWD.B6 (0–5) 1.1 2.7 2.0 3.3 5.6 9.5 5.3 12 1.3 7.4

WWD.B7 (0–5) E.97 2.0 E1.4 E1.4 2.6 4.5 2.6 E5.6 E.63 3.3

WWD.B8 (0–5) E.30 E1.2 E1.0 E1.3 E1.9 2.7 E1.7 3.2 E.25 2.2

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 
Appendix 1 29

WWD.B9 (0–5) E0.72 1.8 1.4 1.9 2.7 3.9 2.5 E4.5 E0.59 2.9

WWD.B10 (0–5) E.26 E.69 E.60 E.69 1.1 1.6 E.99 2.0 E.25 1.5

WWD.B11 (0–5) E.33 E.85 E.74 E.80 E1.2 E1.9 E1.3 2.2 E.30 E1.6

WWD.B12 (0–5) E.23 E.66 E.62 E.71 1.0 1.4 E.86 1.7 E.24 1.3

WWD.B13 (0–5) E.20 E.53 E.63 E.50 E.79 E.99 E.58 E1.1 E.14 E.79

WWD.B14 (0–5) <1.0 E.40 E.44 E.45 E.92 1.0 E.64 1.2 E.16 E.96

WWD.B15 (0–5) <1.0 E.35 E.36 E.34 E.79 E.94 E.57 1.2 E.16 E.91

WWD.B16 (0–5) <2.0 E.26 E.41 E.27 E.49 E.79 E.51 E.75 E.032 E.66

WWD.B17 (0–5) <1.0 E.21 E.24 E.16 E.47 E.61 E.32 .72 E.062 E.55

Suspended and streambed sediment

UMRC <8.0 E.19 E.73 E.31 E.14 E.60 E.31 E.82 <8.0 E.62

UMRC <1.0 <1.0 E.13 E.04 E.01 E.09 E.06 E.16 <1.0 E.08

UMRC <21 <21 <21 <21 <21 <21 <21 <21 <21 <21

UMRC <1.0 <1.0 <1.0 <1.0 E.09 E.07 E.23 <1.0 E.10 <1.0

UMRC env dup <1.0 <1.0 <1.0 <1.0 <1.0 E.07 E.06 E.10 <1.0 E.06

UMRC <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0

UMRC <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0

GRUGGS <14 E.34 E.92 E.47 E.10 E1.1 E.50 E.91 <14 E.60

GRUGGS <1.0 E.12 <1.0 E.20 E.21 E.37 E.20 E.66 E.06 E.44

GRUGGS lab dup <1.0 E.10 <1.0 E.20 E.14 E.33 E.17 E.63 E.08 E.42

GRUGGS <8.0 <8.0 <8.0 <8.0 <8.0 <8.0 <8.0 E.78 E.53 E.70

GRUGGS <2.0 <2.0 <2.0 <2.0 E.02 E.16 E.12 E.63 E.05 E.17

GRUGGS env dup <1.0 <1.0 <1.0 <1.0 E.07 E.33 E.22 E.91 E.12 E.43

GRUGGS <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0

GRUGGS <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.24 E.16 <1.0

TNG <10 <10 E.69 E.34 E.15 E.86 E.50 E1.1 E.14 E.78

TNG <1.0 E.08 <1.0 E.20 E.30 E.46 E.20 E.46 E.08 E.34

TNG <12 E.53 <12 <12 E.30 E1.4 E1.4 E1.6 E.08 E1.5

TNG <1.0 <1.0 <1.0 <1.0 E.04 E.20 E.14 E.59 E.10 E.38

TNG <13 <13 <13 <13 <13 <13 <13 <13 <13 <13

TNG <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.34 <1.0 <1.0

OF4 E.75 E1.6 E2.6 E3.8 E5.1 9.7 E8.0 17 E2.4 E8.4

OF4 E.60 E1.8 E2.3 E3.5 E4.5 E8.3 E6.4 E13 E2.1 E7.1

OF4 <11 E6.6 <11 <11 14 18 E4.4 28 E3.4 14

LMRC E.16 E.60 E.76 E1.2 E1.2 E2.2 E1.3 E2.8 E.36 E1.6

LMRC 1.0 3.8 2.8 E7.9 E9.6 E14 E7.3 E16 2.2 E12

LMRC lab dup E.33 1.1 E.70 2.4 3.2 6.0 3.0 E10 1.1 4.9

LMRC E.21 E1.8 E1.8 <10 <10 E3.6 E.38 E12 <10 E.16

LMRC E.30 E.97 E.62 2.2 2.6 5.5 2.5 E10 1.3 5.0

LMRC env dup E.34 1.1 E.77 2.4 2.9 6.4 2.9 E12 1.4 6.0

LMRC <10 <10 <10 <10 E3.9 E9.2 E1.9 E14 E.26 <10

LMRC env dup <10 <10 <10 <10 E3.9 E9.2 E1.9 E14 E.26 <10

LMRC E.18 1.3 2.8 <1.0 3.2 4.9 E.67 E7.9 1.2 4.4

LMRC lab dup E.19 E.48 1.0 <1.0 1.1 5.0 1.0 E8.2 1.2 4.9

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 

Sample identifier and

depth interval

(cm)

PCB 49 PCB 52 PCB 70 PCB 95 PCB 101 PCB 110 PCB 118 PCB 138 PCB 146 PCB 149
30

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 

Sample identifier and

depth interval

(cm)

PCB

151

PCB

170

PCB

174

PCB

177

PCB

180

PCB

183

PCB

187

PCB

194

PCB

206

Total PCB

congeners

Gravity cores

WWD1 (0–5) E0.51 E0.63 E0.59 E0.13 E0.67 E0.22 E0.52 E0.31 <0.12 13.9

WWD1 (10–20) E.40 1.3 E.63 E.37 1.5 E.47 E.79 E.97 E.51 24.6

WWD1 (30–40) E.43 E.73 E.44 E.22 E.73 E.22 E.69 E.33 <.19 13.8

WWD1 (50–60) E.68 E.95 1.0 E.55 1.6 E.66 1.3 E.62 E.38 49.2

WWD1 (70–80) 2.5 E7.2 4.5 2.4 E9.5 2.4 5.4 E6.5 E1.9 128

WWD1 (80–90) 1.3 1.4 1.5 E.85 2.3 E.96 1.7 E.64 E.32 64.4

WWD1 (90–100) E.40 E.25 E.16 E.048 E.24 E.10 E.24 E.084 <.11 14.0

WWD1 (100–110) E.087 E.16 E.028 <1.0 E.092 <1.0 E.088 <1.0 <.12 1.50

WWD1 (120–130) <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 0

WWD1 (140–150) <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <.21 0

WWD1 (160–166) <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <.18 0

WWD1 (160–166) dup <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <.12 0

WWD2 (0–5) E.60 E.72 E.79 E.31 1.1 E.35 E.79 E.48 E.23 14.7

WWD2 (10–20) E.51 E.65 E.67 E.39 E.97 E.38 E.81 E.37 <.19 11.4

WWD2 (30–40) 1.8 3.0 2.9 E.78 4.8 1.6 3.3 1.4 E.34 47.6

WWD2 (50–60) E.95 E.76 E.83 E.47 1.2 E.53 1.1 E.56 E.32 22.9

WWD2 (70–80) E.74 E.82 E.98 E.56 1.5 E.49 1.3 E.63 E.39 18.4

WWD2 (70–80) dup E.64 E.69 E.82 E.36 1.3 E.51 1.1 E.64 E.33 17.4

WWD2 (100–110) E.12 E.095 E.078 E.026 E.078 E.024 E.017 E.053 <.14 2.96

WWD2 (100–110) dup E.15 E.085 E.076 E.0058 E.069 E.024 E.033 E.050 <.12 3.05

WWD2 (130–140) <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <.047 0

WWD2 (160–170) <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <.0021 0

WWD3 (0–5) E.71 E.68 E.68 E.34 1.1 E.42 E.78 E.53 E.26 20.7

WWD3 (10–20) E.71 1.1 1.1 E.63 1.8 E.75 1.4 E.74 E1.0 32.5

WWD3 (20–30) 2.1 3.0 2.9 1.5 5.5 1.7 3.3 1.5 E.67 135

WWD3 (30–40) 2.1 3.0 3.0 1.6 4.6 1.8 3.5 1.6 E1.0 141

WWD3 (40–50) 3.7 5.7 5.9 2.8 10 3.7 7.5 3.1 E1.6 251

WWD3 (50–60) 8.9 12 13 6.8 21 7.6 15 7.5 E1.8 349

WWD3 (60–70) 3.4 4 3.9 1.8 6.5 3.2 3.7 1.1 E.44 207

WWD3 (70–80) E.23 E.27 E.17 E.041 E.23 E.10 E.20 E.17 E.28 8.98

WWD3 (80–90) E.084 E.11 E.053 E.045 E.088 <1.0 E.10 E.054 <.098 1.91

WWD3 (100–110) E.064 E.089 <1.0 <1.0 E.087 <1.0 <1.0 E.021 <.0090 1.09

WWD3 (120–130) <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <.012 .77

WWD3 (120–130) dup <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 .62

Box cores

WWD.B1 (0–5) E.73 E.93 E.87 E.52 1.5 E.47 1.0 E.51 E.26 15.9

WWD.B2 (0–5) E.62 E.85 E.69 E.39 1.0 E.43 E.81 E.36 E.26 14.9

WWD.B2 (0–5) dup E.73 E.73 E.77 E.47 1.2 E.53 E.96 E.36 <.15 17.2

WWD.B3 (0–5) E.30 E.78 E.33 E.18 E.46 E.17 E.38 <3.0 <3.0 8.06

WWD.B4 (0–5) E.32 E.62 E.42 E.17 E.67 E.17 E.52 E.28 E.20 8.09

WWD.B5 (0–5) E.42 E.58 E.41 E.15 E.23 E.63 E.49 E.30 E.27 10.9

WWD.B6 (0–5) 1.5 3.0 2.6 1.3 5.4 1.6 2.8 1.9 E.74 73.8

WWD.B7 (0–5) E.91 E1.1 E1.2 E.64 E1.8 E.83 E1.3 E.63 E.31 36.7

WWD.B8 (0–5) E.82 E1.0 E.79 E.32 E1.1 E.52 E.82 E.48 <.20 22.9

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 
Appendix 1 31

WWD.B9 (0–5) E0.71 1.0 1.0 E0.53 1.6 E0.67 1.2 E0.73 E0.32 34.0

WWD.B10 (0–5) E.54 E.53 E.53 E.22 E.78 E.28 E.58 E.33 E.22 14.7

WWD.B11 (0–5) E.60 E.59 E.65 E.25 E.92 E.32 E.64 E.38 E.24 16.9

WWD.B12 (0–5) E.52 E.47 E.46 E.21 E.69 E.26 E.52 E.30 E.20 13.2

WWD.B13 (0–5) E.33 E.35 E.40 E.099 E.42 E.15 E.34 E.26 E.23 10.0

WWD.B14 (0–5) E.36 E.38 E.42 E.12 E.50 E.17 E.38 E.28 <.15 9.00

WWD.B15 (0–5) E.39 E.35 E.32 E.12 E.61 E.17 E.39 E.18 E.22 8.50

WWD.B16 (0–5) E.22 E.46 E.25 E.087 E.46 E.12 E.33 E.23 E.19 6.54

WWD.B17 (0–5) E.22 E.26 E.20 E.072 E.10 E.097 E.22 E.17 <.090 4.75

Suspended and streambed sediment

UMRC E.47 E.57 E.17 E.34 E.50 E.18 E.28 <8.0 <.18 6.23

UMRC E.05 E.09 E.04 E.05 E.09 E.03 E.05 E.06 <.03 1.03

UMRC <21 <21 <21 <21 <21 <21 <21 <21 <21 0

UMRC <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 E.05 <1.0 <1.0 .54

UMRC env dup E.05 E.07 E.02 <1.0 E.08 E.02 E.03 E.04 <.03 .60

UMRC <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 0

UMRC <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 0

GRUGGS E.60 E.54 E.03 E.50 E.52 E.17 E.15 <14 <.25 7.45

GRUGGS E.20 E.39 E.24 E.21 E.51 E.16 E.33 E.28 <.05 4.58

GRUGGS lab dup E.19 E.41 E.22 E.23 E.53 E.14 E.31 E.20 <.05 4.30

GRUGGS <8.0 E.55 <8.0 <8.0 E.83 <8.0 E.62 E.47 <8.0 4.48

GRUGGS E.08 E.25 E.09 E.04 E.33 E.11 E.18 <2.0 <2.0 2.23

GRUGGS env dup E.02 E.55 E.26 E.19 E.66 E.16 E.35 E.27 <.12 4.54

GRUGGS <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 <5.0 0

GRUGGS <1.0 <1.0 <1.0 <1.0 E.24 <1.0 E.13 E.33 <1.0 1.10

TNG E.53 E1.9 E.50 E.53 E1.5 E.44 E1.0 E1.6 <1.4 12.6

TNG E.30 E.25 E.33 E.19 E.61 E.19 E.56 E.32 <.44 4.89

TNG E.30 E2.2 E.38 E.19 E1.9 E.62 E.95 E1.2 <1.6 14.8

TNG E.08 E.31 E.44 E.20 E.89 E.25 E.78 E.40 <.56 4.80

TNG <13 <13 <13 <13 <13 <13 <13 <13 <13 0

TNG <1.0 E.17 E.10 <1.0 E.54 <1.0 E.46 E.27 E.40 2.28

OF4 E3.5 E5.4 E4.5 E2.4 9.9 E3.4 E5.3 E2.8 <.16 99.2

OF4 E1.5 E4.2 E3.2 E2.0 E8.8 E2.2 E4.4 E2.1 <1.0 81.3

OF4 E4.4 12 E10 E5.4 24 E5.0 13 E3.4 <11 166

LMRC E.62 E.96 E.44 E.42 E1.2 E.38 E.63 E.66 <.21 17.8

LMRC 2.1 3.2 2.7 1.6 E6.2 1.8 3.0 1.2 E.68 103

LMRC lab dup 1.2 1.9 1.7 1.0 4.0 1.1 2.2 E.85 E.48 48.1

LMRC <10 E8.7 E5.5 E2.8 E1.8 E1.6 E8.8 E4.9 E.69 57.0

LMRC 1.3 2.0 1.8 1.1 4.3 1.2 2.4 E.94 E.69 47.5

LMRC env dup 1.5 2.4 2.2 1.3 4.9 1.4 2.8 1.0 E.64 55.2

LMRC <10 E2.8 E1.9 E.53 E5.5 E.51 E3.2 E.78 <10 44.5

LMRC env dup <10 E2.8 E1.9 E.53 E5.5 E.51 E3.2 E.78 <10 44.5

LMRC 1.4 2.1 1.7 1.1 3.8 1.2 2.3 1.0 E.50 41.7

LMRC lab dup 1.8 2.2 1.9 1.1 3.9 1.2 2.4 1.2 E.53 39.6

Appendix 1.2. Selected polychlorinated biphenyl (PCB) Aroclor and PCB congener concentrations in core, surficial bottom, suspended, 

and streambed sediment samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 

Sample identifier and

depth interval

(cm)

PCB

151

PCB

170

PCB

174

PCB

177

PCB

180

PCB

183

PCB

187

PCB

194

PCB

206

Total PCB

congeners
32

Blank Page
Appendix 2—Analytical Data for Major and 

Trace Elements, Selected Polycyclic Aromatic 

Hydrocarbons, and Selected Organochlorine 

Pesticides From Core, Surficial Bottom, 

Suspended, and Streambed Sediment Samples, 

Woods Inlet and Tributaries, Lake Worth, 

Fort Worth, Texas
34

Blank Page
Appendix 2 35

Appendix 2

The trace element, polycyclic aromatic hydrocarbon 

(PAH), and organochlorine pesticide data reported here expand 

and complement the data of Harwell and others (2003). 

However, the combined data (this study and Harwell and others 

[2003]) are insufficient to describe the distribution and sources 

of trace elements, PAHs, and organochlorine pesticides in 

Woods Inlet. 
36

Appendix 2.1. Selected major and trace element concentrations in surficial bottom, suspended, and streambed sediment samples, 

Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003. 

[Concentrations in micrograms per gram except organic carbon, which is in weight percent; cm, centimeters; dup, duplicate; --, not analyzed; na, not applicable; 

env dup, environmental duplicate; lab dup, laboratory duplicate] 

Sample identifier and

depth interval

(cm)

Sample

type

Minimum

depth

(cm)

Maximum

depth

(cm)

Middepth

(cm)

Sample

date

Organic

carbon

Aluminum Calcium Iron PotassiumMagnesium Sodium PhosphorusTitanium Arsenic Barium

Gravity cores

WWD1 (0–5) core 

(surficial)

0 5 2.5 04/21/03 2.44 48,200 99,400 21,000 7,700 5,770 521 517 4,460 7.53 246

Box cores

WWD.B2 (0–5) surficial 0 5 2.5 04/22/03 2.66 18,100 61,400 9,180 3,930 2,400 724 332 4,720 4.80 209

WWD.B3 (0–5) surficial 0 5 2.5 04/22/03 2.76 55,100 97,600 24,200 8,970 6,120 702 615 4,380 8.72 288

WWD.B3 (0–5) dup surficial 0 5 2.5 04/22/03 -- 56,500 98,500 24,700 9,050 6,170 698 631 4,320 8.32 294

WWD.B5 (0–5) surficial 0 5 2.5 04/22/03 2.32 32,200 79,200 14,400 5,940 3,710 912 384 4,590 6.08 241

WWD.B7 (0–5) surficial 0 5 2.5 04/22/03 2.88 37,700 130,000 17,000 6,040 4,360 746 464 4,560 6.20 232

WWD.B8 (0–5) surficial 0 5 2.5 04/22/03 2.25 44,600 109,000 20,100 6,840 4,970 582 488 4,520 6.63 245

Suspended and streambed sediment

UMRC suspended na na na 8/30/2003 2.62 40,200 198,000 17,200 6,150 5,100 784 617 2,100 6.4 171

UMRC streambed na na na 8/31/2003 .87 38,400 135,000 18,000 6,900 5,420 1,490 530 2,000 5.6 175

UMRC suspended na na na 9/11/2003 4.58 52,000 170,000 22,000 8,020 6,560 740 830 2,600 6.7 208 

UMRC streambed na na na 9/16/2003 1.03 48,100 182,000 20,000 7,290 5,550 716 320 2,400 6.9 154 

UMRC env dup streambed na na na 9/16/2003 1.03 48,000 196,000 20,000 7,300 5,560 702 330 2,300 6.6 148 

UMRC suspended na na na 10/5/2003 3.19 45,000 166,000 20,000 6,640 5,520 764 590 2,500 7.0 196 

UMRC streambed na na na 10/6/2003 .95 46,500 201,000 19,000 6,810 5,740 684 290 2,100 5.9 141 

GRUGGS suspended na na na 8/30/2003 5.20 39,200 161,000 17,800 7,060 5,710 999 894 2,120 6.8 206

GRUGGS streambed na na na 8/31/2003 2.12 45,700 204,000 18,000 7,100 6,050 796 310 2,100 5.5 140

GRUGGS suspended na na na 9/11/2003 4.40 44,500 183,000 20,000 7,680 6,070 845 770 2,200 6.4 201 

GRUGGS streambed na na na 9/16/2003 1.90 40,400 94,400 20,000 7,160 4,670 1,700 510 2,500 7.2 189 

GRUGGS env dup streambed na na na 9/16/2003 2.20 42,400 127,000 21,000 7,230 5,240 1,400 650 2,600 8.6 195 

GRUGGS suspended na na na 10/5/2003 3.78 58,300 146,000 24,000 7,690 7,280 681 650 3,100 7.3 215 

GRUGGS streambed 10/6/2003 2.63 41,400 159,000 20,000 7,250 5,460 1,220 670 2,200 7.7 183 

TNG suspended na na na 8/30/2003 3.85 28,600 178,000 15,600 5,700 4,370 1,150 583 1,590 6.2 268

TNG streambed na na na 8/31/2003 1.91 26,200 184,000 15,000 4,180 3,730 686 380 1,300 6.2 133 

TNG lab dup streambed na na na 8/31/2003 na 26,500 188,000 15,000 4,250 3,840 707 390 1,300 6.2 135 

TNG lab dup streambed na na na 8/31/2003 na 25,800 185,000 14,000 4,080 3,730 688 360 1,300 5.4 129 

TNG suspended na na na 9/11/2003 7.37 37,700 183,000 20,000 6,480 5,260 985 920 2,100 6.6 253 

TNG streambed na na na 9/16/2003 2.64 40,700 187,000 19,000 6,420 5,030 979 560 2,200 6.8 187 

TNG lab dup streambed na na na 9/16/2003 -- -- -- -- -- -- -- -- -- -- --

TNG lab dup streambed na na na 9/16/2003 -- -- -- -- -- -- -- -- -- -- --

TNG suspended na na na 10/5/2003 7.04 34,100 169,000 21,000 5,790 4,620 885 810 2,100 6.6 211 

TNG streambed na na na 10/6/2003 2.84 40,900 179,000 19,000 6,720 5,130 1,020 550 2,100 7.3 192 

OF4 suspended na na na 8/30/2003 6.89 28,800 162,000 21,800 5,020 5,180 922 798 2,340 7.4 301

LMRC suspended na na na 8/30/2003 2.19 7,040 25,100 2,430 1,010 792 99 121 316 1.4 27.2

LMRC lab dup suspended na na na 8/30/2003 na 44,000 183,000 18,800 6,930 5,350 711 542 2,170 6.41 170 

LMRC streambed na na na 8/31/2003 1.37 44,300 155,000 20,000 7,440 5,460 1,040 420 2,400 6.4 184

LMRC lab dup streambed na na na 8/31/2003 -- 43,700 152,000 20,000 7,330 5,540 1,060 410 2,000 6.0 185

LMRC lab dup streambed na na na 8/31/2003 -- 43,800 152,000 20,000 7,330 5,610 1,090 420 2,300 6.4 185

LMRC suspended na na na 9/11/2003 4.08 59,300 128,000 27,000 8,320 7,130 684 680 3,200 7.0 213 

LMRC lab dup suspended na na na 9/11/2003 -- -- -- -- -- -- -- -- -- -- --

LMRC streambed na na na 9/16/2003 1.66 42,900 155,000 19,000 6,950 4,930 1,010 430 2,300 6.1 186 

LMRC env dup streambed na na na 9/16/2003 1.84 43,400 162,000 19,000 7,020 4,830 995 440 2,500 5.7 193 

LMRC suspended na na na 10/5/2003 4.17 46,700 150,000 22,000 7,460 5,460 874 620 2,600 6.2 215 

LMRC env dup suspended na na na 10/5/2003 4.24 45,800 150,000 21,000 7,340 5,470 924 630 2,500 6.3 210 

LMRC streambed na na na 10/6/2003 1.63 46,800 156,000 20,000 7,400 5,380 960 390 2,300 6.3 192 

LMRC lab dup streambed na na na 10/6/2003 -- 47,100 153,000 20,000 7,410 5,290 962 390 2,400 6.0 186 

LMRC lab dup streambed na na na 10/6/2003 -- 48,100 157,000 21,000 7,530 5,330 955 400 2,400 6.0 191 
Appendix 2 37

Appendix 2.1. Selected major and trace element concentrations in surficial bottom, suspended, and streambed sediment samples, 

Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued.

Sample identifier and

depth interval

(cm)

BerylliumCadmium Cobalt Chromium Copper MercuryLithiumManganese

Nickel Lead Scandium

StrontiumVanadium Zinc

Gravity cores

WWD1 (0–5) 1.48 0.585 6.25 46.2 21.0 0.05 29.9 557 21.3 24.0 8.32 170 67.3 73.2

Box cores

WWD.B2 (0–5) .399 .454 4.73 21.3 12.5 .03 11.5 256 12.4 24.6 3.85 121 33.5 47.5

WWD.B3 (0–5) 1.42 .584 7.49 51.4 23.3 .05 32.8 670 24.4 30.7 8.81 194 75.2 79.7

WWD.B3 (0–5) dup 1.38 .581 7.21 51.9 24.9 na 32.5 647 24.5 30.7 9.08 198 76.6 82.3

WWD.B5 (0–5) .867 .606 5.62 35.2 17.7 .04 19.8 367 16.9 27.0 5.70 144 48.3 61.0

WWD.B7 (0–5) .880 1.08 5.62 48.6 21.4 .06 24.9 359 22.0 35.0 6.65 215 56.2 98.4

WWD.B8 (0–5) 1.21 .780 5.95 47.8 20.5 .05 27.5 569 21.5 29.7 7.52 188 61.7 83.8

Suspended and streambed sediment

UMRC 1.1 .50 5.5 43.6 14.6 .04 26.4 478 23.9 30.7 6.6 298 56.8 122

UMRC 1.5 .35 6.2 43.3 15.8 .02 26.0 318 12.6 54.9 6.4 202 60.5 77.1

UMRC 1.6 .68 7.0 54.5 22.2 .05 32.8 640 17.7 37.9 8.6 278 73.2 184 

UMRC 1.4 .16 5.9 50.5 9.9 .04 35.7 254 15.0 17.9 8.7 281 69.9 43.6 

UMRC env dup 1.4 .15 5.8 51.4 9.2 .04 34.6 277 13.1 15.4 8.4 289 70.7 44.5 

UMRC 1.4 .42 5.9 48.6 16.7 .04 32.1 542 14.0 31.6 8.0 266 67.6 107 

UMRC 1.4 .14 5.1 48.3 8.7 .02 33.2 245 12.4 14.5 8.3 285 66.1 37.2 

GRUGGS 1.1 .73 6.0 43.9 27.5 .08 24.2 408 25.9 50.8 6.2 262 60.6 207

GRUGGS 1.4 .18 5.0 50.3 8.6 .04 36.5 257 10.9 17.3 7.8 293 67.1 44.5

GRUGGS 1.5 .69 6.1 52.3 19.2 .05 29.2 375 17.9 48.8 7.5 268 76.8 134 

GRUGGS 1.6 .33 7.4 40.8 14.4 .04 21.0 306 14.2 34.1 7.2 153 62.1 67.1 

GRUGGS env dup 1.4 .41 8.0 44.5 15.8 .08 23.6 450 15.2 43.8 7.4 188 68.8 83.8 

GRUGGS 1.8 .76 7.2 59.3 17.6 .05 35.7 354 20.1 34.9 9.6 217 89.3 112 

GRUGGS 1.5 .30 6.6 44.9 14.4 .05 24.5 486 15.4 41.1 7.0 219 67.4 77.7 

TNG .9 7.5 9.2 89.5 23.6 .15 17.7 557 25.4 73.6 5.0 321 48.0 369

TNG .93 1.1 4.2 36.2 11.0 .05 17.2 216 14.9 45.4 5.1 248 47.6 68.8 

TNG lab dup 1.1 1.1 4.3 33.7 10.8 na 17.5 220 15.2 44.8 5.2 249 48.0 70.8 

TNG lab dup .88 1.1 4.2 33.3 11.2 na 16.5 216 14.5 43.8 4.8 248 41.0 67.9 

TNG 1.2 8.7 10.5 88.4 28.1 .16 22.6 610 19.0 108 6.5 336 65.3 412 

TNG 1.4 2.2 6.0 52.1 18.8 .06 25.3 351 15.9 54.2 7.0 237 67.6 130 

TNG lab dup -- -- -- -- -- -- -- -- -- -- -- -- -- --

TNG lab dup -- -- -- -- -- -- -- -- -- -- -- -- -- --

TNG 1.1 5.7 6.5 54.8 23.8 .10 21.6 508 16.0 59.7 6.4 276 57.0 306 

TNG 1.3 2.2 6.0 51.4 15.4 .06 25.2 349 16.4 43.8 7.2 232 64.5 126 

OF4 .9 12.6 9.6 125 110 .29 16.1 604 60.4 203 4.8 441 48.7 1,990

LMRC .2 .11 .90 5.8 1.7 .05 4.54 51.0 4.66 6.34 .936 34.3 9.41 15.0

LMRC lab dup 1.45 .718 5.81 53.8 17.8 na 32.2 414 13.7 34.3 7.52 263 65.9 100 

LMRC 1.5 3.6 6.0 100 35.3 .16 32.9 242 17.0 85.8 7.5 202 66.2 211

LMRC lab dup 1.4 3.5 6.0 94.5 34.8 -- 32.3 241 16.5 85.5 7.2 200 65.0 205

LMRC lab dup 1.4 3.6 5.9 98.2 34.9 -- 32.5 239 16.4 87.6 7.3 202 65.2 206

LMRC 1.8 4.2 13.1 79.0 36.4 .13 31.4 450 23.3 80.2 10.1 214 79.5 570 

LMRC lab dup -- -- -- -- -- -- -- -- -- -- -- -- -- --

LMRC 1.4 2.4 5.7 69.1 26.9 .10 28.6 229 16.3 57.0 7.3 211 61.3 155 

LMRC env dup 1.3 2.5 5.6 71.5 26.2 .11 28.7 210 16.0 58.5 7.6 230 62.2 168 

LMRC 1.4 3.1 7.1 74.0 36.0 .11 31.7 387 20.7 71.7 8.2 231 71.8 283 

LMRC env dup 1.5 3.3 7.0 72.8 35.9 .10 31.0 383 21.1 72.8 8.1 230 70.7 296 

LMRC 1.5 2.3 5.8 81.2 26.6 .10 31.7 226 16.1 59.7 8.0 200 66.6 142 

LMRC lab dup 1.5 2.1 5.8 83.3 26.6 -- 31.0 220 17.8 59.5 8.4 195 64.2 141 

LMRC lab dup 1.5 2.2 6.0 82.9 26.8 -- 31.5 225 16.8 57.6 8.2 199 66.7 142 
38

Appendix 2.2. Selected polycyclic aromatic hydrocarbon concentrations in surficial bottom, suspended, and streambed sediment 

samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003. 

[Concentrations in micrograms per kilogram; cm, centimeter; E, estimated; lab dup, laboratory duplicate; na, not applicable; env dup, environmental duplicate; <, 

nondetection at indicated concentration]

Sample identifier and

depth interval

(cm)

Sample

type

Minimum

depth

(cm)

Maximum

depth

(cm)

Middepth

(cm)

Sample

date

Naphthalene9HFluorenePhenanthreneAnthraceneFluoranthene

Gravity cores

WWD1 (0–5) core (surficial) 0 5 2.5 4/21/2003 E8.0 21.2 220 55.7 520

Box cores

WWD.B2 (0–5) surficial 0 5 2.5 4/22/2003 E7.1 E8.1 67.6 22.8 198

WWD.B2 (0–5) lab dup surficial 0 5 2.5 4/22/2003 E6.9 11.2 104 28.9 276

WWD.B3 (0–5) surficial 0 5 2.5 4/22/2003 E9.9 E15.4 123 33.6 263

WWD.B5 (0–5) surficial 0 5 2.5 4/22/2003 E5.3 16.4 200 46.5 633

WWD.B7 (0–5) surficial 0 5 2.5 4/22/2003 14.0 27.1 312 70.3 653

WWD.B8 (0–5) surficial 0 5 2.5 4/22/2003 E7.6 25.6 240 61.7 568

Suspended and streambed sediment

UMRC suspended na na na 8/30/2003 E26.5 80.7 1,070 149 2,490

UMRC streambed na na na 8/31/2003 E2.9 17.2 217 47.6 453

UMRC suspended na na na 9/11/2003 E30.4 E38.4 576 E88.0 1,540

UMRC streambed na na na 9/16/2003 E5.5 E26.4 E323 E64.3 E820

UMRC env dup streambed na na na 9/16/2003 E5.3 27.8 358 52.5 887

UMRC suspended na na na 10/5/2003 E15.7 E27.2 414 68.4 1,160

UMRC streambed na na na 10/6/2003 E4.5 25.1 369 48.7 746

GRUGGS suspended na na na 8/30/2003 E26.9 E28.2 569 82.2 1,530

GRUGGS streambed na na na 8/31/2003 E2.6 E4.5 47.7 10.2 133

GRUGGS lab dup streambed na na na 8/31/2003 E2.7 E4.2 48.9 11.0 124

GRUGGS suspended na na na 9/11/2003 E14.9 E13.3 150 36.1 503

GRUGGS env dup streambed na na na 9/16/2003 E1.9 E4.5 37.8 E10.4 128

GRUGGS streambed na na na 9/16/2003 E3.7 E4.5 E60.2 E14.2 E180

GRUGGS suspended na na na 10/5/2003 E25.6 E28.5 E105 E51.7 332

GRUGGS streambed na na na 10/6/2003 E2.3 E3.8 36.7 11.1 116

TNG suspended na na na 8/30/2003 E25.1 E34.6 1,040 123 3,380

TNG streambed na na na 8/31/2003 E3.0 7.8 231 41.6 808

TNG suspended na na na 9/11/2003 E42.1 E64.4 E1,580 E224 E5,210

TNG streambed na na na 9/16/2003 E4.3 9.4 216 42.4 796

TNG suspended na na na 10/5/2003 E34.7 E51.8 735 E125 1,010

TNG streambed na na na 10/6/2003 E3.8 7.6 163 27.2 492

OF4 suspended na na na 8/30/2003 369 316 2,510 518 4,360

OF4 suspended na na na 9/11/2003 E190 E300 E2,860 E648 E6,380

OF4 suspended na na na 10/5/2003 85.9 155 3,120 424 8,200

LMRC suspended na na na 8/30/2003 E6.7 E12.2 213 36.6 460

LMRC streambed na na na 8/31/2003 59.1 101 856 201 1,290

LMRC lab dup streambed na na na 8/31/2003 E5.4 19.9 186 46.4 450

LMRC suspended na na na 9/11/2003 E21.0 E30.1 294 E107 859

LMRC streambed na na na 9/16/2003 10.4 27.6 302 76.7 776

LMRC env dup streambed na na na 9/16/2003 13.4 35.9 489 90.6 1,190

LMRC env dup suspended na na na 10/5/2003 E21.4 E42.0 484 121 1,100

LMRC suspended na na na 10/5/2003 E19.1 26.3 373 74.4 928

LMRC streambed na na na 10/6/2003 158 222 1,460 346 1,740

LMRC lab dup streambed na na na 10/6/2003 32.8 56.7 467 120 822
Appendix 2 39

Appendix 2.2. Selected polycyclic aromatic hydrocarbon concentrations in surficial bottom, suspended, and streambed sediment 

samples, Woods Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003—Continued. 

Sample identifier and

depth interval

(cm)

Pyrene

Benz(a)

anthraceneChrysene Benzo(a)

pyrene

Dibenzo

(a,h)

anthracene

Coronene Total

PAH

Combustion

PAH 

 (2+3)/

Combustion

PAH

Gravity cores

WWD1 (0–5) 409 225 227 209 41.4 E14.7 4,270 2,518 0.37

Box cores

WWD.B2 (0–5) 153 80.9 104 97 <10 E10.7 1,990 1,042 .54

WWD.B2 (0–5) lab dup 207 109 125 110 <10 E10.7 2,474 1,295 .52

WWD.B3 (0–5) 211 116 131 118 25.9 E11.6 2,494 1,389 .50

WWD.B5 (0–5) 502 267 286 281 57.5 E23.1 4,931 3,232 .25

WWD.B7 (0–5) 492 265 290 259 67.0 E30.6 5,032 3,117 .33

WWD.B8 (0–5) 431 240 254 230 54.3 E28.5 4,725 2,726 .34

Suspended and streambed sediment

UMRC 1,840 555 1,090 687 138 E120 16,101 10,631 .27

UMRC 360 143 191 155 30.9 E18.6 3,019 2,002 .24

UMRC 1,180 431 876 631 114 E96.9 11,875 8,071 .25

UMRC E650 E296 E310 E328 E57.7 na 5,672 3,715 .23

UMRC env dup 698 312 332 348 54.9 na 5,870 3,937 .23

UMRC 907 413 584 730 73.2 E39.8 9,938 6,963 .22

UMRC 588 261 317 451 36.9 E18.8 5,803 4,223 .19

GRUGGS 1,080 497 931 563 131 E116 11,818 7,907 .22

GRUGGS 103 51.7 78.7 53.4 11.6 E8.5 1,204 712 .37

GRUGGS lab dup 97.0 53.1 83.6 60.1 13.5 E9.2 1,269 736 .37

GRUGGS 397 169 273 237 45.3 E39.4 4,264 2,819 .32

GRUGGS env dup 99.4 43.7 59.9 55.9 E12.7 na 1,102 674 .29

GRUGGS E143 E67.8 E102 E86.1 E17.4 E21.2 1,429 1,035 .22

GRUGGS 266 E120 206 166 E56.6 E40.9 3,546 2,021 .55

GRUGGS 91.4 40.6 62.0 51.5 8.4 E5.9 896 622 .28

TNG 2,590 816 1,690 1,210 261 E198 22,740 16,536 .15

TNG 602 336 351 340 66.7 na 5,360 3,886 .14

TNG E3,960 E1,420 E2,380 E1,950 E512 E368 33,634 24,170 .15

TNG 618 316 354 351 64 na 5,593 3,698 .18

TNG 1,750 671 983 901 E180 E101 13,408 9,459 .26

TNG 373 192 245 329 37.0 E16.1 4,404 3,203 .13

OF4 3,330 1,570 2,630 1,720 408 E509 38,177 23,060 .37

OF4 E5,460 E2,580 E3,250 E2,760 E443 E279 49,723 31,850 .27

OF4 6,600 3,210 4,720 5,650 493 E203 79,622 56,660 .14

LMRC 324 153 252 157 33.1 E38.9 3,580 2,213 .33

LMRC 991 613 540 509 96.7 na 9,912 5,904 .37

LMRC lab dup 345 191 188 192 41.8 na 3,391 2,146 .25

LMRC 684 338 536 424 E88.8 E69.1 8,156 4,999 .39

LMRC 604 342 342 314 66.5 na 5,838 3,718 .25

LMRC env dup 914 456 466 467 88.6 na 8,394 5,521 .24

LMRC env dup 869 437 588 496 83.4 E46.4 9,229 5,934 .28

LMRC 732 518 752 556 62.2 E31.6 8,389 5,722 .23

LMRC 1,240 892 858 1,130 168 E34.5 16,379 10,094 .37

LMRC lab dup 642 389 396 560 50.4 E15.7 7,166 5,202 .21
40

Appendix 2.3. Selected organochlorine pesticide concentrations in surficial bottom, suspended, and streambed sediment samples, Woods 

Inlet and tributaries, Lake Worth, Fort Worth, Texas, 2003. 

[Concentrations in micrograms per kilogram; cm, centimeter; g, grams; --, not analyzed; E, estimated; <, nondetection at indicated value; dup, duplicate; env dup, 

environmental duplicate; lab dup, laboratory duplicate] 

Sample identifier and

depth interval

(cm)

Sample

type

Minimum

depth

(cm)

Maximum

depth

(cm)

Middepth

(cm)

Sample

date

Sediment

mass

(g)

Technical

chlordane Dieldrin DDE DDD DDT

Gravity cores

WWD1 (0–5) core (surficial) 0 5 2.5 4/21/2003 -- E3.2 <1.5 E0.86 <1.5 <1.5

Box cores

WWD.B2 (0–5) surficial 0 5 2.5 4/22/2003 -- 22 E.56 1.1 E.46 <.5

WWD.B2 (0–5) dup surficial 0 5 2.5 4/22/2003 -- 24 E.38 1.4 E.44 E.32

WWD.B3 (0–5) surficial 0 5 2.5 4/22/2003 -- E4.4 <1.5 E.69 <1.5 <1.5

WWD.B5 (0–5) surficial 0 5 2.5 4/22/2003 -- E3.1 <1.0 E.89 <1.0 <1.0

WWD.B7 (0–5) surficial 0 5 2.5 4/22/2003 -- E8.4 <1.0 1.4 <1.0 E.14

WWD.B8 (0–5) surficial 0 5 2.5 4/22/2003 -- E5.0 <1.0 E.9 <1.0 <1.0

Suspended and streambed sediment

UMRC suspended -- -- -- 8/30/2003 2.848 E34 <4.0 E1.6 <4 <4.0

UMRC streambed -- -- -- 8/31/2003 20.665 E3.4 <.5 E.24 <.5 <.5

UMRC suspended -- -- -- 9/11/2003 1.17 <105 <11 <11 <11 <11

UMRC streambed -- -- -- 9/16/2003 17.998 5 <.5 E.19 <.5 <.5

UMRC env. dup. streambed -- -- -- 9/16/2003 19.958 E2.3 <.5 E.15 <.5 <.5

UMRC suspended -- -- -- 10/5/2003 4.203 <25 <2.5 E1.1 E1.6 <5.0

UMRC streambed -- -- -- 10/6/2003 21.652 <5.0 <.5 <.5 <.5 <.5

GRUGGS suspended -- -- -- 8/30/2003 1.757 90 <7 E3.0 <7.0 <7.0

GRUGGS streambed -- -- -- 8/31/2003 16.694 30 1.1 .86 <.5 <.5

GRUGGS lab dup. streambed -- -- -- 8/31/2003 16.805 30 1.1 .82 <.5 <.5

GRUGGS suspended -- -- -- 9/11/2003 2.91 <40 <4.0 1.2 E2.5 <4.0

GRUGGS streambed -- -- -- 9/16/2003 8.753 16 E.75 E.43 1.1 <1.0

GRUGGS env. dup. streambed -- -- -- 9/16/2003 12.587 E34 E1.5 E.75 E2.3 E.66

GRUGGS suspended -- -- -- 10/5/2003 4.780 <25 <2.5 E1.7 E2.0 E.4

GRUGGS streambed -- -- -- 10/6/2003 19.59 <5.0 <.5 .57 1.1 E.25

TNG suspended -- -- -- 8/30/2003 2.418 E17 <5.0 E1.6 <5.0 <5.0

TNG streambed -- -- -- 8/31/2003 18.774 7.2 <.5 E.3 <.5 <.5

TNG suspended -- -- -- 9/11/2003 1.997 E24 <6.0 E3.7 <6.0 <6.0

TNG streambed -- -- -- 9/16/2003 14.806 9.8 E.6 .51 .44 E.43

TNG suspended -- -- -- 10/5/2003 1.801 <65 <6.5 E1.1 <6.5 6.9

TNG streambed -- -- -- 10/6/2003 20.729 <5.0 <.5 .51 E.24 <.5

OF4 suspended -- -- -- 8/30/2003 2.578 E26 <4.5 E4.3 <4.5 <4.5

OF4 suspended -- -- -- 9/11/2003 5.653 E25 <2.0 E3.2 <2.0 <3.0

OF4 suspended -- -- -- 10/5/2003 2.146 <55 <5.5 E2.4 <5.5 <5.5

LMRC suspended -- -- -- 8/30/2003 5.294 E12 <2.0 E1.3 <2.0 <2.0

LMRC streambed -- -- -- 8/31/2003 22.928 5.1 <.5 E1.4 <.5 <.5

LMRC lab dup streambed -- -- -- 8/31/2003 23.708 E3.3 <.5 E.93 <.5 <.5

LMRC suspended -- -- -- 9/11/2003 1.201 <100 <10 E2.5 E1.3 <10

LMRC streambed -- -- -- 9/16/2003 15.093 5.5 <.54 E1.0 <.5 <.5

LMRC env dup streambed -- -- -- 9/16/2003 14.806 7.4 E E1.3 <.5 <.5

LMRC suspended -- -- -- 10/5/2003 4.938 E10.10 <2.5 <2.5 <2.5 <2.5

LMRC env dup suspended -- -- -- 10/5/2003 2.275 <50 <5.0 <5.0 <5.0 <5.0

LMRC streambed -- -- -- 10/6/2003 23.005 <5.0 <.5 <.5 <.5 <.5

LMRC lab dup streambed -- -- -- 10/6/2003 2.146 <5.0 <.5 1.3 <.5 <.5
Prepared by the USGS Texas Water Science Center:

8027 Exchange Drive

Austin, TX 78754–4733

Information regarding water resources in Texas is available at 

http: //tx.usgs.gov/