U.S. Department of the Interior

U.S. Geological Survey

Hydrogeology, Water Quality, and Ecology 

of Anderton Branch near the Quail Hollow 

Landfill, Bedford County, Tennessee, 

1995-99

By James J. Farmer

Prepared in cooperation with the 

Bedford County Solid Waste Authority

Scientific Investigations Report 2004-5074
U.S. Department of the Interior

Gale A. Norton, Secretary

U.S. Geological Survey

Charles G. Groat, Director

U.S. Geological Survey, Reston, Virginia: 2004

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, it contains copyrighted materials that are noted in the text. 

Permission to reproduce those items must be secured from the individual copyright owners.

Suggested citation:

Farmer, James J., 2004, Hydrogeology, water quality, and ecology of Anderton Branch near the Quail Hollow Landfill, 

Bedford County, Tennessee, 1995-99: U.S. Geological Survey Scientific Investigations Report 2004-5074, 33 p.
 iii

Contents

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

Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2

Purpose and scope . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2

Approach . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2

Description of study area. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 4

Karst hydrogeology. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6

Data collection . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 10

Ground-water data. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 10

Surface-water and rainfall data . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 10

Biologic data. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 11

Soil and sediment data . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 13

Results and discussion . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 13

Ground-water quality. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 13

Surface-water quality . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 21

Anderton Branch. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 21

Sons Spring . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 22

Benthic macroinvertebrates . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 26

Laboratory toxicity studies. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 29

Biomarkers . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 29

Summary. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 30

Acknowledgments . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 31

References. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 31
iv 

Figures

1. Map showing location of study area and sampling sites at the Quail Hollow Landfill, 

Bedford County, Tennessee . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .3

2. Diagrammatic geologic sections through Quail Hollow Landfill showing relations 

among the fill, the regolith, the rock units, water table, springs, and streams. . . . . . . . . . . . . . . . . . . . . . . . .5

3-5. Maps showing:

3. Altitude of the potentiometric surface of the Manchester aquifer in the area of 

Quail Hollow Landfill, Bedford and Moore Counties, Tennessee, March 1996. . . . . . . . . . . . . . . . . .7

4. Structure of the top of the Chattanooga Shale underlying the Quail Hollow Landfill . . . . . . . . . . . .8

5. Altitude of the potentiometric surface of the Central Basin aquifer system in 

the area of Quail Hollow Landfill, Bedford and Moore Counties, 

Tennessee, March 1996 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .9

6. Graph showing chloride concentrations for selected water samples collected 

between 1974 and 1999 in Sons Spring, Bedford County, Tennessee . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 21

7. Hydrograph showing comparison of specific conductance for Anderton and 

Anthony Branches, Bedford County, Tennessee, during a storm on December 12, 1996 . . . . . . . . . . . 22

8. Graphs showing the concentrations of selected metals and specific 

conductance during storm flow and base flow on 

Anderton Branch, Bedford County, Tennessee . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 23

9. Graph showing chloride load calculations for Anthony and Anderton Branches, 

Bedford County, Tennessee . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 24

10. Hydrograph showing specific conductance and rainfall at Sons Spring, Bedford County, 

Tennessee, March 1998 through May 1999 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 24

11-14. Graphs showing:

11. Relation between specific conductance and concentrations of selected constituents 

for three sampling events at Sons Spring, Bedford County, Tennessee. . . . . . . . . . . . . . . . . . . . . . 25

12. Mean abundance and standard error of benthic macroinvertebrates for 

Anderton Branch, Bedford County, Tennessee . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 26

13. Mean taxa richness and standard error of benthic macroinvertebrates for 

Anderton Branch, Bedford County, Tennessee . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 27

14. Mean concentrations of nickel, cadmium, cytochrome P450, and metallothionein 

present in hepatopancreas tissue from crayfish collected at sites near 

Quail Hollow Landfill, Bedford County, Tennessee. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 28

Tables

1. Site number, site description, and type of sampling performed for sampling sites near

Quail Hollow Landfill, Bedford County, Tennessee. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .4

2. Nickel concentrations in soil or sediment samples at selected locations near 

Quail Hollow Landfill, Bedford County, Tennessee. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 10

3. Major ions and selected metals analyzed and detection limits . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 11

4. Volatile organic compound analytes and reporting limits. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 12

5. Inorganic constituents in and physical properties of water from surface water, springs, 

and wells in the Quail Hollow Landfill area, Bedford County, Tennessee. . . . . . . . . . . . . . . . . . . . . . . . . . . 14

6. Volatile organic compounds from surface sites, springs, and wells near 

Quail Hollow Landfill, Bedford County, Tennessee, 1995-98. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 20

7. Results of toxicity tests on water collected from selected locations during base-flow 

and storm-flow conditions near Quail Hollow Landfill, Bedford County, Tennessee . . . . . . . . . . . . . . . . 29
 v

Conversion Factors, Abbreviated Units, Datums, 

and Site-Numbering System

Temperature in degree Fahrenheit (oF) can be converted to degree Celsius (oC) in the following 

manner: o

C= 5/9 x (oF-32)

Abbreviated Units

μm micrometer

g gram

mL milliliter 

mg/L milligrams per liter 

μg/L micrograms per liter

μS/cm microsiemens per centimeter

μg/g micrograms per gram

Vertical coordinate information is referenced to the National Geodetic Vertical Datum of 1929 

(NGVD 29); horizontal coordinate information is referenced to the North American Datum of 1927 

(NAD 27).

Site-Numbering System: In this report, sites are identified with four-digit numbers in which the 

first digit designates the drainage basin and the remaining digits designate the unique site. 

Within a basin, site numbers increase upstream, accounting for tributaries before continuing up 

the main stem. Numbers are commonly separated by five in order to allow for additional sites.

Multiply By To obtain

Length

inch (in.) 2.54 centimeter (cm)

inch (in.) 25.4 millimeter (mm)

foot (ft) 0.3048 meter (m)

mile (mi) 1.6048 kilometer (km)

foot per mile (ft/mi) 0.1894 meter per kilometer (m/km)

Area

acre 4,047 square meter (m2)

acre 0.4047 hectare 

square mile (mi2) 2.590 square kilometer (km2)

Volume

gallon (gal) 3.785 liter (L)

Flow

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

gallon per minute (gal/min) 0.06308 liter per second (L/s)
Hydrogeology, Water Quality, and Ecology of Anderton 

Branch near the Quail Hollow Landfill, Bedford County, 

Tennessee, 1995-99

By James J. Farmer

Abstract

The Quail Hollow Landfill, located in southeastern Bedford County on the Highland Rim overlooking the Central 

Basin karst region of Tennessee, is constructed on the gravelly, 

clay-rich residuum of the Fort Payne Formation of Mississippian age. A conceptual hydrologic model of the landfill indicated that Anderton Branch was at risk of being affected by the 

landfill. Ground water flowing beneath the landfill mixes with 

percolating rainwater that has passed through the landfill and 

discharges to the surface from numerous weeps, seeps, and 

springs present in the area. Anderton Branch, adjacent to the 

landfill site on the north and east, receives most of the discharge 

from these weeps, seeps, and springs. Anderton Branch also 

receives water from the Powell Branch drainage basin to the 

west and south because of diverted flow of ground water 

through Harrison Spring Cave. The U.S. Geological Survey, in 

cooperation with the Bedford County Solid Waste Authority, 

conducted a study to evaluate the effect of the Quail Hollow 

Landfill on ground- and surface-water quality.

During storm runoff, specific conductance was elevated, 

and cadmium, iron, manganese, lead, and nickel concentrations 

in Anderton Branch frequently exceeded maximum contaminant levels for drinking water for the State of Tennessee. High 

chloride inputs to Anderton Branch were detected at two locations—a barnyard straddling the stream and a tributary draining 

a pond that receives water directly from the landfill. The chloride inputs probably contribute to chloride load levels that are 

three times higher for Anderton Branch than for the control 

stream Anthony Branch. Although toxic volatile organic compounds were detected in water from monitoring wells at the 

landfill, no organic contaminants were detected in domestic 

water wells adjacent to the landfill or in Anderton Branch. 

Sons Spring, a karst spring near the landfill, has been 

affected by the landfill as indicated by an increase in chloride 

concentrations from 4 milligrams per liter in 1974 to 59 milligrams per liter in 1996. Analysis of water samples from Sons 

Spring detected concentrations of nickel that exceeded primary 

drinking-water standards and Tennessee Department of Environment and Conservation fish and aquatic life chronic standards. Trichloroethene, 1,1-dichloroethene, and 

1,1-dichloroethane also were detected at Sons Spring. The presence of these chlorinated solvents imply the landfill origin of 

the contaminants in Sons Spring. Continuous monitoring at 

Sons Spring indicated a pattern of decreased specific conductance and lower contaminant concentrations after a storm. Contaminant concentrations increased with specific conductance to 

pre-storm levels after several days. 

The benthic macroinvertebrate community in Anderton 

Branch adjacent to the landfill was not different from the communities at control sites upstream and in Anthony Branch. Sons 

Spring, however, has low abundance and numbers of benthic 

macroinvertebrate taxa. Toxicity studies using Ceriodaphnia 

dubia indicated no toxicity in the base flow or storm water in 

Anderton Branch or in a tributary draining a pond that receives 

water from the landfill and Sons Spring; however, water collected from Sons Spring resulted in 100 percent mortality to all 

organisms within 48 hours. 

High concentrations of nickel were detected in crayfish tissue from control sites and Anderton Branch. Analysis of sediment samples also indicates nickel concentrations are high at 

control sites upstream of the landfill. Increased levels of the 

biomarker metallothionein detected in crayfish from Anderton 

Branch likely are not caused by nickel or cadmium because the 

levels present in the tissue are not correlated with metallothionein levels. 

Despite the high levels of certain metals in Anderton 

Branch during storm flow, the lack of toxicity and the health of 

the benthic community imply no detectable negative effect 

from the landfill to the stream. Sons Spring, however, is toxic 

and almost devoid of organisms. A high chloride concentration 

in the water from Brinkley tributary indicates the landfill as the 

origin of this water; however, the lack of contamination and 

toxicity in this water imply that biologic activity and filtering 

occurring in Brinkley Pond is improving the water quality. The 

overall negative effect from landfill-contaminated water 

appears to be localized to the area in the immediate vicinity of 

Sons Spring and in short reaches of Anderton Branch adjacent 

to the landfill.
2 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

Introduction 

In August 1994, the Bedford County Solid Waste Authority (BCSWA) entered into a cooperative agreement with the 

U.S. Geological Survey (USGS) to obtain background waterquality data near the Quail Hollow Landfill because of suspected contamination of regional ground- and surface-water 

resources. As part of a reconnaissance study, background 

water-quality data were collected from streams in nine drainage 

basins in the vicinity of the landfill. Several areas were identified close to the landfill and were characterized by low diversity 

and abundance of benthic macroinvertebrates, high specific 

conductance, high concentrations of chloride, iron, manganese, 

and unidentified organic compounds (Hollyday and Byl, 1995). 

Because of the environmental concerns of the BCSWA and the 

USGS’s continuing scientific research into contaminant transport in karst terranes, the study was expanded to include the spatial and temporal distribution of landfill-associated contaminants in the karst system and to assess possible risk to the 

ecology of the area. 

Water-quality deterioration associated with landfills has 

been well documented (Merz and Stone, 1968; Hughes and others, 1971; Borden and Yanoschak, 1990). Borden and 

Yanoschak (1990) determined that water samples near 53 percent of the landfills in a North Carolina study contained concentrations of heavy metals and organic compounds that exceeded 

drinking-water standards. Landfill leachate, formed by rainwater percolating through the landfill waste, is the primary cause 

of ground-water contamination according to Chain and 

DeWalle (1976). Increases in concentrations of chloride, iron, 

and manganese along with elevated alkalinity and specific conductance in both surface and ground water have been attributed 

to the effect of landfill leachate (Falwell and others, 1990; Heck 

and others, 1992; Parks and Mirecki, 1992; Helgesen and others, 1993; Myers and others, 1993; Mack, 1994; Rasmussen and 

others, 1994; Ferrell and Smith, 1995; Nielsen and others, 

1995). The concentrations of contaminants in surface and 

ground water near a landfill are usually several orders of magnitude lower than contaminants in landfill leachate due to dilution (Borden and Yanoschak, 1990). Even with dilution, concentrations of contaminants can remain high enough to pose a 

potential risk to human health and the ecology. Soil erosion 

from landfills also can produce detrimental quantities of sediment. Belval and others (1992) concluded that sediment produced by erosion from a landfill was the primary factor that 

resulted in negative effects on the abundance and taxa richness 

to the benthic community of a stream associated with a landfill. 

Purpose and Scope

From 1995 to 1998, a study was conducted to characterize 

the hydrology and water quality of Anderton Branch, a stream 

adjacent to the Quail Hollow Landfill in Bedford County, Tennessee. During this time, the chemistry and toxicity of water 

during base-flow and storm conditions and the health of the 

benthic community were evaluated. This report summarizes the 

chemical and biologic effects of the landfill on surface and 

ground water in a karst area. 

Approach

The effect of the Quail Hollow Landfill on the biota and 

the surface- and ground-water quality near the landfill was evaluated through a three phase approach: problem formulation, 

analyses, and risk characterization (U.S. Environmental Protection Agency, 1992). The reconnaissance study conducted in 

nine surface-water basins near the landfill (Hollyday and Byl, 

1995) provided the data to identify and formulate the potential 

problem associated with the landfill. Two locations near the 

landfill had high chloride (>20 mg/L) concentrations and specific conductance (>500 μS/cm). A low abundance and diversity of organisms were identified in Sons Spring and in reaches 

of Anderton Branch adjacent to the east side of the landfill 

(fig. 1, near Yellow Boy 1).

The analysis phase of the investigation included the development of a conceptual model of water and contaminant movement and sample collection to test the model and to evaluate the 

temporal and spatial effects of the landfill on ground- and 

surface-water quality and on the aquatic biota. Water samples 

were collected from local domestic wells and springs to evaluate the effect of the landfill on ground water. The results of 

these analyses were compared to the analyses of samples collected from landfill monitor wells. Surface-water quality data 

were collected under base-flow and storm conditions. Biological samples were collected to evaluate the abundance and diversity of the benthic community. Toxicity studies were conducted 

using Ceriodaphnia dubia to evaluate the toxicity of water from 

Sons Spring and Anderton Branch. Results from this type of 

study have been shown to correlate with other instream biologic 

indicators (Eagleson and others, 1990). Crayfish were collected 

to conduct biomarker studies evaluating the response of 

enzymes or other biologic markers to stress induced as a result 

of exposure to contamination. Samples were collected from 

Anderton Branch at sites upstream (control site), adjacent to, 

and downstream of the landfill (fig. 1). Sites on Anthony 

Branch and other nearby streams were used as additional control sites for biological and storm-water sampling. The type of 

sampling conducted and the sampling sites are listed in table 1.

The risk characterization phase of the study incorporated 

the potential problems associated with the landfill and the 

results of the data collection and analyses to determine the overall ecological risk. Concentrations of the inorganic compounds 

in the stream and sediment were compared to the State of Tennessee Department of Environment and Conservation criteria 

for fish and aquatic life (Tennessee Department of Environment 

and Conservation, 1999). The concentrations of organic and 

inorganic compounds also were compared to the primary and 

secondary maximum contaminant levels established for drinking water by the Tennessee Department of Environment and 

Conservation (1999).
Introduction 3
4 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

Description of Study Area

The Quail Hollow Landfill is located in southeastern Bedford County, Tennessee, on 352 acres, of which 77 acres are 

permitted for waste disposal as a Class I Sanitary landfill. 

Springs and streams adjacent to the landfill may be adversely 

affected by landfill operations or leachate migration. The landfill was originally permitted by Bedford County and operated as 

a commercial landfill. During the first several years of operation, the landfill received a variety of municipal, commercial, 

and industrial wastes. The landfill was permitted in three sections (fig. 1); sections I and II are the oldest sections and are not 

underlain by a liner. Vertical expansion of Section II resulted in 

leachate migrating from the landfill proper onto adjacent, privately owned land. The migrating leachate apparently was associated with the death of numerous deciduous trees along the 

south-southeastern segment of the landfill perimeter. In 1998, a 

vertical clay barrier was constructed down to bedrock to prevent 

additional migration of leachate off the landfill property along 

this segment of the perimeter. After the construction of the clay 

barrier, a geomembrane cap was placed on top of Section II and 

covered with soil. Vertical expansion of Section III resulted in 

waste being deposited on top of a liner to a depth near the top of 

the Chattanooga Shale. A leachate collection system was 

installed with this expansion. Landfill operations were discontinued at the Quail Hollow Landfill in 1998. 

Land use in the area around the landfill may have an effect 

on water quality. Land adjacent to both Anderton and Anthony 

Branches is used predominantly for cattle grazing and hay farming, and the areas between the pastures are deciduous forest. A 

few homes with septic systems are present next to both streams, 

and residential developments with septic systems are common 

on the Highland Rim above the springs that form the headwaters 

of Anthony and Anderton Branches. During the period of the 

study, the surface of the landfill was mostly bare with only a 

thin grass cover.

The landfill is located in the Duck River drainage basin 

and is positioned on a spur of the Highland Rim overlooking the 

Central Basin, both physiographic regions of Tennessee 

(Miller, 1974) (fig. 2). The elevation in the study area ranges 

from about 1,100 feet above NGVD 29 on the Highland Rim to 

about 900 feet above NGVD 29 on Anderton Branch north of 

the landfill. Two streams border the landfill, Powell Branch to 

the southwest and Anderton Branch to the north, northeast, and 

east (fig. 1). Powell Branch drains an area of approximately 

0.7 mi2 and has a gradient of approximately 160 ft/mi. Powell 

Branch flows on the surface exposure of the Ordovician Leipers 

and Catheys Formations and the Cannon Limestone. The topography suggests that surface water leaving the southwest side of 

the landfill flows into Powell Branch and eventually into Bennett Branch and Thompson Creek. However, on May 6, 1998, 

water released from a holding pond at the landfill borrow-pit 

area (fig. 1) entered a sinking pond near the headwaters of Powell Branch and flowed under a surface divide through solution 

cavities and discharged into Anderton Branch. The water from 

the pond contained large amounts of suspended red clay, which 

served as a natural tracer, clearly indicating the connection 

between the pond in the Powell Branch drainage basin and the 

resurgence at Harrison Spring Cave in the Anderton Branch 

drainage basin. This natural tracer demonstrates that drainage 

from the southwest and west, as well as from the east and north, 

flows into Anderton Branch through karst solution channels. 

Anderton Branch, with a drainage area of approximately 

2 mi2, flows off the Highland Rim and has a gradient of 

170 ft/mi. As the stream moves onto the Central Basin, the gradient changes to 150 ft/mi. Anderton Branch originates from 

springs in the Fort Payne Formation. Anderton Branch historically sank into a swallet shortly after flowing onto the surface 

exposure of the Cannon Limestone and then flowed underground for approximately 1,500 ft before resurging. Stream 

channel modifications since the study began, however, have 

resulted in approximately two-thirds of the stream flow remaining on the surface. Anthony Branch, which generally parallels 

Anderton Branch in the adjacent drainage basin to the north, 

was used as a control stream because of its similarity to Anderton Branch. Anthony Branch drains 1.97 mi2, flows over similar 

geology, and has a similar losing reach (fig. 1).

Table 1. Site number, site description, and type of sampling performed for sampling sites near Quail Hollow Landfill, Bedford 

County, Tennessee.

[B, Biomarkers; Cs, Control site; Be, Benthic macroinvertebrates; Ss, Storm 

sampling; T, Toxicity study; G, Gaging station; C, Chemistry; Sa, Soil or sediment analysis]

Site No. Description Type of sampling

2005

2026

2050

3005

3040

3045

3090

3185

3135

3110

3200

4050

5005

6005

S1

S2

S3

S4

S5

S6

S7

S8

S9

S10

S11

S12

Riffle

Riffle

Culvert

Riffle

Riffle

Culvert

Riffle

Riffle

Riffle

Riffle

Riffle

Spring house

Pool

Pool

Field

Pond bank

Stream bank

Stream

Stream bank

Borrow pit

Borrow pit

Borrow pit

Road cut

Road cut

Road cut

Stream

B, Cs

Be, Cs

Ss, T, Cs

B, Be

Be, Cs

T

G, Ss, T, Be

Be

Be

B, Be, C, G, Ss, Sa, T

B, Be, Sa

Cs, Ss, T

Be

Be

Sa

Sa

Sa

Sa

Sa

Sa

Sa

Sa

Sa

Sa

Sa

Sa
Introduction 5
6 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

Karst Hydrogeology

The primary geologic formations, in descending order 

from the land surface, are the Mississippian Fort Payne Formation, the Devonian Chattanooga Shale, and the Ordovician 

Leipers and Catheys Formations, Cannon Limestone, and the 

Hermitage Formation. The two aquifers potentially affected by 

the landfill are the Manchester aquifer and the Central Basin 

aquifer system (fig. 2). 

The Quail Hollow Landfill is developed in the gravels and 

residuum of the Manchester aquifer and weathered Fort Payne 

Formation (fig. 2). The thick residuum of the Fort Payne Formation has been considered a good location for landfills 

because the residuum acts as a thick filter medium (Miller and 

Maher, 1972) and it overlies the Chattanooga Shale, a regional 

confining layer. The Ordovician formations underlie the Chattanooga Shale and have numerous karst features including disappearing stream reaches in Anderton and Anthony Branches, 

springs, sinkholes, and interconnected cave systems.

The Manchester aquifer is a regional aquifer composed of 

chert (gravel to silt-sized) particles in the residuum of the upper 

part of the Fort Payne Formation and solution openings in the 

bedrock (Burchett and Hollyday, 1974). The Fort Payne Formation bedrock is predominantly soluble dolomitic limestone with 

50 percent or greater insoluble residue of silt, clay, and blocky 

chert. Manganese oxides present in this formation are reported 

to contain up to 2 percent nickel and 4 percent cobalt (Larson, 

1970). In the area of the landfill, the Fort Payne Formation is 

weathered to the degree that no carbonate bedrock is present. In 

the area around the landfill, the residuum contains layers of 

insoluble chert. Locally, the water in the aquifer can become 

perched above the chert layers. Regionally, the Manchester 

aquifer receives diffuse recharge from rainfall on the Highland 

Rim. A recent study by Farmer and Williams (2001) includes 

long-term monitoring data that confirm the diffuse-flow 

recharge characteristic of this aquifer. The potentiometric surface of the Manchester aquifer is lower at the landfill than 

within the Highland Rim to the south and east of the landfill 

(fig. 3). The potentiometric surface in the Manchester aquifer 

indicates a general direction of ground-water flow to the north 

under the landfill.

The Late Devonian and Early Mississippian Chattanooga 

Shale underlies the Fort Payne Formation. Chattanooga Shale is 

a regional layer that divides the Central Basin from the Highland Rim (Miller and Maher, 1972). The unweathered Chattanooga Shale, predominantly an insoluble, dense, black, carbonaceous shale with some sandy zones, is a major confining unit 

in Tennessee (Burchett, 1977). The landfill is located on the 

northeast edge of a Chattanooga Shale structural high with a 

structural dip of about 1.5 o northeast (NE) (C.W. Wilson, Tennessee Division of Geology, unpublished structure maps). 

Detailed mapping confirms a northeast dip of approximately 

1o NE (fig. 4). Water percolating through the landfill mixes 

with ground water moving along the Chattanooga Shale. The 

combined flow exits as seeps and springs along the outcrop 

(fig. 2). Fracturing and weathering near the outcrop of the shale, 

however, can result in water moving vertically through this confining unit into the Central Basin aquifer system (fig. 2, line of 

section A-A'). In some sites, the very thin (less than 3 ft) Maury 

Shale may be present at the top of the Chattanooga Shale. 

Hydrologically, the Maury Shale is part of the regional confining layer.

The Central Basin aquifer system is separated from the 

Manchester aquifer by the Chattanooga Shale regional confining unit (Brahana and Bradley, 1986) (fig. 2). Several Ordovician limestones comprise this aquifer system. The first formations below the Chattanooga Shale are the Leipers and Catheys 

Formations; soluble, thin-bedded, silty, clay-rich limestones 

that weather to a thin residuum (Miller and Maher, 1972) and 

are considered to be poor aquifers (E.F. Hollyday, U.S. Geological Survey, written commun., 1997). Soils associated with the 

Leipers and Catheys Formations in control areas not associated 

with the landfill (site S11, table 2) contain as much as 38.7 μg/g 

of nickel. These high concentrations may indicate that nickel 

has leached from the Fort Payne or the Maury Formations (Basseler, 1932), or both, and precipitated in soils formed from the 

Leipers and Catheys Formations (table 2). Below the Leipers 

and Catheys Formations is the Cannon Limestone (Wilson, 

1990), a soluble coarse-grained, dark, dense, medium- to thickbedded limestone with less than 10 percent insoluble residue. 

The Cannon Limestone is considered to be an excellent aquifer 

(E.F. Hollyday, U.S. Geological Survey, written commun., 

1997). Beneath the Cannon Limestone is the laminated Argillaceous Limestone Member of the Hermitage Formation. The 

lithology of this unit is limestone with a greater than 49 percent 

fine-grained insoluble residue and is a major confining unit in 

Middle Tennessee (Tucci and others, 1990). Because much of 

the Hermitage Formation is a confining unit, ground water 

influenced by the landfill is unlikely to migrate into older and 

deeper formations. The Hermitage Formation is considered to 

be the base of ground-water hydrology near the landfill. 

The Central Basin aquifer system is a karst aquifer (Wolfe 

and others, 1997). Regional recharge is from rainfall in the Central Basin and from sinking streams primarily in, or near, the 

Highland Rim escarpment area. The potentiometric surface of 

the Central Basin aquifer system (fig. 5) has more than twice the 

relief of the Manchester aquifer (fig. 3). The degree of karst 

development is well indicated in the area. Sinkholes have developed at the headwaters of Powell Branch. A large swallet has 

developed at Brinkley Pond where water from the pond disappears underground. In the vicinity of the landfill, several caves 

are developed near the top of the Cannon Limestone. Parts of 

the caves have been mapped (fig. 4) and recorded (Nashville 

Grotto, American Speleological Society, written commun. 

1997). Losing reaches are present on both Anderton and 

Anthony Branches, and karst springs are present at several locations (fig. 1). In May 1998, turbid water was released from a 

borrow pit to a sinking pond. The water flowed through solution 

openings in the aquifer to the cave system and was discharged 

to Anderton Branch at the mouth of Harrison Spring Cave. The 

turbid water acting as a natural dye tracer indicates that the 
Karst Hydrogeology 7
8 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County
Karst Hydrogeology 9
10 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

Harrison cave system and connected solution openings extend 

for 4,200 ft on the west side of the landfill. The existence of 

such a large cave system near the landfill leads to the hypothesis 

that water percolating through the landfill and surface runoff 

from the landfill in the Powell Branch drainage basin could possibly enter this system and discharge into Anderton Branch. 

Data Collection

The study at Quail Hollow Landfill includes the collection 

of a wide range of hydrologic and biologic data at several sampling sites (table 1). Water-quality samples were collected from 

domestic wells, landfill monitoring wells, and from springs in 

the area. Surface-water flow was monitored and water-quality 

samples were collected during base-flow and storm-flow conditions. Because biologic indicators are excellent integrators of 

environmental conditions, the benthic macroinvertebrate community was evaluated as an indicator of stream health; water 

toxicity studies with the water flea, Ceriodaphnia dubia, were 

conducted; and biomarkers in crayfish were analyzed as the 

most sensitive indicator of water quality. Soil and sediment 

samples were collected at selected locations and analyzed for 

nickel content to supplement the biomarker results. 

Ground-Water Data

Samples were collected at domestic wells located closest 

to the landfill to evaluate the quality of ground water near the 

landfill. Three domestic water wells (fig. 1) were sampled in 

May 1996 and May 1998 according to the method outlined by 

Wood (1976). Samples were sent to the USGS laboratory at 

Ocala, Fla., for analysis of selected inorganic constituents 

(table 3). Three landfill monitoring wells and Sons Spring were 

sampled in June and September 1996 to evaluate the effect of 

the landfill on ground water in the vicinity of the landfill. This 

sampling was conducted according to the methods of Wood 

(1976), and samples were sent to the USGS laboratory for 

analysis of selected inorganic constituents. Organic analyses 

were conducted at the laboratories of Quanterra Environmental 

Services. 

Surface-Water and Rainfall Data

Streamflow gaging stations were established at site 3110 

on Anderton Branch and at site 3090 (Sons Spring) (fig. 1) in 

February 1996, according to the procedures described by Carter 

and Davidian (1968). Site 3110, a continuous-stage recorder, as 

described by Buchanan and Somers (1969), was used to collect 

Table 2. Nickel concentrations in soil or sediment samples at selected locations near Quail Hollow Landfill, Bedford County, 

Tennessee.

[OWQL, duplicate sample analyzed at the U.S. Geological Survey Water Quality Laboratory, Ocala, Fla.; --, Not applicable]

Site Nickel concentrations, 

in micrograms per liter

No. 

(see fig. 1) Description

Replicate

1 2 3 Mean OWQL

S1 Soil from Kemps pasture—Warsaw Formation 2.0 2.2 2.3 2.2 --

S2 Near Kemps pond from base of fallen tree—Fort Payne Formation 6.8 -- -- -- --

Northeast pond bank—Fort Payne Formation -- 15.5 -- -- --

South pond bank—Fort Payne Formation -- -- 10.0 10.8 --

S3 Anderton Branch stream bank—500 feet upstream from Kemps pool 6.3 9.7 12.1 9.4 --

S4 Anderton Branch stream sediments near base of Fort Payne Formation—Maury 

Shale

45.2

--

--

--

66.6

--

--

--

30.0

--

--

47.3

44.1

47.3

--

S5 Anderton Branch stream bank near base of Fort Payne Formation—Maury Shale 27.0 15.0 28.3 23.4 --

S6 Borrow pit area near base of landfill material—Fort Payne Formation 14.9 63.0 89.3 55.7 --

S7 Borrow pit area—weathered Chattanooa Shale 1.2 5.2 2.3 2.9 --

S8 From borrow pit just below Chattanooga Shale—Catheys and Leipers Formations 124

--

--

30.4

--

9.8

--

54.7

129.4

--

S9 Brinkley Road, road cut, near top of Highland Rim—Fort Payne Formation 25.7

--

--

26.1

50.2

--

34.0

--

--

30.6

S10 Brinkley Road, road cut—weathered Chattanooga Shale 10.5 9.0 11.3 10.3 --

S11 Brinkley Road, road cut—Catheys and Leipers Formations 276

--

--

48.7

53.0

--

125.9

--

--

38.7

S12 Anderton Branch stream sediment 39.1

--

--

29.0

--

31.7

--

32.7

40.8

--
Data Collection 11

stage (water-level) data in 0.01-ft increments at 15-minute 

intervals. Discharge measurements were made for several 

stages following procedures described by Buchanan and Somers (1969), and a discharge rating was developed following procedures described by Kennedy (1983). This rating was applied 

to the continuous-stage data to produce continuous-discharge 

records. Periodic discharge measurements, instead of 

continuous-discharge measurements, were made at site 3090. 

Rainfall data were recorded with a tipping-bucket rain gage and 

data recorder at a site west of site 3090.

Field measurements of water quality were made at sites 

3110 and 3090 according to the general procedures described 

by Wood (1976). Field measurements of specific conductance 

and temperature were made at 30-minute intervals at both sites 

by using a multiparameter data recorder. Instruments were calibrated using standard reference solutions and procedures recommended by the manufacturer at approximately 1-month 

intervals and were recalibrated as necessary. 

Water samples were collected at selected sites during baseflow conditions and sent to the USGS laboratory to be analyzed 

for major ions and selected inorganic constituents (table 3). 

Storm-water samples were collected at sites 3110 and 3090 near 

the landfill. During selected storms, water samples were collected at site 3110 every 15 minutes, either as grab samples or 

by using an automatic sampler. Samples collected during peaks 

in specific conductance were sent to the USGS laboratory for 

analysis of selected inorganic constituents. During a storm in 

December 1996, control sites 2050 (Anthony Branch) and 4050 

(Yasui Spring) were monitored at 15-minute intervals for specific conductance and temperature following procedures 

described by Wood (1976). The sites were selected to provide 

background water-quality values. During the same storm, samples were collected at Sons Spring (site 3090) every 3 hours 

with an automatic sampler to evaluate the possible range in concentrations in a karst spring. Samples representing approximately the high, low, and medium specific-conductance measurements were sent to the USGS laboratory for analysis of 

selected inorganic constituents. 

Specific conductance and temperature were measured in 

Anderton Branch between sites 3110 and 3005. Changes in specific conductance and temperature identified spring discharges 

to Anderton Branch. Discharge was measured (Buchanan and 

Somers, 1969) above and below the spring, and grab samples 

(Wood, 1976) were collected and analyzed for chloride concentrations (Hach, 1992). Discharge data and chloride concentrations were used to calculate instantaneous chloride loads at each 

site, and daily loads were estimated from these calculations. 

Grab samples for the analysis of volatile organic compounds 

(VOCs) were collected at sites 3110 and 3090 by dipping 

40-milliliter VOC vials into the water by hand. These samples 

were analyzed for selected organic compounds (table 4) by 

Quanterra Environmental Services, Denver, Colo. 

Biologic Data

In May, September, and December 1996 and May 1997, 

benthic macroinvertebrates were sampled at sites 2026, 3005, 

3040, 3090, 3110, and 3200 and again in December 1998 at 

site 3005 using artificial substrates. Sampling was conducted 

using a 15x15x5-centimeter plastic-covered wire basket filled 

with local substrate. Flat substrate was used to construct three 

sampling layers in each basket. A Hester-Dendy style 

multiplate artificial substrate sampler was attached to each basket by a 1-meter length of nylon cord. Minimums of three replicates of each sampling device were collected at each site on 

four dates between 1996 and 1997. At each harvest, a 250-μm 

mesh “D” net was first placed downstream of the sampling 

device to catch organisms displaced as the device was removed. 

The baskets and multiplate samplers were disassembled and 

handpicked for organisms. Organisms were preserved in the 

field in 80 percent ethanol and were later identified to genus 

where appropriate by using a variable power dissecting microscope and a taxonomic key (Merritt and Cummins, 1996). The 

numbers of organisms on the multiplate samplers and rock baskets were converted into organism density using a conversion 

Table 3. Major ions and selected metals analyzed and detection 

limits.

[mg/L, milligrams per liter; μg/L, micrograms per liter]

Description Detection limits

Major ions

Calcium (dissolved and total) 0.02 mg/L

Magnesium (dissolved and total) 0.03 mg/L

Sodium (dissolved and total) 0.1 mg/L

Potassium (dissolved and total) 0.1 mg/L

Chloride (dissolved) 0.1 mg/L

Sulfate (dissolved) 0.2 mg/L

Fluoride (dissolved) 0.1 mg/L

Metals

Arsenic (total) 1 μg/L

Barium (total) 0.5 μg/L

Beryllium (total) 0.5 μg/L

Cadmium (dissolved and total) 0.5 μg/L

Chromium (dissolved and total) 1 μg/L

Cobalt (dissolved and total) 1 μg/L

Copper (total) 2 μg/L

Iron (dissolved and total) 2 μg/L

Lead (dissolved and total) 1 μg/L

Manganese (dissolved and total) 1 μg/L

Nickel (dissolved and total) 1 μg/L

Silver (total) 1 μg/L

Vanadium (total) 1 μg/L

Zinc (dissolved and total) 2 μg/L

Antimony (total) 1 μg/L

Aluminum (dissolved) 3 μg/L

Selenium (total) 1 μg/L
12 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

factor based on surface area of each device. The organism densities from the multiplate samplers and the rock baskets at each 

site were compared with Student’s t test at a 0.05 level of significance (Zar, 1996). No differences were found; therefore, the 

data from both devices at each site were treated as equal replicates. Differences in taxa richness and total abundance of macroinvertebrates were determined by analysis of variance at a 

0.05 level of significance. Data were log-transformed, and comparisons of these differences were computed using the RyanEinot-Gabriel-Welsh Multiple Range Test (SAS Institute Inc., 

1990). 

Separate 2-L water samples were collected during base 

flow on October 31, 1996, and during storm flow on December 

12, 1996. The water samples were tested for toxicity using Ceriodaphnia dubia as a test organism according to the USEPA 

method 1002.0 (Lewis and others, 1994). The chronic C. dubia

test begins with a neonate less than 24 hours old and follows it 

through three reproductive cycles lasting at least 7 days. In this 

study, the numbers of offspring reproduced in water from each 

site during the toxicity tests were compared to offspring 

spawned in moderately hard water (negative control) using 

Dunnett’s test at a 0.05 level of significance (Zar, 1996).

The contaminants near Quail Hollow Landfill most likely 

to affect the indicator organisms were organic solvents and 

trace metals (Hollyday and Byl, 1995). The concentrations of 

the biomarker cytochrome P450 in hepatopancreas (primitive 

liver) tissue of crayfish were evaluated to indicate the potential 

effect of organic solvents. Specific contaminants induce specific isomers of cytochrome P450 in fish livers (Stegeman, 

1989; Stegeman and Lech, 1991). Because of the lack of 

research on isomers of crayfish cytochrome P450, total cytochrome P450 was evaluated in this study. The biomarker metallothionein, a peptide which is induced in organisms to bind to 

metals and render them biologically inactive, was evaluated as 

an indication of the environmental stress caused by cadmium 

and nickel.

From August 1998 to August 1999, crayfish were collected from selected sites on Thompson Creek, and Bennett, 

Anderton, and Anthony Branches (sites 2005, 3005, 3110, 

3200, 5005, and 6005) using baited traps. At each harvest, crayfish were removed from the traps, and the hepatopancreas of 

each crayfish was removed and frozen immediately in liquid 

nitrogen. A set of control crayfish was captured at site 5005. 

The control crayfish were purged for 2 weeks in moderately 

hard water (Lewis and others, 1994) in the laboratory at Middle 

Tennessee State University, Murfreesboro, Tenn., and the 

hepatopancreas tissue was then removed and frozen in liquid 

nitrogen. Samples of hepatopancreas tissue were extracted from 

the frozen tissue and digested in nitric acid. The digested tissue 

samples were analyzed for nickel and cadmium concentrations 

using an absorption spectrophotometer equipped with a Zeeman 

graphite furnace module. 

Crayfish tissue were prepared and centrifuged according to 

the procedures described by Ashley and others (1996). Total 

cytochrome P450 levels in the microsomal preparations were 

determined by carbon monoxide difference spectroscopy 

(Omura and Sato, 1962), and total microsomal protein was 

determined by the Lowery Method (Lowery and others, 1951). 

Supernatant resulting from the centrifuge process was analyzed 

to determine levels of metallothionein present in the hepatopancreas tissue. Metallothionein concentrations were determined 

by the cadmium-hemoglobin affinity assay (Eaton and Toal, 

1982). Concentrations of nickel, cadmium, cytochrome P450, 

and metallothionein present in crayfish from each site were 

compared using analysis of variance at a significance level 

of 0.05.

Table 4. Volatile organic compound analytes and reporting 

limits. 

[All reporting limits in micrograms per liter]

Volatile organic compound analyte Reporting limits

Benzene 1.0 

Bromodichloromethane 1.0 

Bromoform 1.0 

Bromomethane 2.0 

Carbon disulfide 1.0 

Carbon tetrachloride 1.0

Chlorobenzene 1.0 

Chlorodibromomethane 1.0 

Chloroethane 2.0 

Chloroform 1.0

Chloromethane 2.0

1,1-Dichloroethane 1.0 

1,2-Dichloroethane 1.0 

1,1-Dichloroethene 1.0 

Cis-1,2-Dichloroethene 0.50 

Trans-1,2-Dichloroethene 0.50 

1,2 -Dichloropropane 1.0 

Cis-1,3-Dichloropropene 1.0 

Trans-1,3-Dichloropropene 1.0 

Ethylbenzene 1.0 

2-Hexanone 5.0 

Methylene chloride 1.0 

4-Methyl-2-pentanone 5.0 

Styrene 1.0 

1,1,2,2-Tetrachloroethane 1.0 

Tetrachloroethane 1.0 

Toluene 1.0 

1,1,1-Trichloroethane 1.0 

1,1,2-Trichloroethane 1.0 

Trichloroethene 1.0

Vinyl chloride 2.0 

Xylenes (total) 1.0 

2-Butanone 5.0 
Results and Discussion 13

Soil and Sediment Data

In October 1999, soil and sediment samples from 12 sites 

(sites S1-S12, fig. 1) were analyzed for cadmium and nickel 

concentrations. At each sampling location, five separate samples were collected and thoroughly mixed. Three 100-g replicate samples were taken from each mixture. A 0.5-g sample was 

taken from each replicate and digested in heated nitric acid for 

24 hours. Digested samples were diluted appropriately and 

analyzed on an atomic absorption spectrophotometer at Middle 

Tennessee State University. For quality control, six duplicate 

samples were sent to the USGS National Water Quality Laboratory, Denver, Colo., for analysis. 

Results and Discussion

Contaminant movement in the vicinity of the Quail Hollow Landfill is influenced by the complex hydrogeology of the 

Highland Rim, the escarpment, and the Central Basin. Recharge 

to the ground-water system, stream and spring flow, and 

ground-water movement and occurrence are affected by the 

karst hydrogeology of the study area.

A conceptual model of water movement in the vicinity of 

the landfill indicates that rainfall recharges the ground-water 

system and can transport contaminants to surface and ground 

water. Rain falling on the landfill during storms results in sheet 

flow off the landfill and percolation of water through the landfill 

to seeps and fractures. Sheet flow enters Anderton Branch on 

the east and north sides through several tributaries that drain the 

landfill (fig. 1). Brinkley tributary carries surface runoff from 

the landfill and water from Sons Spring to the middle reaches of 

Anderton Branch. Surface water moving to the Powell drainage 

basin can intercept sinkholes and can be diverted to Anderton 

Branch through karst conduits. 

During base-flow conditions, flow to Anderton Branch is 

supplied by ground water issuing from seeps and springs primarily along the trunk stream and from seeps in sedimentcatchment basins adjacent to the landfill. The flow is small but 

perennial, except in the dry or losing reaches on Anderton 

Branch. Water from these springs and seeps could be contaminated as precipitation percolating through the landfill commingles with landfill refuse to form leachate. The leachate is either 

deflected by chert layers in the Fort Payne regolith or continues 

downward through fractures in the chert beds or by flowing off 

the edge of a discontinuous chert layer. Leachate that is 

deflected by the chert moves along the top of the chert layer and 

returns to the surface at seeps or springs along the outcrop of the 

bed. Leachate that continues downward is diluted by mixing 

with ground water migrating along the top of the Chattanooga 

Shale. The contaminated ground water moves downgradient 

and re-enters the surface-water system as seeps and springs 

along the outcrop of the Chattanooga Shale.

Ground water at the top of the Chattanooga Shale also can 

move downward through fractures into the Central Basin aquifer system. Water entering the Central Basin aquifer system in 

this manner discharges to the surface as springs along minor 

confining units in this area of steep hydraulic gradient along the 

Highland Rim escarpment (fig. 5). Sons Spring (fig. 2) is an 

example of this type of contaminated spring. The other types of 

springs and seeps have all been observed in the vicinity of the 

landfill. Kemps seep (fig. 1) emerged at the top of a chert layer, 

and a large sheet flow spring was observed on the east fork of 

Anderton Branch (Hollyday and Byl, 1995, site 3195). 

The landfill is positioned on a spur of the Highland Rim 

bordered on the south by Powell Branch and on the north by 

Anderton Branch. Although both streams appear to have the 

potential to be affected by contaminant movement in the vicinity of the landfill, the conceptual model indicates that Anderton 

Branch is the stream most likely to be affected.

Ground-Water Quality

Ground-water quality in the area of the landfill was evaluated by analyzing water samples from the landfill monitoring 

wells and several domestic water wells near the landfill (fig. 1). 

Domestic well DW1 upgradient of the landfill is completed near 

the base of the Manchester aquifer in a stratigraphic position 

similiar to monitoring wells GW1, GW2, and GW3 at the landfill. Domestic well DW2, also upgradient of the landfill, is completed near the top of the Central Basin aquifer system. Domestic well DW3 downgradient from the landfill is completed 

stratigraphically deeper in the Central Basin aquifer system 

than the discharge point for Sons Spring. Monitoring wells 

GW1, GW2, and GW3 are downgradient of the landfill and are 

completed in the Manchester aquifer at a depth close to the top 

of the Chattanooga Shale. The monitoring wells are positioned 

for sampling ground water almost directly beneath the landfill. 

Sons Spring issues from the top of the Central Basin aquifer 

system in a stratigraphic position similar to DW2. Results of 

analyses of water samples from monitoring wells GW1, GW2, 

and GW3 and domestic wells DW1, DW2, and DW3 were used 

to evaluate local ground-water quality (tables 5 and 6). The analytical results are compared to maximum contaminant levels for 

public drinking waters established by the Tennessee Department of Environment and Conservation (TDEC) (1999) and to 

acute and chronic criteria for fish and aquatic life (Tennessee 

Department of Environment and Conservation, 1999). 

The results of quarterly sampling between March 1995 and 

September 1996 for monitoring wells GW1, GW2, and GW3 

and for Sons Spring were evaluated to identify potential contaminants. Total concentrations of cadmium, nickel, and thallium occasionally exceeded primary maximum contaminant 

levels (PMCLs), and total iron and manganese exceeded secondary maximum contaminant levels (SMCLs) (E.F. Hollyday, 

U.S. Geological Survey, written commun., 1997). Additional 

samples were collected at other springs and domestic wells to 

evaluate background conditions and to identify possible contamination (table 5). Cadmium exceeded PMCLs and TDEC 

fish and aquatic life chronic standards in GW3 (E.F. Hollyday, 
14 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

Table 5. Inorganic constituents in and physical properties of water from surface water, springs, and wells in the Quail Hollow Landfill 

area, Bedford County, Tennessee.

[mg/L, milligrams per liter; μg/L, micrograms per liter; μS/cm, microsiemens per centimeter; <, less than detection limit; NA, not analyzed for; PMCL, primary 

maximum contaminant level for drinking water; SMCL, secondary maximum contaminant level for drinking water; fish and aquatic life standards based on water 

hardness range of 50 to 200 mg/L; Sp., spring; Br., branch; trib., tributary]

U.S. Geological Survey 

Identification No. Site No. Date Time Conditions pH

PMCL (Tennessee Department of Environment and Conservation, 1999)

SMCL (Tennessee Department of Environment and Conservation, 1999) 6.5-8.5

Fish and aquatic life acute standards (Tennessee Department of Environment and Conservation, 1999)

Fish and aquatic life chronic standards (Tennessee Department of Environment and Conservation, 1999) 6.5-9.0

352351086183701 Sons Sp. Site 3090 3/22/1995 6.1

352351086183701 Sons Sp. Site 3090 4/25/1995 6.7

352351086183701 Sons Sp. Site 3090 6/10/1996 7.0

352351086183701 Sons Sp. Site 3090 9/26/1996 6.7

352351086183701 Sons Sp. Site 3090 6/4/1998 7.1

352351086183701 Sons Sp. Site 3090 6/5/1998 0811 Storm flow 7.1

352351086183701 Sons Sp. Site 3090 6/6/1998 0211 Storm flow 6.8

352351086183701 Sons Sp. Site 3090 1/28/1999 1700 Storm flow 7.1

352351086183701 Sons Sp. Site 3090 1/30/1999 0500 Storm flow 6.9

352351086183701 Sons Sp. Site 3090 1/31/1999 1100 Storm flow 6.6

352351086183701 Sons Sp. Site 3090 3/13/1999 0330 Storm flow 7.0

352351086183701 Sons Sp. Site 3090 3/14/1999 1830 Storm flow 7.0

352351086183701 Sons Sp. Site 3090 3/14/1999 2130 Storm flow 6.5

35977607 Anderton Br. Site 3110 12/12/1996 0815 Storm flow 7.8

35977607 Anderton Br. Site 3110 12/12/1996 1015 Storm flow 7.9

35977607 Anderton Br. Site 3110 4/28/1998 1415 Base flow 7.8

35977607 Anderton Br. Site 3110 4/30/1998 1600 Storm flow 7.5

35977607 Anderton Br. Site 3110 5/6/1998 1152 Base flow 7.7

35977607 Anderton Br. Site 3110 5/7/1998 1540 Storm flow 7.5

35977607 Anderton Br. Site 3110 6/4/1998 1032 Storm flow 7.6

35977607 Anderton Br. Site 3110 1/20/1999 1530 Base flow 7.7

35977607 Anderton Br. Site 3110 1/22/1999 2100 Storm flow 7.4

35977607 Anderton Br. Site 3110 3/19/1999 1000 Storm flow 7.4

3597766 Anderton Br. Site 3006 5/6/1998 1350 Base flow 7.9

3597764 Anderton Br. Site 3030 5/6/1998 1515 Base flow 7.4

3597764 Anderton Br. Site 3030 5/7/1998 1400 Pond release 7.2

352413086185001 Anderton Br. Site 3031 5/6/1998 1300 Base flow 7.6

3597762 Brinkley trib. Site 3045 5/6/1998 1455 Base flow 8.1

352418086194101 Painters Sp. 5/6/1998 1625 Base flow 7.4

3597765 J.W. Brinkley Sp. 5/19/1998 1610 Base flow 7.2

35977645 Mitchell Sp. No. 3 5/19/1998 1639 Base flow 7.4

3597754 Joyce King Sp. 5/19/1998 1050 Base flow 7.4

352544086192501 Lower Midway Sp. 5/7/1998 1010 Base flow 7.1

352411086185701 Well DW3 5/7/1996 Base flow 7.2

352411086185701 Well DW3 5/6/1998 Base flow 7.7

352411086185701 Well DW3 5/6/1998 Base flow 7.5

352324086182801 Well DW2 5/7/1996 Base flow 7.5

352313086182001 Well DW1 5/7/1996 Base flow 5.7

352329086181101 Monitoring well GW1 6/10/1996 Base flow 6.0

352329086181101 Monitoring well GW1 9/26/1996 Base flow 5.9

352338086180901 Monitoring well GW2 6/10/1996 1045 Base flow 5.1

352338086180901 Monitoring well GW2 9/26/1996 1426 Base flow 5.1

352343086181801 Monitoring well GW3 6/10/1996 Base flow 5.2

352343086181801 Monitoring well GW3 9/26/1996 Base flow 5.1
Results and Discussion 15

Table 5. Inorganic constituents in and physical properties of water from surface water, springs, and wells in the Quail Hollow Landfill 

area, Bedford County, Tennessee.—Continued

Site No.

Hardness, 

total

(mg/L as CaCO3)

Specific 

conductance 

(μS/cm)

Calcium, 

dissolved 

(mg/L as Ca)

Magnesium, 

total 

(mg/L as Mg)

Magnesium, 

dissolved 

(mg/L as Mg)

Sodium, 

dissolved 

(mg/L as Na)

PMCL None None None None None None

SMCL None None None None None None

Fish and aquatic life acute standards None None None None None None

Fish and aquatic life chronic standards None None None None None None

Sons Sp. Site 3090 200 617 NA NA NA NA

Sons Sp. Site 3090 NA 532 77 NA 6.1 20

Sons Sp. Site 3090 270 660 96 NA 8 21

Sons Sp. Site 3090 NA 784 NA 9 NA NA

Sons Sp. Site 3090 180 483 63 5.7 5.6 18

Sons Sp. Site 3090 110 261 38 3.2 3.2 7.3

Sons Sp. Site 3090 130 330 44 4 3.9 11

Sons Sp. Site 3090 190 520 69 5.8 5.4 14

Sons Sp. Site 3090 160 462 57 5.1 5 14

Sons Sp. Site 3090 120 329 40 3.9 3.9 9.8

Sons Sp. Site 3090 190 500 67 5.5 5.4 16

Sons Sp. Site 3090 120 350 43 3.8 3.9 10

Sons Sp. Site 3090 100 280 35 3.4 3.4 8.8

Anderton Br. Site 3110 47 210 24 5 NA 6.4

Anderton Br. Site 3110 65 218 26 5 NA 10

Anderton Br. Site 3110 36 80 12 NA 1.5 1.7

Anderton Br. Site 3110 60 119 21 3.4 1.8 2.8

Anderton Br. Site 3110 36 83 12 NA 1.4 1.8

Anderton Br. Site 3110 44 100 15 1.6 1.6 1.2

Anderton Br. Site 3110 69 163 24 2.4 2.3 2.5

Anderton Br. Site 3110 39 96 13 NA 1.6 1.9

Anderton Br. Site 3110 60 102 21 2.7 1.9 2.3

Anderton Br. Site 3110 44 105 15 1.8 1.7 2

Anderton Br. Site 3006 99 216 35 NA 2.7 1.9

Anderton Br. Site 3030 96 203 34 2.8 2.7 2.5

Anderton Br. Site 3030 110 194 38 3.2 3.1 2.6

Anderton Br. Site 3031 57 135 20 NA 1.7 2.8

Brinkley trib. Site 3045 130 263 46 NA 3 4.2

Painters Sp. 150 290 55 NA 2.1 0.4

J.W. Brinkley Sp. 130 230 45 NA 3.3 1.6

Mitchell Sp. No. 3 150 265 54 NA 4.6 1.5

Joyce King Sp. 110 230 41 NA 2.9 2.1

Lower Midway Sp. 160 289 53 NA 5.6 1.1

Well DW3 170 1,600 57 NA 7.9 100

Well DW3 260 3,020 74 NA 19 470

Well DW3 170 345 61 NA 5 5.1

Well DW2 83 221 28 NA 3.2 4.7

Well DW1 13 42 3.9 NA 0.7 1.7

Monitoring well GW1 18 265 4 NA 2 23

Monitoring well GW1 NA 157 NA 1 NA NA

Monitoring well GW2 7 32 1.1 NA 1 2.7

Monitoring well GW2 NA 29 NA 1 NA NA

Monitoring well GW3 6 151 1.1 NA 0.8 16

Monitoring well GW3 NA 148 NA 1 NA NA
16 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

Table 5. Inorganic constituents in and physical properties of water from surface water, springs, and wells in the Quail Hollow Landfill 

area, Bedford County, Tennessee.—Continued

Site No.

Potassium, 

total

(mg/L as K)

Potassium, 

dissolved 

(mg/L as K)

Chloride, 

dissolved 

(mg/L as Cl)

Sulfate, 

dissolved (mg/L 

as SO4)

Arsenic,

total

(μg/L as As)

Barium,

total

(μg/L as Ba)

PMCL None None None None 50 2,000

SMCL None None 250 250 None None

Fish and aquatic life acute standards None None None None 360 None

Fish and aquatic life chronic standards None None None None 190 None

Sons Sp. Site 3090 NA NA NA NA NA NA

Sons Sp. Site 3090 NA 5.2 34 26 NA NA

Sons Sp. Site 3090 NA 6.8 NA NA <1 NA

Sons Sp. Site 3090 6.7 NA 59 42 <1 29

Sons Sp. Site 3090 7.3 7.2 36 27 <1 42

Sons Sp. Site 3090 3.7 3.6 12 14 2 35

Sons Sp. Site 3090 4.8 4.3 18 16 <1 31

Sons Sp. Site 3090 5.3 5.2 35 29 <1 27

Sons Sp. Site 3090 5.7 6 30 27 <1 31

Sons Sp. Site 3090 4.3 4.5 18 18 <1 31

Sons Sp. Site 3090 4.8 4.8 34 27 <1 28

Sons Sp. Site 3090 3.8 3.8 19 17 <1 30

Sons Sp. Site 3090 3.2 3.3 15 14 <1 26

Anderton Br. Site 3110 7 4.4 NA NA <1 300

Anderton Br. Site 3110 7.2 6.5 NA NA <1 80

Anderton Br. Site 3110 NA 1 3 4.2 NA NA

Anderton Br. Site 3110 5.4 2.7 NA NA 4.8 82

Anderton Br. Site 3110 NA 0.8 2.9 3.6 NA NA

Anderton Br. Site 3110 1.8 1.7 3.1 4.9 <1 13

Anderton Br. Site 3110 3.2 3.2 7.6 9.4 <1 17

Anderton Br. Site 3110 NA 1.2 4.4 5.5 NA NA

Anderton Br. Site 3110 2.6 2.5 4.6 6.7 3.4 120

Anderton Br. Site 3110 1.3 1.4 3.8 5.2 <1 15

Anderton Br. Site 3006 NA 1.4 3.5 5.6 NA NA

Anderton Br. Site 3030 1.2 1 3.8 6 <1 14

Anderton Br. Site 3030 3.9 1.4 3.1 7.2 5.9 84

Anderton Br. Site 3031 NA 1.4 4.5 4.8 NA NA

Brinkley trib. Site 3045 NA 2 7.8 6.9 NA NA

Painters Sp. NA 0.5 1.6 3.1 NA NA

J.W. Brinkley Sp. NA 1 2.7 3.9 NA NA

Mitchell Sp. No. 3 NA 0.8 2.1 5.1 NA NA

Joyce King Sp. NA 0.9 2.5 4.9 NA NA

Lower Midway Sp. NA 1.3 4.1 9.7 NA NA

Well DW3 NA 2.6 220 240 NA NA

Well DW3 NA 8.2 320 840 NA NA

Well DW3 NA 1.2 3.6 10 NA NA

Well DW2 NA 0.5 2.3 11 NA NA

Well DW1 NA 0.1 2.3 1.5 NA NA

Monitoring well GW1 NA 3.8 NA NA <1 NA

Monitoring well GW1 2 NA 21 0.3 <1 89

Monitoring well GW2 NA 0.3 NA NA <1 NA

Monitoring well GW2 0.2 NA <0.1 <0.2 1.1 13

Monitoring well GW3 NA 1.2 NA NA <1 NA

Monitoring well GW3 1 NA 36 4.4 <1 130
Results and Discussion 17

Table 5. Inorganic constituents in and physical properties of water from surface water, springs, and wells in the Quail Hollow Landfill 

area, Bedford County, Tennessee.—Continued

Site No.

Barium, 

dissolved 

(μg/L as Ba)

Beryllium, 

total

 (μg/L as Be)

Cadmium, 

total

(μg/L as Cd)

Cadmium, 

dissolved 

(μg/L as Cd)

Chromium, 

total

(μg/L as Cr)

Cobalt,

total

 (μg/L as Co) 

Cobalt, 

dissolved 

(μg/L as Co) 

PMCL 2,000 4 5 5 100 None None

SMCL None None None None None None None

Fish and aquatic life acute standards None None None 1.8-8.6 None None None

Fish and aquatic life chronic standards None None None 0.7-2.0 100 None None

Sons Sp. Site 3090 NA NA NA NA NA NA NA

Sons Sp. Site 3090 NA NA NA 3.1 NA NA NA

Sons Sp. Site 3090 36 NA NA 1.1 NA NA 130

Sons Sp. Site 3090 NA <0.5 1 NA <1 140 NA

Sons Sp. Site 3090 NA <0.5 1.5 2.6 <1 78 NA

Sons Sp. Site 3090 NA <0.5 <0.5 0.8 <1 46 NA

Sons Sp. Site 3090 NA <0.5 0.6 0.8 <1 42 NA

Sons Sp. Site 3090 NA <0.5 1.3 1.4 <1 74 NA

Sons Sp. Site 3090 NA <0.5 1.2 2.7 <1 65 NA

Sons Sp. Site 3090 NA <0.5 1 1.6 <1 37 NA

Sons Sp. Site 3090 NA <0.5 1.2 1.4 <1 68 NA

Sons Sp. Site 3090 NA <0.5 1.3 1.9 <1 36 NA

Sons Sp. Site 3090 NA <0.5 0.7 0.7 <1 29 NA

Anderton Br. Site 3110 NA 1.6 6 NA 45 50 NA

Anderton Br. Site 3110 NA <0.5 2 NA 22 20 NA

Anderton Br. Site 3110 NA <0.5 NA 0.7 NA NA NA

Anderton Br. Site 3110 NA <0.5 <0.5 <0.5 8.1 9 NA

Anderton Br. Site 3110 NA NA NA <0.5 NA NA NA

Anderton Br. Site 3110 NA 0.7 <0.5 <0.5 <1 <1 NA

Anderton Br. Site 3110 NA 0.5 <0.5 <0.5 <1 <1 NA

Anderton Br. Site 3110 NA NA NA <0.5 NA NA NA

Anderton Br. Site 3110 NA <0.5 <0.5 <0.5 4.3 20 NA

Anderton Br. Site 3110 NA <0.5 0.5 <0.5 <1 1.5 NA

Anderton Br. Site 3006 NA NA NA <0.5 NA NA NA

Anderton Br. Site 3030 NA NA <0.5 <0.5 <1 <1 NA

Anderton Br. Site 3030 NA NA <0.5 1.6 12 7.3 NA

Anderton Br. Site 3031 NA NA NA <0.5 NA NA NA

Brinkley trib. Site 3045 NA NA NA <0.5 NA NA NA

Painters Sp. NA NA NA <0.5 NA NA NA

J.W. Brinkley Sp. NA NA NA <0.5 NA NA NA

Mitchell Sp. No. 3 NA NA NA <0.5 NA NA NA

Joyce King Sp. NA NA NA <0.5 NA NA NA

Lower Midway Sp. NA NA NA <0.5 NA NA NA

Well DW3 NA NA NA <1.0 NA NA NA

Well DW3 NA NA NA <0.5 NA NA NA

Well DW3 NA NA NA <0.5 NA NA NA

Well DW2 NA NA NA <1 NA NA NA

Well DW1 NA NA NA <1 NA NA NA

Monitoring well GW1 15 <1 NA <0.5 NA NA 99

Monitoring well GW1 NA <1 <0.5 NA 3.1 58 NA

Monitoring well GW2 17 <1 <0.5 <0.5 NA NA 6

Monitoring well GW2 NA <1 <0.5 NA <1 2.3 NA

Monitoring well GW3 130 <1 NA <0.5 NA NA 10

Monitoring well GW3 NA <1 <0.5 NA 2 7.2 NA
18 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

Table 5. Inorganic constituents in and physical properties of water from surface water, springs, and wells in the Quail Hollow Landfill 

area, Bedford County, Tennessee.—Continued

Site No.

Copper,

total 

(μg/L as Cu)

Iron,

total

(μg/L as Fe)

Iron, 

dissolved 

(μg/L as Fe)

Lead,

total

(μg/L as Pb) 

Lead, 

dissolved 

(μg/L as Pb) 

Manganese, 

total 

(μg/L as Mn)

Manganese, 

dissolved 

(μg/L as Mn)

PMCL None None None 5 None None None

SMCL 1,000 300 300 None 50 50

Fish and aquatic life acute standards 9.2-34.1 None None 33.8-197 None None None

Fish and aquatic life chronic standards 6.5-21.4 None None 1.3-7.7 None None None

Sons Sp. Site 3090 NA NA 5,700 NA NA NA NA

Sons Sp. Site 3090 NA NA 80 NA <1 NA 2,800

Sons Sp. Site 3090 1.3 NA 330 NA <1 NA 4,800

Sons Sp. Site 3090 1.5 160 NA <1 NA 4,500 NA

Sons Sp. Site 3090 16 483 17 <1 <1 2,600 2,600

Sons Sp. Site 3090 35 21,530 4.5 <1 <1 1,100 870

Sons Sp. Site 3090 17 1,600 3.6 <1 <1 1,500 1,400

Sons Sp. Site 3090 11 172 13 <1 <1 2,300 2,200

Sons Sp. Site 3090 8.4 161 8.4 <1 <1 2,100 2,000

Sons Sp. Site 3090 7.2 250 4.9 <1 <1 1,300 1,300

Sons Sp. Site 3090 20 310 4.8 <1 <1 2,300 2,200

Sons Sp. Site 3090 11 814 7.4 1.2 <1 1,300 1,300

Sons Sp. Site 3090 9.6 430 5.2 <1 <1 1,100 1,000

Anderton Br. Site 3110 59 72,000 NA 59 NA 2,900 NA

Anderton Br. Site 3110 39 17,000 NA 22 NA 1,100 NA

Anderton Br. Site 3110 NA NA 10 NA <1 NA 8.8

Anderton Br. Site 3110 15 12,294 10 8.2 <1 760 2.8

Anderton Br. Site 3110 NA NA 20 NA <1 NA 7.7

Anderton Br. Site 3110 <1 330 120 <1 4 63 47

Anderton Br. Site 3110 10 469 33 <1 <1 45 6.4

Anderton Br. Site 3110 NA NA 13 NA <1 NA 6.2

Anderton Br. Site 3110 24 8,100 254 17 <1 4,300 270

Anderton Br. Site 3110 7.9 850 68 1.6 <1 220 51

Anderton Br. Site 3006 NA NA 120 NA <1 NA 26

Anderton Br. Site 3030 <1 210 30 4.7 1 25 11

Anderton Br. Site 3030 7.1 10,874 280 5.7 9 260 150

Anderton Br. Site 3031 NA NA 30 NA <1 NA 16

Brinkley trib. Site 3045 NA NA 150 NA <1 NA 39

Painters Sp. NA NA 10 NA <1 NA 3.7

J.W. Brinkley Sp. NA NA 5 NA <1 NA 7.1

Mitchell Sp. No. 3 NA NA 10 NA 1 NA 3.5

Joyce King Sp. NA NA 5 NA <1 NA 3.5

Lower Midway Sp. NA NA 250 NA 2 NA 39

Well DW3 NA NA 10 NA 1 NA 25

Well DW3 NA NA 100 NA <1 NA 72

Well DW3 NA NA 40 NA 2 NA 13

Well DW2 NA NA 10 NA 1 NA 41

Well DW1 NA NA 620 NA 1 NA 870

Monitoring well GW1 NA NA 440 NA 1 NA 24,000

Monitoring well GW1 2 55 NA <1 1 12,000 NA

Monitoring well GW2 NA NA 9 NA 1 NA 2,000

Monitoring well GW2 2 550 NA 3.2 NA 960 NA

Monitoring well GW3 NA NA 1,200 NA 1 NA 6,500

Monitoring well GW3 1.7 1,200 NA 1.2 NA 5,300 NA
Results and Discussion 19

Table 5. Inorganic constituents in and physical properties of water from surface water, springs, and wells in the Quail Hollow Landfill 

area, Bedford County, Tennessee.—Continued

Site No.

Nickel,

total 

(μg/L as Ni)

Nickel,

dissolved 

(μg/L as Ni)

Vanadium, 

total

(μg/L as V)

Zinc, 

total

(μg/L as Zn)

Zinc, 

dissolved 

(μg/L as Zn)

Antimony, 

total

(μg/L as Sb)

Aluminum, 

dissolved

(μg/L as Al)

PMCL 100 100 None None None 6 None

SMCL None None None 5,000 5,000 None 200

Fish and aquatic life acute standards None 789-2,549 None None 120 None None

Fish and aquatic life chronic standards None 87.7-283 None None 106 None None

Sons Sp. Site 3090 NA NA NA NA NA NA NA

Sons Sp. Site 3090 NA 110 NA NA 64 NA 20

Sons Sp. Site 3090 NA 150 NA NA 67 NA NA

Sons Sp. Site 3090 170 NA <1 78 71 <1 NA

Sons Sp. Site 3090 98 99 <1 66 27 <1 13

Sons Sp. Site 3090 56 38 <1 88 40 <1 11

Sons Sp. Site 3090 55 53 <1 43 NA <1 8.7

Sons Sp. Site 3090 94 87 <1 85 100 <1 7

Sons Sp. Site 3090 83 81 <1 72 100 <1 7.2

Sons Sp. Site 3090 50 50 <1 43 58 <1 8

Sons Sp. Site 3090 88 88 <1 56 57 <1 16

Sons Sp. Site 3090 49 49 <1 43 53 <1 13

Sons Sp. Site 3090 41 41 <1 30 32 <1 12

Anderton Br. Site 3110 71 NA 110 210 NA 1 NA

Anderton Br. Site 3110 40 NA 34 140 NA 1 NA

Anderton Br. Site 3110 NA 1.5 NA NA 3.8 <1 14

Anderton Br. Site 3110 22 1.3 19 59 1.8 1.8 31

Anderton Br. Site 3110 NA 1.9 NA NA 4.6 NA 24

Anderton Br. Site 3110 2.1 1.8 <1 4.7 21 <1 84

Anderton Br. Site 3110 4.1 2.7 <1 12 13 <1 50

Anderton Br. Site 3110 NA <1 NA NA 5 NA 19

Anderton Br. Site 3110 35 3.7 1.2 58 6.2 <1 219

Anderton Br. Site 3110 5.3 3.4 <1 8.6 7.8 <1 75

Anderton Br. Site 3006 NA <1 NA NA 3.5 NA 39

Anderton Br. Site 3030 1.5 <1 <1 9.3 5.6 <1 28

Anderton Br. Site 3030 7.9 3.1 31 17 45 <1 890

Anderton Br. Site 3031 NA 1.2 NA NA 15 NA 40

Brinkley trib. Site 3045 NA <1 NA NA 1.7 NA 51

Painters Sp. NA 1.3 NA NA 4 NA 16

J.W. Brinkley Sp. NA <1 NA NA 5 NA 12

Mitchell Sp. No. 3 NA <1 NA NA 6.4 NA 10

Joyce King Sp. NA <1 NA NA 5.6 NA 9.5

Lower Midway Sp. NA <1 NA NA 9.1 NA 270

Well DW3 NA <10 NA NA 6 NA <20

Well DW3 NA 1.2 NA NA 8.6 NA 40

Well DW3 NA 2 NA NA 5.4 NA 29

Well DW2 NA 10 NA NA 5 NA <20

Well DW1 NA <1 NA NA 30 NA <20

Monitoring well GW1 NA 240 NA NA 37 NA NA

Monitoring well GW1 160 NA <1 38 NA <1 NA

Monitoring well GW2 NA 23 NA NA 16 NA NA

Monitoring well GW2 16 NA <1 21 NA <1 NA

Monitoring well GW3 NA 94 NA NA 35 NA NA

Monitoring well GW3 110 NA <1 48 NA <1 NA
Table 6. Volatile organic compounds from surface sites, springs, and wells near Quail Hollow Landfill, Bedford County, Tennessee, 1995-98. [MCL, maximum contaminant level for drinking water as established by the State of Tennessee (Tennessee Department of Environment and Conservation, 1999); μg/L, microgr

below the reporting limit; ND, not detected; Sp., spring; Br., branch] USGS site identification number Site number Date Time Conditions Benzene (μg/L) Chloro- benzene (μg/L) 1,4- Dichloro- benzene (μg/L) Chloro- ethane (μg/L) 1,1- Dichloro- ethane (μg/L) 1,1- Dichloro- ethene (μg/L) Cis

Dich

eth

(μ

Primary maximum contaminant level 5 100 -- -- -- 7 70 352351086183701 Sons Sp. Site 3090 3/22/1995 ND ND ND ND ND ND ND 352351086183701 Sons Sp. Site 3090 6/10/1996 ND ND ND ND 7.2 ND 0.5352351086183701 Sons Sp. Site 3090 9/26/1996 ND ND ND ND 6.3 ND 1.1 352351086183701 Sons Sp. Site 3090 6/4/1998 2311 ND ND ND ND 12 ND 0.335977607 Anderton Br. Site 3110 6/4/1998 1032 Storm flow ND ND ND ND ND ND ND 352329086181101 Monitoring well GW1 6/10/1996 Base flow 2.9 0.27 1 4.8 17 0.40 e 4.4 352329086181101 Monitoring well GW1 9/26/1996 Base flow 1.7 ND 0.39 e 4.1 14 0.44 e 3.9 352338086180901 Monitoring well GW2 6/10/1996 1045 Base flow 0.78 e ND ND 3.9 5.6 0.45 e 1.1 352338086180901 Monitoring well GW2 9/26/1996 1426 Base flow 1.2 ND ND 5.3 9 0.46 e 2.4 352343086181801 Monitoring well GW3 6/10/1996 Base flow 0.38 e ND ND 0.77 e 1.1 ND ND 352343086181801 Monitoring well GW3 9/26/1996 Base flow 0.33 e ND ND ND 0.65 e ND ND 

Methylene chloride (μg/L) Trichloro- fluoro- methane (μg/L) Tetrachloro- ethene (μg/L) 1,1,1- Trichloro- ethane (μg/L) Trichloro- ethene (μg/L) Vinyl chloride (μg/L) Xyle

to

(μ

Primary maximum contaminant level 5 -- 5 200 5 2 10,00352351086183701 Sons Sp. Site 3090 3/22/1995 ND ND ND ND ND ND N352351086183701 Sons Sp. Site 3090 6/10/1996 ND ND 0.69 e 1.7 0.23 e ND N352351086183701 Sons Sp. Site 3090 9/26/1996 ND ND 0.55 e 0.83 e 0.29 e ND N352351086183701 Sons Sp. Site 3090 6/4/1998 2311 ND ND 0.73 e 6.4 0.29 e ND N35977607 Anderton Br. Site 3110 6/4/1998 1032 Storm flow ND ND ND ND ND ND N352329086181101 Monitoring well GW1 6/10/1996 Base flow 1.8 ND 1.7 0.87 e 1.8 5.3 N352329086181101 Monitoring well GW1 9/26/1996 Base flow 1.9 0.86 e 2.3 1.5 2.2 3.7 N352338086180901 Monitoring well GW2 6/10/1996 1045 Base flow 3.9 3.7 6.7 2.5 3.5 11 352338086180901 Monitoring well GW2 9/26/1996 1426 Base flow 7.6 0.76 7.4 2.9 5 9.4 352343086181801 Monitoring well GW3 6/10/1996 Base flow ND ND 0.21 e 0.21 e ND 0.8e N352343086181801 Monitoring well GW3 9/26/1996 Base flow ND ND ND ND ND ND 
Results and Discussion 21

U.S. Geological Survey, written commun., 1997) but was not 

detected above detection limits at wells DW1, DW2, or DW3. 

Dissolved cobalt was detected in GW1 (99 μg/L) and Sons 

Spring (130 μg/L) but was not analyzed in the background 

wells (table 5). The USEPA does not presently have an ambient 

water-quality criterion for cobalt; however, research has indicated that the levels present in these waters are not toxic to fish 

and at times may exceed the no observable effect concentration 

for invertebrates (Diamond and others, 1992).

Dissolved manganese and iron often exceeded the SMCLs 

in samples collected from GW1, GW2, and GW3 with concentrations as high as 24,000 μg/L for dissolved manganese and 

1,200 μg/L for dissolved iron. In Sons Spring, concentrations of 

these metals also exceeded SMCLs with 4,800 μg/L for dissolved manganese and 5,700 μg/L for dissolved iron. Dissolved 

manganese and iron concentrations were considerably less in 

the upgradient well DW1 with values of 870 μg/L for dissolved 

manganese and 620 μg/L for dissolved iron, which may reflect 

background concentrations in the area. Nickel concentrations 

exceeded the PMCL and TDEC fish and aquatic chronic criteria 

in samples collected from GW1, GW3, and Sons Spring, but 

was not detected above detection limits in the domestic wells 

(table 5). Thallium concentrations exceeded the PMCL at Sons 

Spring (E.F. Hollyday, U.S. Geological Survey, written commun., 1997). Chloride concentrations have increased from 3 to 

59 mg/L in Sons Spring since the landfill began operating in 

1974 (fig. 6). High concentrations of chloride were detected at 

DW3 on two occasions (table 5); however, these high concentrations are thought to be the result of inadequate purging as 

indicated by the duplicate samplings on May 6, 1998. 

Among VOCs detected at the landfill, methylene chloride, 

tetrachloroethene (PCE), trichloroethene (TCE), and vinyl 

chloride equaled or exceeded PMCLs in ground water (table 6). 

Methylene chloride, a common laboratory solvent, was 

the only VOC detected in the 

samples of water from domestic wells; these results are not 

included in table 6. Methylene chloride detections were 

below PMCLs and probably 

were related to laboratory procedures rather than presence 

at the site. The organic compounds 1,1-dichloroethane 

(DCA) and 1,1-dichloroethene (DCE) also were 

detected (DCA in Sons 

Spring, GW1, GW2, and 

GW3 and DCE in GW1 and 

GW2). No PMCL has been 

established for DCA, and the 

levels of DCE are well below 

the PMCL (table 6). No fish 

and aquatic chronic criteria 

have been established for 

DCE or DCA by TDEC.

Surface-Water Quality

Surface-water quality near the landfill was monitored in 

Anderton Branch and Sons Spring. Water quality at these sites 

was compared to surface-water sites on Anthony Branch and 

Yasui Spring on Powell Branch. Continuous water-quality 

monitors were used to identify water-quality changes during 

storms. Water-quality samples were analyzed for major constituents, trace metals, and organic compounds. The analytical 

results are compared to maximum contaminant levels for public 

drinking water established by TDEC (1999) and are compared 

to acute and chronic criteria for fish and aquatic life (Tennessee 

Department of Environment and Conservation, 1999).

Anderton Branch

Continuous monitoring of Anderton Branch at site 3110 

during 1996, 1998, and 1999 indicated increases in specific 

conductance associated with increased gage height after storms. 

During a storm on December 12, 1996 (fig. 7), the water in 

Anderton Branch changed from clear to a cloudy reddish color 

and the specific conductance increased from about 100 μS/cm 

to greater than 200 μS/cm. During the same storm, however, 

Anthony Branch showed no change in clarity or color, and the 

specific conductance decreased from about 160 to 120 μS/cm 

(fig. 7).

Water samples were collected from Anderton Branch during base- and storm-flow periods. Analysis of these samples 

indicated increased concentrations of iron, manganese, cadmium, lead, and nickel as compared with concentrations of 

these same metals detected during base flow (fig. 8). Concentrations of iron and manganese exceeded SMCLs on each 
22 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

storm-flow sampling date with the exception of June 4, 1998, 

when the manganese concentration was only 5 μg/L below the 

SMCL. Lead concentration exceeded PMCLs and TDEC fish 

and aquatic life standards (table 5) in December 1996. Cadmium exceeded PMCLs in December 1996 and TDEC fish and 

aquatic life standards in May 1998, but showed levels as low as 

the base-flow concentrations on the remaining sampling dates 

(table 5 and fig. 8). 

Analysis of samples for VOCs collected from Anderton 

Branch during a storm on June 4, 1998, indicated only the presence of 2-butanone at an estimated concentration (2.1 μg/L) 

below the reporting limit (table 6). The compound 2-butanone, 

a common laboratory contaminant, was not detected in any 

other sample and is not considered to be relevant to Anderton 

Branch.

Dissolved-solids concentrations in rainwater are low and 

storm runoff entering a stream typically is associated with a 

decrease in specific conductance. The increased metal concentrations detected in water samples from site 3110 during storm 

flow, along with increased specific conductance, leads to the 

hypothesis that a contaminant source upstream of the sampling 

site on Anderton Branch is being flushed by runoff from intense 

rains. 

Chloride-load calculations indicate that Anderton Branch 

contains greater amounts of chloride than Anthony Branch. 

Studies of the stream indicate two point sources of chloride: 

Brinkley tributary, which drains a pond receiving water from 

both the landfill and Sons Spring; and a barnyard that straddles 

Anderton Branch (fig. 9). The discharge from Sons Spring 

flows a short distance on the surface before submerging into the 

gravel tributary that discharges into Brinkley Pond. Surfacewater runoff from the landfill also discharges into and is 

detained in Brinkley Pond, which is a constructed pond that 

maintains a low water level because of a swallet in the northwestern corner of the pond. Because of the low water level, the 

pond resembles a wetland with ample amounts of vegetation 

present. Water escaping from the swallet, as well as seepage 

under the dam, results in a perennial tributary that drains into 

Anderton Branch. This tributary is a source of increased chloride load in Anderton Branch. 

Sons Spring 

Surface discharge from Sons Spring occurs about 10 ft 

below the Chattanooga Shale at a location approximately 300 ft 

from the toe of the landfill (fig. 2). Mean flow during the study 

period was 0.024 ft3

/s. Continuous monitoring during 1996, 

1998, and 1999 indicated a distinct pattern of specificconductance variations related to rainfall. Specific conductance 

shows an abrupt short-term increase beginning several hours 

after the onset of rainfall, followed by a sharp decrease (fig. 10). 

After the decrease, specific conductance gradually increases 

over the next several days and returns to pre-storm levels. Previous studies indicate that abrupt water-quality changes in 

response to storms are common to springs in mature karst environments (Quinlan and Alexander, 1987; Hess and White, 

1988; Dreiss, 1989; Brown and Ewers, 1991; Ryan and 

Meiman, 1996; Farmer and Williams, 2001). 

Comparisons of specific conductance to concentrations of 

total cobalt, dissolved manganese, dissolved nickel, dissolved 

chloride, dissolved iron, and dissolved magnesium during the 

storm flow and through the recovery period indicate a direct 
Results and Discussion 23
24 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County
Results and Discussion 25

correlation between concentrations of these constituents and the 

specific conductance (fig. 11). Total iron concentrations tend to 

have an opposite response (fig. 11). Dissolved iron showed a 

direct correlation with specific conductance for sampling dates 

in June 1998 and January 1999, but showed an increase and then 

a decrease for the March 1999 sampling date, which was identical to the response of total iron for this sampling date (fig. 11). 

The contaminants identified at Sons Spring apparently are 

being diluted with the influx of rainwater. One possibility is that 

the recharge to Sons Spring during storms is through a solution 

channel or fracture near the face of the escarpment and not from 

water passing through the landfill. Another possibility is that 

the storm recharge is passing through the contaminants in the 

landfill without mobilizing them, causing dilution of contaminants already in the ground-water reservoir feeding the spring.

Chloride concentrations in samples not associated with 

storms at Sons Spring have increased from 3 mg/L in 1974 to 

59 mg/L in 1996 (fig. 6). Specific conductance has increased 
26 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

from less than 300 to more than 800 μS/cm (fig. 10). The control spring, Yasui Spring (site 4050), had a specific conductance 

of 330 μS/cm and a chloride concentration of 8 mg/L in 1995, 

considerably lower than values at Sons Spring (Hollyday and 

Byl, 1995). The increased chloride concentrations and specific 

conductance values indicate the effect of the landfill on Sons 

Spring. 

From 1995 through 1999, PMCLs of inorganic and trace 

constituents frequently were exceeded in samples from Sons 

Spring. Nickel concentrations exceeded PMCLs, and iron and 

manganese concentrations exceeded SMCLs. Dissolved zinc 

ranged from 27 to 100 μg/L. The 100-μg/L concentration 

approaches but does not exceed the TDEC fish and aquatic life 

standards. Total cobalt ranged from 29 to 140 μg/L, and dissolved cobalt was 130 μg/L on June 10, 1996 (table 5). No 

water-quality standards have been established for cobalt. Iron, 

manganese, and nickel (table 2) are present as natural constituents of the soil and sediments in the area. Analysis of water 

sampled during base flow in Anderton Branch (table 5) and at 

the control sites on Anthony Branch and Yasui Spring during 

the 1995 reconnaissance study (Hollyday and Byl, 1995) indicated low dissolved concentrations for these metals; iron less 

than 36 μg/L, manganese less than 

25 μg/L, and nickel less than 

10 μg/L. In Sons Spring during the 

current study, dissolved levels are 

high (iron 3.6 to 5,700 μg/L, manganese 870 to 4,800 μg/L, and 

nickel 38 to 150 μg/L) (table 5). 

Landfill activity may have caused 

increased mobilization of iron, 

manganese, and nickel from naturally occurring sources. The presence of chlorinated solvents in 

water samples from Sons Spring 

indicates that these contaminants 

originated in the landfill, but no 

detections exceeded PMCLs. TCE 

was detected four times and DCE 

six times (E.F. Hollyday, U.S. 

Geological Survey, written commun., 1997).

Benthic Macroinvertebrates

Benthic macroinvertebrates 

were collected at nine sites near 

the landfill to determine the abundance of organisms (fig. 12) and 

the number of different taxa at 

each site (fig. 13). The sites sampled included a control site on 

Anthony Branch (site 2026), sites 

on Anderton Branch upstream of 

the landfill (sites 3185 and 3200), 

sites on Anderton Branch adjacent to the landfill (sites 3040, 

3110, 3135), Sons Spring (site 3090), Anderton Branch (site 

3030) downstream of the resurgence of Anderton Branch and 

Harrison Cave Spring, and a location near the mouth of Anderton Branch (site 3005).

The high mean abundance (939 organisms per square 

meter) for May 1996 was at site 3030 downstream of the landfill. The mean abundance at site 3030 was not statistically different from all other sites except for Sons Spring (site 3090). 

The mean low abundance (47 organisms per square meter) was 

at site 3090, Sons Spring, and was statistically different from all 

other sites (fig. 12). The high mean taxa richness (nine taxa) 

was present at site 3135 and the low mean taxa richness (one 

taxa), at site 3090 (fig. 13). The mean taxa richness for site 3030 

is lower than mean taxa richness at sites adjacent to (site 3135) 

and upstream of the landfill (site 3200); however, multiple comparison tests show that overlap occurs among these sites and all 

other sites upstream of, adjacent to, and downstream of the 

landfill (fig. 13). 

An analysis of variance (95-percent confidence level) of 

abundance and taxa richness data from the sites upstream of, 

adjacent to, and downstream of the landfill indicated a statistical 
Results and Discussion 27

difference at sites during different seasons. A multiple comparison test was used to group similar sites (not different statistically). Similar sites are designated on figures 12, 13, and 14 by 

the same letter label. Groups that are statistically different are 

assigned different letters. Some groups overlap, are similar to 

multiple groups, and are labeled with multiple letters. For 

example, abundance of macroinvertebrates in December 1996 

(fig. 12) shows sites 3005, 3030, and 3090 to be statistically different and are designated C, A, and D, respectively. Site 3040 

has an ABC designation indicating no difference between this 

site and sites 3005 (C), 3030 (A), 3110 (BC), 3200 (ABC), and 

2026 (AB). Similarly site 2026 is designated AB indicating no 

difference statistically between site 2026 and sites 3030 (A), 

3040 (ABC), 3110 (BC), and 3200 (ABC).

The high mean abundance 

(1,299 organisms per square meter) 

for September 1996 was present at 

site 3030 and the low mean abundance (170 organisms per square 

meter) at site 3090. The mean abundance for both of these sites is statistically different from all other 

sites, which are not statistically different and are grouped by the multiple comparison test into one category (fig. 12). The high mean taxa 

richness (six taxa) for September 

1996 occurs at site 3135, which is 

not statistically different from site 

3200. The low mean taxa richness 

(less than one organism) occurs at 

site 3090 (Sons Spring), and is statistically different from all other 

sites. The mean number of taxa is 

low for site 3030 but not statistically 

different from sites 3005, 3040, 

3110, and 3185. The multiple comparison test indicates overlap occurs 

among sites 3005, 3040, 3110, and 

3185 and among sites 3135 and 

3200 (fig. 13).

The high mean abundance 

(1,525 organisms per square meter) 

for December 1996 was present 

again at site 3030, and the low mean 

abundance (2 organisms per square 

meter) again at site 3090. The mean 

abundance at site 3090, Sons Spring 

is statistically different from all 

other sites. Site 3030 is different 

from sites 3110 and 3005 but is not 

different from all other sites on 

Anderton Branch and the control 

site 2026 on Anthony Branch. The 

mean abundance at site 3005 is low 

but is not statistically different from 

sites adjacent to the landfill (sites 3040 and 3110) and upstream 

of the landfill (site 3200). The high mean taxa richness (10 taxa) 

for December 1996 was at site 3040, which was not different 

from the control site 2026 on Anthony Branch and site 3110 

adjacent to the landfill or site 3200 upstream of the landfill. The 

lowest mean taxa richness (less than one) again occurred at site 

3090, which is statistically different from all other sites. Sites 

3005 and 3030 have mean taxa richness values in the middle 

range, and are different from all other sites (fig. 13). 

The high mean abundance (767 organisms per square 

meter) for May 1997 was again present at site 3030. The mean 

abundance at this site was not different from site 3005, and both 

are not different from site 3040 adjacent to the landfill and site 

3200 upstream of the landfill. The low mean abundance (three 
28 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

organisms per square meter) at site 3090 was statistically different from all other sites. The mean abundance at site 3110 was 

statistically different from the lowest and the highest sites but 

was not statistically different from the remainder of the sites 

(fig. 12). The high mean taxa richness for May 1997 occurred at 

site 3005 near the mouth of Anderton Branch. The mean taxa 

richness at each site on Anderton Branch tends to increase 

downstream, but overlap exists among all of the sites except for 

site 3090. The low mean taxa richness (less than one) occurs at 

site 3090, Sons Spring, and is statistically different from all of 

the other sites (fig. 13).

Although seasonal variations exist, Sons Spring (site 

3090) is consistently lower in mean abundance and mean taxa 

richness from all other sites. Sons Spring had the lowest mean 

abundance and lowest mean taxa richness during all four sampling events. Among the other sites some significant differences 

are apparent, but in general, the multiple comparison tests show 

that considerable overlap exists among the sites downstream of, 

adjacent to, and upstream of the landfill. 

Site 3030 is high in abundance and low in taxa richness. 

Although low in taxa, this site is considered to be a healthy site. 

Physically different from the other sites, site 3030 is shady in 

spring, summer, and fall and has shallow water and a mosscovered substrate. The site also is downstream from the resurgence of Anderton Branch at Harrison Cave Spring where the 

water resurges from the upstream losing reach on Anderton 

Branch and mixes with the water from Harrison Spring Cave. 

The substrate is dominated by snails, and the moss contains 

high densities of the amphipod Gammarus.

Site 3005 (near the mouth of Anderton Branch) showed 

low values of taxa richness for the first three samplings; however, several samplers were lost during storm conditions. 

Because of the loss of samplers, the number of traps was 

increased in May 1997 for site 3005. The data collected in 

May 1997 are considered to be the most representative data for 

this site, having higher values of abundance and taxa richness 

than during the other sampling periods (figs. 12 and 13). 

In October 1998, benthic invertebrate samples were collected near site 3005. Counts of abundance and taxa richness 

were statistically compared to the December 1996 sampling by 

using a Student’s t test (significance 0.05). Results of this 

analysis indicated significant increases in abundance and 
Results and Discussion 29

richness. The increased number and diversity of benthic invertebrates present indicates an overall improvement in the water 

quality of Anderton Branch.

Laboratory Toxicity Studies

Chronic toxicity studies (Lewis and others, 1994) were 

conducted using the water flea, Ceriodaphnia dubia, as a test 

organism for water samples from a site on Anderton Branch 

adjacent to the landfill (site 3110), Brinkley tributary downstream of the landfill (site 3045), Sons Spring (site 3090), 

Anthony Branch (site 2050), and Yasui Spring (site 4050). The 

test detects toxicity by comparing the means of the number of 

offspring from parent organisms living in the water sample with 

the means of the number of offspring from parents living in the 

negative control water designed for ideal growth conditions 

(moderately hard water; Lewis and others, 1994). All parent 

organisms placed in storm- and base-flow water samples from 

Sons Spring died within 48 hours; therefore, no offspring were 

produced (table 7). All parent organisms also died within 

48 hours when placed in the positive control (2,000 mg/L salt 

water, designed to kill the organisms).

Statistical comparison of the means of reproduction data 

(table 7) from all other sites tested (Dunnett’s test, 95-percent 

confidence level) showed no difference in the toxicity for all 

sites as compared to the negative control, moderately hard 

water, including Brinkley tributary (site 3045), which contained 

water affected by the landfill as indicated by a chloride concentration of 7.8 mg/L (table 5). The toxicity study indicates that 

the contaminated water from the landfill and toxic water from 

Sons Spring is no longer toxic after flowing through the wetland 

in Brinkley Pond and discharging to Brinkley tributary. 

Although storm water in Anderton Branch (site 3110) contained 

higher levels of certain contaminants (table 5 and fig. 8) than 

base-flow water, no toxicity was detected in either sample.

Biomarkers

Crayfish hepatopancreas tissue was analyzed for nickel 

and cadmium concentrations, two metals that were detected in 

water samples from Anderton Branch. Nickel and cadmium 

exceeded TDEC criteria for fish and aquatic life (table 5).

Cadmium concentrations in crayfish hepatopancreas tissue 

ranged from a high of 1.1 μg/g of tissue (dry weight) in crayfish 

collected from the mouth of Anthony Branch (site 2005) (control site) to a low of 0.2 μg/g in crayfish collected from the 

mouth of Anderton Branch (site 3005) (fig. 14). Analysis of 

variance (95-percent confidence level) indicates cadmium concentrations in crayfish tissue from site 2005 are higher than concentrations in tissue from site 3005 and the control site on Bennett Branch (site 5005). Multiple comparison grouping analysis 

indicates considerable overlap occurs among most of the sites 

with the exception of site 2005 (fig. 14). Cadmium levels found 

in crayfish tissue are similar to background levels found in fish 

tissue in northern Bedford County (Knight and Powell, 2001). 

Table 7. Results of toxicity tests on water collected from selected locations during base-flow and storm-flow conditions near Quail 

Hollow Landfill, Bedford County, Tennessee.

[Control +, Positive control (2,000 milligram per liter salt water designed to kill all organisms); Control–, Negative control (ideal water for growth and reproduction)]

Site location and number

Number of Ceriodaphnia dubia offspring

Replicates

Live 

adults at 

end of test 1 2 3 4 5 6 7 8 9 10 Mean

Base-flow conditions, October 31, 1996

Anderton Branch adjacent to landfill 3110 34 31 25 21 10 31 12 17 18 12 21 10

Anthony Branch 2050 25 31 28 29 31 28 16 28 20 17 25 10

Yasui Spring 4050 30 33 25 29 32 15 15 3 14 18 21 9

Sons Spring 3090 0 0 0 0 0 0 0 0 0 0 0 0

Control- 31 16 31 1 31 31 14 15 14 15 20 10

Control+ 0 0 0 0 0 0 0 0 0 0 0 0

Storm-flow conditions, December 12, 1996

Anderton Branch adjacent to landfill 3110-filtered 29 26 17 26 37 31 37 21 30 13 28.5 9

Anderton Branch adjacent to landfill 3110-unfiltered 37 32 6 24 24 24 0 20 10 25 20.2 8

Anthony Branch 2050 32 34 16 27 26 24 26 23 16 11 23.5 0

Yasui Spring 4050 27 16 14 16 21 22 24 30 11 20 20.1 9

Sons Spring 3090 0 0 0 0 0 0 0 0 0 0 0 0

Brinkley tributary 3045 28 28 12 21 33 31 28 18 25 22 24.6 9

Control- 10 4 17 21 20 30 7 23 11 20 16.3 9

Control+ 0 0 0 0 0 0 0 0 0 0 0 0
30 Hydrogeology, Water Quality, and Ecology of Anderton Branch near the Quail Hollow Landfill, Bedford County

Analysis of variance (95-percent confidence level) indicates nickel concentrations in crayfish hepatopancreas tissue 

were higher in samples from site 3200 (control site) in the headwaters of Anderton Branch than from all other sites (fig. 14). 

Naturally high nickel concentrations in the sediment from this 

site are the probable cause for these high nickel concentrations 

in crayfish collected from this site (site S4, table 2). 

Organic compounds were detected in water samples from 

landfill monitoring wells and Sons Spring (table 6). Cytochrome P450 is a diverse family of enzymes that can be used as 

biomarkers and are induced by exposure to certain organic compounds. Analysis of variance (95-percent confidence level) 

indicates that cytochrome P450 concentrations in crayfish 

hepatopancreas tissue samples from control sites on Bennett 

Branch (site 5005), upstream of the landfill (site 3200), and the 

laboratory were not different from the samples from sites on 

Anderton Branch adjacent to (site 3110) and downstream of 

(site 3035) the landfill. The cytochrome P450 concentrations in 

tissue samples taken from control site 2005 on Anthony Branch 

were higher than in samples from all other sites (fig. 14). This 

high concentration may be caused by organic inputs from a 

facility near the sampling site or possibly from agricultural 

chemicals in use in the Anthony Branch drainage basin. 

Metallothionein is a small peptide that reduces toxicity of 

some metals by binding the metals and making them less bioavailable. Metallothionein is induced by exposure to certain 

metals including nickel and cadmium. Analysis of variance 

(95-percent confidence level) indicates metallothionein concentrations in crayfish hepatopancreas tissue were lower in 

laboratory-purged crayfish than in tissue from crayfish from 

Anderton (sites 3005 and 3110) and Anthony Branches (site 

2005) (fig. 14). The high concentrations of metallothionein 

present in tissue samples from crayfish collected on Anderton 

and Anthony Branches indicate that metallothionein may have 

been induced in the organisms tested. Because the cadmium and 

nickel concentrations in the purged crayfish are statistically not 

different from field crayfish collected at the sample sites, other 

metals may be present causing the induction of this biomarker. 

Summary

Landfills can affect nearby ground-water and surfacewater sources by increasing concentrations of chloride, heavy 

metals, and organic compounds in water. Increased turbidity 

caused by surface runoff over areas denuded of vegetation also 

can negatively affect the benthic community of streams draining landfills. From 1996 to 1998 the USGS, in cooperation with 

the Bedford County Solid Waste Authority, conducted a study 

to characterize the hydrology and water quality of Anderton 

Branch adjacent to the Quail Hollow Landfill. 

Quail Hollow Landfill, located on the Highland Rim overlooking the Central Basin of Middle Tennessee, is constructed 

on the clay-rich gravelly residuum of the Fort Payne Formation 

above the Chattanooga Shale confining unit. Underlying the 

Chattanooga Shale are the Leipers and Catheys Formations, the 

Cannon Limestone, and the Hermitage Formation. The Cannon 

Limestone is characterized by sinking streams, sinkholes, and 

caves including the Harrison Cave system, an extensive network of solution channels of which the mapped portion is adjacent to the landfill. Evidence of the importance of this cave system to the hydrology of the area was obtained when a natural 

dye trace resulted from the release of impounded water that 

entered a sinking pond in the Powell Branch drainage basin and 

emerged overnight 4,200 feet away in the Anderton Branch 

drainage basin. This connection demonstrates that the karst 

solution channels can direct water from the south and west, as 

well as from the north and east, into Anderton Branch.

Surface- and ground-water data collected for this study 

from domestic and landfill monitoring wells, springs, and several streams in the landfill area were analyzed and compared 

with data collected during an earlier study of the landfill. 

Surface- and ground-water quality data were collected during 

base- and storm-flow conditions and were analyzed for specific 

conductance, metals, and organic and inorganic compounds. 

Abundance and taxa richness of the benthic community was 

sampled, and toxicity using Ceriodaphnia dubia was determined. Concentrations of nickel and cadmium and the biomarkers cytochrome P450 and metallothionein in crayfish hepatopancreas tissue were evaluated as more sensitive indicators of 

water quality. 

Specific conductance and concentrations of iron, manganese, lead, and nickel increased in Anderton Branch during 

storm-flow conditions. Specific conductance at site 3110 in 

Anderton Branch increased from 100 to 200 μS/cm during 

storm flow. In contrast during the same storm, the specific conductance at site 2050 in Anthony Branch decreased from 160 to 

120 μS/cm. Concentrations of total iron, manganese, lead, and 

nickel were greater (72,000, 2,900, 59, and 71 μg/L, respectively) during storm runoff in Anderton Branch than during 

base-flow conditions (17 and 34 μg/L, for iron and manganese, 

respectively, and no detections for lead and nickel). Concentrations of lead and nickel exceeded PMCLs (5 and 100 μg/L, 

respectively) and concentrations of iron and manganese 

exceeded SMCLs (300 and 50 μg/L, respectively) for drinking 

water. Cadmium also was detected during the December 1996 

storm (6 μg/L, total) and again in May 1998 (0.7 μg/L, dissolved) at a concentration equal to the lowest TDEC fish and 

aquatic life standard, but its concentration remained below 

detection limits during other storms. Chloride-load levels in 

Anderton Branch are three times greater than for Anthony 

Branch. Chloride-load calculations in Anderton Branch established two point sources of chloride: Brinkley tributary, which 

drains Brinkley Pond that receives surface water and ground 

water from the landfill and ground water from Sons Spring, and 

a barnyard that is divided by Anderton Branch. Although volatile organic compounds were detected in the monitoring wells at 

the landfill and at Sons Spring, these contaminants were not 

detected in Anderton Branch or in domestic wells.

Sons Spring is a karst spring discharging about 10 feet 

below the Chattanooga Shale at a location approximately 
Acknowledgments 31

300 feet from the toe of the landfill. Chloride concentrations at 

Sons Spring increased from 3 mg/L in 1974 to 59 mg/L in 1996. 

Specific conductance increased from 230 to 800 μS/cm during 

storm events. Both increases are indicators of the effect of the 

landfill on water quality at this spring. Water samples from 

Sons Spring contained concentrations of nickel that exceeded 

primary drinking-water standards and TDEC fish and aquatic 

life chronic criteria, and concentrations of iron and magnesium 

that exceeded secondary drinking-water standards. Cobalt also 

was detected at high concentrations. 

Volatile organic compounds present in the ground water at 

the landfill included PCE, TCE, and vinyl chloride; each of 

these compounds equaled or exceeded PMCLs. Other volatile 

organic compounds detected at the ground-water monitoring 

wells at the landfill and in Sons Spring included DCA and DCE. 

The presence of these chlorinated solvents indicate the landfill 

origin of the contaminants in Sons Spring.

Analysis of variance (95-percent confidence level) of the 

data from benthic macroinvertebrate samples in Anderton 

Branch indicated some differences in abundance of organisms 

and number of taxa at sites upstream of the landfill as compared 

with sites adjacent to and downstream of the landfill as well as 

a control site on Anthony Branch. However, the ecological significance of these differences is doubtful because the multiple 

comparison tests indicate considerable overlap among many of 

these sites, and differences seen cannot be definitively attributed to landfill influence. As an example, even though site 3030 

on Anderton Branch is low in taxa, this site is considered to be 

a healthy site because of the high abundance of organisms. The 

low number of taxa is probably not due to poor water quality, 

but rather to a unique environment. Sons Spring (site 3090) was 

statistically different from other sites and consistently had the 

lowest mean abundance and the lowest mean taxa richness. 

These differences do appear to be attributable to landfill influence. Annual monitoring and analysis of data from site 3005 on 

Anderton Branch in 1998 indicated that the number and types 

of benthic macroinvertebrates has increased at that site.

Toxicity studies evaluating the Ceriodaphnia dubia, water 

flea, indicated no toxicity in base flow or storm water from 

Anderton Branch. Water from Sons Spring resulted in 

100-percent mortality to the test organisms within 48 hours for 

both base- and storm-flow water samples. Toxicity studies confirm results of benthic studies and are in agreement with the 

benthic studies in this project.

Biomarker studies indicated that cytochrome P450 was not 

induced in crayfish hepatopancreas tissue in samples from 

Anderton Branch. Cytochrome P450, however, was at statistically higher levels in tissue samples from the control stream 

Anthony Branch than in tissue samples from all the other sites 

studied. Metallothionein concentrations in crayfish hepatopancreas tissues showed increased levels in samples from Anderton 

Branch as compared with control samples, but the levels were 

not significantly increased. The increased levels of metallothionein were probably caused by the presence of other metals that 

were not studied because levels of nickel or cadmium detected 

in these same tissues were not different from control samples, 

which showed no metallothionein induction. Statistically high 

levels of nickel in crayfish hepatopancreas tissue detected in 

samples from an upstream control site probably were caused by 

naturally occurring high levels of nickel.

This study confirms the observations from the 1995 reconnaissance study that Sons Spring has been severely affected by 

the landfill; however, the overall effect of the landfill on water 

in Anderton Branch is minimal. Surface runoff and ground 

water from the landfill and ground water from Sons Spring flow 

into and through Brinkley Pond and then discharge through 

seeps into Brinkley tributary. High chloride concentrations 

detected in water from Brinkley tributary indicate that the water 

is affected by the landfill; however, the metal concentrations are 

not elevated and the water is not toxic. The lack of toxicity and 

metals in water from Brinkley tributary indicates that Brinkley 

Pond is reducing contaminant levels in the water received from 

the landfill. High concentrations of metals were detected in 

storm-water samples in Anderton Branch; however, this water 

was not toxic and the benthic community downstream of this 

site was not affected. These observations indicate that the overall effect of the Quail Hollow Landfill on the ecology of Anderton Branch is restricted primarily to Sons Spring and the short 

reaches on the east flank of the landfill identified in the 1995 

study.

Acknowledgments

The author thanks Jim Kemp, John Sons, and James 

Brinkley for granting access to the various sites on their properties; Frank Bailey, Middle Tennessee State University, for his 

guidance and assistance and for the use of equipment for the 

toxicity and biomarker studies; and also Keith Walters, Middle 

Tennessee State University, for the use of the optic microscope.

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