Project ID #15-0425
Proctor Creek Watershed Monitoring
Final Summary Report
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Fulton County, GA
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Project Dates: September 2015 - July 2017
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Report Date: September 14, 2018
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Project Leader: Susan Dye
Ecology Section
Field Services Branch
Science & Ecosystem Support Division
USEPA - Region 4
980 College Station Road
Athens, Georgia 30605-2720
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The activities described in this report are accredited under the US EPA Region 4 Science and
Ecosystem Support Division ISO/IEC 17025 accreditation issued by the ANSI-ASQ National
Accreditation Board. Refer to certificate and scope of accreditation AT-1644.

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Requestor:
Analytical Support:
Cynthia Edwards
Water Protection Division
USEPA Region 4
61 Forsyth St. SW
Atlanta, GA 30303-8960
Analytical Services Branch
Science & Ecosystem Support Division
USEPA Region 4
980 College Station Road
Athens, GA 30605-2720
Approvals:
SESD Project Leader:

Susan Dye	Date
Ecology Section
Field Services Branch
Approving Official:
Stacey Box, Chief
Ecology Section
Date/
Field Services Branch
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Table of Contents
1.0 Introduction	4
2.0 Methods	5
2.1	Site Description	5
2.2	Study Design	5
2.3	Sampling Methods	6
2.4	Data Analysis	7
3.0 Results	8
3.1	Precipitation and Discharge	8
3.2	Surface Water Data	8
3.2.1	In Situ Data	8
3.2.2	Escherichia coli	9
3.2.3	Inorganic Water Chemistry	9
3.2.4	Organic Water Chemistry	10
3.3	Sediment Data	11
3.3.1	Inorganic Sediment Chemistry	11
3.3.2	Organic Sediment Chemistry	11
3.4	Habitat Bioassessments	12
3.5	Macroinvertebrate Data	12
3.6	Fish Tissue Data	13
4.0 Discussion	13
4.1	Upper Watershed: Downtown and CSO Facilities	13
4.2	Mainstem Proctor Creek	15
4.3	Proctor Creek Tributaries	15
4.4	Macroinvertebrate Bioassessments	16
4.5	Fish Consumption Advisories	17
5.0 Conclusions	17
6.0 References	18
Tables	21
Figures	28
Appendix	32
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1.0 Introduction
Proctor Creek is an urban stream that drains the west side of Atlanta, Georgia, and flows into the
Chattahoochee River. It is currently on the Georgia Environmental Protection Division (GAEPD) 303(d)
list for impairment due to fecal coliform bacteria, resulting from exceedances of the GAEPD water quality
standard of 200 CFU per 100 mL from May to October and 1000 CFU per 100 mL from November to
April (Ga. Comp. R. & Regs. r. 391-3-6-.03). Prior to the listing, a 1998 federal consent decree to address
combined sewer overflows (CSOs) and sanitary sewer overflows (SSOs) required the City of Atlanta
(COA) to improve and expand sewer infrastructure in order to reduce the frequency of overflow events.
Since then, the COA has separated some of the combined basins, developed a new CSO storage and
treatment system, and repaired many collapsed sewer lines and cross-connections. However, ongoing
monitoring by community watershed groups (ARC 2010, ARC 2011, CRK 2018) and by the EPA (U SEP A
2013) has still indicated high levels of Escherichia coli in multiple reaches and tributaries of Proctor
Creek.
There is also a lack of recent data from the Proctor Creek watershed for chemical parameters, including
nutrients, metals and organic compounds. While community groups have been consistently monitoring
for E. coli, which is a relatively easy and low-cost analysis, other parameters can be prohibitively
expensive. Select ions and metals have been evaluated in association with suspended sediment studies,
which have focused primarily on sediment-associated chemical parameters (e.g., Horowitz el al. 2008,
Horowitz 2009). A suite of organic wastewater indicators has also been analyzed to characterize spatial
distribution in the watershed as well as detect any effects of flow rate or season (Lawrence and LaFontaine
2010). However, these assessments were performed between 2003 and 2006, before many of the sewer
infrastructure improvements were completed. More recently, the United States Geological Survey (USGS)
conducted a comprehensive water quality study at the James Jackson Parkway gauging station on Proctor
Creek (Van Metre and Journey 2014). While this included an extensive list of inorganic and organic
parameters, less is known about contaminant sources throughout the basin. Furthermore, there has not
been a watershed-scale assessment to specifically compare concentrations of constituents in Proctor Creek
to existing water quality standards.
The current study was designed to provide baseline data for water quality parameters throughout the
Proctor Creek watershed. The primary goals were to assess current surface water conditions, during both
baseflow and stormflow, and to identify any constituents which may exceed water quality standards.
Sampling events included in situ water quality measurements, surface water and sediment sampling for
chemical parameters, stream discharge calculations, macroinvertebrate and habitat assessments, and fish
tissue analyses. Fifteen locations were monitored quarterly for two years, in order to account for potential
seasonal and/or inter-annual variability, and to establish a sufficient database for statistical analyses and
modeling efforts. This report provides a summary of the quarterly data collected throughout the watershed.
A concurrent effort to sample stormwater during significant rain events has been led by USGS, the results
of which will be presented in a separate report.
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2.0 Methods
2.1	Site Description
The Proctor Creek watershed (HUC 031300020101) is located entirely within the City of Atlanta in Fulton
County, GA. Its headwaters begin near the city center, then the stream flows northwest for approximately
9 miles to its confluence with the Chattahoochee River just west of Interstate-285 (Figure 1). The
Chattahoochee (HUC 03130001) joins the Flint River at the Georgia-Florida border to form the
Apalachicola, then drains across the Florida panhandle to the Gulf of Mexico.
Multiple types of point and nonpoint source pollution exist throughout the Proctor Creek watershed, which
drains approximately 10,000 acres of land. The headwaters, most of which are either piped underground
or channelized aboveground, receive urban runoff from the west side of downtown Atlanta, including
large complexes such as the Atlanta University Center, the Georgia World Congress Center, the Philips
Arena and the Mercedes-Benz Stadium. Two combined sewer overflow (CSO) facilities are located just
west of downtown: North Avenue CSO and the now-decommissioned Greensferry CSO. Norfolk
Southern railroad runs along the northern boundary of the watershed, with a large freight yard near the
mid-point of Proctor Creek. Several landfills, automotive salvage yards, and illegal trash dumps are
located throughout the basin. There are also dense residential and commercial neighborhoods with high
proportions of impervious surface, as well as industrial areas at the downstream end of the watershed
(ARC 2009).
2.2	Study Design
Fifteen sampling locations were established throughout the watershed, including seven in the main
channel of Proctor Creek and eight in tributaries of various size (Table 1, Figure 2). Locations were
selected to encompass areas with potential influence on water quality (e.g., railyards, landfills, industrial
parks, and the urban center), as well as points along the main channel downstream of larger tributaries.
Most locations also overlapped long-term monitoring stations in use by volunteer groups, including the
Chattahoochee Riverkeeper and the West Atlanta Watershed Alliance, so that project data could be
compared with historical databases as well as ongoing monitoring activities.
Eight quarterly sampling events were conducted over a two-year period, starting in September 2015 and
then in January, April, July and October 2016, and January, April and July 2017. The first event was more
extensive, targeting a wider range of sample media and chemical parameters, in order to identify analytes
of interest during baseflow conditions and to inform selection of subsequent parameters. Events were
scheduled to capture a range of low-to-moderate baseflow conditions throughout the year. In February
2017, aquatic macroinvertebrate and habitat bioassessments were performed at four locations
representative of upstream and downstream portions of the watershed. Fish were also collected from the
main channel of Proctor Creek in April 2016 and July 2017, to evaluate the risk of fish tissue consumption
on human health following detections of organic contaminants in water and sediment samples.
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2.3 Sampling Methods
During each quarterly sampling event, measurements of flow and in situ physicochemical parameters were
recorded at all 15 sampling locations, and water samples were collected for biological and chemical
analyses according to methods outlined in the quality assurance project plan (USEPA 2015a). Discharge
was estimated at most locations using a SonTek FlowTracker acoustic Doppler velocimeter and standard
stream gauging techniques (SESDPROC-501). Discharge data for Hortense (PC6) and James Jackson
(PC8) were obtained via the USGS real-time streamflow data for station numbers 02336517 and
02336526, respectively, available online at http://waterdata.usgs.gov. In situ water quality measurements
of temperature, pH, specific conductance, dissolved oxygen and turbidity were obtained using YSI multi-
parameter sondes (SESDPROC-111). Photographs were taken from water sampling locations, as well as
from bridges, where present, to document site conditions during each visit (SESDPROC-005).
Water samples for fecal bacteria, nutrients, classical parameters, total recoverable metals and organic
analytes were collected in accordance with the SESD standard operating procedure for surface water
sampling (SESDPROC-201). A complete list of analytes with routine reporting limits is provided in the
Appendix. The full suite of organic parameters was only analyzed in September 2015, but samples for
pesticides and PCBs were collected again in April 2016 and July 2017. Sediment samples for total
recoverable metals and organic parameters were collected during the September 2015 sampling event,
except at Greensferry (PC2) where sediment is absent, in accordance with the SESD standard operating
procedure for sediment sampling (SESDPROC-200). All samples, except those for fecal bacteria, were
analyzed by the Analytical Support Branch (ASB) at SESD in accordance with the ASB Laboratory
Operations and Quality Assurance Manual (USEPA 2018b), following methods listed in the Appendix.
Water samples for fecal bacteria analysis were delivered to the EPA Office of Research and Development
(ORD) laboratory in Athens, GA for processing and analysis within 6 hours of collection (USEPA 2017).
On February 6, 2017, during the Georgia Department of Natural Resources (GADNR) index period of
mid-September through February, aquatic macroinvertebrates were collected at four locations for
calculation of biotic indices according to GADNR methods (GADNR 2007). Macroinvertebrate taxonomy
and metric calculations were performed by Rhithron Associates, Inc. in Missoula MT. Visual habitat
assessments were conducted using the EPA Rapid Bioassessment Protocol for high-gradient streams
(Barbour et al. 1999), both at macroinvertebrate sampling reaches during the collection period, and at all
quarterly monitoring stations on July 18-19, 2017. Fish were also sampled for a range of potential
contaminants in a screening study on April 20, 2016 and then a follow-up study on July 25, 2017 (USEPA
2016a, USEPA 2018a), according to GADNR sampling methods (GADNR 2016), EPA fish tissue
screening protocols (USEPA 2000b), and SESD standard operating procedures for fish collection
(SESDPROC-512) and tissue processing (SESDPROC-714). See Table 1 and Figure 2 for
macroinvertebrate and fish sampling locations.
In conjunction with this project, stream flow conditions were monitored at automated USGS gauging
stations. In addition to the existing gauge at Jackson Parkway (#02336526), a second was installed at a
previously-gauged location on the main channel at Hortense Way (#02336517) and a third was installed
at Spring Street on the largest tributary, which flows into Proctor Creek from the south (Figure 2). These
stations have profiled discharge from the upper watershed, the lower watershed, and the tributary which
drains approximately one-third of the watershed. Continuous water level and discharge data have been
collected at each of the gauges, in addition to precipitation data at Hortense and Jackson Parkway, and in
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situ data (temperature, pH, specific conductance, dissolved oxygen and turbidity) at the Jackson Parkway
station only. Stormwater samples for chemical analysis are being collected at these three locations during
significant rain events by the USGS South Atlantic Water Science Center, and will be completed by
October 2018.
2.4 Data Analysis
Water chemistry data were compared to Georgia Water Quality Standards (WQS) applicable to Proctor
Creek, which has a designated use of Fishing. WQS include freshwater aquatic life criteria at both chronic
and acute exposure levels, calculated using hardness concentrations at each station and conversion factors
for total recoverable metals where applicable, as well as standards which apply at discharge above 7-day,
10-year minimum flow conditions (7Q10) and above annual average flow conditions (Ga. Comp. R. &
Regs. r. 391-3-6-.03). Since Proctor Creek is not used as a drinking water source, water chemistry data
were not compared to state drinking water standards. Sediment chemistry data were compared to EPA
threshold effect levels (TEL) and probable effect levels (PEL) for impacts on aquatic life, which are used
in risk assessment to provide guidance for follow-up investigations (USEPA 2000c). Fish tissue data were
compared to EPA screening values (USEPA 2000b) as well as trigger values used to establish
consumption advisories, provided by GAEPD (personal communication).
Precipitation data were obtained from the USGS gauges at Hortense Way and Jackson Parkway, available
online at http://waterdata.usgs.gov. Total rainfall at each station was summed over the 1, 2, 3, and 7 days
prior to sampling in order to assess precipitation as a causal variable in regression analyses. Since sampling
was scheduled to avoid recent rainfall whenever possible, only two events were conducted following rain
within 24 hours.
Data were analyzed using the statistical software R, version 3.1.2 (RCore Team 2014). Summary statistics
(count, mean and standard error) were generated for all numerical data, organized by sampling event and
station. Values below detection were replaced with a surrogate value of half the detection limit for
calculation of summary statistics. Several metals were below detection in most water samples, so the
following analytes were removed from further statistical analyses: aluminum, antimony, arsenic, lead,
selenium, titanium, and vanadium. Spearman's Rank correlations were calculated to determine strength
of relationships between relevant continuous variables, as well as to detect autocorrelation between related
parameters. For each of the variables selected for multivariate analysis, Q-Q plots and Shapiro-Wilk tests
were performed to detect violations of normality. Where appropriate, data transformations were applied
and maintained throughout all further analyses. The majority of distributions were right-skewed due to
fewer occurrences of high data points, and log transformations improved the normality of most of these
variables. Multiple regression analysis was used to identify the strongest predictors of E. coli. Parameters
were added sequentially and Akaike's Information Criterion (AIC) was used to evaluate the goodness of
fit for each model. Individual parameters were also analyzed according to the categorical variables station
and season, using repeated measures one-way analysis of variance or the Friedman rank sum test.
Statistical results presented in this report were significant at p<0.001 unless otherwise indicated.
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3.0 Results
3.1	Precipitation and Discharge
Total precipitation amounts during the study period are summarized in Table 2. As recorded at the Jackson
Parkway gauge, rainfall in the week prior to sampling ranged from 0.03" in October 2016 to 4.38" in April
2017, with no precipitation in the 24 hours before most sampling events. However, there were storms
totaling 1.08" and 0.36" over the 2 days prior to the January 2017 and July 2017 events, respectively.
Total rainfall was likely higher in the upper watershed than was captured by this gauge in July 2017, since
parts of downtown Atlanta received over 1" the day before sampling (http://water.weather.gov/precip/).
Both of these events included samples collected during the receding limb of the hydrograph, after
discharge had fallen below the annual average level and was closer to baseflow conditions. Annual average
discharge at Jackson Parkway, calculated over 14 years of data (2004-2017), is approximately 18 cfs.
During the study period, flow atPC4, PC10, and PC 14 was consistently too low to measure using acoustic
Doppler current profilers for stream gauging, the quality control threshold for which is 0.1 cfs. Only
shallow pools of water were present at PC14 in both July and October 2016, so samples were not collected
during those periods and in situ measurements were not representative of flowing water. Discharge
fluctuated across quarterly events according to seasonal variation and rainfall. For example, flow at the
furthest site downstream (Northwest; PC9) ranged from 1.54 cfs in October 2016 to 12.01 cfs in July
2017.
3.2	Surface Water Data
3.2.1 In Situ Data
A summary of data from in situ measurements is provided in Table 3. Temperature and dissolved oxygen
were both significantly different among seasons, with lower temperature and higher dissolved oxygen in
winter and the inverse in summer (temperature F3,ioo= 181, DO F3,ioo=62.8). Dissolved oxygen was
significantly lower at North CSO (PC4), and slightly lower at Lillian Cooper (PC 14), than all other stations
{F 14,96=1%2). Measurements of pH were significantly lower at North CSO and Lindsay Street (PC10) than
most other stations (Fm,96=3.65). These three stations had consistently low flows throughout the study,
often forming stagnant pools. Specific conductance ranged from 104 to 1190 |iS/cm across stations, with
higher levels in North CSO (PC4), AD Williams (PC 13) and West Highlands (PC 15) (Figure 3). Turbidity
was typically low (<10 NTU) during most sampling events, but increased up to 40 NTU in July 2017.
Measurements of turbidity in the lower main channel (PC6-PC9) were higher and more variable overall,
mainly because these stations were sampled first following the two storm events in January and July 2017,
when flows were still slightly elevated. Turbidity was significantly correlated with precipitation totals in
the 24, 48 and 72 hours prior to sampling, as well as aluminum and zinc (Table 4).
Temperature and pH were both within acceptable ranges according to Georgia WQS. No numeric criteria
exist for specific conductance or turbidity, but a narrative criterion states that turbidity should not create
"a substantial visual contrast in a water body due to a man-made activity," with comparisons of water
clarity made upstream and downstream of that activity (Ga. Comp. R. & Regs. r. 391-3-6-.03(5)(d)).
Although some portion of turbidity is generated by urban development in Proctor Creek, it is not solely
attributed to 'man-made activity' during higher flows, which also erode stream banks and resuspend
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bedload sediments. At North CSO (PC4) on all dates, and at Lillian Cooper (PC 14) on two occasions,
dissolved oxygen was below the WQS of 4.0 mg/L required to support species of warm water fish.
However, these two small tributaries were both very shallow, with little to no flow present during sampling
events. Dissolved oxygen criteria are applicable at one meter below the surface, or at mid-depth if less
than two meters, which suggests that the criterion may not apply to such streams with minimal discharge.
3.2.2	Escherichia coli
Data for fecal bacteria counts are provided in Table 3, reported as the most probable number (MPN) of E.
coli per 100 mL. While the Georgia WQS for Proctor Creek is written in terms of fecal coliform, not
specifically E. coli, the E. coli data provide a conservative estimate of fecal coliform since they are a
subset of this group. Therefore, exceedance of the standard by E. coli indicates a likely exceedance by
fecal coliform bacteria as a whole. The standard is also based on sampling period, with geometric mean
limits of 200 MPN per 100 mL (May through October) or 1,000 MPN per 100 mL (November through
April), calculated using at least four samples during a 30-day period (Ga. Comp. R. & Regs. r. 391-3-6-
.03(6)). Only one sample was collected at each station during each sampling event, which precludes
calculation of a geometric mean, so data are not directly comparable to WQS. However, counts are also
not to exceed 4,000 MPN per 100 mL for any single sample collected between November and April,
whereas there is no single sample threshold for May through October.
Counts were consistently above WQS at Burbank (PCI), Greensferry (PC2) and North Avenue (PC3),
and above the 4,000 maximum threshold at these stations in three out of four sampling periods when this
limit was applicable. There was a sanitary sewer overflow observed at West Highlands (PC 15) in January
2017, which led to a count of 15,770 MPN per 100 mL, whereas all other samples from that station were
below WQS. This incident was reported to the City of Atlanta and the blocked sewer pipe causing the
overflow was cleared before the next sampling date. Another high value of 41,060 MPN per 100 mL was
detected at PC 10 in October 2016, which also likely resulted from a sewer leak, and counts were relatively
high for this station again at 4,989 MPN per 100 mL in July 2017. Average E. coli counts over the study
period were above 1,000 MPN per 100 mL, with high variability, at all stations except North CSO (PC4),
Grove Park (PCI 1), AD Williams (PC13) and Lillian Cooper (PC14) (Table 3, Figure 4).
E. coli was significantly correlated with all nutrient species except ammonia, and most strongly associated
with total phosphorus levels (Table 4). Counts were also significantly correlated with precipitation totals
in the 24 hours, 48 hours and 72 hours prior to sampling, with higher counts throughout the watershed in
January and July 2017 following storm events, but not correlated with turbidity. Counts were less
significantly related to discharge, although flow measurements were not collected concurrently with fecal
bacteria sampling at all locations, with some measurements in the upper watershed performed the
following day. Total alkalinity, total organic carbon (TOC), pH, specific conductance, calcium, sodium
and chloride were inversely related to E. coli. Based on results of the multiple linear regression model,
total dissolved phosphorus (TDP; t = 5.82) and 24-hour precipitation totals (t = 5.17) were the best
predictors of E. coli concentration (F2,101 = 26.44, adjusted R2 = 0.33, AIC=357).
3.2.3	Inorganic Water Chemistry
Nutrients were highest at the upper end of the watershed, then declined downstream, with moderate levels
in the lower tributaries (Figures 5-6). Maximum values at upstream stations depended on the species of
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nutrient. Total nitrogen (TN) was highest at Greensferry (PC2) and Lindsay Street (PC 10), with nitrate-
nitrite comprising the majority of TN at Lindsay Street, versus organic sources and ammonia contributing
approximately one-third of TN at Greensferry (Table 5). Total phosphorus (TP) was higher at Greensferry
than all other stations, with elevated concentrations in the main channel below that tributary and
decreasing downstream (Figure 6). About 90% of all phosphorus originating from Greensferry was in
dissolved form, versus an average of approximately 65% dissolved P across the other seven tributaries
(Table 5). While there are currently no numeric nutrient criteria in place for rivers and streams in Georgia,
the EPA recommended criteria for Ecoregion IX (Southeastern Temperate Forested Plains and Hills),
based on the 25th percentile of reference streams, are 0.69 mg/L TN and 0.036 mg/L TP (USEPA 2000a).
Average concentrations were above that level of TN in all locations except Lillian Cooper (PC 14), and
above that level of TP in all locations except Grove Park (PC11), AD Williams (PC13), Lillian Cooper
(PC 14), and West Highlands (PC 15).
Other classical parameters and metals varied more widely throughout the watershed (Tables 5-6). Bromide
was only detected at AD Williams (PC 13). Chloride was significantly higher at North CSO (PC4) and AD
Williams (PC 13) than all other stations (x2i4=66.95), and fluoride was somewhat higher at Greensferry
(PC2) than all other stations. Specific conductance (x214=61.13), total alkalinity (j2i4=49.24), hardness
(j214=62.80), calcium (%214=72.93), sodium (j^i4=65Al) and TOC (j214=41.07) were all higher at North
CSO (PC4), AD Williams (PC13) and West Highlands (PC15) (Figure 3). These three stations generally
had elevated arsenic, lead, strontium and titanium as well. Two other tributaries had slightly different
detections of metals. In addition to elevated calcium and sulfate, Lindsay Street (PC 10) samples contained
antimony, barium, lead, strontium, titanium, and significantly higher zinc (/2/4=43,79), Lillian Cooper
(PC 14) did not have elevated conductivity or associated ions, but was higher in aluminum, iron, lead and
zinc.
None of these metals were detected above the acute exposure WQS for protection of aquatic life. However,
aluminum, lead and zinc were found at higher concentrations following the two rain events in January and
July 2017, primarily in the main channel of the lower watershed, and were significantly correlated with
precipitation totals (Table 4). These stations (PC6-PC9) were sampled while flows were still receding.
During these two events, and in January 2016, concentrations of lead were above WQS for chronic
exposure impacts on aquatic life at one or more locations: North CSO (PC4), four stations in the lower
main channel (PC6-PC9) and Lillian Cooper (PC 14). There was a total of 7 detections of lead above
chronic criteria, distributed across these 6 locations and 3 events. In January 2017, cadmium and zinc were
also detected at West Highlands (PC 15) and Lillian Cooper (PC 14), respectively, just above chronic
criteria. Chronic criteria are defined as the "highest concentration of a pollutant to which aquatic life can
be exposed for an extended period of time (4 days) without deleterious effects" (Ga. Comp. R. & Regs. r.
391-3-6-.03(3)). Since the majority of these detections followed rain events, it is unlikely that exposure
was maintained at these levels for more than 4 days. However, Georgia's listing assessment methodology
indicates that a waterbody is not supporting its designated use if more than one sample exceeds the chronic
criterion in three years. Thus, it may be necessary to examine concentrations of lead in the water column
with respect to Georgia's 303(d) listing for Proctor Creek.
3.2.4 Organic Water Chemistry
A full suite of organic analytes, which included herbicides, pesticides, PCBs, semi-volatile organics and
volatile organics, were analyzed during the initial sampling event in September 2015. Of the 163 organic
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compounds, only 8 were detected in one or more samples (USEPA 2016b). The pesticide gamma-
chlordane was present at 0.099 |ag/L at Greensferry (PC2) and 0.055 ng/L at North Avenue (PC3) (Figure
7), which are levels considerably higher than the WQS of 0.0043 ng/L of chlordane applicable at or above
7Q10 flow conditions (Ga. Comp. R. & Regs. r. 391-3-6-.03(5)). One or more volatile and/or semi-volatile
organic compounds were also identified at about half of the stations, but were not consistent with any
particular location and were not at levels near WQS (USEPA 2016b; Appendix).
Since the minimum reporting limits (MRLs) for many PCBs and pesticides were higher than their
respective WQS, and there were potential exceedances, samples were collected for these groups again in
April 2016 and July 2017. In April, the laboratory was able to reduce the detection limit by a factor of 10
using a lower extraction volume. During both follow-up sampling events, dieldrin, heptachlor epoxide
and alpha- and gamma-chlordane were found at many locations in the watershed, but only above the 7Q10
WQS at a few stations. Heptachlor epoxide was above the standard at Burbank (PCI), Greensferry (PC2)
and North Avenue (PC3) on both dates and at Hollowell (PC5) and Hortense (PC6) in July 2017 only.
Total chlordane was above the standard at PCI and PC2 in September 2015 and at PC2 in July 2017.
During the July 2017 event, water samples for organics were collected at the beginning of the sampling
period when flows were still elevated from rainfall, to assess potential storm effects on concentrations.
Three locations in the main channel (PCI, PC5, PC7) were also sampled the next day for comparison, and
concentrations of detected analytes were similar between the two time periods. A summary of pesticide
data is provided in Figure 7.
3.3 Sediment Data
3.3.1	Inorganic Sediment Chemistry
The majority of targeted metals were found in sediment samples (Table 7), whereas mercury,
molybdenum, selenium, silver and thallium were all below detection (Appendix). The highest
concentrations of most metals were found at North CSO (PC4), with additional elevated values at North
Avenue (PC3), Lindsay Street (PC10) and West Highlands (PC15). None of the metal concentrations
found in sediment samples during this study were above the specific probable effect concentrations (PECs)
examined (Jones & Suter 1997, USEPA 2000c). However, there were a few stations with copper and/or
lead concentrations that were above a threshold effect concentration (TEC) at which some toxicity to
aquatic organisms has been found to occur (Table 7).
3.3.2	Organic Sediment Chemistry
Organic compounds detected in sediment samples are shown in Table 8, while those not detected in any
samples are listed in the Appendix. No herbicides were found, but four pesticides and two PCB-Aroclors
were detected at a few locations. Of note were the relatively high deposits of 59 |ig/kg gamma-chlordane
and 24 |ig/kg alpha-chlordane at Lindsay Street (PC 10). Eighteen semi-volatiles were also present across
the watershed, with many occurring at nearly half of all stations. These compounds also followed the
pattern of elevated concentrations upstream, particularly at North CSO (PC4) where all 18 were present,
with levels declining downstream. In general, organics were low in sediment at Burbank (PCI) and AD
Williams (PC13), and nearly absent at Spring Street (PC12).
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As with metals, organic compounds found in sediments were compared to several toxicity benchmarks to
evaluate the potential for harmful effects on aquatic life. Total chlordane (summing alpha- and gamma-
chlordane) of approximately 83 |ig/kg at Lindsay Street (PC 10) may be a concern, as one published PEC
for chlordane is 17.6 |ig/kg (USEPA 2000c). Several polycyclic aromatic hydrocarbons (PAHs), which
are generally classified as coal tar and diesel exhaust byproducts, were also elevated at North Avenue
(PC3), North CSO (PC4), and Hollowell (PC5). Concentrations were above either the PEC or TEC for
several PAHs at these three locations in particular, and the total concentration of PAHs approached levels
of potential concern for combined effects. Those compounds above PECs included benzo(a)pyrene,
fluoranthene, and pyrene, all of which are associated with gasoline, motor oil, and wood preservatives.
However, toxic effects in situ depend on a variety of environmental factors, including sediment
characteristics, residence time and target organism (Wenning et al. 2005), so literature benchmarks are
provided for comparison only.
3.4	Habitat Bioassessments
Habitat bioassessment scores ranged widely, from 55 to 149 points out of a possible 200 (Table 3). In the
upper watershed, closer to downtown, stations generally had more channel alteration, less bank stability,
less diverse riparian vegetation, and narrower buffer zones. In the main channel of Proctor Creek in the
lower watershed, these parameters improved, but there was increased sediment deposition and
embeddedness. Tributaries were more variable. For example, Lillian Cooper (PC 14) received the lowest
score due in part to low flow, high sediment deposition and heavily eroded banks. Spring Street (PC 12)
and AD Williams (PC 13) scored similarly, each with relatively good benthic substrates and a variety of
flow regimes, but some bank stability issues and suboptimal riparian zones. The Greensferry tributary
(PC2) could not be scored appropriately using this method, since the stream is entirely contained within a
concrete channel, which extends several meters on either side into the riparian zone. This provides very
poor habitat conditions with only a single substrate, fast-shallow flow, and sparse organic detritus that is
flushed downstream during periods of high discharge.
3.5	Macroinvertebrate Data
Macroinvertebrates were collected at four locations in February 2016, along with additional habitat
assessments performed at these locations, two of which were in reaches that differed slightly from the
regular water chemistry stations (Table 1 and Figure 2). Macroinvertebrate Multimetric Index (MMI) and
habitat assessment scores are listed in Table 9. All stations received similar MMI scores, ranging from 21
to 26 out of 100. While there are currently no narrative rankings associated with the numeric scores, these
low numbers would likely fall into the poor to very poor categories, which are those below the 25th
percentile (Gore et al. 2005). All stream reaches had high proportions of midges (Chironomidae) and
relatively high numbers of aquatic worms (Oligochaeta). Dominant taxa included two species of caddisfly
(Trichoptera): Hydropsyche betteni and Cheumatopsyche sp. These species have tolerance values of 7.9
and 6.6 out of 10, respectively, with higher values indicating higher tolerance to pollution or degraded
habitat conditions (NCDEQ 2016). At Spring Street (PC 12), the dominant tax on was the crustacean
subclass Copepoda, which is a type of zooplankton. Also present at all stations was the snail Physella.
There were no mayflies (Ephemeroptera) or stoneflies (Plecoptera) found at any of the sampling locations.
Habitat assessment scores associated with macroinvertebrate sampling locations were more variable,
ranging from 92 to 157 out of a possible 200 (Table 9). Hortense-Hollowell (PC5/6) and Spring Street
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(PC 12) received higher scores, with most parameters falling into the sub-optimal to optimal categories.
Both are in less developed areas with wide riparian zones, but exhibited reduced bank stability. James
Jackson (PC8) and Grove Park (PC11) received lower scores, mostly due to sedimentation and
embeddedness issues, as well as infrequent riffles. James Jackson also had a poor rating for unstable banks.
Grove Park, which was the most urban location, received the lowest score overall with a marginal rating
for vegetative protection and a poor rating for riparian zone width.
3.6 Fish Tissue Data
Because certain organochlorine pesticides and PCBs were detected in both the sediment and the water
column of the upper watershed, there was concern that these parameters could bioaccumulate in aquatic
species to levels potentially harmful to human health via consumption of fish. In a screening study in April
2016, fish were collected from a sampling reach in the main channel of Proctor Creek at North Avenue
(PC3), including a fishing pond at the confluence of the tributary which flows past the North Avenue CSO
(PC4). Redbreast sunfish and green sunfish were collected in sufficient quantities to analyze three
composite samples for metals and organics. No metals were found at harmful levels, but concentrations
of dieldrin, heptachlor epoxide and/or PCBs were above trigger values established by GADNR for no
more than one meal per week of both species (USEPA 2016a). Dieldrin was above the trigger value for
no more than one meal per month in redbreast sunfish only.
A follow-up sampling event in July 2017 was conducted both at the screening study location (PC3) and
in the lower watershed at Jackson Parkway (PC8), to assess spatial variability (Table 1, Figure 2).
Sufficient redbreast sunfish, green sunfish, and yellow bullhead catfish were collected at PC3, while only
redbreast sunfish and brown bullhead catfish were collected at PC8 in adequate numbers to meet listing
requirements. Levels of PCB Aroclor 1254 in redbreast and green sunfish in the upper watershed were
above concentrations corresponding to a consumption advisory of no more than one meal per month
(USEPA 2018a). Levels of PCB Aroclor 1254 in yellow bullhead catfish in the upper watershed, and in
redbreast sunfish and brown bullhead catfish in the lower watershed, were above the threshold for a
recommendation of no more than one meal per week. A summary of findings is shown in Table 10. More
details are provided in the final reports for the Proctor Creek Fish Tissue Screening (USEPA 2016a) and
the Proctor Creek Fish Tissue study (USEPA 2018a).
4.0	Discussion
4.1	Upper Watershed: Downtown and CSO Facilities
Overall, the majority of constituents found in both water and sediment samples were highest in tributaries
draining the western Atlanta urban area, and in the main channel below their confluences with Proctor
Creek. These stations included Greensferry, Lindsay Street, North Avenue CSO, and Proctor Creek at
both North Avenue and Hollowell Parkway (Figure 2). In the water column, nutrients were elevated at all
five of these locations, although the fractions of nitrogen and phosphorus varied according to location. A
range of metals and organic compounds were also present in both the water column and the sediment at
these stations, at concentrations higher than most other locations in the watershed.
The tributary that flows through the decommissioned Greensferry CSO facility originates in an area of
high-density residential and commercial land use. Below the Greensferry station, both nitrogen and
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phosphorus were very high, with ammonia accounting for nearly 20% of TN and dissolved phosphorus
accounting for approximately 90% of TP. E. coli levels there were typically 10-20X higher than the
applicable fecal coliform water quality standard, and approximately 100X higher than the standard in
September 2015 and July 2017. In an urban environment, these high dissolved nutrient and E. coli
concentrations can be indications of leaking sewer infrastructure. This location is entirely channelized at
the sampling point, receiving urban runoff from the neighborhood as well as the outskirts of downtown
Atlanta. Most of this catchment is also channelized or piped underground, which can make it difficult to
locate and repair potential sewage leaks.
The Lindsay Street tributary flows through a similar high-density residential neighborhood before
eventually reaching the North Avenue CSO downstream. Upstream at Lindsay Street, this tributary had
the highest total nitrogen concentrations in the watershed, with an average of 96% occurring as nitrate-
nitrite, and the widest range in E. coli levels due to the single highest data point observed during the study,
yet relatively low phosphorus concentrations. Lindsay Street also had high calcium, nitrate, and sulfate, a
deposit of chlordane in the sediment, and several metals including lead, strontium, titanium, and zinc. All
of these can occur in urban runoff, with major sources including the residential or commercial application
of fertilizers and pesticides, and the accumulation of automotive fluids, exhaust and tire wear on roads.
Further downstream in this tributary, below the North Avenue CSO facility, there were higher proportions
of organic nitrogen and particulate phosphorus compared to the Greensferry tributary, and significantly
lower E. coli concentrations that were typically below the water quality standard. Effects of urban runoff
were also evident at this station, which had higher conductivity, including component ions, as well as
increased heavy metals including arsenic, lead and zinc. Both sodium and chloride were elevated, with
maximum values of each following the January 2017 storm event, likely due to runoff of salt used to deice
roads. There were also significantly higher levels of TOC, iron and manganese than most other stations,
and significantly lower total nitrogen than upstream at Lindsay Street, with nitrate levels dropping
approximately 10-fold. This tributary flows from the English Avenue neighborhood through an open field
towards the North Avenue CSO facility, which could allow for increased microbial denitrification rates.
Additionally, metabolic activity of iron-oxidizing bacteria at the sampling location, where iron was
observed in high concentrations, could contribute to decreased nitrate as well as the low dissolved oxygen
levels observed throughout the study.
Additional metals and organics were elevated primarily in the downtown area. In the water column, the
organochlorine pesticides chlordane and heptachlor epoxide were above 7Q10 WQS at several downtown
locations, while dieldrin was at lower levels. In the sediment, concentrations of copper, lead, and PAHs
were at levels of potential concern for aquatic organisms, particularly in Proctor Creek at both North
Avenue and Hollowell Parkway, and the North Avenue CSO tributary. PAHs include compounds
associated with automotive emissions that accumulate on roads, then wash into receiving waters during
storm events. It is therefore unsurprising to find them in higher concentrations near downtown Atlanta.
Together, the combination of parameters found in downtown tributaries of Proctor Creek is characteristic
of urban streams across the country, which typically have elevated nutrients, fecal bacteria, pesticides and
PAHs (Paul & Meyer 2001), as well as a range of metals including copper, lead, and zinc (Sansalone and
Buchberger 1997). These contaminants are commonly found in urban runoff, as commercial properties
and high-density residential areas create a high proportion of impervious surface in the form of roads,
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buildings and parking lots. Automotive fluids and exhaust, fertilizers and pesticides, and leaking sewer
infrastructure all contribute to the mixture of contaminants entering the upper reaches of Proctor Creek.
4.2	Mainstem Proctor Creek
Proctor Creek originates in a medium-density residential neighborhood bordering 1-20 to the north, then
flows along the western edge of downtown Atlanta before heading northwest to its confluence with the
Chattahoochee River. The upstream reach sampled at Burbank Drive had relatively low phosphorus and
moderate nitrogen, but E. coli counts were consistently above fecal coliform water quality standards. The
pesticides chlordane and dieldrin were also detected in the water column, and the breakdown product
heptachlor epoxide was above the 7Q10 standard. Thus, both E. coli and pesticides originate from
neighborhoods in the upper watershed as well as those closer to downtown. However, there were no
elevated ions or metals in the upper reach, which appears to have primarily residential impacts versus the
urban impacts evident further downstream.
The majority of contaminants appear to enter the main channel of Proctor Creek at the Greensferry and
North Avenue CSO tributaries, as described above. Surface water concentrations of nutrients were low in
the upper reach of the main channel, with peaks at North Avenue below the Greensferry tributary and
gradual decreases downstream of Hollowell Parkway (Figures 5-6). Metals and organic compounds in the
sediment followed a similar pattern in the main channel, with the highest concentrations at North Avenue
and Hollowell Parkway (Tables 7-8). In contrast, organochlorine pesticides were elevated throughout the
upper watershed, with detections at Burbank, then declined in the lower watershed (Figure 7).
The residual effects of storms were also evident in the main channel of Proctor Creek. Discharge following
precipitation in this watershed is extremely flashy, with rapid rise and fall of the hydrograph due to the
high proportion of impervious surfaces in the watershed contributing more overland runoff versus slower
subsurface infiltration. Following the two storms that occurred prior to quarterly sampling events,
aluminum, lead and zinc were elevated in the lower portion of the watershed, which was sampled while
flows receded. These three metals are all associated with higher turbidity, as they bind to particulates that
become suspended in the water column during storms (Horowitz et al. 2008, Horowitz 2009). The targeted
pesticides and PCBs were not noticeably higher during post-storm sampling, but these compounds may
increase during the 'first flush' of a rain event, during which certain chemicals are washed into receiving
waters and spike in concentration earlier in the hydrograph. The stormwater sampling currently in progress
should elucidate general patterns, and help to identify any parameters which potentially exceed water
quality standards applicable at or above annual average flow conditions.
4.3	Proctor Creek Tributaries
Eight tributaries of Proctor Creek were sampled in this study, each with unique characteristics likely
influenced by differing land uses in the associated subcatchment. The three tributaries which drain the
upper watershed near downtown Atlanta were the largest sources of nutrients, E. coli, pesticides, and
PAHs, as discussed previously. Urban effects were less evident in the Grove Park tributary, where metals
and organics were not at levels of concern in the sediment or the water column during baseflow conditions,
and E. coli was below the water quality standard for fecal coliform on most dates sampled. This
subcatchment is also on the western edge of downtown, but land use transitions to medium-density
residential here with fewer commercial properties and less impervious surface (ARC 2009).
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Spanning the northern boundary of the watershed are two large rail yards operated by CSX and Norfolk
Southern. Impacts of this infrastructure were evident downstream, in the tributary flowing through the
West Highlands neighborhood. Some metals, such as cadmium and lead, were at sediment concentrations
similar to those found near downtown, and other metals such as barium, manganese, strontium, and zinc
were elevated in the water column. Total organic carbon and specific conductance, including component
ions calcium, magnesium, sodium and potassium, were also relatively high in this tributary. All of these
constituents could be attributed to the rail yard, with track beds composed of crushed rock, treated lumber
and steel tracks, oil and grease lubricants, and various components of the train cars as well as materials
hauled (Wilkomirski et al. 2011, Vo et al. 2015). There was also one extremely high measurement of E.
coli during a sanitary sewer overflow in the neighborhood itself, caused by a blocked sewer pipe that was
quickly resolved by the city, but otherwise E. coli levels were consistently below the water quality
standard. The sampling reach was in a central part of the neighborhood, which is a new development still
partially under construction, and common residential effects such as nutrients and pesticides were
therefore low.
At the downstream end of the watershed, the Lillian Cooper Park and AD Williams tributaries are furthest
removed from urban Atlanta. However, Lilian Cooper Park and AD Williams are both near industrial
plants, and the latter flows along a large landfill. Each of these streams had some elevated metals as well
as a few detections of organic parameters. AD Williams had higher arsenic, strontium and titanium levels,
which could be associated with either industrial parks or the landfill. Conductivity was also higher here,
possibly resulting from crushed rock fill material or runoff from the landfill. Lillian Cooper Park had
higher turbidity, as well as higher aluminum, iron, lead and zinc, which can all bind to sediment particles
(Horowitz et al. 2008). This stream was highly incised, with primarily sandy substrate. Additionally, the
Lillian Cooper Park tributary was lower in dissolved oxygen, compared to other stations, which was likely
due to the very low flows and shallow water levels on most sampling dates.
In contrast, the Spring Street tributary contributes nearly a third of the drainage area to Proctor Creek, yet
was the lowest in nearly all parameters. This subcatchment is dominated by medium-density residential
neighborhoods, with one large cemetery and several small parks that consist of both forested and open
spaces. No contaminants were detected at levels of concern in either the surface water or sediment in this
tributary except E. coli, which exceeded the fecal coliform standard during six of the eight quarterly
events. All other analytes were at or below average levels for the watershed, with only low detections of
organochlorine pesticides in the water column and no detections of organic compounds in the sediment.
4.4 Macroinvertebrate Bioassessments
The macroinvertebrate data collected in Proctor Creek indicated relatively poor conditions at all four
locations, with habitat scores that were more variable according to location in the watershed. Biological
assessments are useful in water quality studies because aquatic organisms integrate the effects of
pollutants over time, and macroinvertebrates in particular have been shown to correlate well with
ecological condition in urban environments, versus other biological indicators such as algae or fish (Paul
& Meyer 2001). Chironomids (non-biting midges) and oligochaetes (aquatic worms) were the main taxa
present, and are those commonly found in urban watersheds (Walsh et al. 2005). These organisms are well
adapted to high deposition environments with sandy substrates that shift during storm events, which was
a common habitat characteristic in most reaches of Proctor Creek assessed in this study. The dominant
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species identified at three of the four macroinvertebrate sampling locations, Hydropsyche betteni, is a net-
spinning caddisfly with high tolerance to pollution. No individuals in the sensitive orders Ephemeroptera
(mayflies) or Plecoptera (stoneflies) were found at any of the sampling locations, as these taxa are
generally less tolerant to pollution, and require more stable substrates and higher detrital inputs for feeding
and habitat (Merritt el al. 2008). Scouring and flushing of organic detritus during high flows can also
hinder colonization, and frequent disturbances were evident from the incised banks and heavy
sedimentation throughout the watershed.
4.5 Fish Consumption Advisories
Since concentrations of some organochlorine pesticides and PCBs were detected at several locations above
sediment quality benchmarks and aquatic life criteria, fish tissue was examined to determine whether
contaminants were at levels of concern for human health. Fish collected in the upper and lower watershed
included redbreast and green sunfish, and yellow and brown bullhead catfish. No metals were found at
harmful levels in any of the fish collected. However, the pesticides dieldrin and heptachlor epoxide were
above trigger values for consumption advisories in the upper watershed, and the PCB Aroclor 1254 was
above trigger values at both locations. These chemicals, known as persistent organic pollutants, were
banned in the United States in the late 20th century, but remain in the environment at levels that can be
toxic or carcinogenic to aquatic organisms as well as humans via bioaccumulation (USEPA 2000b,
Gilliom et al. 2006). Overall, these data point to a recommended consumption limit of no more than one
meal per week for all fish species caught for food in Proctor Creek. An additional advisory is
recommended for no more than one meal per month of both redbreast and green sunfish caught in the
upper Proctor Creek watershed, where contaminants were found at higher levels.
5.0 Conclusions
This monitoring study was designed to assess current baseline conditions in the Proctor Creek watershed.
Results confirm that E. coli levels are still high throughout the watershed, with the most significant inputs
occurring primarily at the Greensferry tributary near downtown. E. coli was strongly correlated with
precipitation, as higher levels were detected following storm events, and with total dissolved phosphorus,
which is also associated with sewer leaks in urban environments. Nutrients, both nitrogen and phosphorus,
were also elevated in the downtown area. Metals and organic compounds were present at relatively low
levels during baseflow conditions, mainly in downtown reaches, and generally not at levels of concern
except for lead, which was found above chronic exposure limits for the protection of aquatic life. However,
many of these constituents are exported during high flow events, especially during the 'first flush' of
storms as contaminants are washed off impervious surfaces into receiving waters. Stormwater collections
currently in progress will therefore assess whether any contaminants may be above annual average water
quality standards during higher flows.
Potentially harmful concentrations of organochlorine pesticides and PCBs were also detected in Proctor
Creek. Levels of chlordane and heptachlor epoxide in the water column were above 7Q10 water quality
standards in the upper watershed, and chlordane was above probable effect thresholds in sediment at
Lindsay Street. Dieldrin, heptachlor epoxide, and PCBs were all elevated in fish tissue at concentrations
that correspond to a potential human health risk through consumption of fish, particularly in the upper
watershed. Fish consumption advisories, along with community education efforts and signs posted at
popular fishing locations in the watershed, will hopefully reduce human exposure to these contaminants.
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Projects currently planned for the Proctor Creek watershed, including the installation of green
infrastructure along roads and in public parks, should help to reduce stormwater runoff and improve water
quality conditions. The replacement of impervious surface with permeable substrates allows more
filtration of nutrients and contaminants, and can also reduce stream velocity during storm events, which
can in turn decrease the rates of flooding and stream bank erosion. Ongoing efforts by the City of Atlanta
to address leaking sewer infrastructure may also reduce nutrient and fecal bacteria levels. As these projects
move forward in Proctor Creek, potential improvements in water chemistry, habitat quality,
macroinvertebrate communities, and fish tissue contaminants may be tracked in comparison with data
generated by this study.
6.0 References
ARC. 2009. Visual field survey for Proctor Creek impaired stream segment in the Chattahoochee River
basin. Atlanta Regional Commission, Atlanta, GA.
ARC. 2010. Monitoring report for Proctor Creek: Headwaters to Chattahoochee River. Atlanta Regional
Commission, Atlanta, GA.
ARC. 2011. Monitoring report for Proctor Creek watershed targeted sampling: Headwaters to North
Avenue. Atlanta Regional Commission, Atlanta, GA.
Barbour, M.T., J. Gerritsen, B.D. Snyder and J.B. Stribling. 1999. Rapid Bioassessment Protocols for Use
in Streams and Wadeable Rivers: Periphyton, Benthic Macroinvertebrates and Fish, Second
Edition. EPA 841-B-99-002. U.S. EPA, Office of Water, Washington, D.C.
CRK. 2018. Neighborhood water watch monitoring data, www.chattahoochee.org/nww. Chattahoochee
Riverkeeper, Atlanta, GA. Accessed 04/30/18.
GADNR. 2007. Macroinvertebrate Biological Assessment of Wadeable Streams in Georgia. Standard
Operating Procedures. Version 1.0. Watershed Protection Branch, Environmental Protection
Division, Georgia Department of Natural Resources, Atlanta, GA.
GADNR. 2016. Georgia Department of Natural Resources Fish Consumption Guidance. Watershed
Protection Branch, Environmental Protection Division, Georgia Department of Natural
Resources, Atlanta, GA.
Gilliom, R.J., J.E. Barbash, C.G. Crawford, P.A. Hamilton, J.D. Martin, N. Nakagaki, L.H. Nowell, J.C.
Scott, P.E. Stackelberg, G.P. Thelin and D.M. Wolock. 2006. The Quality of Our Nation's Waters:
Pesticides in the Nation's Streams and Ground Water, 1992-2001. U.S. Geological Survey Circular
1291.
Gore, J. A., A. Middleton, D.L. Hughes, U. Rai and M. Brossett. 2005. Reference Conditions for Wadeable
Streams in Georgia with a Multimetric Index for the Bioassessment and Discrimination of
Reference and Impaired Streams. Georgia Department of Natural Resources, Atlanta, GA.
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Horowitz, A.J. 2009. Monitoring suspended sediments and associated chemical constituents in urban
environments: lessons from the city of Atlanta, Georgia, USA water quality monitoring program.
Journal of Soils and Sediments 9:342-363.
Horowitz, A.J., K.A. Elrick and J.J. Smith. 2008. Monitoring urban impacts on suspended sediment, trace
element, and nutrient fluxes within the City of Atlanta, Georgia, USA: program design,
methodological considerations, and initial results. Hydrological Processes 22:1473-1496.
Jones, D.S. and G.W. Suter, II. 1997. Toxicological benchmarks for screening contaminants of potential
concern for effects on sediment-associated biota: 1997 revision. ES/ER/TM-95/R4.
Lawrence, S.J. and J.H. LaFontaine. 2010. Occurrence of organic wastewater-indicator compounds in
urban streams of the Atlanta area, Georgia, 2003-2006: U.S. Geological Survey Scientific
Investigations Report 2010-5209, 113 pp.
Merrit, R.W., K.W. Cummins and M.B. Berg, Eds. 2008. An Introduction to the Aquatic Insects of North
America. Fourth Edition. Kendall Hunt, Dubuque, IA.
NCDEQ. 2016. Standard Operating Procedures for the Collection and Analysis of Benthic
Macroinvertebrates. Version 5.0. Division of Water Resources, North Carolina Department of
Environmental Quality, Raleigh, NC.
Paul, M.J. and J.L. Meyer. 2001. Streams in the urban landscape. Annual Review of Ecology and
Systematics 32:333-365.
R Core Team. 2014. R: A language and environment for statistical computing. R Foundation for Statistical
Computing, Vienna, Austria. ISBN 3-900051-07-0, URL http://www.R-proiect.org/.
Sansalone, J.J. and S.G. Buchberger. 1997. Partitioning and first flush of metals in urban roadway storm
water. Journal of Environmental Engineering 123:134-143.
USEPA. 2000a. Ambient Water Quality Criteria Recommendations. Information Supporting the
Development of State and Tribal Nutrient Criteria. Rivers and Streams in Nutrient Ecoregion IX.
EPA 822-B-00-019. Office of Science and Technology, Office of Water, Washington, D.C.
USEPA. 2000b. Guidance for Assessing Chemical Contaminant Data for Use in Fish Advisories:
Volume 1, Fish Sampling and Analysis. Third Edition. EPA 823-B-00-007. Office of Science
and Technology, Office of Water, Washington, D.C.
USEPA. 2000c. Prediction of sediment toxicity using consensus-based freshwater sediment quality
guidelines. EPA-905/R-00/007. Great Lakes National Program Office, Chicago, IL.
USEPA. 2013. Proctor Creek Microbial Sampling Study, Atlanta, GA. Final Report. SESD Project ID
#12-0300. Region 4, SESD, Athens, GA.
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USEPA. 2015a. Proctor Creek Watershed Monitoring, Quality Assurance Project Plan. SESD Project ID
#15-0425. Region 4, SESD, Athens, GA.
USEPA. 2016a. Proctor Creek Fish Tissue Screening. Final Report. Project ID #16-0373. Region 4, SESD,
Athens, GA.
USEPA. 2016b. Proctor Creek Watershed Monitoring: First Quarterly Sampling Event. Final Report.
SESD Project ID #15-0425. Region 4, SESD, Athens, GA.
USEPA. 2017. Procedure for Enumerating Total Coliforms and E. coli using Idexx Colilert. SOP ID D-
EMMD-MEB-SOP-1062-0. Office of Research and Development, National Exposure Research
Laboratory, Athens, GA.
USEPA. 2018a. Proctor Creek Fish Tissue. Final Report. Project ID #17-0445. Region 4, SESD, Athens,
GA.
USEPA. 2018b. SESD Analytical Services Branch Laboratory Operations and Quality Assurance Manual
(ASB LOQAM). United States Environmental Protection Agency. Region 4, SESD, Athens, GA.
Van Metre, P.C. and C.A. Journey. 2014. The Southeast Stream Quality Assessment: U.S. Geological
Survey Fact Sheet 2014-3023, 2 p.
Vo, P.T., H.H. Ngo, W. Guo, J.L. Zhou, A. Listowski, B. Du, Q. Wei and X.T. Bui. Stormwater quality
management in rail transportation: Past, present and future. Science of the Total Environment
512(353-363).
Walsh, C.J., A.H. Roy, J.W. Feminella, P.D. Cottingham, P.M. Groffman and R.P. Morgan II. 2005. The
urban stream syndrome: current knowledge and the search for a cure. Journal of the North
American Benthological Society 24(706-723).
Wenning, R.J., G.E. Batley, C.G. Ingersoll and D.W. Moore (Eds.). 2005. Use of sediment quality
guidelines and related tools for the assessment of contaminated sediments. Pensacola, FL: Society
of Environmental Toxicology and Chemistry (SETAC).
Wilkomirski, B., B. Sudnik-Qojcikowska, H. Galera, M. Wierzbicka and M. Malawska. 2011. Railway
transportation as a serious source of organic and inorganic pollution. Water, Air, and Soil Pollution
218(333-345.
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Table 1: Quarterly, macroinvertebrate and fish tissue sampling locations in the mainstem (MAIN) and
tributaries (TRIB) of Proctor Creek.

Station
Station Name
Location
Location Description
Location (Decimal Degrees)

ID
Type
Latitude
Longitude

PCI
Burbank
MAIN
Proctor Creek at Burbank Drive
33.75710
-84.42892

PC2
Greensferry
TRIB
Tributary below decommissioned Greensferry CSO
33.76075
-84.42691

PC3
North Avenue
MAIN
Proctor Creek at North Avenue
33.76800
-84.42769

PC4
North CSO
TRIB
Tributary downstream of North Avenue CSO outfall
33.76863
-84.42689

PC5
Hollowell
MAIN
Proctor Creek at Hollowell Parkway
33.77199
-84.42990
oo
c
PC6
Hortense
MAIN
Proctor Creek at Hortense Place
33.77562
-84.44072
Q.
E
PC7
Kerry Circle
MAIN
Proctor Creek at Kerry Circle
33.79214
-84.45208
oo
>•
PC8
James Jackson
MAIN
Proctor Creek at James Jackson Parkway
33.79461
-84.47417
QJ
¦4—'
PC9
Northwest
MAIN
Proctor Creek at Northwest Drive
33.79931
-84.48682
D"
PC10
Lindsay Street
TRIB
Tributary at Lindsay Street Park
33.76941
-84.41611

PC11
Grove Park
TRIB
Tributary at Grove Park
33.77406
-84.44029

PC12
Spring Street
TRIB
Tributary at Spring Street
33.78849
-84.46597

PC13
AD Williams
TRIB
Tributary at Northwest Drive
33.79633
-84.48602

PCM
Lillian Cooper
TRIB
Tributary at Lillian CooperShepherd Park
33.79799
-84.47842

PC15
West Highlands
TRIB
Tributary at Hollingsworth Boulevard
33.79076
-84.44724

PC5/6
Hortense/
MAIN
Macroinvertebrate sampling reach: upstream end
33.77676
-84.43568
oo
QJ
•M
n:
Hollowell
Macroinvertebrate sampling reach: downstream end
33.77633
-84.43674
PC8
James Jackson
MAIN
Macroinvertebrate sampling reach: upstream end
33.79497
-84.47330
QJ
•M
QJ
>
C
Macroinvertebrate sampling reach: downstream end
33.79458
-84.47411
PC11
Grove Park
TRIB
Macroinvertebrate sampling reach: upstream end
33.77435
-84.44035
u
n:
Macroinvertebrate sampling reach: downstream end
33.77507
-84.44014
E
PC12
Spring Street
TRIB
Macroinvertebrate sampling reach: upstream end
33.78577
-84.46365

Macroinvertebrate sampling reach: downstream end
33.78649
-84.46378

PC3
North Avenue
MAIN
Fish sampling reach: upstream end
33.76862
-84.42725
D
oo
oo
(UPPER)
Fish sampling reach: downstream end
33.77199
-84.42990
•M
_c
oo
PC8
James Jackson
MAIN
Fish sampling reach: upstream end
33.79493
-84.47372
M—
(LOWER)
Fish sampling reach: downstream end
33.79526
-84.47643
Table 2: Precipitation totals (inches) at 24, 48, 72 hours and 7 days prior to the start of each sampling
event.

Sampling Date
Increment
9/2/15
1/12/16
4/5/16
7/26/16
10/18/16
1/24/17
4/11/17
7/18/17
24 hours
0.00
0.00
0.00
0.00
0.00
0.32
0.00
0.21
48 hours
0.19
0.03
0.00
0.00
0.03
1.08
0.00
0.36
72 hours
0.75
0.27
0.04
0.00
0.03
3.09
0.00
0.37
7 days
0.75
0.51
1.45
0.51
0.03
3.60
4.38
0.45
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 21 of 36

-------
Table 3: Data from in situ water quality measurements, discharge calculations, fecal bacteria analysis (E. coli), and rapid visual
habitat assessment scores (out of 200). Values are means and one standard error, with number of data points (n) listed.


PCI
PC2
PC3
PC4
PC5
PC6
PC7
PC8
PC9
PC10
PC11
PC12
PC 13
PC 14
PC15


Burbank
Greens-
North
North
Hollowell
Hortense
Kerry
James
North-
Lindsay
Grove
Spring
AD
Lillian
West
Analyte
n
ferry
Avenue
CSO
Circle
Jackson
west
Street
Park
Street
Williams
Cooper
Highlands
Temperature
8
18.28
20.13
19.08
17.55
17.78
18.27
19.12
17.91
17.02
19.08
17.69
17.91
17.03
15.02
17.76
(°C)

(2.13)
(1.23)
(1.76)
(2.05)
(2.00)
(2.74)
(2.59)
(2.59)
(2.55)
(1.10)
(2.53)
(2.60)
(2.34)
(2.14)
(1.58)
PH
8
7.33
7.07
7.41
6.84
7.10
7.51
7.44
7.58
7.31
6.89
7.52
7.43
7.56
7.16
7.47
(s.u.)

(0.09)
(0.03)
(0.09)
(0.07)
(0.09)
(0.12)
(0.04)
(0.15)
(0.13)
(0.06)
(0.12)
(0.04)
(0.06)
(0.17)
(0.06)
Sp Conductance
8
187
303
281
506
286
262
284
248
252
381
205
180
514
137
578
(|iS/cm)

(3)
(9)
(17)
(111)
(5)
(18)
(15)
(18)
(22)
(18)
(6)
(8)
(47)
(7)
(14)
Dissolved Oxygen
8
9.19
7.36
9.13
2.13
8.56
9.29
9.05
9.79
8.97
7.96
9.16
9.35
8.91
6.95
8.28
(mg/L)

(0.45)
(0.42)
(0.43)
(0.36)
(0.71)
(0.63)
(0.55)
(0.62)
(0.66)
(0.37)
(0.63)
(0.53)
(0.52)
(1.22)
(0.33)
Turbidity
8
1.93
1.80
2.06
1.95
1.60
5.30
7.60
7.10
9.25
0.51
2.44
3.13
2.31
9.22
6.71
(NTU)

(0.34)
(0.26)
(0.25)
(0.51)
(0.35)
(2.61)
(3.54)
(3.76)
(4.76)
(0.10)
(0.43)
(0.81)
(0.64)
(3.68)
(1.30)
Discharge
8
0.35
1.07
1.45
<0.1
1.69
2.57
3.93
7.06
7.88
<0.1
0.59
1.25
0.34
<0.1
0.20
(cfs)

(0.07)
(0.07)
(0.16)
NA
(0.11)
(0.40)
(0.69)
(1.52)
(1.41)
NA
(0.14)
(0.32)
(0.08)
NA
(0.03)
E. coli
8
4,121
12,853
11,801
520
2,217
1,548
3,059
1,232
2,039
6,410
509
1,543
361
580
2,162
(MP N/100 mL)

(1,114)
(2,956)
(3,247)
(221)
(986)
(657)
(1,581)
(752)
(1,117)
(4,988)
(155)
(493)
(116)
(163)
(1,946)
Habitat Score
1
97
NA
116
95
132
129
104
131
149
118
108
125
123
55
132
Table 4: Coefficients for Spearman Rank correlations between E. coli data, turbidity, precipitation totals in the 24h, 48h and 72h
prior to sampling, select water chemistry parameters and discharge. All correlation coefficients shown in bold are significant at
p<0.05.

Spearman Rank Coefficients
Parameter
Turbidity
24h
48h
72h
TP
TDP
TN
TKN
N03
TOC
Sp. Cond.
Total Alk.
PH
Ca
Na
CI
Discharge
E. coli
0.17
0.35
0.32
0.29
0.50
0.45
0.39
0.33
0.34
-0.35
-0.33
-0.27
-0.29
-0.23
-0.28
-0.22
0.23
Turbidity
--
0.47
0.37
0.32

Aluminum
0.49
0.34
0.29
0.23
Lead
0.16
0.19
0.13
0.05
Zinc
0.19
0.35
0.30
0.28
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 22 of 36

-------
Table 5: Surface water data means (with one standard error) for nutrients and classical parameters, with the number of data points (n)
from a maximum of eight sampling events. Dissolved nutrients are also expressed as a percentage of total nitrogen (TN) or total
phosphorus (TP). Cells shaded in grey indicate values below detection at the minimum reporting limit indicated.


PCI
PC2
PC3
PC4
PC5
PC6
PC7
PC8
PC9
PC10
PC11
PC12
PC13
PCM
PC15
Analyte

Burbank
Greens-
North
North
Hollowell
Hortense
Kerry
James
North-
Lindsay
Grove
Spring
AD
Lillian
West
n

ferrv
Avenue
CSO


Circle
Jackson
west
Street
Park
Street
Williams
Cooper
Highlands
Total Nitrogen
8
1.51
3.65
2.51
0.88
2.28
1.69
1.66
1.31
1.27
4.30
0.82
1.04
1.71
0.61
1.54
(mg/L)

(0.17)
(0.23)
(0.22)
(0.20)
(0.14)
(0.10)
(0.17)
(0.17)
(0.15)
(0.18)
(0.09)
(0.11)
(0.19)
(0.18)
(0.17)
Total Kjehdal N
8
0.26
1.30
0.46
0.50
0.35
0.32
0.35
0.27
0.31
0.17
0.23
0.32
0.48
0.27
0.50
(mg/L)

(0.06)
(0.17)
(0.09)
(0.07)
(0.02)
(0.03)
(0.04)
(0.04)
(0.04)
(0.01)
(0.03)
(0.05)
(0.10)
(0.14)
(0.17)
Nitrate/Nitrite
8
1.25
2.35
2.05
0.39
1.93
1.37
1.31
1.03
0.96
4.14
0.59
0.72
1.24
0.33
1.04
(mg/L)

(0.13)
(0.10)
(0.21)
(0.22)
(0.12)
(0.10)
(0.17)
(0.17)
(0.15)
(0.18)
(0.09)
(0.06)
(0.10)
(0.16)
(0.04)
% of TN

83
64
82
44
85
81
79
79
76
96
72
69
72
55
68
Ammonia
8
0.04
0.69
0.14
0.23
0.09
0.06
0.04
0.04
0.05
0.03
0.03
0.10
0.15
0.13
0.27
(mg/L)

(0.02)
(0.15)
(0.05)
(0.05)
(0.02)
(0.02)
(0.01)
(0.01)
(0.02)
(0.00)
(0.00)
(0.03)
(0.09)
(0.09)
(0.09)
% of TN

3
19
6
27
4
3
3
3
4
0
0
10
9
22
18
Total Phosphorus
8
0.04
0.41
0.24
0.13
0.17
0.08
0.05
0.04
0.04
0.05
0.03
0.05
0.03
0.03
0.02
(mg/L)

(0.01)
(0.08)
(0.06)
(0.02)
(0.04)
(0.01)
(0.01)
(0.01)
(0.01)
(0.01)
(0.01)
(0.01)
(0.01)
(0.01)
(0.01)
Total Dissolved P
7
0.02
0.37
0.22
0.06
0.13
0.05
0.03
0.02
0.02
0.04
0.02
0.02
0.02
0.02
0.02
(mg/L)

(0.01)
(0.09)
(0.07)
(0.02)
(0.04)
(0.01)
(0.01)
(0.01)
(0.00)
(0.01)
(0.01)
(0.01)
(0.00)
(0.00)
(0.01)
% of TP

58
90
89
46
76
59
49
52
54
82
65
49
63
45
100
Total Organic Carbon
6
1.00
2.23
1.73
5.65
1.92
1.63
2.62
2.72
2.95
1.90
1.78
2.47
7.08
2.60
7.85
(mg/L)

(0.25)
(0.39)
(0.42)
(0.94)
(0.51)
(0.31)
(0.53)
(0.52)
(0.43)
(0.54)
(0.27)
(0.40)
(1.05)
(0.56)
(1.17)
Total Suspended Solids
4
4.00
4.00
4.00
4.95
4.00
4.00
4.00
4.00
4.00
4.75
4.00
4.00
4.00
4.00
4.00
(mg/L)

(0.00)
(0.00)
(0.00)
(1.71)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(2.75)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
Bromide
4
0.10
0.10
0.10
0.10
0.10
0.10
0.10
0.10
0.10
0.10
0.10
0.10
1.25
0.10
0.10
(mg/L)

(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.35)
(0.00)
(0.00)
Chloride
8
11.75
20.13
22.00
82.50
21.13
19.96
14.89
12.98
14.58
18.00
13.64
12.25
58.63
9.32
21.38
(mg/L)

(0.41)
(1.14)
(5.22)
(33.41)
(2.00)
(4.41)
(1.78)
(1.43)
(1.75)
(0.46)
(0.83)
(0.53)
(9.24)
(0.88)
(0.65)
Fluoride
8
0.11
0.31
0.24
0.20
0.22
0.19
0.18
0.19
0.19
0.14
0.14
0.21
0.23
0.11
0.22
(mg/L)

(0.03)
(0.03)
(0.03)
(0.02)
(0.03)
(0.03)
(0.02)
(0.02)
(0.01)
(0.03)
(0.02)
(0.04)
(0.04)
(0.01)
(0.01)
Sulfate
8
15.50
35.88
30.00
22.21
30.13
28.25
39.88
33.13
30.38
66.25
24.50
16.75
18.20
13.03
67.25
(mg/L)

(1.02)
(1.38)
(0.93)
(6.40)
(1.08)
(1.63)
(3.65)
(2.97)
(3.28)
(4.74)
(1.70)
(1.46)
(3.67)
(3.59)
(2.99)
Total Alkalinity
6
51.83
68.33
63.50
123.00
75.33
71.00
72.17
65.83
73.33
74.83
51.67
43.67
161.67
34.00
205.00
(mg/LCaC03)

(2.44)
(2.36)
(2.64)
(32.28)
(7.17)
(5.57)
(2.68)
(3.45)
(3.62)
(4.90)
(1.96)
(1.71)
(10.14)
(6.16)
(8.85)
Hardness
7
60.44
88.44
82.89
129.46
89.16
80.45
93.70
80.69
79.30
129.55
64.19
52.60
127.59
37.68
214.81
(mg/LCaC03)

(2.06)
(3.27)
(2.69)
(33.00)
(2.91)
(3.91)
(6.33)
(6.09)
(6.97)
(8.76)
(2.94)
(3.11)
(10.83)
(2.31)
(9.92)
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 23 of 36

-------
Table 6: Surface water data means (with one standard error) for total recoverable metals, with the number of data points (n) from a
maximum of eight sampling events. Metals not detected in any water samples are listed in the Appendix. Cells shaded in grey indicate
values below detection at the minimum reporting limit indicated.


PCI
PC2
PC3
PC4
PC5
PC6
PC7
PC8
PC9
PC10
PC11
PC12
PC13
PCM
PC 15


Burbank
Greens-
North
North
Hollowell
Hortense
Kerry
James
North-
Lindsay
Grove
Spring
AD
Lillian
West
Analyte
n
ferry
Avenue
CSO
Circle
Jackson
west
Street
Park
Street
Williams
Cooper
Highlands
Aluminum
8
100
100
100
100
100
118
206
189
240
100
100
100
100
238
100
(|Jg/L)

(0)
(0)
(0)
(0)
(0)
(41)
(117)
(103)
(145)
(0)
(0)
(0)
(0)
(141)
(0)
Antimony
8
0.50
0.50
0.50
2.39
0.50
0.50
0.50
0.50
0.50
1.23
0.50
0.50
0.50
0.50
0.58
(|Jg/L)

(0.00)
(0.00)
(0.00)
(1.42)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.13)
(0.00)
(0.00)
(0.00)
(0.00)
(0.08)
Arsenic
8
0.50
0.50
0.50
0.80
0.50
0.50
0.50
0.50
0.50
0.50
0.50
0.50
0.56
0.50
0.61
(|Jg/L)

(0.00)
(0.00)
(0.00)
(0.15)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.06)
(0.00)
(0.11)
Barium
8
60.50
59.00
56.88
59.75
60.00
51.38
51.13
44.75
45.63
86.50
37.13
38.50
58.38
55.83
106.38
(|Jg/L)

(3.52)
(1.77)
(2.81)
(8.68)
(1.72)
(2.19)
(1.77)
(2.25)
(2.56)
(1.97)
(1.67)
(2.88)
(4.88)
(2.21)
(5.97)
Calcium
8
18250
26625
25000
45875
27125
24500
28875
24875
24375
41000
19750
16375
35375
11333
67000
(|Jg/L)

(701)
(1068)
(866)
(12558)
(895)
(1165)
(1807)
(1787)
(2078)
(2976)
(861)
(1085)
(2803)
(667)
(3443)
Iron
8
206
244
311
1738
313
401
419
413
479
126
325
424
291
1038
606
(|Jg/L)

(19)
(21)
(19)
(210)
(20)
(46)
(96)
(102)
(148)
(33)
(38)
(56)
(72)
(186)
(99)
Lead
8
0.50
0.50
0.50
2.00
0.63
2.25
1.66
1.33
1.36
1.43
0.50
0.50
0.50
0.72
1.20
(|Jg/L)

(0.00)
(0.00)
(0.00)
(0.57)
(0.13)
(1.01)
(0.41)
(0.46)
(0.67)
(0.30)
(0.00)
(0.00)
(0.00)
(0.22)
(0.38)
Magnesium
8
3538
5500
4950
3950
5238
4725
5000
4500
4513
6425
3725
2888
9575
2217
11488
(|Jg/L)

(112)
(177)
(124)
(592)
(169)
(279)
(363)
(392)
(448)
(324)
(186)
(119)
(869)
(162)
(429)
Manganese
8
20.90
81.38
64.63
491.25
65.25
57.00
58.00
49.75
54.56
24.75
52.00
48.23
137.90
173.50
553.75
(|Jg/L)

(4.97)
(15.23)
(13.01)
(75.91)
(14.84)
(12.78)
(13.57)
(14.31)
(14.24)
(2.66)
(8.07)
(14.24)
(48.87)
(47.62)
(53.82)
Potassium
8
3100
5613
4725
5238
4975
4388
5450
4563
4638
5663
3100
3113
6225
2450
6675
(|Jg/L)

(105)
(287)
(177)
(410)
(216)
(180)
(221)
(146)
(167)
(223)
(135)
(120)
(454)
(126)
(108)
Selenium
8
2.00
2.00
2.00
2.00
2.00
2.00
2.00
2.00
2.00
2.15
2.00
2.00
2.00
2.00
2.00
(|Jg/L)

(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.11)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
Sodium
8
9800
18000
17625
56625
16750
15850
15413
13650
14838
20125
11963
11588
51875
9317
34875
(|Jg/L)

(292)
(1134)
(2890)
(18751)
(1048)
(2558)
(1302)
(1302)
(1557)
(693)
(565)
(637)
(6531)
(908)
(2048)
Strontium
8
90.00
108.00
108.25
183.63
117.50
101.88
110.63
103.63
104.50
222.50
83.75
80.00
182.50
81.83
321.25
(|Jg/L)

(2.90)
(3.84)
(3.17)
(45.86)
(3.13)
(5.15)
(6.30)
(8.12)
(8.99)
(13.59)
(3.45)
(4.67)
(15.78)
(6.83)
(12.17)
Titanium
8
5.00
5.00
5.00
5.00
5.00
5.00
7.25
7.13
9.00
5.00
5.00
5.00
5.00
7.12
5.00
(|Jg/L)

(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(3.69)
(3.47)
(4.96)
(0.00)
(0.00)
(0.00)
(0.00)
(3.68)
(0.00)
Vanadium
8
5.00
5.00
5.00
5.00
5.00
5.00
5.00
5.00
5.00
5.00
5.00
5.00
5.00
5.00
5.03
(|Jg/L)

(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.00)
(0.03)
Zinc
8
11.63
9.13
7.75
22.00
9.38
11.50
13.88
10.88
10.38
72.00
8.63
12.00
7.50
22.83
45.13
(|Jg/L)

(3.33)
(1.61)
(1.36)
(7.96)
(1.83)
(2.10)
(4.62)
(3.29)
(2.80)
(4.99)
(1.85)
(3.01)
(1.68)
(8.79)
(19.77)
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 24 of 36

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Table 7: Metals data from sediment samples collected in September 2015. Samples below detection (U) at the minimum reporting
limit indicated are highlighted in grey. Additional data qualifiers are omitted for clarity. Sediment quality benchmarks are provided for
comparison, with values above the TEC highlighted in orange.

PCI
PC3
PC4
PC5
PC6
PC7
PC8
PC9
PC10
PC11
PC 12
PC13
PC 14
PC15
Analyte
(mg/kgdry)
ARCS
TEC
ARCS
PEC
Burbank
North
Avenue
North CSO
Hollowell
Hortense
Kerry
Circle
James
Jackson
Northwest
Lindsay
Street
Grove
Park
Spring
Street
AD
Williams
Lillian
Cooper
West
Highlands
Aluminum

58030
2500
3500
4100
2800
1900
1900
1200
1800
2600
2300
1400
1400
2200
2900
Antimony


0.20 U
0.23
0.43
1.2
0.20 U
0.20 U
0.20 U
0.20 U
0.59
0.20 U
0.20 U
0.24
0.20 U
2.0
Arsenic
12.1
57
0.24
0.49
0.67
0.37
0.26
0.28
0.23
0.26
0.95
0.20 U
0.20 U
0.37
0.27
2.8
Barium


41
50
64
35
18
18
12
17
41
23
19
28
26
42
Beryllium


0.30 U
0.30 U
0.29 U
0.30 U
0.30 U
0.30 U
0.30 U
0.29 U
0.35
0.30 U
0.29 U
0.30 U
0.30 U
0.30 U
Cadmium
0.59
11.7
0.099 U
0.099 U
0.20
0.13
0.11
0.099 U
0.099 U
0.098 U
0.23
0.10 U
0.098 U
0.099 U
0.52 U
0.37
Calcium


490
1100
3200
650
430
320
220
370
990
340
200
610
170
950
Chromium
56
159
8.5
12
8.0
11
4.8
7.7
3.0
4.3
6.2
4.5
2.5
3.1
13
5.8
Cobalt


2.2
3.1
2.4
2.1
1.3
1.2
0.95
1.1
2.1
1.5
1.6
1.7
1.6
3.2
Copper
28
77.7
15
17
43
19
6.7
6.7
6.0
5.8
41
7.3
3.1
11
4.2
18
Iron


5100
8100
7100
5800
3500
4000
2600
2700
7900
4200
2400
3900
4700
7900
Lead
34.2
396
19
36
30
44
15
20
7.0
22
95
20
5.9
12
6.4
100
Magnesium


1200
1800
2100
1400
810
740
440
440
1100
930
430
490
740
1400
Manganese
1673
1081
91
130
110
80
54
58
38
47
94
67
73
290
60
320
Nickel
39.6
38.5
2.7
4.6
3.7
3.5
1.7
2.3
1.4
1.1
3.5
1.3
0.98 U
3.7
1.5
5.5
Potassium


1000
1600
1500
1200
770
760
490
510
760
900
550
570
900
1200
Sodium


99 U
99 U
140
99 U
99 U
99 U
99 U
98 U
140
100 U
98 U
99 U
99 U
99 U
Strontium


3.8
5.9
21
4.0
3.9
3.3
1.7
14
11
2.1
1.6
2.7
1.9
4.6
Tin


3.4
3.8
5.0
14
1.5 U
6.7
2.4
1.7
20
1.6
1.5 U
2.3
1.5 U
6.1
Titanium


240
350
360
260
170
170
110
120
200
220
120
110
200
230
Vanadium


10
13
12
10
7.0
6.8
3.7
4.4
6.9
8.4
3.5
4.2
9.1
9.8
Yttrium


1.8
3.4
4.1
2.5
1.8
2.1
1.0
1.3
2.7
2.0
1.3
1.7
1.8
2.7
Zinc
159
1532
44
69
92
61
28
34
19
21
130
33
16
43
23
120
ARCS = Assessment & Remediation of Contaminated Sediments Program (Jones & Suter 1997)	U = The analyte was not detected at or above the reporting limit.
TEC = Threshold Effect Concentration
PEC = Probable Effect Concentration
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 25 of 36

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Table 8: Organic chemistry data from sediment samples collected in September 2015. Samples below detection (U) at the minimum
reporting limit indicated are highlighted in grey. Additional data qualifiers are omitted for clarity. Sediment quality benchmarks are
provided for comparison, with values above the TEC highlighted in orange and those above the PEC highlighted in yellow.
Compounds contributing to Total PAHs are indicated in green.
SEDIMENT PESTICIDES AND PCBs

PCI
PC3
PC4
PC5
PC6
PC7
PC8
PC9
PC10
PC11
PC12
PC13
PCM
PC15
Analyte (ng/kgdry)
ARCS
TEC
ARCS
PEC
CB
PEC
Burbank
North
Avenue
North CSO
Hollowell
Hortense
Kerry
Circle
James
Jackson
Northwest
Lindsay
Street
Grove
Park
Spring
Street
AD
Williams
Lillian
Cooper
West
Highlands
4,4'-DDT(p,p'-DDT)


62
5.0
11 U
13 U
11 U
11 U
2.2 U
2.2 U
11 U
2.2 U
2.2 U
12 U
2.2 U
2.3 U
11 U
Dieldrin


61.8
2.3 U
11 U
13 U
11 U
11 U
2.2 U
2.2 U
11 U
5.8
2.2 U
12 U
2.2 U
2.3 U
11 U
alpha-Chlordane
CB PEC = 17.6
for chlordane
2.3 U
11 u
13 U
11 u
11 u
2.2 U
2.2 U
11 u
24
2.2 U
12 U
2.2 U
2.3 U
11 u
gamma-Chlordane
2.3 U
11 u
13 U
11 u
11 u
2.2 U
2.2 U
11 u
59
2.5
12 U
2.2 U
2.3 U
11 u
PCB-1254 (Aroclor 1254)



85
27 U
12 U
21 U
13 U
46
11 U
18 U
54 U
11 U
11 U
22 U
11 U
12 U
PCB-1260 (Aroclor 1260)



86 U
26
12 U
20
12
47 U
11 U
11 U
54 U
11 U
11 U
21
11 U
11
SEDIMENT SEMI-VOLATILES

PCI
PC3
PC4
PC5
PC6
PC7
PC8
PC9
PC10
PC11
PC12
PC13
PCM
PC15
Analyte (ng/kgdry)
ARCS
TEC
ARCS
PEC
CB
PEC
Burbank
North
Avenue
North CSO
Hollowell
Hortense
Kerry
Circle
James
Jackson
Northwest
Lindsay
Street
Grove
Park
Spring
Street
AD
Williams
Lillian
Cooper
West
Highlands
(3-and/or4-)
Methylphenol



460 U
430 U
99
430 U
430 U
430 U
430 U
430 U
420 U
430 U
450 U
430 U
450 U
420 U
Acenaphthene



91 U
45
57
85 U
87 U
86 U
86 U
87 U
85 U
87 U
90 U
86 U
89 U
84 U
Anthracene
31.6
547.7
845
91 U
170
150
90
87 U
86 U
86 U
87 U
85 U
87 U
90 U
86 U
89 U
84 U
Benzo(a)anthracene
260
4200

91 U
750
750
540
290
74
64
89
78
87 U
90 U
86 U
110
84 U
Benzo(a)pyrene
350
393.7

91 U
850
830
650
370
88
82
120
86
55
90 U
86 U
110
44
Benzo(b)fluoranthene



48
1000
1200
770
460
100
85
110
110
80
90 U
44
150
57
Benzo(g,h,i)perylene
290
6300

91 U
570
530
460
250
51
59
76
92
47
90 U
86 U
83
84 U
Benzo(k)fluoranthene



47
890
890
620
390
85
83
100
87
65
90 U
86 U
120
49
Bis(2-ethyl hexyl)
phthalate



460 U
430 U
590
430 U
430 U
430 U
430 U
430 U
420 U
430 U
450 U
430 U
450 U
420 U
Carbazole



91 U
180
180
120
50
86 U
86 U
87 U
85 U
87 U
90 U
86 U
89 U
84 U
Chrysene
500
5200
1290
49
1000
970
740
420
94
80
110
99
71
90 U
86 U
150
47
Dibenz(a,h)anthracene

28.2

91 U
240
180
170
84
86 U
86 U
87 U
85 U
87 U
90 U
86 U
89 U
84 U
Fluoranthene
64.23
834.3
2230
76
1900
1500
1300
600
150
130
130
160
120
90 U
51
250
76
Fluorene
34.64
651.9
536
91 U
59
66
85 U
87 U
86 U
86 U
87 U
85 U
87 U
90 U
86 U
89 U
84 U
Hexadecanoic acid (TIC)



-
800
4000
-
-
-
-
-
-
-
-
-
-
-
Indeno (1,2,3-cd) pyrene
78
836.7

91 U
530
480
420
230
47
53
65
72
87 U
90 U
86 U
75
84 U
Phenanthrene


1170
91 U
1000
860
590
210
47
71
87 U
120
87 U
90 U
86 U
110
84 U
Pyrene
570
3225
1520
80
1800
1500
1200
580
150
150
170
170
100
90 U
58
220
91
Total PAHs
3553
13660
22800
300
10804
9963
7550
3884
886
857
970
1074
538
0
153
1378
364
ARCS = Assessment & Remediation of Contaminated Sediments Program (Jones &Suter 1997)	U = The analyte was not detected at or above the reporting limit.
TEC = Threshold Effect Concentration; PEC = Probable Effect Concentration
CB = Consensus-Based sediment quality guidelines (USEPA 2000)
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 26 of 36

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Table 9: Individual metrics, dominant taxa, and the macroinvertebrate multimetric index (MMI) score,
as well as habitat scores, for data collected at macroinvertebrate sampling locations in February 2017.
Station ID
PC5/6
PC8
PC11
PC12
Station Name
Hortense-Hollowell
James Jackson
Grove Park
Spring Street
Metrics
Value
Score
Value
Score
Value
Score
Value
Score
Coleoptera Taxa
0
0
0
0
1
11.36
0
0
% Oligochaeta
0.42%
99.51
7.27%
91.39
4.00%
95.26
8.49%
89.94
% Plecoptera
0.00%
0
0.00%
0
0.00%
0
0.00%
0
Shredder Taxa
0
0
1
9.09
3
27.27
3
27.27
Scraper Taxa
5
56.82
2
22.73
2
22.73
3
34.09
Swimmer Taxa
0
0
0
0
0
0
0
0
Dominant Taxa
Hydropsyche betteni
Hydropsyche betteni
Hydropsyche betteni
Copepoda
Hydropsychidae
Cheumatopsyche sp.
Polypedilum flavum
Cricotopus bicinctus
Cheumatopsyche sp.
Hydropsyche sp.
Thienemannimyia gp.
Thienemannimyia gp.
MMI Score (of 100)
26
21
26
25
Habitat Score (of 200)
157
114
92
145
Table 10: Summary of consumption advisory recommendations from the fish tissue screening study
conducted in April 2016 and the follow-up study conducted in July 2017. Advisories are suggested for
no more than one meal per month (1/MONTH) or no more than one meal per week (1 /WEEK), as
indicated, for fish species collected in the upper watershed near North Avenue (PC3) or in the lower
watershed near Jackson Parkway (PC8).
SUMMARY OF
RECOMMENDATIONS
UPPER WATERSHED
LOWER WATERSHED
redbreast
sunfish
green
sunfish
yellow
bullhead
brown
bullhead
redbreast
sunfish
brown
bullhead
1/MONTH
1/MONTH
1/WEEK
1/WEEK
1/WEEK
1/WEEK
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 27 of 36

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Figure 1: Study site location in Fulton County, GA. The Proctor Creek watershed drains to the
Chattahoochee River, which flows across the Florida panhandle to the Gulf of Mexico.
- Mainstem of Prodor Creek
' — Streams and tributaries
i i Watershed boundary
Atlanta

Figure 2: Map of sampling locations in the Proctor Creek watershed. The darker blue line indicates the
mainstem of Proctor Creek, with tributaries shown in lighter blue. See Table 1 for station descriptions
Proctor Creek Watershed
Atlanta, GA
PC14
Lillian Cooper
LOWER WATERSHED
SAMPLING REACH
PC9
Northwest
PC7
Kerry Circle
PC13
AD Williams
PC15
West Highlands
PC8
James Jackson / •
PC12
Spring Street
PC5
Hollow ell
PC5/6
PC6
Hortense
\ PC11
j Grove Park
Hfe PC1°
BHBfi Lindsay Street
UPPER WATERSHED
SAMPUNG REACH
PC3
North Avenue
PC2
Greensferry
_l Proctor Creek Basin
	Proctor Creek
O Sampling Locations
~ CSO Facilities
USGS gauges
0.45 0.9
PC1
Burbank
WpSIVlEW
fefi Sptfce £{ri.\Gi9!lalSl'c
frefCCF.lt?, iis^.-flna-th.
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 28 of 36

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Figure 3: Specific conductance (|iS/cm) ± 1SE in Proctor Creek and its tributaries.
Locations are shown from upstream to downstream, in order from left to right. Similar
patterns in concentration were found for component ions, including Ca, K, Mg, and Na.
700
C	Tributaries T
5 500	,	t
Proctor Creek	t
PCI PC2 PC3 PC10 PC4 PC5 PC11 PC6 PC15 PC7 PC12 PC8 PC13 PCM PC9
Station ID
Figure 4 E. co/i (MPN per 100 mL) ± 1SE in Proctor Creek and its tributaries. Locations are shown
from upstream to downstream, in order from left to right.
16,000
Tributaries
Proctor Creek
-------
Figure 5: Total nitrogen (mg/L) ± 1SE in Proctor Creek and its tributaries. Locations are
shown from upstream to downstream, in order from left to right.
5.0
4.5

rr





4.0
~5o 35 "
E
— 3.0
c
QJ
on o 5
o zo
4s
FF



^¦Tributarie
# Proctor Cr
s
eek

L





4—»
ii 2.0
| 15
3
S


M

1.0
0.5 -


IffWI
i
PCI PC2 PC3 PC10
PC4 PCS PC11 PC6 PC
Station ID
15 PC7 PC12 PC8 PC13 PC14 PC9
Figure 6: Total phosphorus (mg/L) ± 1SE in Proctor Creek and its tributaries. Locations
are shown from upstream to downstream, in order from left to right.
0.6
0.5
	I
00
0.4
1/1
3
Q_
i/>
O
0.3
0.2
fC
,o
0.1
i Tributaries
- Proctor Creek
TT
PCI PC2 PC3 PC10 PC4 PC5 PC11 PC6 PC15 PC7 PC12 PCS PC13 PCM PC9
Station ID
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 30 of 36
-------
Figure 7: Summary of pesticide data collected in the water column in April 2016 and July
2017, including post-storm sampling in July 2017. Only chlordane was detected in
September 2015, at a minimum reporting limit (MRL) of 0.05 jig/L for each pesticide.
Those values are plotted on a secondary axis due to scale. Locations are shown from
upstream to downstream, in order from left to right. BD = below detection.
-------
APPENDIX
Analytical methods, routine minimum reporting limits for water and sediment matrices, and water
quality standards (WQS) for each of the parameters analyzed during this study, according to analyte
group. WQS are shown where applicable only, and are for annual average criteria unless otherwise
indicated. 1Q10 = one-day 10-year minimum low flow. 7Q10 = 7-day 10-year minimum low flow.
NUTRIENTS & CLASSICALS

TOTAL RECOVERABLE METALS
Analyte
Method
WATER
(Mg/L)

Analyte
Method
WATER
(Hg/L)
WQS (ng/L)
SEDIMENT
(mg/kgdry)
Alkalinity
SM 2320B
1.0

Antimony
EPA 200.8
0.5
640
0.05
Ammonia
EPA 350.1
0.05

Arsenic
EPA 200.8
0.5
50
1Q10 = 340
7Q10 = 150
0.05
Bromide
EPA 300.0
0.1

Aluminum
EPA 6010C
100

10
Chloride
EPA 300.0
0.1

Barium
EPA 6010C
5.0

0.5
Fluoride
EPA 300.0
0.05

Beryllium
EPA 6010C
3.0*
***
0.3
Hardness
SM 2340B
1.654

Cadmium**
EPA 200.8
0.25
1Q10 = 1.0
7Q10 = 0.15
0.025
Nitrate+Nitrite
EPA 353.2
0.05

Calcium
EPA 6010C
250

25
Sulfate
EPA 300.0
0.1

Chromium III**
EPA 6010C
5.0*
1Q10 = 320
7Q10 = 42
0.5
Total Dissolved Phosphorus
EPA 365.1
0.01

Chromium VI**
EPA 6010C
5.0*
1Q10 = 16
7Q10 = 11
0.5
Total Kjeldahl Nitrogen
EPA 351.2
0.05

Cobalt
EPA 6010C
5.0*

0.5
Total Organic Carbon
SM5310/ASB 107C
1.0

Copper**
EPA 6010C
10*
1Q10 = 7.0
7Q10 = 5.0
1.0
Total Phosphorus
EPA 365.1
0.01

Iron
EPA 6010C
100

10
Total Suspended Solids
USGS 1-3765-85
4.0

Lead**
EPA 200.8
0.5
1Q10 = 30
7Q10 = 1.2
0.05



Magnesium
EPA 6010C
250

25
MICROBIOLOGY

Manganese
EPA 6010C
5.0

0.5
Analyte
Method
(MPN/
100m L)

Mercury**
EPA 245.1 (water)
EPA 7473 (sediment)
0.10*
1Q10 = 1.4
7Q10 = 0.012
0.05*
Escherichia coli
IDEXX Colilert
1.0

Molybdenum
EPA 6010C
10*

1.0*



Nickel**
EPA 6010C
10*
1Q10 = 260
7Q10 = 29
1.0
* This analyte was NOT detected at the reporting limit
Potassium
EPA 6010C


100
indicated in this sample matrix.

Selenium
EPA 200.8
1.0
7Q10 = 5
0.10*
** WQS for these metals are calculating using the total
Silver
EPA 6010C
5.0*
***
0.5*
hardness of the water body. Formulae are listed in Ga.
Sodium
EPA 6010C
1000

100
Comp. R. & Regs. r. 391-3-6-.03(5)(e)(ii). Values shown
Strontium
EPA 6010C
5.0

0.5
assume a hardness of 50 mg/LCaCo3.

Thallium
EPA 200.8
0.5*
0.47
0.05*
*** This pollutant is addressed in section 391-3-6-.06 of
Tin
EPA 6010C
15*

1.5
Georgia's Water Quality Control regulations.

Titanium
EPA 6010C
5.0

0.5



Vanadium
EPA 6010C
5.0*

0.5



Yttrium
EPA 6010C
3.0*

0.3



Zinc**
EPA 6010C
10
1Q10 = 165
7Q10 = 65
1.0
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 32 of 36
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Analyte
Method
WATER
(Hg/L)
WQS (ng/L)
SEDIMENT
(mg/kgdry)
4,4'-DDD(p,p'-DDD)
Mod. 8270/EPA 8081B
0.04
0.00031
1.3
4,4'-DDE (p,p'-DDE)
Mod. 8270/EPA 8081B
0.04
0.00022
1.3
4,4'-DDT(p,p'-DDT)
Mod. 8270/EPA 8081B
0.04
0.00022
7Q10 = 0.001
1.3*
Aldrin
Mod. 8270/EPA 8081B
0.04
0.00005
1.3
Dieldrin
Mod. 8270/EPA 8081B
0.04*
0.000054
7Q10 = 0.056
1.3*
Endosulfan 1 (alpha)
Mod. 8270/EPA 8081B
0.04
89
7Q10 = 0.056
1.3
Endosulfan II (beta)
Mod. 8270/EPA 8081B
0.04
89
7Q10 = 0.056
1.3
Endosulfan Sulfate
Mod. 8270/EPA 8081B
0.04
89
7Q10 = 0.056
1.3
Endrin
Mod. 8270/EPA 8081B
0.04
0.060
7Q10 = 0.036
1.3
Endrin aldehyde
Mod. 8270/EPA 8081B
0.04
0.30
1.3
Endrin ketone
Mod. 8270/EPA 8081B
0.04*

1.3
Heptachlor
Mod. 8270/EPA 8081B
0.04
0.000079
7Q10 = 0.0038
1.3
Heptachlor epoxide
Mod. 8270/EPA 8081B
0.04*
0.000039
7Q10 = 0.0038
1.3
Methoxychlor
Mod. 8270/EPA 8081B
0.04
7Q10 = 0.03
1.3
Toxaphene
Mod. 8270/EPA 8081B
5.0
0.00028
7Q10 = 0.0002
170
alpha-BHC
Mod. 8270/EPA 8081B
0.04
0.0049
1.3
alpha-Chlordane
Mod. 8270/EPA 8081B
0.04*
0.00081
7Q10 = 0.0043
1.3*
gamma-Chlordane
Mod. 8270/EPA 8081B
0.04*
1.3*
trans-Nonachlor
Mod. 8270/EPA 8081B
0.5
20
cis-Nonachlor
Mod. 8270/EPA 8081B
0.5
20
beta-BHC
Mod. 8270/EPA 8081B
0.04
0.017
1.3
delta-BHC
Mod. 8270/EPA 8081B
0.04

1.3
gamma-BHC (Lindane)
Mod. 8270/EPA 8081B
0.04
1.8
1Q10 = 0.95
1.3
1.



1
Analyte
Method
WATER
(Hg/L)
WQS (ng/L)
SEDIMENT
(mg/kg dry)
2,4,5-T
EPA 8321B
1.0

300
2,4,5-TP
(Silvex)
EPA 8321B
1.0
7Q10 = 50
300
2,4-D
EPA 8321B
1.0
7Q10 = 70
NA
2,4-DB
EPA 8321B
2.0

NA
Dicamba
EPA 8321B
1.0

NA
Dichlorprop
EPA 8321B
1.0

NA
m
Analyte
Method
WATER
(Hg/L)
WQS (ng/L)
MR
SEDIMENT
(mg/kg dry)
PCB-1016
(Aroclor 1016)
EPA 8082A
1.0

33
PCB-1221
(Aroclor 1221)
EPA 8082A
1.0

33
PCB-1232
(Aroclor 1232)
EPA 8082A
1.0

33
PCB-1242
(Aroclor 1242)
EPA 8082A
1.0
forall PCBs:
33
PCB-1248
(Aroclor 1248)
EPA 8082A
1.0
0.000064
7Q10 =
33
PCB-1254
(Aroclor 1254)
EPA 8082A
1.0*
0.014
33*
PCB-1260
(Aroclor 1260)
EPA 8082A
1.0*

33*
PCB-1262
(Aroclor 1262)
EPA 8082A
1.0

33
PCB-1268
(Aroclor 1268)
EPA 8082A
1.0

33
* This analyte was detected above the reporting limit in one or
more samples, in the watercolumn or sediment, as indicated.
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 33 of 36
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mm



Analyte
WATER
(Hg/L)
WQS
(Hg/L)
SEDIMENT
(mg/kgdry)
Analyte
WATER
(Hg/L)
WQS
(Hg/L)
SEDIMENT
(mg/kg dry)
(3-and/or 4-)Methyl phenol
10

330*
Benzo(a)pyrene
2.0
0.018
66*
1,1-Biphenyl
2.0

66
Benzo(b)fluoranthene
2.0
0.018
66*
1,4-Dioxane
2.0*

66
Benzo(g,h,i)perylene
2.0
**
66*
1-Methyl naphthalene
2.0

66
Benzo(k)fluoranthene
2.0
0.018
66*
2,3,4,6-Tetrachlorophenol
10

330
Benzyl butyl phthalate
10
1900
330
2,4,5-Trichlorophenol
10

330
Bis(2-chloroethoxy)methane
10

330
2,4,6-Trichlorophenol
10
2.4
330
Bis(2-chloroisopropyl) ether
10
65000
330
2,4-Dichlorophenol
10
290
330
Bis(2-ethylhexyl) phthalate
10
2.2
330*
2,4-Dimethylphenol
10
850
330
Caprolactam
10

330
2,4-Dinitrophenol
20
5300
330
Carbazole
2.0

66*
2,4-Dinitrotoluene
10
3.4
330
Chrysene
2.0
0.018
66*
2,6-Dinitrotoluene
10

330
Di-n-butylphthalate
10
4500
330
2-Chloronaphthalene
10
1600
330
Di-n-octylphthalate
10

330
2-Chlorophenol
10
150
330
Dibenz(a,h)anthracene
2.0
0.018
66*
2-Methyl-4,6-dinitrophenol
10
280
330
Dibenzofuran
2.0

66
2-Methyl naphthalene
2.0

66
Diethyl phthalate
10
44000
330
2-Methylphenol
10

330
Dimethyl phthalate
10
1100000
330
2-Nitroaniline
10

330
Fluoranthene
2.0
140
66*
2-Nitrophenol
10

330
Fluorene
2.0
5300
66*
3,3'-Dichlorobenzidine
10
0.028
330
Hexachlorobenzene (HCB)
10
0.00029
330
3-Nitroaniline
10

330
Hexachlorocyclopentadiene (HCCP)
10
1100
330
4-Bromophenyl phenyl ether
10

330
Hexachloroethane
10
3.3
330
4-Chloro-3-methyl phenol
10
**
330
Indeno (1,2,3-cd) pyrene
2.0
0.018
66*
4-Chloroaniline
10

330
Isophorone
10
960
330
4-Chlorophenyl phenyl ether
10

330
Naphthalene
2.0

66
4-Nitroaniline
10

330
Nitrobenzene
10
690
330
4-Nitrophenol
10

330
Pentachlorophenol
10
3.0
7Q10=15
330
Acenaphthene
2.0
990
66
Phenanthrene
2.0
**
66*
Acenaphthylene
2.0
**
66*
Phenol
10
857000
7Q10=300
330
Acetophenone
10

330
Pyrene
2.0
4000
66*
Anthracene
2.0
40000
66*
bis(2-Chloroethyl) Ether
10
0.53
330
Atrazine
10

330
n-Nitroso di-n-Propylamine
10
0.51
330
Benzaldehyde
10

330
n-Nitrosodiphenylamine/
10
6.0
330
Benzo(a)anthracene
2.0
0.018
66*
Diphenylamine
All semi-volatile compounds were analyzed by EPA Method 8270D.
* This analyte was detected above the reporting limit in one or more samples, in the water column or sediment, as indicated.
** Special rules for these pollutants are found in section 391-3-6-.06 of Georgia's Water Quality Control regulations.
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 34 of 36
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-	J*
Analyte
WATER
(Hg/L)
WQS
(Hg/L)
Analyte
WATER
(Hg/L)
WQS
(Hg/L)
(m- and/or p-)Xylene
1.0

Chloromethane
0.5
**
1,1,1,2-Tetrachloroethane
0.5

Cyclohexane
0.5

1,1,1-Trichloroethane
0.5

Dibromochloromethane
0.5
13
1,1,2,2-Tetrachloroethane
0.5
4.0
Dibromomethane
0.5

1,1,2-Trichloro-1,2,2-
Trifluoroethane (Freon 113)
0.5

Dichlorodifluoromethane
(Freon 12)
0.5

1,1,2-Trichloroethane
0.5
16
Ethyl Benzene
0.5
2100
1,1-Dichloroethane
0.5

Hexachlorobutadiene
0.5
18
1,1-Dichloroethene
(1,1-Dichloroethylene)
0.5
7100
Isopropylbenzene
0.5

1,1-Dichloropropene
0.5

Methyl Acetate
0.5

1,2,3-Trichlorobenzene
0.5

Methyl Butyl Ketone
1.0

1,2,3-Trichloropropane
0.5

Methyl Ethyl Ketone
4.0*

1,2,4-Trichlorobenzene
0.5
70
Methyl Isobutyl Ketone
1.0

1,2,4-Tri methyl benzene
0.5

Methyl T-Butyl Ether (MTBE)
0.5

l,2-Dibromo-3-
Chloropropane (DBCP)
1.0

Methylcyclohexane
0.5

1,2-Dibromoethane (EDB)
1.0

Methylene Chloride
0.5
590
1,2-Dichlorobenzene
0.5
1300
Napthalene
0.5

1,2-Dichloroethane
0.5
37
Styrene
0.5

1,2-Dichloropropane
0.5
15
Tetrachloroethene
0.5*
3.3
1,3,5-Tri methyl benzene
0.5

Toluene
0.5
5980
1,3-Dichlorobenzene
0.5
960
Trichloroethene
(Trichloroethylene)
0.5
30
1,3-Dichloropropane
0.5

Trichlorofluoromethane
(Freon 11)
0.5

1,4-Dichlorobenzene
0.5
190
2,2-Dichloropropane
0.5

Vinyl chloride
0.5
2.4
Acetone
4.0*

cis-l,2-Dichloroethene
0.5*

Benzene
0.5
51
cis-l,3-Dichloropropene
0.5

Bromobenzene
0.5

n-Butylbenzene
0.5

Bromochloromethane
0.5

n-Propylbenzene
0.5

Bromodichloromethane
0.5*
17
o-Chlorotoluene
0.5

Bromoform
1.0
140
o-Xylene
0.5

Bromomethane
2.0
1500
p-Chlorotoluene
0.5

Carbon Tetrachloride
0.5
1.6
p-lsopropyltoluene
0.5

Carbon disulfide
2.0

sec-Butylbenzene
0.5

Chlorobenzene
0.5
1600
tert-Butylbenzene
0.5

Chloroethane
2.0

trans-l,2-Dichloroethene
0.5
10000
Chloroform
0.5*
470
trans-l,3-Dichloropropene
0.5

All volatile compounds were analyzed by EPA Method 8260C, in water samples only.
* This analyte was detected above the reporting limit in one or more samples, in the water column or
sediment, as indicated.
** Special rules for these pollutants are found in section 391-3-6-.06 of Georgia's Water Quality Control
regulations.
Project ID #15-0425
Proctor Creek Watershed Monitoring: Final Summary Report
Page 35 of 36
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END OF DOCUMENT
Project ID #15-0425	Proctor Creek Watershed Monitoring: Final Summary Report	Page 36 of 36
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