NC0000396_Methodology_20150823

Duke Energy Progress — Asheville Steam Electric Plant
Groundwater Assessment Report
Comprehensive Site Assessment Report
Appendix C - Methodology
The approach to conducting the Comprehensive Site Assessment (CSA) at the Asheville Steam
Electric Plant was described in the Groundwater Assessment Work Plan (Revision 1, December
2014). The objective was to collect and analyze samples of soil, ash, groundwater, surface
water, and sediment to more accurately determine the vertical and horizontal concentrations of
Constituents of Interest (COIs). A COI is defined as a parameter detected at a concentration
greater than NCDENR/DWR Title 15, Subchapter 2L and Interim Maximum Allowable
Concentrations (IMAC). This section describes equipment and methods employed to collect
and preserve appropriate samples and obtain representative analytical results.
1. Subsurface Investigation
Characterization of subsurface material was conducted by collecting ash, soil, sediment, ash
pore water, groundwater, seep water and surface water samples for analysis. Ash, soil, ash
pore water, and groundwater samples were obtained through completion of drilled borings and
monitoring wells. The approach for subsurface sample acquisition and analysis follows.
1.1 Drilling Methods
Two different drilling methods were employed to collect subsurface samples. The
selection of drilling technology was dependent on soil conditions, sample depth, and
accessibility.
Drilling tools (sonic core barrels and casings, and hand auger buckets) were thoroughly
decontaminated prior to starting a boring. Daily equipment rinse samples were
collected to confirm the effectiveness of decontamination (Appendix D). Drinking water
purchased locally was used for drilling fluid. A sample of the "source water' was
analyzed for the full set of GAP parameters (Appendix D).
1.1.1 Sonic Coring
The primary method used for drilling soil borings and monitoring wells was
rotary sonic drilling. The advantages provided by this method include less
disturbance of the borehole wall and minimized groundwater sample turbidity.
A track -mounted and tire -mounted Boart Longyear LSTM600 rotary sonic drill
was used. A mini -rotary sonic drill rig (spider rig) was utilized for borings with
limited access.
1.1.2 Hand Auger
A hand auger was used at locations where sample depth was shallow or site
conditions precluded the use of mechanized drilling equipment.
1.2 Packer Testing
During drilling, aquifer testing was performed within the borehole to identify zones that
would yield sufficient groundwater for monitoring by isolating targeted depth intervals
within bedrock with inflatable packers connected to the string of drill rods. A 5 -foot
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Groundwater Assessment Report
Comprehensive Site Assessment Report
Appendix C - Methodology
interval packer system was used to isolate intervals of interest at bedrock locations.
Targeted depth intervals were selected by the Lead Geologist based on observation of
the rock core. The U.S. Bureau of Reclamation test method and calculation procedures
as described in Chapter 17 of their Engineering Geology Manual (2nd Edition, 2001) will
be used. Aquifer testing within the isolated depth intervals consisted of either slug
testing or pump testing, or both. Slug testing procedures are described later in this
document. Pump testing consisted of monitoring purging and recovery rates using a
pressure transducer and/or manual depth to water measurements with a water level
indicator.
1.3 Monitoring Well Installation
Each monitoring well was constructed by North Carolina -licensed well drillers using
sonic and hand auger techniques and in accordance with 15A NCAC 02C (Well
Construction Standards). Drilling equipment was decontaminated prior to use at each
location.
Monitoring wells were constructed of 2 -inch ID, National Sanitation Foundation (NSF)
grade polyvinyl chloride (PVC) (ASTM D-1785-12) schedule 40 flush -joint threaded
casing and 0.010 -inch machine -slotted pre -packed screens. Well construction also
included the use of pre -packed screens with additional sand in the annular space, to
minimize sample turbidity. Packed well screens for each well were filled with clean,
well-rounded, washed high grade No. 1A silica sand. The filter pack was placed
approximately two feet above the top of the pre -packed screen and then an approximate
two -foot pelletized bentonite seal was placed above the filter pack. The remainder of the
annular space was filled with a neat cement grout from the top of the upper bentonite
seal to near ground surface.
Wells completed beneath the ash -soil interface and bedrock surface were installed as
double -cased wells as a precautionary measure to prevent potential COI migration from
overlying material along annular space of the borehole and beneath the ash -soil interface
and bedrock surface. Bedrock wells installed beneath the ash were effectively installed
as triple -cased wells, using a temporary 10 -inch steel casing set to the base of the ash and
then drilling through the temporary casing to install the permanent 6 -inch PVC casing to
the bedrock surface as described below.
Protective outer casing was installed using sonic drilling equipment with a 10 -inch core
barrel (or a 9 -inch core barrel in the case of bedrock wells beneath the ash) drilling just
into the top of the bedrock surface, which was determined based on observation of
continuous cores recovered during initial coring. A permanent 6 -inch diameter schedule
40 PVC protective outer casing was then installed and grouted in-place. After the grout
had sufficient time to set (approximately 24 hours), drilling was advanced through the
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Groundwater Assessment Report
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Appendix C - Methodology
outer casing using a smaller diameter drilling core barrel (~5 -inch diameter) and into the
bedrock to the targeted depth of the (determined based on observation of continuous
cores) at least 10 feet below the depth of the surface casing. Wells were then installed in
a similar approach as shallow monitoring wells as described above.
Monitoring wells were completed with steel above ground protective casings with
locking caps with locking expansion caps, and well tags. Protective covers were secured
and completed in a concrete collar and a minimum two -foot square concrete pad and
bollards.
Drinking water purchased locally was used for drilling fluid. A sample of the "source
water" was analyzed for the full set of GAP parameters (Appendix D).
1.3.1 Monitoring Well Development
Following installation, monitoring wells were developed to remove drill fluids,
clay, silt, sand, and other fines which may have been introduced into the
formation or sand pack during drilling and well installation, in addition to
establishing connectivity of the well with the aquifer. Well development was
performed using a portable submersible pump that was repeatedly moved up
and down the well screen interval until the water was relatively clear. Some
wells were developed with a bailer due to slow recharge rates. Development
continued by sustained pumping until monitoring parameters (e.g., conductivity,
pH, DO, and temperature) were generally stabilized, estimated quantities of
drilling fluids, if used, were removed, and turbidity decreased to acceptable
levels (approximately 10 NTUs). Wells were developed no sooner than 24 hours
after well installation to allow for an adequate grout cure time.
1.4 Sample Collection and Analytical Methods
Methods used for the collection and preservation of samples for various analyses are
described in this section. Samples were collected in accordance with the quality
assurance and quality control procedures outlined in the Work Plan.
1.4.1 Soils and Ash Sampling and Analysis
Borings were logged and ash/soil samples were photographed, described, and
visually classified in the field for origin, consistency/relative density, color, and
soil type in accordance with the Unified Soil Classification System (ASTM
D2487/D2488).
Rinse blanks from soil sample collection equipment were collected for each soil
boring/well installation location. At times, drilling for one location took more
than one day and the rinse blank was collected on the first day. Rinse blanks for
soil samples were collected by pouring deionized water through the sonic drill
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Appendix C - Methodology
bit or through the hand auger bit. These pieces of equipment are normally the
first introduced into the subsurface for a soil boring. Laboratory results for the
rinse blanks are provided in Appendix D.
Soil and ash samples were collected wearing nitrile gloves and prepared and
analyzed using the following methods:
1.4.1.1 Metals
Soil and ash samples were placed in amber glass bottles and stored on ice
for shipment for total metals analysis. Concentrations of metals present
in soils and ash were determined using analytical parameters presented
in Table 8.2.
1.4.1.2 Organic Constituents
Soil and ash samples were placed in amber glass bottles and stored on ice
for shipment for total organic carbon (TOC) analysis. TOC content of
soils and ash were determined in accordance with EPA Method 9060.
1.4.1.3 Leaching Characteristics
Select soil and ash samples were placed in amber glass bottles and stored
on ice for shipment for the mobility of inorganic analytes present using
the Synthetic Precipitation Leaching Procedure (SPLP) following U.S.
EPA Method 1312.
1.4.1.4 Bulk Chemistry
Select soil and ash samples were stored and shipped in sealable plastic
bags for bulk chemistry analysis. Identification and relative
concentration of bulk chemistry was determined by American Assay
Laboratories. Samples were dried at 80 °C overnight and pulverized to -
150 mesh and analyzed as follows:
XRF-PP - a known sample amount was combined with binder,
ground finer, and pressed into a disk. The disk was then analyzed
by X-ray fluorescence (XRF).
ICP-D4A - A sample pulp was digested with a combination of HF,
HC1O4, HCl, and HNO3 for a near-total digestion. The solution
was then analyzed by Inductively Coupled Plasma (ICP) -Atomic
Emission Spectroscopy (AES) and ICP -Mass Spectroscopy (MS).
ICP -NF - A sample pulp was fused with Na2O2 and digested with
HCl. The solution was then analyzed by ICP -AES and ICP -MS.
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Appendix C - Methodology
Eltra Carbon & Sulfur - A sample pulp was combined with
tungsten and iron accelerator and combusted in Eltra furnace for
analysis of carbon and sulfur.
Loss of Ignition (LOD - A sample pulp was gradually heated in a
gravimetric furnace to 1000C while sample loss was calculated.
1.4.1.5 Mineralogy
Select samples were stored and shipped in sealable plastic bags for
mineralogical analysis. Identification and relative concentration of
mineral types were determined by using X-ray diffraction (XRD). The
original sample was dried at 80 °C (no pulp) and combined with water
and disaggregated in an ultrasonic bath. The sample was then wet sieved
at 63 µm to separate and quantify the sand fraction. The slurry is
centrifuged at a calculated rotation per minute and time to separate the
clay particles from the silt. The clay solution is then decanted off. Sand
and silt fractions were dried, quantified, and analyzed using XRD as
random mounts (XRD is a process by which X-rays are scattered by atoms
that comprise the crystal structure of a given mineral, creating a pattern).
Clay particles are deposited on slides forming an oriented mount for
XRD. After the analysis, the clay particles are placed in an ethylene
glycol environment overnight to test for expanding clays. When
necessary, the clay particles are then heated to 400C and re -analyzed for
collapsing layers.
1.4.1.6 Development of Kd Terms
To determine the sorption capacity of site soils, select samples were
collected along proposed flowpath transects. Samples were collected,
handled, and preserved in order to eliminate impacts of ambient air on
the oxidation-reduction potential (ORP) and hydrous ferrous oxide
(HFO) on sampled materials. Samples were collected in plastics bags and
sealed with a conventional vacuum sealer. The samples were stored on
ice for shipment and kept out of direct sunlight.
Samples were prepared and analyzed by the Civil and Environmental
Engineering Department of the University of North Carolina at Charlotte
(UNCC). Prior to sorption determinations, soil samples were dried at
room temperature and periodically mixed throughout the drying process
to prevent grain aggregation. Once dry, samples were sieved using a No.
10 U.S. standard sieve (10 mm) with 0.0787 inch openings. To quantify
soil partition coefficients (Kd), Column and Batch tests were performed.
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Appendix C - Methodology
Effluent samples collected from these tests were analyzed by inductively
coupled plasma -mass spectroscopy and ion chromatography. To provide
a basis for estimating COI source terms, leaching tests were performed on
ash samples. Details of the analytical procedures/methods are briefly
discussed below with more detail included in the analytical reports.
1.4.1.6.1 Column Tests
Column tests were conducted by compacting soil and ash samples
into 8 inch long (20.3 cm) polyethylene tubes (with dimensions
0.675 in. (16 mm) I.D. by 0.75 in. (19 mm) O.D) and plugged with
two polypropylene end caps. Using groundwater and ash pore
water analytical results from the site, feed solutions amended with
all COPCs found above the NCAC 15A 02L .0106(g) standards
were produced and pumped into the columns. Analyses and
equipment used are provided in the table below:
Analyte
Method
Trace metals (Sb, As, B, Cd,
Cr, Fe, Mn, Pb, Tl)
EPA 200.8
Sulfate
EPA 300.0
pH
Standard Method 4500 B
Conductivity
Standard Method 2510
Oxidation-reduction potential
(ORP)
ASTM method G200-19
1.4.1.6.2 Batch Tests
Batch tests were conducted in accordance with U.S.
Environmental Protection Agency Technical Resource Document
EPA/530/SW-87/006-F. COPC-amended feed solution (described
above in 1.3.1.6.1) and soil samples were mixed across a range of
soil -to -solution ratios, followed by shaking until chemical
equilibrium was achieved. Once equilibrium was achieved,
solutions were drawn and analyzed as described in the above
table.
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Groundwater Assessment Report
Comprehensive Site Assessment Report
Appendix C - Methodology
1.4.1.6.3 Hydrous Ferrous Oxides Analysis
The method for HFO determination in soil and ash samples was
adapted from Chao and Zhou (1983). Following this method, soil
samples were extracted using a 0.25M NH2OH•HCl-0.25M HCl
combined solution.
1.4.1.6.4 Ash Leaching Tests
Ash leach tests were performed to provide a basis for estimating
COCs source terms to develop the Kd terms. Ash samples were
prepared and analyzed using EPA Method 1313 [2] (Liquid -Solid
Partitioning as a Function of Extract pH Using a Parallel Batch
Extraction Procedure) and EPA Method and EPA Method 1316 [3]
(Liquid -Solid Partitioning as a Function of Liquid -Solid Ratio
using a Parallel Batch Extraction Procedure). Method 1313
provides COCs concentration as a function of pH (the test was
conducted only at natural pH). Method 1316 provides COI
concentration as a function of liquid to solid ratio.
1.4.1.7 Index Property Sampling and Analysis
Select soil and ash samples were collected for laboratory analysis of
physical properties to provide data for use in groundwater modeling.
Samples were collected at selected locations for the following analyses
using the described methods:
• Natural Moisture Content Determination (ASTM D-2216)
Grain size with hydrometer determination (ASTM Standard D-
422)
In addition, thin-walled undisturbed tubes ("Shelby" Tubes) were
advanced in ash and soil at select locations. Shelby Tubes were tested for
the following:
• Natural Moisture Content Determination (ASTM D-2216)
• Grain size with hydrometer determination (ASTM Standard D-
422)
• Hydraulic Conductivity Determination (ASTM Standard D-5084)
• Specific Gravity of Soils (ASTM Standard D-854)
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Comprehensive Site Assessment Report
Appendix C - Methodology
1.4.2 Ash Pore Water and Groundwater Sampling and Analysis
New and existing wells were sampled using low -flow sampling techniques in
accordance with the USEPA Region 1 Purging and Sampling Procedure for the
Collection of Groundwater Samples from Monitoring Wells (revised January 19, 2010),
the Groundwater Monitoring Program Sampling, Analysis and Reporting Plan,
Asheville Steam Electric Plant (SynTerra, July 2014), updated by the Low Flow
Sampling Plan, Duke Energy Facilities, Ash Basin Groundwater Assessment Program,
North Carolina, June 10, 2015. NCDENR conditionally approved the Low Flow
Sampling Plan in a June 11, 2015 email with an attachment summarizing their
approval conditions.
Equipment blanks for groundwater sampling were collected daily. The sample
was collected from a laboratory -supplied container of deionized water into
laboratory -supplied bottle ware. The equipment consisted of the pump to be
used for sample collection that day and tubing was pulled from the supplies
planned for the day.
Ash pore water and groundwater samples were analyzed in the field and
laboratory. The analytical parameters and associated analytical methods are
summarized on Table 10-2. Only select samples were analyzed for radionuclides
and metals speciation included on Table 10-7. For speciation analysis, select ash
pore water and/or groundwater samples were collected with a peristaltic pump
as described above but with acid -washed tubing and following a condensed
version of EPA Method 1669. Speciation analytical results are displayed in Table
10-5.
2. Hydrogeologic Testing
Hydrogeologic tests were performed and measurements were made to characterize
hydrogeologic conditions. These activities include measuring water levels as well as
conducting slug tests and packer tests.
2.1 Water Level Measurements
During groundwater sampling activities, water level measurements were recorded at
existing site monitoring wells, observation wells, piezometers, and newly installed
wells. The measurements were made using electrical tapes that indicate the contact with
water. A tape was lowered into a well and a graduated scale on the tape was used to
measure the depth of the water level below the top of the casing. The uncertainty in this
measurement is approximately +/- 0.01 ft, which is the resolution of the scale on the tape.
The elevation of a reference point on the top of each casing was determined by a
licensed surveyor, and we estimate the accuracy of these elevations to be +/- 0.01 ft
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Comprehensive Site Assessment Report
Appendix C - Methodology
Elevations were measured relative to a common datum, which was then referenced to
mean sea level. Depth to water and the elevation of the top of casing were used to
calculate the elevation of the water level in the well. This elevation was assumed to be
the hydraulic head at the mid -point of the screen on the well.
The hydraulic heads measured in shallow wells were contoured using standard linear
interpolation methods to generate water level maps for shallow, water table conditions.
These maps were used to infer approximate directions of horizontal groundwater flow
within the constraints that the hydraulic conductivity was isotropic in the horizontal
direction. Measurements from clusters of piezometers were used to estimate vertical
hydraulic head gradients. Water levels in wells in the ash basins were used to estimate
the elevation of saturated conditions, and multiple measurements provided
approximate estimates of the directions of ground water flow. Water level
measurements used for preparation of hydraulic head maps were collected during a
single 24-hour period and prior to purging for sampling.
2.2 Slug Tests
2.2.1 Field Methods
After the development and sampling of monitoring wells, hydraulic conductivity
tests (rising head and/or falling head slug tests) were conducted on each of the
new wells. Slug tests were performed in general accordance with ASTM D4044-
96 Standard Test Method (Field Procedure) for Instantaneous Change in Head (Slug)
Tests for Determining Hydraulic Properties of Aquifers and NCDENR Performance and
Analysis of Aquifer Slug Test and Pumping Test Policy, dated May 31, 2007.
A slug test involves the injection or withdrawal of a known volume (slug) while
measuring the resulting fluctuation of the groundwater level. Site slug tests
employed both the solid cylinder (PVC slug) and the water withdrawal (bailer)
methods. When a PVC slug was utilized, both a falling -head (slug -in) and a
rising -head (slug -out) test were performed. However, when a bailer was used,
only a rising- head slug test was performed.
Prior to the performance of each slug test, static water level was measured and
recorded. A Solinst Model 30010 Edge electronic pressure transducer, or
equivalent was placed in a well at least one foot beneath the lowest level that
would be reached by the submerged slug. This ensured that the cross-sectional
area of the well bore remained uniform during the slug test, which facilitates
analysis of the results. The Levelogger® was connected to a field laptop and
programmed with the well identification, date, and time. The pressure
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Appendix C - Methodology
transducer was then allowed to equilibrate to the conditions in the well for at
least 10 minutes.
Failing -Head Slug Test
Falling -head slug tests were conducted by rapidly lowering a slug into the well
and positioning the top of the slug approximately one foot below the initial static
water level. This caused the water level to rise, and then the water level fell and
the resulting pressure change was measured and recorded electronically using
the pressure transducer. The water level in the well was allowed to recover to
between 60 and 80 percent of the initial water level. After falling -head slug tests
were completed, sufficient time was allowed for the water level to reach
equilibrium before conducting the rising -head slug test.
Rising -Head Slug Test
A rising -head slug test, also known as a slug -out test, was conducted by rapidly
withdrawing a submerged slug, dropping the water level in the well. Most
rising- head slug tests were performed until the water level in the well recovered
to 60 to 80 percent of the pre-test water level. Slug tests in wells completed in
low permeability formations were terminated after 70% recovery or one hour,
whichever occurred first.
When using a bailer to withdrawal a slug of water, the rising -head procedure
was followed, first allowing time for the well to equilibrate with the bailer in the
water before removing the slug of water.
Hydraulic well tests were conducted with packers in some borings into bedrock.
Packer tests utilized a double packer system arranged to straddle an interval of
the borehole between of 5 feet and 10 feet long. The straddle packer system was
used to isolate and characterize depth intervals identified from observations of
the rock core. Typically depth intervals of the core containing fractures that were
thought to be open in the subsurface were selected for packer testing. This will
bias the hydraulic conductivity determined from packer tests, but it is justified
because our goal was to characterize the depth intervals that controlled ground
water flow. The U.S. Bureau of Reclamation test method and calculation
procedures as described in Chapter 17 of their Engineering Geology Field
Manual (2nd Edition, 2001) was utilized.
Slug tests were conducted with packers using a solid cylinder as described in
Section 2.2. Packers were also used during a purge -recovery investigation. The
purge -recovery investigation involved purging the well and monitoring the
recovery of water level in the packed off zone. Purge -recovery results were used
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Appendix C - Methodology
as an indicator of the location of water bearing zones to and determine well
screen placement.
2.2.2 Parameters
Slug test data were analyzed using AQTESOLVTM for Windows, version 4.5
(AQTESOLVTM). This involved using pressure data from transducers, aquifer
data thickness data from cross-sections and boring logs and well completion
data, such as screen length, inside radius of well casing, radius of well obtained
from CSA boring logs.
2.2.3 Analytical Methods
In selecting a method for analyzing the slug tests, we assumed the formations
intersected by the wells were isotropic and uniform over the scale influenced by
the well. Furthermore, we assumed that Darcy's Law was valid in all the
formations, and that the wells sampled a scale that was large enough so that flow
through fractures could be characterized using an equivalent hydraulic
conductivity. This is an accepted approach for characterizing flow through
porous and fractured media.
We ignored anisotropy when analyzing the slug tests. This is because slug tests
are only weakly sensitive to anisotropy and we felt that the resulting large
uncertainty in parameters would not warrant pursuing the interpretation of
anisotropy using slug tests.
Wells were recently developed prior to slug testing, and we assumed that
development was sufficient to remove well skin. As a result, effects of well skin
were ignored in the analyses.
Slug tests are weakly sensitive to storage properties in aquifers. Methods of
analysis are available to estimate storativity from slug tests, but the uncertainty is
typically large because of the weak sensitivity. Pressure transients were of minor
importance compared to steady state conditions during this investigation.
Storativity is unnecessary for steady state analyses, so we ignored methods of
analyzing slug tests that provided estimates of storativity.
Slug tests were analyzed using the Hvorslev method. This method is consistent
with the assumptions outlined above, and it is the most widely used method of
analyzing slug tests among practicing hydrogeologists.
AQTESOLVTM was used to input parameters listed above and plotted
normalized head vs. time. Hvorslev method was chosen in AQTESOLVTM and
visual line matching used for the Hvorslev equation was used to calculate the
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Appendix C - Methodology
transmissivity. The Hvorslev method involves plotting the log of the normalized
head as a function of time and fitting the data with a straight line (Butler, 1998).
The slope of the straight line is used in a calculation to determine the
transmissivity of the aquifer. We assumed that the length of the well screen was
the characteristic thickness of the aquifer, and this length was used to calculate
the hydraulic conductivity from the transmissivity.
Three Hvorslev equations were used while using AQTESOLVTM under three
different conditions: partially penetrating wells within confined aquifer; a well
abutting a confined aquifer; and a fully penetrating well within a confined or
unconfined aquifer. The equations are listed below:
(1) Hvorslev's equation for a partially penetrating well not in contact with an impermeable
boundary.
In(HO) — In(H) _
2KrLt
r2 In( L +1 + ( L )2
2r,,,2rwe
rwe=rw KIKr
(2) Hvorslev's equation for a well abutting a confining unit.
2KrLt
In(HO) — In(H) = r, In(200)
(3) Hvorslev's equation for a fully penetrating well in an unconfined or confined aquifer.
where:
In(HO) — In(H) _
2KrLt
r2 In( L +1 + ( L )2
2rwe 2rwe
'610 Ho = initial displacement at t=0 [L]
'61' H = displacement at time t [L]
'610 K,. = radial (horizontal) hydraulic conductivity [L/T]
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Appendix C - Methodology
167 L = screen length [L]
47 t = elapsed time since initiation of the test [T]
'67 r, = nominal casing radius [L]
161' rH, = well radius [L]
'61' KZ = vertical hydraulic conductivity [L/T]
The hydraulic head data obtained during slug tests from this investigation could
always be approximated by a straight line, but the degree of approximation
varied between the tests. A concave -upward curvature of the slug test data was
common, and this could result from storage processes in the aquifer (Butler,
1998)—in general, storage is ignored in the Hvorslev analysis. In such cases, the
two most common approaches to fit a straight line to the plotted curve for the
Hvorslev method were exercised (Butler, 1998). The most common approach
matches the early time data of the slug test while ignoring the late time data
where the curvature is typically manifested. Another approach breaks up the
curve into two separate line segments and the analysis uses the slope of the
second linear segment. This approach was applied when the slug test was
affected by storage in a well sand pack, which affected the early response of the
test.
Bouwer and Rice analytical method was used if the well was not fully
submerged. Well parameters and transducer data were inputted into
AQTESOLVTM. AQTESOLVTM automatic methods for matching the Bouwer and
Rice solutions to the slug test data were used.
3. Screening Level Risk Assessments
To support the groundwater assessment, potential risks to human health and the environment
were assessed in accordance with applicable federal and state guidance. Screening level human
health and ecological risk assessments were conducted that included development of
conceptual exposure models (CEM) to serve as the foundation for evaluating potential risks to
human and ecological receptors. The purpose of the human health and ecological CEMs was to
identify potentially complete exposure pathways to environmental media associated with the
site and to specify the types of exposure scenarios relevant to include in the risk analysis.
Potential exposure pathways were considered complete when all of the following elements
applied: 1) a constituent source; 2) mechanisms of constituent release and transport from the
source area to an environmental medium; and 3) feasible routes of potential exposure at the
point of contact (e.g., ingestion, inhalation, dermal or ambient contact). Maximum constituent
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Duke Energy Progress — Asheville Steam Electric Plant
Groundwater Assessment Report
Comprehensive Site Assessment Report
Appendix C - Methodology
concentrations were compared to appropriate risk-based screening values as a preliminary step
in evaluating potential for risks to human and ecological receptors. Based on results of the
screening level risk assessments, a refinement of COPCs will be conducted and more definitive
risk characterization will be performed as part of the corrective action process, if needed.
3.1 Human Health Risk Assessment
The screening level human health risk assessment process involved comparison of
constituent concentrations in various media to the following risk-based screening
criteria:
• Soil analytical results collected from the 0 to 2 foot depth interval compared to US
EPA residential and industrial soil Regional Screening Levels (RSLs) (US EPA, June
2015);
• Groundwater results compared to NCDENR Title 15A, Subchapter 2L Standards
(NCDENR, 2006);
• Surface water analytical results compared to North Carolina surface water standards
(Subchapter 2B) and US EPA national recommended water quality criteria
(NCDENR, 2007; US EPA, 2006).
• The surface water classification as it pertains to drinking water supply, aquatic life,
high/exceptional quality designations and other requirements for other activities
(e.g., landfill permits, NPDES wastewater discharges) were noted;
• Sediment results compared to US EPA residential and industrial soil RSLs (US EPA,
October 2014 or latest update); and
• Sediment, soil and ground water results compared to available local, regional and
national background sediment, soil and ground water data, as available.
• If warranted as part of corrective action decisions, site and media specific risk-based
remediation standards can be calculated in accordance with the Eligibility
Requirements and Procedures for Risk -Based Remediation of Industrial Sites
Pursuant to N.C.G.S. 130A-310.65 to 310.77, North Carolina Department of
Environment and Natural Resources, Division of Waste Management, 29 July 2011.
3.2 Ecological Risk Assessment
The screening level ecological risk assessment (SLERA) for the site included a
description of the ecological setting and development of the ecological CEM specific to
the ecological communities and receptors potentially exposed to site -related COPCs. A
list of potential ecological receptors (e.g., plants, benthic invertebrates, fish, mammals,
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Groundwater Assessment Report
Comprehensive Site Assessment Report
Appendix C - Methodology
birds, etc.) was compiled, as well as identification of sensitive ecological populations
and critical habitat based on information from the North Carolina Natural Heritage
Program, and U.S. Fish and Wildlife Service.
Step 1 of the SLERA consisted of completion of an ecological checklist as required by
Guidelines for Performing Screening Level Ecological Risk Assessment within North
Carolina (NCDENR, 2003).
Step 2 of the SLERA consisted of performing screening level exposure estimates and risk
calculations. This involved comparison of maximum detected concentrations or
maximum detection limits for non-detected constituents to applicable ecological
screening values (ESVs) intended to be protective of ecological receptors. If exposure
concentrations exceeded ESVs, potential ecological impacts could not be ruled out.
The following ESV sources were used in the SLERA:
• US EPA Ecological Soil Screening Levels;
• US EPA Region 4 Recommended Ecological Screening Values; and
US EPA National Recommended Water Quality Criteria and North Carolina
Standards.
Constituents were identified as a Step 2 COPCs as follows:
• Category 1- Constituents whose maximum detection exceeded the media -specific
ESV;
• Category 2 - Constituents that generated a laboratory sample quantitation limit that
exceeded the US EPA Region IV media -specific ESV;
• Category 3 - Constituents with no US EPA Region IV media -specific ESV but were
detected above the laboratory sample quantitation limit;
• Category 4 - Constituents that were not detected above the laboratory sample
quantitation limit and had no US EPA Region IV media -specific ESV; and
• Category 5 - Constituents with a sample quantitation limit or maximum detection
that exceeded the North Carolina Surface Water Quality Standards.
3.3 Surface Investigation
Samples were collected at the ground or water surface to support the screening level risk
assessment. Samples were collected wearing nitrile gloves.
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Groundwater Assessment Report
Comprehensive Site Assessment Report
Appendix C - Methodology
3.3.1 Surface Water Sampling
Surface water samples were collected to assess groundwater to surface water
pathways and evaluate surface water quality. Sample jars that did not contain a
preservative were used to collect the water directly from the source. The water
was decanted from the sample jars into the jars that required preservative.
Surface water samples were analyzed for parameters listed in Table 10-2, except
for radionuclides and metals speciation parameters. Stream flow measurements
were recorded at the time of sampling with the exception of measurements
within major waterways.
3.3.2 Sediment Sampling
Sediment samples were collected from the bed surface and co -located with
surface and seep samples to evaluate sediment quality and provide data to be
used in the screening level risk assessment. Where possible, samples were
collected directly into sample jars. If surface water was too deep to safely collect
sediment samples directly, sediment was obtained using a sampling dredge.
Sediment samples were analyzed for parameters listed in Table 8-2.
3.3.3 Seep Sampling
Seep samples were collected wearing nitrile gloves to assess groundwater to
surface water pathways at the site and support the human health and ecological
risk assessment. Seep samples were analyzed for parameters listed in Table 10-2,
except for radionuclides and metals speciation parameters. Seep flow
measurements were recorded at the time of sampling.
References:
Butler, J.J., Jr., The Design, Performance, and Analysis of Slug Tests, Lewis Publishers, New
York, 1998, 64-71; 87-90.
US Bureau of Reclamation, 2001. Engineering Geology Field Manual, 2nd Edition, Volume
2, US Department of the Interior.
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