NC0089621_More Information Received_20180924

novozymes
Rethink Tomorrow
September 24, 2018
Via U.S. Mail and E-Mail
Julie Grzyb
Supervisor, Complex Permitting Unit
NCDEQ - Division of Water Resources RECEIVE
1611 Mail Service Center
Raleigh, North Carolina 27699-1611 SEP 2 5 2018
[e-mail]
Water Resources
Teresa Rodriguez Permitting Section
Complex Permitting Unit
NCDEQ - Division of Water Resources
1611 Mail Service Center
Raleigh, North Carolina 27699-1611
[e-mail]
Jeff Manning
Classifications, Standards & Rules Review Branch Chief
NCDEQ - Division of Water Resources
1611 Mail Service Center
Raleigh, North Carolina 27699-1611
[e-mail]
Connie Brower
Classifications, Standards & Rules Review Branch
NCDEQ - Division of Water Resources
1611 Mail Service Center
Raleigh, North Carolina 27699-1611
[e-mail]
RE: NPDES Permit Application NC0089621
Novozymes North America, Inc.
Franklin County
Dear Ms. Grzyb, Ms. Rodriguez, Mr. Manning, and Ms. Brower:
This letter follows up on the meeting on Friday, August 24, 2018 among representatives of
Novozymes North America, Inc. ("Novozymes") and the Department of Environmental Quality
and my letter to the Division of Water Resources (the "Division") dated August 30, 2018 that
recounted the meeting. As we agreed at the meeting and as forecast in my August 30 letter,
Ramboll Group has completed the review of potassium issues and has finalized the enclosed
302515488 v1

i
Potassium Aquatic Life Values Study Report (the "Study Report"). The Study Report is provided
for review by the DWR-Standards Branch.
As discussed in the Study Report, Ramboll derived acute and chronic water quality values for
potassium that would be protective of aquatic life in the receiving stream, including freshwater
mussels. Using available data and scientific research, and applying DEQ regulations and EPA
guidelines, Ramboll determined protective potassium aquatic life values of 16.5 mg/L chronic
and 17.14 mg/L acute. References are noted in the Study Report and are provided on the USB
flash drive attached at the end of the report. Please let us know if you have questions regarding
the Study Report. If it would be helpful during your review, we can make the scientists at
Ramboll Group available for a teleconference or in-person meeting.
Thank you again for your time and efforts regarding review and processing of the Permit
Application. We look forward to working with the Division toward issuance of a draft NPDES
permit.
Sincerely,
6PI GiA-\\
Angela J. Walsh
Novozymes North America, Inc.
Enclosure
cc: Bill Lane, DEQ General Counsel
Linda Culpepper, Division of Water Resources Director
Mary Penny Kelley, Special Advisor, Office of the Governor
Jeffrey Poupart, Water Quality Permitting Section Chief
Andrew Hargrove, DEQ Assistant General Counsel
Mike Templeton, Water Quality Permitting Section
Bing Bai, Complex Permitting Unit
Chris Ventaloro, Classifications, Standards & Rules Review Branch
Rick Bolich, DWR - Raleigh Regional Office
Steve Tedder, Tedderfarm Consulting
(all via e-mail only without enclosure)
2
302515488 v1

Date
September 2018
POTASSIUM AQUATIC
LIFE VALUES
STUDY REPORT
..
„. .. 7
. , , ;4''-' '4(''''',7: ' ''' ',,•!'-;'''. ' '-!,4e:'
- ..,� w :
-f.:ft- ' 1
:"'
r.r4 %. .M ."
N
_ w,..
24172.w
y
I.
RAMB LL

POTASSIUM AQUATIC LIFE VALUES
STUDY REPORT
Project no. 1690000122 Ramboll
Version Final 201 Summit View Drive
Date September 19,2018 Suite 300
Prepared by Rick Lockwood and Liza Heise Brentwood,TN 37027
Checked by Robin Richards USA
T [phone]
F [phone]
www.ramboll.com

Ramboll-Potassium Aquatic Life Values
CONTENTS
1. Introduction 3
1.1 General 3
1.2 Problem Definition 4
1.3 Study Design 4
2. Study Plan 7
2.1 "Site"and "Occur at the Site" Definition 7
2.2 Aquatic Life Value Development 8
2.2.1 Literature Review 8
2.2.2 Supplemental Toxicity Testing 8
2.2.3 Species-Specific Procedures 11
3. Results and Cirteria Derivation 12
3.1 Literature Review 12
3.2 Toxicity Test Results 12
3.2.1 Acute Test Results 13
3.3 Potassium-Hardness Relationship 13
3.4 In-Stream Site-Specific Aquatic Life Value Calculations 15
3.4.1 Final In-Stream Site-Specific Aquatic Life Values 15
4. Report References 17
5. Potassium Toxicity References 18
TABLES
Table 1: Acute Potassium Toxicity Test Results for Lampsilis siliquoidea and Lampsilis radiata
Table 2: Supporting Analytical Data
Table 3: Chronic Potassium Toxicity Database
Table 4: Acute to Chronic Ratio Calculation
Table 5: Calculation of In-Stream Site-Specific Acute and River Segment Specific Chronic Potassium
Aquatic Life Values
1/22

Ramboll-Potassium Aquatic Life Values
APPENDICES
Appendix 1
Acceptable Aquatic Acute Toxicity Database for Potassium Site-Specific Aquatic
Life Value Derivation
Appendix 2
Freshwater Potassium Aquatic Toxicity Database Literature Search Results
Appendix 3
Review of Potassium — Hardness Toxicity Relationship for Freshwater Mussels
2/22

Ramboll-Potassium Aquatic Life Values
1. INTRODUCTION
1.1 General
Ramboll conducted a review of potassium limits in the context of a proposed new direct discharge
of treated effluent subject to authorization as per North Carolina Department of Environmental
Quality (NCDEQ) NPDES permitting regulations. Specifically, in issuing a NPDES Permit, the state
assures that the discharge does not have a reasonable potential to cause or contribute to the
exceedance of in-stream criteria that protects the designated uses of the receiving stream. The
state, to assure protection of the designated use of the receiving stream, may develop water
quality-based effluent limits (WQBELs) that would be enforceable in the NPDES Permit. WQBELs
are developed considering a numeric in-stream criterion to protect designated use, stream design
flow appropriate for the criterion, and statistical translation to a continuously discharging
effluent. EPA, in developing the water quality-based toxics control approaches and
methodologies, derives in-stream numerical aquatic life criteria (i.e., National Recommended
Water Quality Criteria) based on a concentration (magnitude) for a set exposure (duration) that
should not be exceeded more than once every 3 years. In-stream criteria are not considered to
protect all aquatic life under all possible conditions at all times, but are considered to protect
950/0 of aquatic life, whether acute or chronic exposure at a frequency of once per three years'
(equates to less than 95% of the time). These EPA approaches and methodologies are referenced
in North Carolina regulations2.
National Recommended Water Quality Criteria can be re-developed when an aquatic ecosystem
need more or less protection for a constituent using site-specific water quality criteria (or
criterion) methods presented in the USEPA 1985"Guidelines for Deriving Numerical National
Water Quality Criteria for Protection of Aquatic Organisms and Their Uses"(EPA Guidelines) and
the EPA"Water Quality Standards Handbook."These guidelines outline development of in-stream
site-specific acute and in-stream site-specific chronic aquatic life criteria'. Elements of the EPA
Guidelines have been updated (in 1994) and subsequently codified in 40 CFR 132 Appendix A
(regulation applicable to the Great Lakes).
As part of a water quality standards program, states present water quality criteria both as
narrative standards and numeric criteria for specific chemicals (typically similar to the National
Recommended Water Quality Criteria). In addition, some states present approaches for
interpreting a narrative criterion as a numeric assessment (e.g., using Whole Effluent Toxicity
testing) and some states present approaches to developing aquatic life criteria for a chemical if a
National Recommended Water Quality Criteria did not exist.
North Carolina presents in 15 NCAC Subchapter 02B three approaches to defining acute aquatic
toxicity for a chemical:
• Acute Approach 1. 1/2 of the Final Acute Value (FAV) determined using the EPA Guidelines;
USEPA, 1985,"Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses"P885-
227049.
Posthuma,Leo,GW Sutter,TP Traas,2002,"Species Sensitivity Distributions in Ecotoxicology,"CRC Press.
2 15A NCAC 28.0202(1)(a); 1SA NCAC 2B.0211(11)(b); 15A NCAC 28.0220(9)(d)
3/22

Ramboll-Potassium Aquatic Life Values
• Acute Approach 2. If a value cannot be determined using Acute Approach 1. then, apply one-
third of lowest'available' LC50; or
• Acute Approach 3. Conduct case-by-case statistical analyses of a dose-response curve3.
In 15 NCAC Subchapter 2B, North Carolina presents its approaches to interpreting the narrative
chronic aquatic toxicity"in the absence of direct measurements of chronic toxicity4":
• Chronic Approach 1. Apply acute-to-chronic ratio (ACR) for lowest LC505,
• Chronic Approach 2. If an ACR is not available, then 0.01 of the lowest LC50, or
• Chronic Approach 3. 0.05 of the lowest LC50 if half-life of chemical less than 96-hr6.
The following sections walk through the steps required to validate data that will be used in acute
and chronic databases. From these databases, a Final Acute Value (FAV), ACR, and chronic value
can be calculated as described below. Ramboll utilized the approach and methodologies
presented in the EPA Guidelines and North Carolina regulations in estimating protective
potassium concentrations for acute data (North Carolina Acute Approach 1) and the North
Carolina Chronic direct measurement.
1.2 Problem Definition
Potassium has been identified as a constituent of concern for mussels based on results of
analytical evaluation of the proposed Novozymes effluent. Freshwater mussels (family
Unionidae) have a demonstrated sensitivity to potassium below that of other regularly tested
freshwater taxa. Of the roughly 300 known species, only Lampsilis siliquoidea (the Fatmucket)
has a robust potassium acute toxicity data base in a range of water quality conditions that is
representative of where this species is found, generally the Mississippi River basin. The data base
for long-term sublethal (growth or reproduction) effects to mussels is very limited.
Numeric in-stream site-specific aquatic life values for potassium have previously been developed
using accepted and recognized methodology under the oversight of the Oklahoma Water
Resource Board (CP Kelco, 2016). Similarly, Ramboll proposes implementing the aquatic life
values for potassium into potassium benchmarks utilizing the statistical procedures to relate
duration of monthly average and daily maximum benchmarks for Novozymes. This Study Report
details the methods used to generate the data and information to confidently develop valid in-
stream site-specific acute and in-stream chronic potassium aquatic life values that are acceptable
to NCDEQ.
1.3 Study Design
To develop in-stream site-specific acute and in-stream chronic potassium aquatic life values, two
regulatory processes were considered: 1) aquatic life value development and 2) site-specific
modification. Potassium is not a Clean Water Act priority pollutant or toxic pollutant, it is not
15A NCAC 26.0202(1)
°The direct measurement of chronic toxicity is to b compared to the chronic value. It would seem the direct measurement would be using
Whole Effluent Toxicity testing methods to generat a chronic value. As per 15A NCAC 213,0202(15),a chronic value is the geomean of the
NOEC(no observable effect concentration)and LO C(lowest observable effect concentration). The chronic value would be site-specific,and for
the proposed Novozymes discharge to Cedar Cree the chronic value would be 56%effluent.For a discharge to the Tar River,the chronic value
would be 31%effluent.
5 LC50 is the concentration that is lethal to 50%oft e test organisms. Acute to Chronic Ratio(15A NCAC 26.0202(2)is the ratio of the LC50 for
a specific toxicant or an effluent to the chronic val a for the same toxicant or effluent.
6 15A NCAC 26.0202(15), 15A NCAC 2B.0208(a)(1)
4/22

Ramboll-Potassium Aquatic Life Values
listed in the EPA National Recommended Water Quality Criteria for non-priority pollutants or
nonconventional pollutants and is not listed in 15A NCAC 26.0211. Further, North Carolina has no
surface water quality standard, drinking water standard, or ground water standard for potassium.
Without any type of potassium standard already in place, it may be appropriate to use the North
Carolina regulations for developing aquatic life values for potassium. As stated above, the
regulation for defining acute water quality values, follows the EPA process of adopting water
quality values for the protection of beneficial use for aquatic life, specifically, the EPA Guidelines.
Chronic values are defined in 15A NCAC 28.0202 with procedures described in 15A NCAC
26.0208. The selected approach is dependent upon the available validated data.
15A NCAC 2B presents approaches to developing site-specific regulatory criteria including mineral
criteria; however, these approaches are specific to heavy metals. NCDEQ regulations (15A NCAC
2B .0211 (11) (b)) reference the EPA Water Quality Standards Handbook; Second Edition, which
within Chapter 3 includes water quality criteria.' The EPA methods apply to non-regulatory
aquatic life criteria as well. Since the EPA Guidelines and Water Quality Standards Handbook are
appropriate to develop criteria, they are applicable to developing aquatic life values. Chapter 3
of the Water Quality Standards Handbook presents the following for modifying water quality
criteria:
"In the early 1980s, EPA recognized that laboratory-derived water quality criteria might not
accurately reflect site-specific conditions and, in response, created three procedures to derive
site-specific criteria. This Handbook contains the details of these procedures, referenced
below.
The Recalculation Procedure is intended to take into account relevant differences between the
sensitivities of the aquatic organisms in the national dataset and the sensitivities of
organisms that occur at the site (See Appendix L, pp. 90-97).
The Water-Effect Ratio Procedure (called the Indicator Species Procedure in USEPA, 1983a;
1984f) provided for the use of a water-effect ratio (WER) that is intended to take into
account relevant differences between the toxicities of the chemical in laboratory dilution
water and in site water (see Appendix L.).
The Resident Species Procedure intended to take into account both kinds of differences
simultaneously (see Section 3.7.6)."
The options for modifying aquatic life values are not specific to a chemical or a waterbody but do
require generation and validation of data and clarity in presenting inputs into the process of
modifying the values. Although development of an in-stream site-specific potassium standard
does not fall entirely within one of the three categories noted above, Ramboll has incorporated
elements of each of the three categories.
We have used the EPA Guidelines as the primary guidance in combination with the EPA 1994
Water Quality Standards Handbook in developing an acute potassium aquatic life value as
described below. The resident species procedure was then applied to modify the acute aquatic
life value specific to the warm-water rivers found in the subject region of North Carolina.
Previous testing with mussel species, Lamplilis siliquoidea (Fatmucket mussel) demonstrated a
relationship between potassium toxicity and hardness where the hardness of the water utilized in
the mussel testing was 100 mg/L CaCO3 or greater. The summer low-flow hardness of the
EPA-823-B-94-005; August 1994 with some additional new information (June 2007)
5/22

Ramboll-Potassium Aquatic Life Values
proposed receiving streams in North Carolina have median values of approximately 33 CaCO3
(USFWS, 2017). Hence, additional aquatic toxicity testing was performed to determine if a
relationship between potassium toxicity and water quality characteristics could be confirmed at a
lower hardness. Details of the path followed to develop in-stream site-specific acute and in-
stream river segment-specific chronic potassium aquatic life values for the low-hardness waters
are presented in the following sections.
6/22

Rambo!!-Potassium Aquatic Life Values
2. STUDY PLAN
The study plan for developing in-stream site-specific acute and in-stream river segment-specific
chronic potassium aquatic life criteria entailed a stepwise process presented in the following
sections:
• Step 1. "Site"and "Occur at the Site" Definition
• Step 2. Criteria Development
• Literature Review
• Review Process
• Data Gap Analysis
• Supplemental Toxicity Testing
• Testing Design
• Testing Execution
• Step 3. Criteria Derivation
2.1 "Site" and "Occur at the Site" Definition
Chapter 3 of the Water Quality Standards Handbook provides guidance on defining the site as an
area. Depending on the application, a site can be defined as a state, region, watershed or
waterbody segment. For the purposes of this study, the in-stream river segment-specific chronic
potassium aquatic life value is applicable to the Tar River at Louisburg (Station #01100000) or
Cedar Creek (just south of the Franklin County POTW discharge).
The term "resident species"or`occur at the site"is defined by EPA as the following:
"The phrase"occur at the site"includes the species, genera, families, orders, classes, and
phyla that:
a. Are usually present at the site.
b. Are present at the site only seasonally due to migration.
c. Are present intermittently because they periodically return to or extend their
ranges into the site.
d. Were present at the site in the past, are not currently present at the site due to
degraded conditions and are expected to return to the site when conditions
improve.
e. Are present in nearby bodies of water, are not currently present at the site due to
degraded conditions and are expected to be present at the site when conditions
improve.
The process of defining if a species occurs at the site was necessary as we suspected that two
particular species (Ceriodaphnia rigaudi, C. rigaudi) and the Rainbow trout (Oncorhynchus
mykiss) included in the potassium dataset did not occur in this region of North Carolina. An
assessment of in-stream temperature indicated the proposed receiving streams consistently
maintained temperatures that would not support Rainbow trout. The distribution of C. rigaudi in
North Carolina is uncommon. This species is known to predominately prefer ponds or lakes and
7/22

Ramboll-Potassium Aquatic Life Values
climates consistent with sub-tropic like conditions. As such, it was not appropriate to consider C.
rigaudi data in the in-stream site-specific potassium criteria development.
Although the EPA Guidelines indicate that acceptable data for a fish in the family Salmonidae be
included in the calculation of criteria, this was deemed inappropriate for the proposed receiving
stream segments because fish in the family Salmonidae do not reside in the proposed receiving
streams. Therefore, to maintain the eight family MDRs, a fish species (the common carp,
Cyprinus carpio) that was known to occur in the proposed rivers was substituted.
2.2 Aquatic Life Value Development
2.2.1 LITERATURE REVIEW
2.2.1.1 Review Process
The first step of developing in-stream site-specific potassium aquatic life criteria was to review
the published literature on the aquatic toxicity of potassium and validate the data, primarily
based on the EPA Guidelines. However, 40 CFR 132 Appendix A (Methodologies for Development
of Aquatic Life Criteria and Values) and MDEQ 1996 were also consulted as these references
provide much more rigorous guidelines for determining data validity. The initial literature search
was conducted in 2017, a second literature search was conducted in August 2018 to ensure all
valid literature was obtained and included in the analysis.
2.2.1.2 Data Gap Analysis
The next step of developing in-stream site-specific aquatic life criteria for potassium was to
determine if there were information gaps in the acceptable dataset to appropriately statistically
analyze the data. As per the EPA Guidelines, aquatic life criteria can be calculated using the
eight minimum data requirements method. Additionally, if it is determined that water quality
characteristics (e.g., hardness and alkalinity) affect toxicity, then a regression-based approach
can be taken to calculate the aquatic life criteria. Ramboll determined that the data gaps for in-
stream site-specific potassium criteria applicable to proposed receiving stream rivers included
acute data for a mussel in a low-hardness water, and representative species indigenous to the
area.
The in-stream site-specific modification process and associated toxicity test design included
addressing the data gaps by investigating the relationship between potassium acute toxicity and
hardness using regression analysis on a low-hardness water, and utilizing an indigenous test
species.
2.2.2 SUPPLEMENTAL TOXICITY TESTING
While the existing acceptable database for potassium toxicity shows acute test results for waters
with a variety of hardness and alkalinity values, the data do not exhibit toxicity test results for a
mussel species in a low-hardness water and/or alkalinity. Thus, the existing data provide insight
to differences in sensitivity among test species to potassium and not differences in toxic response
of any single species to potassium due to changes in hardness and/or alkalinity. Additional
toxicity test results were required to investigate a relationship between potassium toxicity and
waters with low-hardness.
8/22

Ramboll-Potassium Aquatic Life Values
2.2.2.1 Testing Design
Supplemental toxicity testing in support of an in-stream site-specific potassium value included
acute toxicity testing with mussel species exposed to a low-hardness water. Based on the
existing acute acceptable database, and organism availability, supplemental toxicity tests were
conducted with Fatmucket and Lampsilis radiata (Eastern Lampmussel). Eastern Lampmussel was
selected as a representative indigenous test species.
Although Fatmucket were not indigenous to the proposed receiving streams, other species of the
genus Lampsilis were. Furthermore, this species is artificially propagated in quantities needed for
this study; has documented performance in toxicity tests meeting test acceptability criteria; and
is considered an acceptable surrogate for other mussel species. Imlay (1973) utilized Fatmucket
in addition to other mussel species in potassium toxicity tests. His study showed similar
responses between all mussel species tested. Therefore, Fatmucket was considered an
appropriate surrogate species to represent most mussel species found in moderately hard water
rivers.
2.2.2.2 Test Execution
2.2.2.2.1 GENERAL
Potassium, in the form of potassium chloride (KCI), was added to test waters to establish
potassium test concentrations. Reagent-grade or better (98% or higher) provided the potassium
source for all tests. All potassium stock solutions were prepared in the test water to be used in
the respective acute toxicity tests and diluted with the test water appropriate to the toxicity test
to be conducted. Since potassium is stable in water and concentration correlate well to
conductivity, solution conductivity values were confirmed by measuring conductivity daily during
the testing. Actual potassium concentrations were measured only in newly prepared toxicity test
waters for the acute tests.
"Range-finding"toxicity tests were not necessary due to the availability of acute potassium
toxicity data. Potassium test concentrations were established in a dilution series (minimum of
five exposures) utilizing test concentrations of 10, 20, 40, 70, and 100 mg/L nominal potassium
to provide appropriate dose/response curves. Test design was attempted to set dilution series
increments to bracket the midpoint of mortality responses. This was done to avoid "all or
nothing"dose/response curves and develop more meaningful dose/response data. In acute
toxicity tests, every effort was made to generate dose/response data that have between 10
percent and 100 percent mortality (average of replicates) in three exposure concentrations.
Alkalinity and hardness were measured in test dilution waters and potassium was measured in all
test solutions as detailed in this section.
All toxicity testing followed the test methods with key test features as outlined below. All toxicity
tests were supported by analytical analyses, water quality assessments (i.e., pH, conductivity,
dissolved oxygen, temperature), and documentation of test water hardness and alkalinity for
each batch of dilution water prepared. Methodologies for documentation of water quality
parameters (pH, conductivity, hardness, ammonia, etc.) followed standard methodologies (i.e.,
USEPA, Standard Methods) as outlined in the laboratory SOP manual (available upon request).
9/22

Ramboll-Potassium Aquatic Life Values
2.2.2.2.2 TEST DILUTION WATER
Laboratory reconstituted dilution water was prepared at two different hardness values, 25 and 75
mg/L CaCO3,The dilution waters were prepared as described below and used in acute toxicity
tests. The following water quality parameters were documented for each batch of dilution water
used in all toxicity tests:
• Total hardness
• Total alkalinity
• Total Residual Chlorine (TRC)
The low-water hardness water generally followed the recipe of standard reconstituted
USEPA/ASTM dilution waters (USEPA, 2002a, ASTM E729). The following reagent grade salts
were added to de-ionized water to prepare the reconstituted waters listed below:
• Standard USEPA/ASTM waters - NaHCO3, MgSO4, CaSO4, KCI
De-ionized water was obtained from municipal potable water that was passed through a U.S.
Filter, Inc. (or similar) initial deionization unit equipped with five water purifying cartridges
(ultrafiltration membrane, carbon cartridge, mixed bed ion exchange, mixed bed ion polisher,
and organic scavenger). The base water for the laboratory water is tested annually to ensure it's
free of toxics. Results of the annual testing are kept on file.
2.2.2.2.3 ACUTE TESTING
Laboratory acute toxicity test protocols followed the most recent edition of ASTM (2007) and
adhered to the laboratory SOP manual. Ramboll's SOP-specified acute toxicity testing methods
are available upon request. Only tests meeting data quality requirements specified by the EPA
Guidelines, USEPA (2000, 2002a) and ASTM were used in derivation of potassium aquatic value
(i.e., only data from acute tests with 90 percent or higher control survival will be used).
Fatmucket and Eastern Lampmussel acute tests were 96-hour static daily-renewal toxicity tests.
Test durations and protocols were as follows:
• Lampsilis siliquoidea and Lampsilis radiata - 96 hr test following ASTM (2006) protocol.
Mortality was the test endpoint, with mortality assessed as detailed below in the species-specific
test protocols. Water quality parameters (hardness, alkalinity, pH, dissolved oxygen,
conductivity, and temperature) were documented in accordance with specific test protocols.
2.2.2.2.4 TEST ORGANISMS
Test organism sources, culturing, and maintenance procedures adhered to American Society for
Testing and Materials (ASTM) and USEPA protocols, and laboratory Standard Operating
Procedures (SOP). Key elements of the organism culturing and handling program are
summarized below.
Fatmucket were obtained from Missouri State University and Eastern Lampmussel were obtained
from Virginia Department of Game and Inland Fisheries for toxicity testing in Ramboll's aquatic
toxicity testing laboratory. Organisms of known age were received via next-day delivery, in
culture water similar to USEPA very soft water. Upon receipt, the temperate, pH, and dissolved
oxygen content of the water were documented. Mussels are not fed at test initiation and are
placed in designated culture and holding rooms at test temperature until the time of test
10/22

Ramboll-Potassium Aquatic Life Values
initiation. Since potassium chloride is the toxicant used for routine mussel reference toxicant
testing at Ramboll, results were compared to the established data base for determination of
organism heath status.
2.2.3 SPECIES-SPECIFIC PROCEDURES
2.2.3.1 Acute test
Mussel toxicity tests were ASTM (2006) 96 hour static, daily -renewal toxicity tests conducted
under a 16:8 light:dark photoperiod at a test temperature of 25 °C. Test organisms age was
juvenile and less than 5 days post transformation at test initiation. Organisms were not fed
during acute toxicity tests. Four replicates of 5 organisms each were exposed to nominal
potassium concentrations of 0, 10, 20, 40, 70, and 100 mg/L. Water quality parameters (pH,
dissolved oxygen, conductivity, and temperature) were documented in all newly prepared and
24-hour-old test and control water exposures for the duration of the tests at test initiation, daily
renewal, and test termination. Test water temperatures were 25 +/-1 °C and pH was between
6.0-9.0 s.u.
2.2.3.2 QA/QC
The following QA/QC measures were implemented to ensure the validity of potassium analytical
results, and other supporting analyses:
• Use of only high-purity (greater than 98%) potassium chloride to establish potassium test
concentrations. Certification of analysis can be provided upon request.
• Obtaining from the manufacturer, a list of impurities in the potassium chloride used to
establish test concentrations.
• Use of a certified laboratory, and state and NELAC certified laboratory for all potassium
analyses.
• Use of a standardized sample identification and sample labeling system to ensure proper and
consistent sample identification (i.e., organism tested, test date, "new"or aged test solution,
etc.).
• Review of laboratory QA/QC data (method blanks, internal spike recoveries, etc.) to ensure
that all sample analyses are within specified control boundaries.
• Sample shipment under proper chain-of-custody.
• Daily calibration of laboratory meters (pH, dissolved oxygen, conductivity) used to measure
water quality conditions in toxicity tests. All meter calibration and related QA/QC
methodologies followed the approved toxicity testing SOPs. Any corrective measures were
implemented and documented.
• Test water hardness and alkalinity was assessed following procedures outlined in toxicity
testing SOPs. These protocols follow established EPA and ASTM methods, utilize
commercially-prepared reagents, and their accuracy is routinely evaluated using commercially
prepared standards.
11/22

Rambo!!-Potassium Aquatic Life Values
3. RESULTS AND CIRTERIA DERIVATION
3.1 Literature Review
A literature search for potassium freshwater toxicity data was conducted in 2017 and again in
August 2018 to ensure all valid literature was obtained and included in the analysis. The same
data validity requirements, which are detailed in the EPA Guidelines and 15A NCAC 2B, were
applied to any data resulting from the updated literature search. The August 2018 literature
search revealed a recent publication (accepted for publication Wang et al, 7/30/2018,
Environmental Toxicology and Chemistry) in which two chronic toxicity tests were conducted with
Fatmucket exposed to potassium chloride. The testing was conducted in 2013. In this chronic
study, Fatmucket were exposed to potassium concentrations with and without refugia substrate
(sand). The controls in both exposures met test acceptability criteria, however, the results of the
tests vary considerably.
Chronic (28-Day) Fatmucket data (Wang et al, 7/30/2018)
Test Regime ChV Biomass EC20
(NCDEQ Regulatory (mg/L)
Definition) (mg/L)
Water-only 32.0 23.0
Refugia substrate (sand) 6.9 8.7
NOTES:
ChV- geometric mean between the NOEC and LOEC.
Testing was conducted at hardness 100 mg/L CaCO3.
In the Wang study, there is discussion of biofouling of the substrate, indicating toxicity other than
that of potassium is evident. Because of the biofouling, the general trend would suggest that the
water-only exposure yields a more valid test. After Ramboll's review of the paper, it was
determined that the water-only test was valid and should therefore be added to the acceptable
chronic database.
It should be noted that both tests were conducted under general guidance of ASTM E2455-06
(2013) which are under development and have not been subjected to extensive interlaboratory
testing and review. Also, the ASTM guidance does not include refugia substrate in the method.
3.2 Toxicity Test Results
Acute aquatic toxicity testing with potassium, as described above in Section 2, was conducted in
August 2017. Acute test results are summarized and discussed below in terms of average
measured potassium and hardness concentrations. A summary of the testing results, including
95 percent confidence intervals, is presented on Table 1. Acute test results for Fatmucket
showed a greater acute sensitivity to potassium at in a low hardness water than Eastern
Lampmussel. The Eastern Lampmussel, indigenous to the North Carolina streams, is considered a
low-hardness mussel and is much more tolerant of the lower hardness than Fatmucket. In the
two tests conducted, the Eastern Lampmussel was about 1.5 percent more tolerant to potassium
12/22

Ramboll-Potassium Aquatic Life Values
than Fatmucket in the 25 mg/L CaCO3 hardness water and was approximately twice as tolerant
to potassium than Fatmucket in the 75 mg/L CaCO3 hardness water.
3.2.1 ACUTE TEST RESULTS
Test acceptability criteria (i.e. control survival) were met for all acute tests. The 96-hour LC50
results for the testing were calculated based on measured values and are presented on Table 1.
Water quality parameters (i.e., pH, temperature, dissolved oxygen, conductivity) remained within
acceptable limits for all tests. Supporting analytical analysis values measured at the beginning of
each test are presented on Table 2. Since analytical measurements (e.g., hardness, alkalinity,
and potassium) were collected once at the beginning of the test, individual analytical
measurements were compared to nominal concentrations. Individual analytical measurements
were generally within 20% of the nominal test concentrations for each test treatment.
The measured 96-hour LC50 results at hardness 25 were 37.2 mg/L for Eastern Lampmussel and
22.4 for Fatmucket. The measured 96-hour LC50 results at hardness 75 were 60.8 mg/L for
Eastern Lampmussel and 28.1 for Fatmucket. Because these data are valid, they were used in
the in-stream site-specific potassium criteria development.
3.3 Potassium-Hardness Relationship
Ramboll recognizes the relationship between potassium toxicity to Fatmucket mussels and
hardness, based on results of previous acute testing. Linear regression showed a high degree of
predictability (determination) between potassium concentration and hardness (R2 = 0.78)
combined with a slope showing a 20% increase in the potassium LC50 concentration. From these
data, a potassium-hardness toxicity relationship was developed for the Fatmucket mussel in
waters with hardness from 100 to 400 mg/L as CaCO3.
This relationship is defined as: LC50 (mg/L of potassium) = 0.1609(hardness)+26.872.
The relationship is used in a stepwise approach as presented below:
Potassium-Hardness Relationship Calculation
1.Hardness 2.Test Endpoint (EC20 or 3.Ratio of Test 4.Multiply known 5.Test Endpoint
Value (mg/L LC50) values (mg/L Endpoint (EC20 Test Endpoint (EC20 or LC50)
CaCO3) potassium)at hardness or LC50) values (EC20 or LC50) values (mg/L
in Step 1 as generated values by ratio potassium) at
from calculation untested
hardness
25 0.1609(25) + 26.872 = 31
100 0.1609(100) + 26.872 = 43 31/43 = 0.72 32.0 * 0.72 23.0
25 0.1609(25) + 26.872 = 31
31/43 = 0.72 23.0* 0.72 16.5
100 0.1609(100) + 26.872 = 43
Though Ramboll recognizes the slope (adjustment factor), the assumption that toxicity behavior
outside of the tested hardness range is consistent was unknown. To confirm that the slope is
consistent below a hardness of 100 mg/L CaCO3, confirmatory testing of species adapted to low
hardness conditions was necessary. Because the potassium-hardness toxicity relationship
equation was not proven on low hardness waters, extrapolation to a hardness of 25 mg/L CaCO3
13/22

Ramboll-Potassium Aquatic Life Values
utilizing the Fatmucket relationship between 100 mg/L and 400 mg/L CaCO3 hardness was
inappropriate. The results from testing with low hardness waters (presented above) indicate the
potassium-hardness equation is valid for Fatmucket in waters ranging from hardness
concentrations of 25 to 400 mg/L CaCO3.
The potassium-hardness relationship, derived using acute testing, is also appropriate for the
chronic testing with Fatmucket. When the potassium-hardness toxicity relationship is applied to
the species mean acute value (44 mg/L potassium, Table 4) for Fatmucket at a hardness of 100
mg/L CaCO3, the result was 31.2 mg/L potassium at a hardness of 25 mg/L CaCO3.Although this
value is slightly higher than that observed in the acute testing (Table 1), it is within the expected
range of Fatmucket testing and was on-target for the predicted result (Appendix 3).
Applying thepotassium-hardness relationshipto the chronic Wanget al 2018 data, the chronic
value was adjusted to 23.0 mg/L potassium and the Biomass EC20 was adjusted to 16.5 mg/L
potassium, as shown in the calculation above and again presented in the table below.
Chronic (28-Day) Water-Only Fatmucket data (Wang et al, 7/30/2018)
ChV
Water Hardness (NCDEQ Regulatory Definition) Biomass EC20 (mg/L)
(mg/L)
100 mg/L CaCO3 32.0 23.0
25 mg/L CaCO3 23.0 16.5
NOTES:
ChV- geometric mean between the NOEC and LOEC.
In addition to the previous mussel testing, three other species were tested to determine if there
was a potassium-hardness relationship. Conversely, acute tests with C. dubia, C. tentans, and P.
promelas showed a poor degree of determination (maximum R2 = 0.37, 0.07, and 0.22,
respectively) combined with slopes showing an increase of 20% to 17% increase in the
potassium LC50 concentration. Although a useful relationship between hardness and potassium
toxicity was seen with only the mussel Fatmucket, a meaningful slope and relationship (R2 > 70)
for at least two species is required to statistically define the potassium toxicity and hardness
relationship suitable for incorporation into criteria development (EPA Guidelines, Section V.A).
A strong relationship between potassium toxicity and hardness was observed for only the mussel,
and the two species requirement was not met. Criteria development that incorporated hardness
or alkalinity water quality conditions was not further pursued. However, because a potassium-
hardness relationship has been established for mussel species and mussels have been deemed an
important species in the proposed receiving waters, it is appropriate to use the potassium-
hardness relationship for calculating the criterion with respect to mussels, according to the EPA
Guidelines.
14/22

Ramboll-Potassium Aquatic Life Values
Refer to Appendix 3 for a more detailed description of the acute toxicity testing conducted at
Ramboll in 2017 with Fatmucket and Eastern Lampmussel, as well as observations for the
potassium-hardness relationship.
3.4 In-Stream Site-Specific Aquatic Life Value Calculations
Appendix 1 presents the acceptable acute potassium toxicity database and that was used to
develop the acute site-specific value as per the EPA Guidelines, and Appendix 2 summarizes
studies considered but deemed unacceptable for use in aquatic life value derivation. The
acceptable acute potassium toxicity database includes data for 16 species and meets the eight
family requirements. Since Salmonids are likely not residents due to the temperatures of the
proposed receiving streams, the common carp (C. carpio) was substituted for the Salmonid
family data point. The common carp has been documented to be found in the proposed receiving
streams. The Ceriodaphnia species, C. rigaudi in North Carolina is rare as it prefers a tropical
climate. Also, this species is known to predominately prefer larger static waterbodies, such as
ponds or lakes. Because the two aforementioned species are not known to reside in the proposed
receiving streams of North Carolina, they have been removed from the acceptable acute
potassium database. Therefore, the in-stream site-specific acute value is applicable to waters
where Salmonids and C. rigaudi are not resident.
Table 3 presents results from the previous chronic toxicity testing conducted at Ramboll along
with the Wang et al, 7/30/2018 data which were used to develop an acute-to-chronic ratio (ACR)
as per NCDEQ guidelines. The ACR values and Final ACR value applied in derivation of the chronic
aquatic life value are presented in Table 4. Chronic testing for the Ceriodaphnia dubia (C. dubia)
and Pimephales promelas (fathead minnow), and Fatmucket was performed at the average
hardness of 100 mg/L CaCO3. Previous testing indicated a low relationship between hardness
and potassium toxicity for C. dubia and fathead minnow, furthermore, 100 mg/L CaCO3 is a
common hardness for tests included in databases and often results are adjusted to hardness 100
mg/L. Results from acute toxicity tests conducted at the same hardness and alkalinity were
paired with the results from the chronic tests to calculate species specific ACR. The final ACR
(FACR) was calculated as the geometric mean of the individual species ACR. The final ACR was
used to estimate an in-stream river segment-specific chronic value for potassium.
3.4.1 FINAL IN-STREAM SITE-SPECIFIC AQUATIC LIFE VALUES
The in-stream site-specific acute aquatic life value and in-stream site-specific chronic aquatic life
value for potassium were calculated based on the findings of the literature review, results of
aquatic toxicity testing, the procedures outlined the EPA Guidelines, and 15A NCAC 26.0208. The
potassium in-stream site-specific acute concentration calculations are presented in Table 5. The
chronic concentration was a direct measurement. Both values are presented below:
• Acute concentration = 17.14 mg/L (1/2 of the FAV determined using the EPA Guidelines)
• Chronic concentration = 16.5 mg/L (15A NCAC 2B .0208- direct measurement)
The ChV was calculated using the Fatmucket water-only EC20 value adjusted to a hardness of 25
mg/L CaCO3. The EC20 value was used in lieu of the geometric mean of the NOEC and LOEC
adjusted to a hardness of 25 mg/L CaCO3. Should the geometric mean of the NOEC and LOEC be
used, the result would be greater than the acute concentration. According to EPA Guidance
(Section XII, B), if the criterion is not consistent with sound scientific evidence, another criterion
15/22

Ramboll-Potassium Aquatic Life Values
should be derived. Because the traditional ChV for Fatmucket at a hardness of 25 mg/L CaCO3
results in a value greater than the acute criterion (23.0 mg/L potassium vs 17.14 mg/L
potassium) it makes sound scientific sense to use an alternative to the ChV. Using the Biomass
EC20 value is not only scientifically sound, but also it is a direct measurement of chronic toxicity.
The in-stream site-specific acute value and in-stream chronic value for potassium are applicable
for the proposed receiving waterbodies selected by Novozymes in Franklin County, North
Carolina.
16/22

Ramboll-Potassium Aquatic Life Values
4. REPORT REFERENCES
ASTM. 2005. E1241 - 05 Standard Guide for Conducting Early Life-Stage Toxicity Tests with
Fishes. American Society for Testing and Materials. Philadelphia, PA.
ASTM. 2005. E1706 - 05. Standard Test Methods for Measuring the Toxicity of Sediment-
Associated Contaminants with Fresh Water Invertebrates. West Conshohocken, PA.
ASTM. 2006. E2455-06 Standard Guide for Conducting Laboratory Toxicity Tests with Freshwater
Mussels. American Society for Testing and Materials. Philadelphia, PA.
ASTM. 2006. E1295 - 01(2006) Standard Guide for Conducting Three-Brood, Renewal Toxicity
Tests with Ceriodaphnia dubia. American Society for Testing and Materials. Philadelphia, PA.
ASTM. 2007. E729-96 (2007) Standard Guide for Conducting Acute Toxicity Tests on Test
Materials with Fishes, Macroinvertebrates, and Amphibians. American Society for Testing and
Materials. Philadelphia, PA.
CP Kelco US, Inc.-Okmulgee NPDES Discharge Permit, OK0044504 and Fact Sheet. 2016. ODEQ
permit OK0044504 and Fact Sheet effective July 1, 2016.
ENVIRON. 2011. Quality Assurance Project Plan for Site-Specific Potassium Criteria Development
Deep Fork River, near Okmulgee, Oklahoma. Prepared for CP Kelco September 2011.
ENVIRON, 2008. Quality Assurance Manual and Standard Operating Procedures. ENVIRON
International Corporation. 8th Revision. November 1, 2010. Brentwood, Tennessee.
Michigan Department of Environmental Quality (MDEQ). 1996. Great Lakes Water Quality
Guidance Chemicals of Initial Focus Database Evaluation. Prepared for USEPA Region V Office of
Water.
Mohammad, A. 2007. Comparative Sensitivities of the Tropical Cladoceran, Ceriodaphnia rigaudii
and the Temperate Species Daphnia magna to Seven Toxicants. Toxicol. & Envt. Chem.
89(2):347-352.
USEPA. 1985. Guidelines for Deriving Numerical National Water Quality Criteria for the Protection
of Aquatic Organisms, PB85-227049
USEPA. 2000. Methods for Measuring the Toxicity and Bioaccumulation of Sediment-associated
Contaminants with Freshwater Invertebrates. 2nd edition.
USEPA, 2002a. Methods for Measuring the Acute Toxicity of Effluents and Receiving Waters to
Freshwater and Marine Organisms. Fifth Ed. EPA-821-R-02-012. USEPA Office of Water.
Washington, DC.
USEPA, 2002b. Short-term Methods for Estimating the Chronic Toxicity of Effluents and
Receiving Waters to Freshwater Organisms. Fourth Ed. EPA-821-R-02-013. USEPA Office of
Water. Washington, DC.
USFWS. 2017. Estimating Protective Potassium Concentration for Freshwater Mussels. Draft -
March 17, 2017.
17/22

Rambo!!-Potassium Aquatic Life Values
5. POTASSIUM TOXICITY REFERENCES
Academy of Natural Sciences, The Sensitivity of Aquatic Life to Certain Chemicals Commonly
Found in Industrial Wastes, Final Rep.No.RG-3965(C2R1), U.S.Public Health Service Grant,
Acad.of Nat.Sci., Philadelphia, PA :89 p. 1960.
Anderson, B.G., The Apparent Thresholds of Toxicity to Daphnia magna for Chlorides of Various
Metals when Added to Lake Erie Water Trans.Am.Fish.Soc. 78:96-113, 1948.
Anderson, B.G., The Toxicity Thresholds of Various Substances Found in Industrial Wastes as
Determined by the Use of Daphnia magna Sewage Works J. 16(6):1156-1165, 1944.
Anderson, B.G.,T.F. Andrews, D.C. Chandler, and W.J. Jahoda, The Evaluation of Aquatic
Invertebrates as Assay Organisms for the Determination of the Toxicity of Industrial Wastes
Am.Pet.Inst.Proj.Final Rep.No.51,The Ohio State University, Columbus, OH, 1948.
Anderson, K.B., Musculium transversum in the Illinois River and an Acute Potassium Bioassay
Method for the Species, M.S.Thesis, Western Illinois University, Macomb, IL :79 p.(U.S.NTIS PB-
288 088), 1977.
Anderson, K.B., R.E. Sparks, and A.A. Paparo, Rapid Assessment of Water Quality, Using the
Fingernail Clam, Musculium transversum, WRC Res.Rep.No.133, Project No.B-097-ILL, Univ.of
Illinois, Urbana, IL :115 p., 1978.
Becker, A.J.J.Jr., The Effects of Iron and Sulfate Compounds on the Growth of Chlorella, Proc. W.
Va. Acad. Sci. 45(2):127-135, 1973.
Belding, D.L.,Toxicity Experiments with Fish in Reference to Trade Waste Pollution. I. The Problem
of Water Pollution, Trans.Am.Fish.Soc. 57:100-119, 1927.
Bernot, R.J., M.A. Brueseke, M.A. Evans-White, and G.A. Lamberti, Acute and Chronic Toxicity of
Imidazolium-Based Ionic Liquids on Daphnia Magna, Environ.Toxicol.Chem. 24(1):87-92, 2005.
Biesinger, K.E., and G.M. Christensen, Effects of Various Metals on Survival, Growth, Reproduction
and Metabolism of Daphnia magna, J.Fish Res.Board Can. 29(12):1691-1700, 1972.
Boutet, C., and C. Chaisemartin, Specific Toxic Properties of Metallic Salts in Austro-potamobius
pallipes pallipes and Orconectes limosus (Proprietes Toxiques Specifiques des sels Metalliques chez
Austropotamobius pallipes pallipes et Orconectes limosu, C.R.Soc.Biol.(Paris) 167(12):1933-1938
(FRE) (ENG TRANSL), 1973.
Brown, D.J.A. The Effects of Various Cations on the Survival of Brown Trout, Salmo trutta at Low
pHs, J.Fish Biol. 18(1):31-40, 1981.
Burton, G.A.J., T.J. Norberg-King, C.G. Ingersoll, D.A. Benoit, G.T. Ankley, P.V. Winger, and J.
Kubitz, Interlaboratory Study of Precision: Hyalella azteca and Chironomus tentans Freshwater
Sediment Toxicity Assays, Environ.Toxicol.Chem. 15(8):1335-1343 (Author Communication Used),
1996.
Calleja, M.C., G. Persoone, and P. Geladi, Comparative Acute Toxicity of the First 50 Multicentre
Evaluation of In Vitro Cytotoxicity Chemicals to Aquatic Non-Vertebrates
Arch.Environ.Contam.Toxicol. 26(1):69-78, 1994.
18/22

Rambo!!-Potassium Aquatic Life Values
Conrad, A.U., R.J. Fleming, and M. Crane, Laboratory and Field Response of Chironomus riparius to
a Pyrethroid Insecticide, Water Res. 33(7):1603-1610, 1999.
Cressman III, C.P., and P.L. Williams, Reference Toxicants for Toxicity Testing Using Caenorhabdltls
elegans in Aquatic Media, In: F.J.Dwyer,T.R.Doane, and M.L.Hinman (Eds.), Environmental
Toxicology and Risk Assessment: Modeling and Risk Assessment, 6th Volume, ASTM STP 1317,
Philadelphia, PA :518-532, 1997.
Cresswell, R.C., and P.]. Syrett, Uptake of Nitrate by the Diatom Phaeodactylum tricornutum,
J.Exp.Bot. 32(126):19-25, 1981.
De Jong, L.E.D., Tolerance of Chlorella vulgaris for Metallic and Non-Metallic Ions, Antonie
Leeuwenhoek 31:301-313, 1965.
De March, B.G.E., Acute Toxicity of Binary Mixtures of Five Cations (Cu2+, Cd2+, Zn2+, Mg2+, and
K+) to the Freshwater Amphipod Gammarus lacustris (Sars): Alternative Descriptive Models,
Can.J.Fish.Aquat.Sci. 45(4):625-633, 1988.
Demael, A., D. Garin, and G. Peres, Response of the Tench (Tinca tinca L.) to Potassium Nitrate
Enriched Water, J.Fish Biol. 16(1):15-22, 1980.
Dowden, B.F. Cumulative Toxicities of Some Inorganic Salts to Daphnia magna as Determined by
Median Tolerance Limits, Proc.La.Acad.Sci. 23:77-85,a 1961.
Dowden, B.F., and H.J. Bennett, Toxicity of Selected Chemicals to Certain Animals, ].Water
Pollut.Control Fed. 37(9):1308-1316, 1965.
Durand-Hoffman, M.E., Analysis of Physiological and Toxicological Effects of Potassium on
Dreissena polymorpha and Toxicological Effects on Fish, M.S.Thesis, Ohio State University,
Columbus, OH :90 p. 1995.
Eales, J.G., D.G. Cyr, and R.F. Cook, Effect of Excess Iodide on Thyroid Function of Rainbow Trout,
Salmo gairdneri, Fish Physiol.Biochem. 1(4):171-177, 1986.
Fisher, S.W., P. Stromberg, K.A. Bruner, and L.D. Boulet Molluscicidal Activity of Potassium to the
Zebra Mussel, Dreissena polymorphia: Toxicity and Mode of Action, Aquat.Toxicol. 20:219-234,
1991.
Foster, R.W., A.H. Weston, and K.M. Weston, Some Effects of Chemical Irritants on the Membrane
of the Giant Amoeba, Br.J.Pharmacol. 74(2):333-339, 1981.
Freitas,E.C., and O. Rocha. 2011. Acute Toxicity Tests with the Tropical Cladoceran Pseudosida
ramose: The Importance of Using Native Species as Test. Arch Environ Contam Toxicol 60:241-
249.
Hamilton, R.W., J.K. Buttner, and R.G. Brunetti, Lethal Levels of Sodium Chloride and Potassium
Chloride for an Oligochaete, a Chironomid Midge, and a Caddisfly of Lake Michigan,
Environ.Entomol. 4(6):1003-1006, 1975.
Imlay, M. 1973. Effects of Potassium on Survival and Distribution of Freshwater Mussels.
Malacologia 12(1): 97-113.
Ishio, S., Behavior of Fish Exposed to Toxic Substances, In: O.Jaag (Ed.), Advances in Water
Pollution Research, Pergamon Press, NY :19-40, 1965.
19/22

Ramboll-Potassium Aquatic Life Values
Jones, J.R.E., A Further Study of the Relation Between Toxicity and Solution Pressure, with Polycelis
nigra as Test Animal, J.Exp.Biol. 17:408-415, 1940.
Jones, J.R.E. The Relation Between the Electrolytic Solution Pressures of the Metals and Their
Toxicity to the Stickleback (Gasterosteus aculeatus L.), J.Exp.Biol. 16(4):425-437, 1939.
Kanta, S., and T.A. Sarma, Biochemical Studies on Sporulation in Blue-Green Algae II. Factors
Affecting Glycogen Accumulation, Z.Allg.Mikrobiol. 20(7):459-463, 1980.
Keller, A.E., Personal Communication to U.S. EPA:Water Quality and Toxicity Data for Unpublished
Unionid Mussel Tests, Memo to R.Pepin and C.Roberts,U.S.EPA Region 5,Chicago, IL :14 p. (Author
Communication Used), 2000.
Khangarot, B.S., Toxicity of Metals to a Freshwater Tubificid Worm, Tubifex tubifex (Muller),
Bull.Environ.Contam.Toxicol. 46:906-912, 1991.
Khangarot, B.S., and P.K. Ray, Investigation of Correlation Between Physicochemical Properties of
Metals and Their Toxicity to the Water Flea Daphnia magna Straus, Ecotoxicol.Environ.Saf.
18(2):109-120, 1989.
Lazorchak, J.M., and M.E. Smith, Rainbow Trout (Oncorhynchus mykiss ) and Brook Trout
(Salvelinus fontinalis ) 7-Day Survival and Growth Test Method, Arch.Environ.Contam.Toxicol.
53(3):397-405, 2007.
Lilius, H., B. Isomaa, and T. Hastbacka, A Comparison of the Toxicity of 30 Reference Chemicals to
Daphnia magna and Daphnia Pulex, Env. Tox. Chem. 14(12):2085-2088, 1995.
Lilius, H., B. Isomaa, and T. Holmstrom, A Comparison of the Toxicity of 50 Reference Chemicals to
Freshly Isolated Rainbow Trout Hepatocytes and Daphnia magna, Aquat.Toxicol. 30:47-60, 1994.
Litav, M., and Y. Lehrer, The Effects of Ammonium in Water on Potamogeton lucens Aquat.Bot.
5(2):127-138, 1978.
Mahajan, C.L., S.D. Sharma, and S.P. Sharma, Tolerance of Aquatic Organisms to Chloride Salts,
Indian J.Exp.Biol. 17(11):1244-1245, 1979.
Matisoff, G., A. Greenberg, G. Gubanich, and J. Ciaccia, Effects of Potassium, Cloramine, and
Chlorine Dioxide on Control of Adult Zebra Mussels, J.Shellfish Res. 11(1):232-233 (ABS), 1991.
McNulty, E.W., F.J. Dwyer, M.R. Ellersieck, E.I. Greer, C.G. Ingersoll, and C.F. Rabeni. Evaluation
of Ability of Reference Toxicity Tests to Identify Stress in Laboratory Populations of the Amphipod
Hyalella azteca, Environ.Toxicol.Chem. 18(3):544-548, 1999.
Mohammed, A., Comparative Sensitivities of the Tropical Cladoceran, Ceriodaphnia rigaudii and the
Temperate Species Daphnia magna to Seven Toxicants, Toxicol.Environ.Chem. 89(2):347-352,
2007.
Mosslacher, F.Sensitivity of Groundwater and Surface Water Crustaceans to Chemical Pollutants
and Hypoxia: Implications for Pollution Management, Arch.Hydrobiol. 149(1):51-66, 2000.
Mount, D.R., D.D. Gulley, J.R. Hockett, T.D. Garrison, and J.M. Evans, Statistical Models to Predict
the Toxicity of Major Ions to Ceriodaphnia dubia, Daphnia magna and Pimephales promelas
(Fathead Minnows), Environ.Toxicol.Chem. 16(10):2009-2019, 1997.
Mukai, H., Effects of Chemical Pretreatment on the Germination of Statoblasts of the Freshwater
Bryozoan, Pectinatella gelatinosa, Biol.Zentralbl. 96:19-31, 1977.
20/22

Ramboll-Potassium Aquatic life Values
Patrick, R., J. Cairns Jr., and A. Scheier, The Relative Sensitivity of Diatoms, Snails, and Fish to
Twenty Common Constituents of Industrial Wastes, Prog.Fish-Cult. 30(3):137-140 (Author
Communication Used) (Publ in Part As 2406), 1968.
Pickering, Q.H.,J.M. Lazorchak, and K.L. Winks, Subchronic Sensitivity of One-, Four-, and Seven-
Day-Old Fathead Minnow (Pimephales promelas) Larvae to Five Toxicants, Environ.Toxicol.Chem.
15(3):353-359, 1996.
Przytocka-Jusiak, M., Growth and Survival of Chlorella vulgaris in high Concentrations of Nitrogen,
Acta Microbiol.Pol. 25(3):287-289, 1976.
Purcell III, T.W., The Effects of Atrazinc and Nitrate, Alone and in Combination, on a Natural
Phytoplankton Population of the Potomac River, Ph.D.Thesis, Univ.of Maryland, College Park,
MD:133 p.(1988) / Diss.Abstr.Int.B Sci.Eng. 49(8):3080, 1989.
Rao, V.N.R., and G. Ragothaman, Studies on Amphora coffeaeformis II. Inorganic and Organic
Nitrogen and Phosphorus Sources for Growth, Acta Bot.Indica 6(Suppl.1):146-154, 1978.
Rubin, A.J., and G.A. Elmaraghy, Studies on the Toxicity of Ammonia, Nitrate and Their Mixtures to
Guppy Fry, Water Res. 11(10):927-935, 1977.
Sestokas, J., and J. Cukerzis Effect of Chemical Preparations on the Crayfish Astacus astacus and
Astacus leptodactylus, Liet.Tsr Mokslu Akad.Darb., Ser.C(4):119-124 (RUS) (ENG ABS), 1972.
Smith, M.E., J.M. Lazorchak, L.E. Herrin, S. Brewer-Swartz, and W.T. Thoeny, A Reformulated,
Reconstituted Water for Testing the Freshwater Amphipod, Hyalella azteca, Environ.Toxicol.Chem.
16(6):1229-1233, 1997.
Snyder, F.L., S.W. Fisher, and B. Schneider Evaluation of Potassium Chloride for Removal of Zebra
Mussel Veligers from Commercial Fish Shipments, J.Shellfish Res. 11(1):238-239 (ABS), 1992.
Sparks, R.E., and K.B. Anderson, Acute Toxicity of Potassium to the Fingernail Clam, Musculum
transversum,Trans.Ill.State Acad.Sci. 69(2):229, 1977.
Tatara, C.P., M.C. Newman, J.T. McCloskey, and P.L. Williams, Use of Ion Characteristics to Predict
Relative Toxicity of Mono-, Di- and Trivalent Metal Ions: Caenorhabditis elegans, Aquat.Toxicol.
42:255-269, 1998.
Trama, F.B., The Acute Toxicity of Some Common Salts of Sodium, Potassium and Calcium to the
Common Bluegill, Proc.Acad.Nat.Sci.Philadelphia 106:185-205, 1954.
Turoboyski, L.Attempt to Determine the Influence of high Doses of some Chemical Compounds
upon Carp Fry (Proba Okreslenia Wplywu Wysokich Dawek Niektorych Zwiazkow Chemicznych na
Narybek Karpia), Rocz.Nauk Roln. 75B(3):401-445 (POL) (ENG ABS), 1960.
Wallen, I.E., W.C. Greer, and R. Lasater Toxicity to Gambusia affinis of Certain Pure Chemicals
in Turbid Waters Sewage Ind.Wastes 29(6):695-711, 1957.
Waller, D.L., J.J. Rach, W.G. Cope, L.L. Marking, S.W. Fisher, and H. Dabrowska, Toxicity of
Candidate Molluscicides to Zebra Mussels (Dreissena polymorpha) and Selected Nontarget
Organisms, J.Gt.Lakes Res. 19(4):695-702, 1993.
Wang, N., J. Kuynz, R. Dorman, C. Ingersoll, J. Steevens, E. Hammer, C. Bauer, Evaluating Chronic
Toxicity of Sodium Chloride or Potassium Chloride to Unionid Mussel (Lampsilis siliquoidea) in Water
21/22

Rambo ll-Potassium Aquatic Life Values
Exposures Using Standard and Refined Toxicity Test Methods. (Submitted for publication,
Environmental Toxicology &Chemistry, August 2018).
Wildridge, P.J., R.G. Werner, F.G. Doherty, and E.F. Neuhauser, Acute Toxicity of Potassium to the
adult zebra Mussel Dreissena polymorpha, Arch. Environ. Contam. Toxicol. 34, 265-270, 1998.
Wildridge, P.J., R.G. Werner, F.G. Doherty, and E.F. Neuhauser, Acute Effects of Potassium on
Filtration Rates of Adult Zebra Mussels, Dreissena polymorpha, J.Gt.Lakes Res. 24(3):629-636,
1998.
Yarzhombek, A.A., A.E. Mikulin, and A.N. Zhdanova, Toxicity of Substances in Relation to Form of
Exposure, J.Ichthyol /Vopr.Ikhtiol.31(3):496-501(RUS) 31(7):99-106, 1991.
22/22

Cn
W
J
m
H

Rambo!!-Potassium Aquatic Life Values
TABLES

Ramboll-Potassium Aquatic Life Values
Table 1. Acute Potassium ToxicityTest Results for Lampsilis siliquoidea and Lampsilis radiata
(8/16/17)
Measured
Hardness Measured 95%
Test Species (mg/L as 96 hr LC50 Conf. Int.
CaCO3) (mg/L) (mg/L)
Lampsilis radiata (Eastern Lampmussel) 25 37.2 29.3 - 36.5
Lampsilis radiata (Eastern Lampmussel) 75 60.8 56.7 - 65.2
Lampsilis siloquoides(Fatmucket) 25 22.4 19.8 - 25.3
Lam.silis silo•uoides Fatmucket 75 28.1 24.9 - 31.8
Table 2. Supporting Analytical Results for Dilution Waters for Acute Potassium Toxicity Tests
Lampsilis siliquoidea and Lampsilis radiata (8/16/17)
Nominal 25 mg/L Nominal 75 mg/L
Hardness Hardness
Parameter Water Water Units
Hardness 24.8 75.2 mg/L CaCO3
Alkalinity 22.3 39.0 mg/L
TRC < 0.02 < 0.02 mg/L
Calcium 6.28 20.1 mg/L
Magnesium 1.61 4.80 mg/L
Potassium < 1.0 1.72 mg/L
Sodium 6.09 4.61 mg/L
Chloride 2.64 6.93 mg/L
Sulfate 12.7 40.7 mg/L

•
Ramboll-Potassium Aquatic Life Values
Table 3. Chronic Potassium Toxicity Database
Measured 95%
Test Hardness Alkalinity Test Result- Conf.
Genus species Start Test as CaCO3 Endpoint Duration Endpoint K Int. Reference
Date Round (mg/L) (mg/L) Measured (mg/L) (mg/L)
Survival MATC 296
Ceriodaphnia dubia 28-Feb-12 1 220 190 Reproduction 7 days MATC 207 ENVIRON 2012
unpublished
Reproduction IC25 187 177-193 ,
Survival MATC 263
Ceriodaphnia dubia 20-Mar-12 2 208 100 Reproduction 7 days MATC 145 ENVIRON 2012 unpublished
Reproduction IC25 144 128-148
Survival MATC 302
Pimepha/es promelas 12-Jan-12 1 113 80 Growth 32 days MATC 302 ENVIRON 2012 unpublished
Growth IC25 232 16 - 265
Survival MATC 139
Pimepha/es promelas 20-Apr-12 2 226 179 Growth 32 days MATC 139 ENVIRON 2012 unpublished
Growth IC25131 131 87 - 152
Survival MATC 32
Lam silis siloquoidea 2013 without Notgiven 28 days Wanget al, 2018
p Q sand 100 Biomass Y MATC 32
Biomass EC20 23 21 -26
Notes:
1. Hardness and Alkalinity are average measured values during test.
2. MATC = geomean of NOEC and LOEC (aka ChV)
3. K results as average measured K. Test did not meet acceptability criteria and is not used in criteria calculations.

Rambo ll-Potassium Aquatic Life Values
Table 4. Acute to Chronic Ratio Calculation
Acute Chronic ACR
Genus species SMAV SMCV Data Reference
m• L m. L
Ceriodaphnia dubia 365 164 2.22 ENVIRON 2012 unpublished
Pimepha/es porme/as 453 232 1.95 ENVIRON 2012 unpublished
Lampsilis siloquoidea 44 32 1.38 Wan. et al 2018
FACR = 1.81

Rambo!!-Potassium Aquatic Life Values
Table 5. Calculation of In-Stream Site-Specific Acute and River Segment-Specific
Chronic Potassium Aquatic Life Values
A..licable to the .ro.osed Novoz mes North Carolina receivin. streams
CUM SQR LN
GENUS SPECIES RANK PROS ROOT GMAV GMAV (LNGMAV)2
(R) (P) (P) (mg/L) (mg/L) (mg/L)
Chironomus tentans 16 0.9412 0.9701 2,769 7.746 60.005
Hydroptila angusta 15 0.8824 0.9393 2,313 7.356 54.105
Cricotopus trifasciatus 14 0.8235 0.9075 1,565 7.167 51.366
Lepomis macrochirus 13 0.7647 0.8745 1,296 6.250 39.062
Pimephales promelas 12 0.7059 0.8402 518 6.201 38.446
PhY sella acuta 11 0.6471 0.8044 493 6.080 36.966
Cyprinus carpio 10 0.5882 0.7670 437 5.911 34.938
Ceriodaphnia dubia 9 0.5294 0.7276 369 5.429 29.478
Musculium transversum 8 0.4706 0.6860 228 5.389 29.042
Daphnia magna 7 0.4118 0.6417 219 5.147 26.497
Hya/ella azteca 6 0.3529 0.5941 172 4.043 16.346
Lampsilis siloquoidea 5 0.2941 0.5423 57 4.043 16.346
Lampsilis radiata 4 0.2353 0.4851 48 3.871 14.986
Megalonaissas nervosa 3 0.1765 0.4201 47 3.850 14.824
Utterbackia imbecillis 2 0.1176 0.3430 45 3.807 14.491
Lasmigona complanata 1 0.0588 0.2425 34 3.526 12.435
Sum of 4 lowest Ps 0.5882
Sum of the 4 lowest square roots of Ps 1.4907
Square of the sum of the square roots of Ps 2.222
Sum of the four lowest natural logs of the GMAVs 15.05
Sum of the squared natural logs of the GMAVs 56.74
FAV CALCULATION IS AS FOLLOWS:
52 = 0.077
0.03
S2 = 2.36
S = 1.5366
L = 3.1909
A = 3.5345
FAV = 34.28
Acute Concentration = 17.14
NOTES:
1. 1.Used only KCI,KSO4 data
2. Cyprinus carpio substituted for Salmonid data requirement.
3. Lampsilis radiata is shown as a separate mussel/data entry, because it is a representative indigenous
species and responds differently to potassium than L.siliquoidea(Attachment 3).

1 1
1

Rambo!!-Potassium Aquatic Life Values
APPENDIX 1
ACCEPTABLE AQUATIC ACUTE TOXICITY DATABASE FOR POTASSIUM
SITE-SPECIFIC AQUATIC LIFE VALUE DERIVATION
it
I

•
Attachment 1. Acceptable Aquatic Acute Toxicity Database for Potassium Site-Specific Aquatic Life Value Derivation
Ceriodap nia rigau.i and Salmonidae excluded as they .o not reside at the site.
Chemical Hardness as CaCO3 Alkalinity LC50 as K SMAV GMAV
Genus species Common Name Species Group Endpoint Reference
Name (mg/L) (mg/L) Conc(mg/L)
(mg/L) (mg/L)
K2SO4 *Ceriodaphnia dubia Water flea *Crustaceans 48 hr LC50 84 I MHRW 305 Mount,D.R.et al. 1997
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 84 MHRW 330 Mount,D.R.et al. 1997
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 113 68 415 ENVIRON 2012 unpublished •
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 104 66 289 ENVIRON 2012 unpublished •
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 112 102 244 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 110 83 416 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 99.2 68 319 ENVIRON 2012 unpublished •
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 108 58 288 ENVIRON 2012 unpublished •
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 184 80 435 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 220 190 390 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 208 100 287 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 196 88 420 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 220 105 363 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 212 85 334 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 320 148 367 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 340 150 334 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 340 160 437 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 332 132 400 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 328 124 316 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 312 135 458 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 440 198 374 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 456 125 514 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 426 190 377 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 440 150 459 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 444 190 395 ENVIRON 2012 unpublished
KCI Ceriodaphnia dubia Water flea Crustaceans 48 hr LC50 480 210 484 369 369 ENVIRON 2012 unpublished
KCI Daphnia magna Water flea Crustaceans 48 hr LC50 90-100 40-50 219 Mohammed,A.2007
KCI Daphnia magna Water flea Crustaceans 48 hr LC50 84 MHRW 346 Mount,D.R.et al. 1997
KCI Daphnia magna Water flea Crustaceans 48 hr EC50 45.3 42.3 93 Biesinger,K.E.,et al. 1972
K2SO4 Daphnia magna Water flea Crustaceans 48 hr LC50 84 MHRW 323 219 219 Mount,D.R.et al. 1997
KCI Cricotopus trifasciatus Midge Insects 48 hr LC50 unknown unknown 1,565 1,565 1,565 Hamilton,R.W.et al. 1975
KCI Chironomus tentans Midge Insects 48 hr LC50 100 72 2,389 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 104 75 2,943 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 108 90 2,787 ENVIRON 2012 unpublished
• Page 1 of 5

Attachment 1. Acceptable Aquatic Acute Toxicity Database for Potassium Site-Specific Aquatic Life Value Derivation
Ceriodaphnia rigaudi and Salmonidae excluded as they do not reside at the site.
Chemical Hardness as CaCO3 Alkalinity LC50 as K SMAV GMAV
Name Genus species Common Name Species Group Endpoint Reference
(mg/L) (mq/L) Conc(mq/L)
(m9/L) (m4/L)
KCI Chironomus tentans Midge Insects 48 hr LC50 206 142 2,883 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 216 155 3,098 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 194 151 2,869 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 292 185 2,749 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 280 110 2,362 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 304 240 1,993 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 404 205 2,997 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 392 200 3,443 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 398 200 3,119 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 98.4 74 2,647 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 104 70 2,567 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 100 100 3,052 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 206 124 2,520 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 200 100 3,298 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 195 120 2,928 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 300 145 3,049 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 312 110 2,587 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 304 240 2,399 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 369 140 3,076 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 392 115 2,900 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 48 hr LC50 392 110 3,329 ENVIRON 2012 unpublished
KCI Chironomus tentans Midge Insects 96 hr LC50 120-130 MHRW 655 Burton et al.1996
KCI Chironomus tentans Midge Insects 97 hr LC50 ' 120-131 MHRW 1,048 Burton et al.1996
KCI Chironomus tentans Midge Insects 96 hr LC50 ' 120-130 MHRW 1,514 Burton et al.1996
KCI Chironomus tentans Midge Insects 96 hr LC50 ' 120-130 MHRW 1,661 Burton et al.1996
KCI Chironomus tentans Midge Insects 96 hr LC50 120-130 MHRW 1,892 Burton et al.1996
KCI Chironomus tentans Midge Insects 96 hr LC50 ' 120-130 MHRW 2,620 Burton et al.1996
KCI Chironomus tentans Midge Insects 96 hr LC50 120-130 MHRW 2,678 Burton et al.1996
KCI Chironomus tentans Midge Insects 96 hr LC50 120-130 MHRW 2,777 Burton et al.1996
KCI Chironomus tentans Midge Insects 96 hr LC50 . 120-130 MHRW 2,809 Burton et al.1996
KCI Chironomus tentans Midge Insects 96 hr LC50 ' 120-130 MHRW 3,249 Burton et al. 1996
KCI Chironomus tentans Midge Insects 96 hr LC50 120-130 MHRW 3,291 Burton et al. 1996
KCI Chironomus tentans Midge Insects 96 hr LC50 120-130 MHRW 3,458 Burton et al, 1996
KCI Chironomus tentans Midge Insects 96 hr LC50 ' 120-130 MHRW 3,485 Burton et al. 1996
KCI Chironomus tentans Midge Insects 96 hr LC50 : 120-130 MHRW 3,579 2,587 2,587 Burton et al. 1996
KCI Hydroptila angusta Caddisfly Insects 48 hr LC50 unknown unknown 2,313 2,313 2,313 Hamilton,R.W.et al.1975
KCI Cyprinus carpio Common Carp Fish 96 hr LC50 210 102 434 ENVIRON 2012 unpublished
KCI Cyprinus carpio Common Carp Fish 96 hr LC50 214 110 426 ENVIRON 2012 unpublished
Page 2 of S

Attachment 1. Acceptable Aquatic Acute Toxicity Database for Potassium Site-Specific Aquatic Life Value Derivation
Ceriodaphnia rigaudi and Salmonidae exc u.e. as they do not reside at the site.
Chemical Hardness as CaCO3 Alkalinity LC50 as K SMAV GMAV
Name Genus species Common Name Species Group Endpoint Reference
(mp/L) (mg/L) Conc(mp/L)
(mg/L) (mg/L)
KCI Cyprinus carpio Common Carp Fish 96 hr LC50 209 110 451 437 437 ENVIRON 2012 unpublished
KCI Hyalella azteca Scud Crustaceans 96 hr LC50 208 142 230 ENVIRON 2012 unpublished
KCI Hyalella azteca Scud Crustaceans 96 hr LC50 214 155 242 ENVIRON 2012 unpublished
KCI Hyalella azteca Scud Crustaceans 96 hr LC50 120-130 MHRW 122 Burton et al.1996
KCI Hyalella azteca Scud Crustaceans 96 hr LC50 120-130 MHRW 131 Burton et al,1996
KCI Hyalella azteca Scud Crustaceans 96 hr LC50 120-130 MHRW 144 Burton et al.1996
KCI Hyalella azteca Scud Crustaceans 96 hr LC50 120-130 MHRW 168 Burton et al.1996
KCI Hyalella azteca Scud Crustaceans 96 hr LC50 120-130 MHRW 170 Burton et al.1996
KCI Hyalella azteca Scud Crustaceans 96 hr LC50 120-130 MHRW 176 Burton et al.1996
KCI Hyalella azteca Scud Crustaceans 96 hr LC50 120-130 MHRW 177 Burton et al.1996
KCI Hyalella azteca Scud Crustaceans 96 hr LC50 120-130 MHRW 195 172 172 Burton et al.1996
K2SO4 Pimephales promelas Fathead minnow Fish 96 hr LC50 84 MHRW 305 Mount,D.R.et al. 1997
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 84 MHRW 461 Mount,D.R.et al.1997
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 113 67.9 451 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 104 66 505 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 112 102 409 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 110 83 531 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 99.2 68 502 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 108 58 422 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 184 80 617 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 220 190 542 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 208 100 428 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 220 105 542 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 212 85 469 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 320 148 602 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 340 150 605 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 340 160 530 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 332 132 634 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 328 124 620 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 312 135 514 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 426 190 523 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 440 150 636 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 444 190 504 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 440 198 544 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 456 125 619 ENVIRON 2012 unpublished
KCI Pimephales promelas Fathead minnow Fish 96 hr LC50 ' 480 210 603 518 518 ENVIRON 2012 unpublished
Trama,F.B. 1954/Patrick,R.
KCI Lepomis macrochirus Bluegill Fish 96 hr LC50 39.8 43,4 1,053 et al.1968
Page 3 of 5

Attachment 1. Acceptable Aquatic Acute Toxicity Database for Potassium Site-Specific Aquatic Life Value Derivation
Cerio•aphnia rigaudi and Salmonidae exclu.ed as they do not reside at the site.
Chemical Hardness as CaCO3 Alkalinity LC50 as K SMAV GMAV
Name Genus species Common Name Species Group Endpoint Reference
(mg/L) (mg/L) Conc(mg/L)
(mg/L) (mg/L)
K2504 Lepomis macrochirus Bluegill Fish 96 hr LC50 44.5 53.6 1,594 1,296 1,296 Trama,F.B.1954
Eastern
KCI Lampsilis radiata Lampmussel mussel 96 hr LC50 24.8 22.3 37 Ramboll 2017 unpublished
Eastern
KCI Lampsilis radiata Lampmussel mussel 96 hr LC50 75.2 39 61 Ramboll 2017 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 24.8 22.3 22 Ramboll 2017 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 75.2 39 28 Ramboll 2017 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 100 not reported 46 Wang/Ivey et al 2013
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 100 77 33 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 104 72 43 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 100 80 49 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 100 76 38 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 100 79 47 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 100 75 54 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 212 146 63 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 212 147 50 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 208 146 53 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 206 110 62 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 200 118 60 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 204 130 56 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 300 215 55 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 308 200 68 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 304 210 79 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 300 140 79 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 296 296 80 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 296 150 92 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 392 110 107 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 408 150 95 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 404 300 78 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 400 275 72 ENVIRON 2012 unpublished
KCI Lampsilis siloquoidea Fatmucket mussel 96 hr LC50 392 150 84 57 57 ENVIRON 2012 unpublished
KCI Lasmigona complanata White Heelsplitter mussel 96 hr LC50 100 not reported 34 34 34 Wang/Ivey et al 2013
KCI Megalonaisas nervosa Washboard mussel 96 hr LC50 100 not reported 47 47 47 Wang/Ivey et al 2013
KCI Utterbackia imbecillis Paper Pondshell mussel 96 hr LC50 100 not reported 45 45 45 Wang/Ivey et al 2013
Long fingernail Anderson,K.B.,et al.1978(see
KCI Musculium transversum clam Molluscs 96 hr LC50 243 155 280 Note 2)
Page 4 of 5

Attachment 1. Acceptable Aquatic Acute Toxicity Database for Potassium Site-Specific Aquatic Life Value Derivation
Ceriodaphnia rigaudi and Salmonidae excluded as they do not reside at the site.
Chemical Hardness as CaCO3 Alkalinity LC50 as K SMAV GMAV
Name Genus species Common Name Species Group Endpoint Reference
(mg/L) (mg/L) Conc(mg/L)
(mg/L) (mg/L)
Long fingernail Anderson,K.B.,et al.1978(see
KCI Musculium transversum clam Molluscs 96 hr LC50 263 161 185 228 228 Note 2)
KCI Physella acuta European physa Molluscs 96 hr LC50 43 24 493 493 493 Patrick,R.et al. 1968
Notes:
1.MHRW=moderately hard reconstituted water. No hardness and/or alkalinity value given in paper.
2. USEPA 1985 Guidelines suggest using toxicity data generated from the most sensitive life stage for an organism. Anderson 1978 determined
that the adult life stage of the fingernail clam was more sensitive than juvenile. Therefore,test results for the adult life stage are presented here.
3.If endpoint value was given in paper as K,endpoint value as whole salt tested was then calculated(examples:Anderson 1978,Biesinger 1972)
Highlighted cells represent native species.
Page 5 of 5

Ramboll-Potassium Aquatic Life Values
APPENDIX 2
FRESHWATER POTASSIUM AQUATIC TOXICITY DATABASE LITERATURE
SEARCH RESULTS

ATTACHMENT 2. FRESHWATER POTASSIUM AQUATIC TOXICITY DATABASE LITERATURE SEARCH RESULTS
Chemical Value as Conc Test Verified Value Value as K Rejection Justification and Notes
Salt
Species Scientific Name Common Name Name Endpoint Conc Units Duration from paper as Conc Citation
salt
Navicula seminulum Diatom KCI EC50 1337000 ug/L 120 hr 1337000 Academy of Natural Sciences 1960 same study as Patrick 1968
Lepomis macrochirus Bluegill KCI LC50 2010000 ug/L 96 hr 2010000 Academy of Natural Sciences 1960 same study as Patrick 1968
Physastra gibbosa Snail KCI LC50 940000 ug/L 96 hr 940000 Academy of Natural Sciences 1960 same study as Patrick 1968
Daphnia magna Water flea KCI EC50 204000* ug/L 64 hr 432000 Anderson,B.G. 1948 test duraton not standard
Daphnia magna Water flea KCI TLm 176000* ug/L 32 hr 373000 _ Anderson,B.G. 1944 not standard endpt,inappropriate culture
Cyclops vernalis Cyclopoid KCI MATC 640000 ug/L 96 hr 640000 Anderson,B.G.,et al. 1948 not standard endpoint statistic for acute
Daphnia magna Water flea KCI MATC 430000 ug/L 96 hr 430000 Anderson,B.G.,et al. 1948 not standard endpoint statistic for acute
Leptodora kindtii Water flea KCI MATC 127000 ug/L 96 hr 127000 Anderson,B.G.,et al. 1948 not standard endpoint statistic for acute
Mesocyclops leuckarti Cyclopoid copepod KCI MATC 566000 ug/L 96 hr 566000 Anderson,B.G.,et al. 1948 not standard endpoint statistic for acute
Skistodiaptomus oregonensis Calanoid copepod KCI MATC 134000 ug/L 96 hr 134000 Anderson,B.G.,et al. 1948 not standard endpoint statistic for acute
Musculium transversum Long fingernail clam KCI LC50 see note Anderson,K.B. 1977 data from this study is presented in Anderson 1978 Report
Musculium transversum Lo;-,f r uernad clan KCI cm 185000 sq.I 96 hr 185000 Anderson, K et al 1978 For acute tests,both adults and juveniles were tested. Mortality assessed(LC50
Musculium transversum u-,r .ge...al'� clam KCI _ 280000 ug,d. 96 hr 280000 Anderson, K.E.. et at 1978 calculated)at noted intervals. Since the 96hr LC50 is standard endpoint,it was
Musculium transversum Long fingernail clam KCI LC50 1000000 ug/L 96 hr - 1000000 Anderson,K.B.,et al. 1978 deemed acceptable;other test duration endpoints not used. There is concern that
Musculium transversum Long fingernail clam KCI LC50 1825000 ug/L 96 hr 1825000 Anderson,K.B.,et al. 1978 since tests were conducted in well or laboratory reconstitued water with no food,it can
of
Musculium transversum Long fingernail clam KCI LC50 2500000 ug/L 96 hr - 2500000 Anderson,K.B. et al. 1978 note be ruled out studythaorganisms werer not stressed inlaterdstagesdern(after day. Cont10+rol l
tests. Some results also presented in Sparks and Anderson 1977. Control
Musculium transversum Long fingernail clam KCI LC50 520000 ug/L 96 hr - 520000 Anderson,K.B. et al. 1978 mortality excessive for results marked with"*".
Musculium transversum Long fingernail clam KCI LC50 200000 ug/L 10 days - 200000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 270000 ug/L 10 days - 270000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 320000 ug/L 10 days - 320000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 840000 ug/L 10 days - 840000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 850000 ug/L 10 days - 850000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 250000 ug/L 11 days - 250000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 250000 ug/L 12 days - 250000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 200000 ug/L 13 days - 200000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 250000 ug/L 13 days - 250000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 310000 ug/L 13 days - 310000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 540000 ug/L 13 days - 540000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 685000 ug/L 13 days - 685000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 300000 ug/L 16 days - 300000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 495000 ug/L 16 days - 495000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 560000 ug/L 16 days - 560000* Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 440000 ug/L 19 days - 440000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 480000 ug/L 19 days - 480000* Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 2700000 ug/L 48 hr - 2700000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 3150000 ug/L 48 hr - 3150000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 518000 ug/L 48 hr - 518000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 880000 ug/L 48 hr - 880000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 430000 ug/L 22 days - 430000* Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 400000 ug/L 23 days - 400000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 320000 ug/L 25 days - 320000* Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 388000 ug/L 27 days - 388000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 320000 ug/L 29 days - 320000* Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 1680000 ug/L 72 hr - 1680000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 1960000 ug/L 72 hr - 1960000 _Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 255000 ug/L 72 hr - 255000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 2700000 ug/L 72 hr - 2700000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 370000 ug/L 72 hr - 370000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 168000 ug/L 120 hr - 168000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 1800000 ug/L 120 hr - 1800000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 435000 ug/L 120 hr - 435000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 1070000 ug/L 144 hr - 1070000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 1180000 ug/L 144 hr - 1180000 Anderson,K.B. et al. 1978
Musculium transversum Long fingernail clam KCI LC50 228000 ug/L 144 hr - 228000 Anderson,K.B.,et al. 1978
Musculium transversum Long fingernail clam KCI LC50 510000 ug/L 144 hr - 510000 Anderson,K.B.,et al. 1978
Musculium transversum Long fingernail clam KCI LC50 300000 ug/L 168 hr - 300000 Anderson,K.B.,et al. 1978
Musculium transversum Long fingernail clam KCI LC50 980000 ug/L 168 hr - 980000 Anderson,K.B.,et al. 1978
Musculium transversum Long fingernail clam KCI LC50 1020000 ug/L 192 hr - 1020000 Anderson,K.B.,et al. 1978_
Musculium transversum Long fingernail clam KCI LC50 212000 ug/L 192 hr - 212000 Anderson,K.B.,et al. 1978
Musculium transversum Long fingernail clam KCI LC50 350000 ug/L 192 hr - 350000 Anderson,K.B.,et al. 1978
Musculium transversum Long fingernail clam KCI LC50 925000 ug/L 192 hr - 925000 Anderson,K.B.,et al. 1978
Musculium transversum Long fingernail clam KCI LOEC 275000 ug/L 42 day - 275000* Anderson,K.B.,et al. 1978 sign.Control mortality
Musculium transversum Long fingernail clam KCI NOEC 195000 ug/L 42 day - 195000* _Anderson,K.B.,et al. 1978 sign.Control mortality
Musculium transversum Long fingernail clam KCI NOEC 184000 ug/L 42 day - 184000* Anderson,K.B.,et al. 1978 sign.Control mortality
Chlorella vulgaris Green algae KSO4 NR 2012000 ug/L 30 day 2012000 Becker,A.J.J.Jr. 1973 effects seen at all concentrations,can not calculate EC50,test media not appropriate
Salvelinus fontinalis Brook trout K(OH) NR-LETH 50000 ug/L 24 hr 20000000 Belding,D.L. 1927 adult fish used,no std endpt given,just dose that caused lethality
Daphnia magna Water flea KCI LC50 405000 ug/L 48 hr 405000 Bernot,R.J.,et al.2005 study focus was testing other chemicals,KCI results are from a reftox done during the
study. No testing details given for reftox
Page 1 of 8

ATTACHMENT 2. FRESHWATER POTASSIUM AQUATIC TOXICITY DATABASE LITERATURE SEARCH RESULTS
Chemical Value as Conc Test Verified Value Value as K Rejection Justification and Notes
Salt
Species Scientific Name Common Name Name Endpoint Conc Units Duration from paper as Conc Citation
salt _
Daphnia magna Water flea KCI LC50 415000 ug/L 48 hr 415000 Bernot,R.J.,et al.2005 study focus was testing other chemicals,KCI results are from a reftox done during the
.audv. No testing details given for reftox
Daphnia magna Water flea KCI EC50* 149000* ug/L 48 hr ? ? Biesinger, K.E.,and G.M.Christensen 1972 ECOTOX value not verified in original reference
Daphnia magna Water flea KCI EC50* 166000 ug/L 48 hr - 166000 Biesinger, K.E.,and G.M.Christensen 1972 test was fed,paper notes that presence of food affected outcome of tests;test
organisms were more tolerant of toxicant when fed. Therefore,results from fed tests
.09Lused. _
Daphnia magna Water flea KCI EC50* 83000* ug/L 48 hr ? ? Biesinger, K.E.,and G.M.Christensen 1972 ECOTOX value not verified in original reference
—
Daphnia magna '!Vater flea KCI EC50' 93000 ug/L. 49 Or 93000 Biesinger, K.E., and G.M. Christensen 1972
Daphnia magna Water flea KCI EC50* 87000* ug/L 21 day ? ? Biesinger, K.E.,and G.M.Christensen 1972 ECOTOX value not verified in original reference
Daphnia magna Water flea KCI EC50* 97000 ug/L 21 day - 97000 Biesinger, K.E.,and G.M.Christensen 1972 3wk LC50 endpoint not standard endpoint for chronic
Daphnia magna Water flea KCI NR 61000* ug/L 21 day - 53000 Biesinger, K.E.,and G.M.Christensen 1972 16%repro impairment,concentrations not measured,not standard endpoint,
, inade_Quate information provided to calculate NOEC/LOEC
Daphnia magna Water flea KCI NR 68000 ug/L 21 day - 68000 Biesinger, K.E.,and G.M.Christensen 1972 50%repro impairment,concentrations not measured,not standard endpoint,
inadequate information provided to calculate NOEC/LOEC
Pseudosida ramosa Water flea KCI LC50 12070 ug/L 48 hr 12070 Freitas,E.C.,and 0. Rocha 2011 _tropical species found in Cuba,Brazil,not resident to US
Pseudosida ramosa Water flea KCI LC50 12620 ug/L 48 hr 12620 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 12770 ug/L 48 hr 12770 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 12770 ug/L 48 hr 12770 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 12920 ug/L 48 hr 12920 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 12920 ug/L 48 hr 12920 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 13380 ug/L 48 hr 13380 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa _Water flea KCI LC50 14110 ug/L 48 hr 14110 Freitas,E.C.,and 0. Rocha 2011 _tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 14240 ug/L 48 hr 14240 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 16610 ug/L 48 hr 16610 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 17050 ug/L 48 hr 17050 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 17050 ug/L 48 hr 17050 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 18700 ug/L 48 hr 18700 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 18860 ug/L 48 hr — 18860 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US _
Pseudosida ramosa Water flea KCI LC50 21590 ug/L 48 hr 21590 I Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 23760 ug/L 48 hr _ 23760 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 29710 ug/L 48 hr 29710 Freitas,E.C.,and 0. Rocha 2011 _tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 31860 ug/L 48 hr 31860 _Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 39250 ug/L 48 hr 39250 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Pseudosida ramosa Water flea KCI LC50 9680 ug/L 48 hr 9680 Freitas,E.C.,and 0. Rocha 2011 tropical species not resident to US
Austropotamobius pallipes pal Crayfish KCI LC50* 188000* ug/L 30 day ? Boutet,C.,and C.Chaisemartin 1973 article in french,species not resident to US,ECOTOX value not verifed in paper
Austropotamobius pallipes pal Crayfish KCI LC50* _ 210000 ug/L 30 day 210000 Boutet,C.,and C.Chaisemartin 1973 article in french,species not resident to US
Austropotamobius pallipes pal Crayfish KCI LC50* 251000* ug/L 30 day ? Boutet,C. and C.Chaisemartin 1973 article in french,species not resident to US,ECOTOX value not verifed in paper
Austropotamobius pallipes pal Crayfish KCI LC50* 280000 ug/L 30 day 280000 Boutet,C. and C.Chaisemartin 1973 article in french,species not resident to US
Austropotamobius pallipes pat Crayfish KCI LC50* 350000* ug/L 96 hr ? Boutet,C. and C.Chaisemartin 1973 article in french,species not resident to US,ECOTOX value not verifed in paper
Austropotamobius pallipes pal Crayfish KCI LC50* 390000 ug/L 96 hr 390000 Boutet,C. and C.Chaisemartin 1973 article in french,species not resident to US
Orconectes limosus Crayfish KCI LC50* 296000* ug/L 30 day ? Boutet,C. and C.Chaisemartin 1973 article in french,ECOTOX value not verified in original reference
Orconectes limosus Crayfish KCI LC50* 330000 ug/L 30 day 330000 Boutet,C. and C.Chaisemartin 1973 article in french,some test procedure information(organism age,control performance,
feeding during test,dilution water source)is lacking to adequately determine study
acceptability
Orconectes limosus Crayfish KCI LC50* 404000* ug/L 30 day _ ? Boutet,C. and C.Chaisemartin 1973 article in french,ECOTOX value not verified in original reference
Orconectes limosus Crayfish KCI LC50* 450000 ug/L 30 day 450000 Boutet,C. and C.Chaisemartin 1973 article in french,some test procedure information(organism age,control performance,
feeding during test,dilution water source)is lacking to adequately determine study
acceptability
Orconectes limosus Crayfish KCI LC50* 574000* ug/L 96 hr ? _Boutet,C. and C.Chaisemartin 1973 article in french,ECOTOX value not verified in original reference
' Orconectes limosus Crayfish KCI LC50* 640000 ug/L 96 hr 640000 Boutet,C. and C.Chaisemartin 1973 article in french,some test procedure information(organism age,control performance,
feeding during test,dilution water source)is lacking to adequately determine study
acceota b ility
Salmo trutta Brown trout KCI LT50 NR mM/L 100 hr not given not given Brown,D.J.A. 1981 adult brook trout tested in 0.05-2 mM/L KCI solutions. Time to 50%death recorded,
Salmo trutta Brown trout KCI LT50 NR mM/L 100 hr not given not given Brown,D.J.A. 1981 test pH = 3.5-4.0,test duration not standard
Hyalella azteca Scud KCI LC50 141900 ug/L 96 hr — 141900 Burton,G.A.J.,et al. 1996 paper notes test result was excluded from analysis as not standard test procedures
Hyalella azteca Scud KCI LC50 297300 ug/L 96 hr 297300 Burton,G.A.J.,et al. 1996 control failure
Hyale'G azteca S uc KCI LL59 23200 ug.1 96 hr 232000 12156.E. Burton, G a .1 ,al 1995 For Burton et al 1996; standard test procedures followed,adequate control
Hyalella azteca Scon KCI 7850 250003 ug;.L SS hr 250000 13180]. Burton. G.A J.. „ay 1995 performance,although tests were fed at test initiation and at 48hrs,it does not appear
Hyalella azteca Scud KG' 7350 275600 ug,L 95 hr 275600 144414 Burton :IA.:. ,, al. 1996 feeding of tests affected test results when compared to ENVIRON testing results
Hyalella azteca Scud KC] t0SO 320600 ug!L 96 hr 320600 167984 Burton. 1.8 7 et al. 1996
Hyalella azteca Scud KCI IC50 324600 ug/L 96 hr _ 324500 1%0090 Burton, G.A_.I.,at al. 1996
Hyalella azteca Sccd KCI L(50 335600 ug/L 95 hr 335600 175854 Burton,0.A. at al. 1996
Hyalella azteca Scut KCI LCSO 337200 ug!L 96 hr 337200 Burton „ F. .l , al. 198,6
Hyalella azteca Scud KCS Lt3513 372400 ug.L 95 hr 372400 1_6 B.irto^ C A ' ol 1935
Ctnrenemustentans Midge KCI L850 1250000 ug;l_ 96 hr 1250907 _ _i_ tc, ' al 998,.
Chiconomus tentans Midge KGI IC50 2030000 ug;L 96 hr 2000000 .43203 _Berton h.;. et al 199t3
Churonomustentans Midge KG] LC50 2890008 ug/L 95 hr 2890000 5.496`., &.rton P.I 11995
Chironon:us tentans Midge KCI 1050 3170000 ug/L 96 hr 3170000 1C,H053 _Burton (33/33 et al. 1996
Page 2 of 8

ATTACHMENT 2. FRESHWATER POTASSIUM AQUATIC TOXICITY DATABASE LITERATURE SEARCH RESULTS
Chemical Value as Conc Test Verified Value Value as K Rejection Justification and Notes
Salt
Species Scientific Name Common Name Name Endpoint Conc Units Duration from paper as Conc Citation
salt
entarro Midge KG] .056 96 'rr U610000 1891640 Burton, 0.0.3.. et al_ 1996
Chiron onnis teutans Midge KCI LC50 56. ,. c 96 hr ,000000 2620000 Burton, G.A_).,et al. 1996
Ll-,u-oueH.teutaue Midge 0.0 LC50 96 hr 2677640 Burton, G.A.J., et al. 1996
Ledeuuurru z'.entans Midge 96 hr 2777200 Burton. G.A.O.et al. 1996
is tans Midge LC50 :_ _ 96 hr 53600% 2808640 Burton, G.A.1., et al_1996
L hrro0O,rocs tentans Midge KCI L050 6200006 3248800 Burton. G.A.J., et al. 1996
Chi onorous tentans Midge KCI LC50 62£" :. c. 96 hr 6280000 3290720 Burton, G_A.1, et al. 1996 _
testa,-, Midge KCI LC50 (1',1-12A-0-01 _ _ 96 hr 6600000 3458400 Burton, G.A.J., et al. 1996
onr,us tentaro. Midge X050 6650011' 96 h' 6657001. 348460C Burton, 0.0.1., et al. 1996
n euueudu,[erta _ Midge IC50 96 hr 68 .::-.0,-;.0.. 5u—to " A_ 1596 t
Chironomus tentans Midge KCI LC50 6190000 ug/L 96 hr _ 6190000 Burton,G.A.).,et al. 1996 control failure
Chironomus tentans Midge KCI LC50 5300000 ug/L 96 hr 5300000 Burton,G.A.).,et al. 1996 control failure
Chironomus tentans Midge KCI LC50 1770000 ug/L 96 hr 1770000 Burton,G.A.J.,et al. 1996 control failure
Daphnia magna Water flea KCI EC50 7350 umol/L 24 hr 7350 Calleja, M.C.,et al. 1994 test duration not standard
Streptocephalus proboscideus Fairy shrimp KCI LC50 25100 umol/L 24 hr 25100 Calleja, M.C.,et al. 1994 test duration not standard
Brachionus calyciflorus Rotifer KCI LC50 22700 umol/L 24 hr 22700 Calleja,M.C.,et al. 1994 test duration not standard
Chironomus riparius Midge KCI LC50 4810000 ug/L 96 hr 4810000 Conrad,A.U.,et al. 1999 study is tox test on pesticide. Ran reftox on KCI,not enough info on reftox procedures
to determine validity
Caenorhabditis elegans Nematode KCI LC50 29839000 ug/L 24 hr 29839000 Cressman III,C.P.,and P.L.Williams 1997 adults used for testing,test duration not standard
Caenorhabditis elegans Nematode _ KCI LC50 29854000 ug/L _ 24 hr 29854000 Cressman III,C.P.,and P.L.Williams 1997 adults used for testing,tests fed,test duration not standard
Caenorhabditis elegans Nematode KCI LC50 40830000 ug/L 24 hr 40830000 Cressman III,C.P.,and P.L.Williams 1997 adults used for testing,tests fed,test duration not standard
Caenorhabditis elegans Nematode KCI LC50 41200000 ug/L 24 hr 41200000 Cressman III,C.P.,and P.L.Williams 1997 adults used for testing,test duration not standard
Caenorhabditis elegans Nematode KCI LC50 42049000 ug/L 24 hr 42049000 Cressman III,C.P.,and P.L.Williams 1997 adults used for testing,test duration not standard
Caenorhabditis elegans Nematode KCI LC50 43609000 ug/L 24 hr 43609000 Cressman III,C.P.,and P.L.Williams 1997 adults used for testing,tests fed,test duration not standard _
Caenorhabditis elegans Nematode _ KCI LC50 29960000 ug/L 48 hr 29960000 Cressman III,C.P.,and P.L.Williams 1997 adults used for testing,tests fed
Caenorhabditis elegans Nematode KCI LC50 39130000 ug/L 48 hr 39130000 Cressman III,C.P.,and P.L.Williams 1997 adults used for testing,tests fed
Caenorhabditis elegans Nematode KCI LC50 41560000 ug/L 48 hr 41560000 Cressman III,C.P.,and P.L.Williams 1997 adults used for testing,tests fed
Phaeodactylum tricornutum Diatom KNO3 NR 1400* ug/L 4 hr ? Cresswell, R.C.,and P.).Syrett 1981 not std tox test, NO3 uptake
Chlorella vulgaris Green algae KCI LOEC 670000 ug/L NR 670000 _ De Jong,L.E.D. 1965 test duration not reported
Chlorella vulgaris Green algae KCI NOEC 600000 ug/L NR 600000 De Jong,L.E.D. 1965 test duration not reported _
' Gammarus lacustris Scud Potassium LC50 53200 ug/L 96 hr ? De March,B.G.E. 1988 test procedures not appropriate as multiple toxicants in test solution
Tinca tinca Tench KNO3 NR 3400* ug/L NR ? Demael,A.,et al. 1980 not standard tox test, meas effect of K on blood,plasma
Daphnia magna Water flea KCI LC50* 343000 ug/L 24 hr 343000 Dowden,B.F. 1961 used varying ages of 4th instar or adults for each test, 24 hr test duration not
Daphnia magna Water flea KCI LC50* 357000 ug/L 48 hr 357000 Dowden,B.F. 1961 standard,dilution water was lake water without indicatin of presence of other
Daphnia magna Water flea KCI LC50 343000 ug/L 24 hr 343000 Dowden,B.F.,and H.J.Bennett 1965 test duration not standard,lack of test information(e.g.,organism age,controls
presence/performance,feeding during test,dilution water details)prohibits
determination of test acceotability
Daphnia magna Water flea KCI LC50 337000 ug/L 48 hr 337000 Dowden,B.F.,and H.). Bennett 1965 lack of test information(e.g.,organism age,controls presence/performance,feeding
during test,dilution water details)prohibits determination of test acceptability
Daphnia magna Water flea KCI LC50 117000 ug/L 72 hr 117000 Dowden,B.F.,and H.J. Bennett 1965 test duration not standard,lack of test information(e.g.,organism age,controls
presence/performance,feeding during test,dilution water details)prohibits
determination of test acceotability _
Daphnia magna Water flea KCI LC50 29000 ug/L 96 hr 29000 Dowden, B.F.,and H.J. Bennett 1965 lack of test information(e.g.,organism age,controls presence/performance,feeding
during test,dilution water details)prohibits determination of test acceptability
Daphnia magna Water flea KCI LC50 679000 ug/L 100 hr 679000 Dowden, B.F.,and H.J. Bennett 1965 test duration not standard,lack of test information(e.g.,organism age,controls
i presence/performance,feeding during test,dilution water details)prohibits
determination of test acceotabilitv
Lepomis macrochirus Bluegill KCI LC50 5500000 ug/L 24 hr 5500000 Dowden, B.F.,and H.J. Bennett 1965 test duration not standard,lack of test information(e.g.,organism age,controls
presence/performance,feeding during test,dilution water details)prohibits
I determination of test acceotability —
Lymnaea sp. Pond snail KCI LC50 1941000 ug/L 24 hr 1941000 Dowden,B.F.,and H.). Bennett 1965 test duration not standard,lack of test information(e.g.,organism acclimation since
collected from field,organism age,controls presence/performance,feeding during test,
dilution water details) prohibits determination of test acceptability
li Lymnaea sp. Pond snail KCI LC50 1492000 ug/L 48 hr 1492000 Dowden,B.F. and H.). Bennett 1965 test duration not standard,lack of test information(e.g.,organism acclimation since
collected from field,organism age,controls presence/performance,feeding during test,
dilution water details)prohibits determination of test acceptability
Lymnaea sp. Pond snail KCI LC50 1018000 ug/L 72 hr 1018000 Dowden,B.F. and H.J. Bennett 1965 test duration not standard,lack of test information(e.g.,organism acclimation since
collected from field,organism age,controls presence/performance,feeding during test,
dilution water details)prohibits determination of test acceptability
Lymnaea sp. Pond snail KCI LC50 1100000 ug/L 96 hr 1100000 Dowden,B.F. and H.). Bennett 1965 lack of test information(e.g.,organism acclimation since collected from field,organism
age,controls presence/performance,feeding during test,dilution water details)
_orohibits determination of test acceotability
Daphnia magna Water flea KNO3 LC50 490000 ug/L 24 hr 490000 Dowden, B.F. and H.J. Bennett 1965 test duration not standard,lack of test information(e.g.,organism age,controls
presence/performance,feeding during test,dilution water details)prohibits
determination of test acceotability
Daphnia magna Water flea KNO3 LC50 490000 ug/L 48 hr 490000 Dowden, B.F.,and H.J. Bennett 1965 lack of test information(e.g.,organism age,controls presence/performance,feeding
during test,dilution water details)prohibits determination of test acceptability
Page 3 of 8

Ramboll-Potassium Aquatic Life Values
APPENDIX 3
REVIEW OF POTASSIUM - HARDNESS TOXICITY RELATIONSHIP FOR
FRESHWATER MUSSELS

WATER
MEMO
Project no. 1690000122
From Rick Lockwood,Liza Heise,and Robin Richards,REM
REVIEW OF POTASSIUM - HARDNESS TOXICITY RELATIONSHIP
FOR FRESHWATER MUSSELS
INTRODUCTION
Freshwater mussels (family Unionidae) have a demonstrated sensitivity to
potassium below that of other regularly tested freshwater taxa. Of the roughly
300 known species, only Lampsilis siliquoidea (the Fatmucket) has a robust Ramboll
potassium acute toxicity database in a range of water quality conditions that is 201 Summit View Drive
Suite 300
representative of where this species is found, the Mississippi River basin. The Brentwood,TN 37027
database for long-term sublethal (growth or reproduction) effects to mussels is USA
very limited. T+1 615 277 7570
F+1 615 377 4976
In 2017, Ramboll conducted testing with mussels to address the key data gaps www.ramboll.com
related to the toxicity of potassium to mussels for very soft water conditions
(similar to those observed for the Cedar Creek and Tar River). A further gap in
the potassium toxicity database is a lack of data for any Atlantic Slope (which
includes the Tar/Pamlico river watershed in North Carolina) mussel species. The
testing results met the following objectives.
1) Generate acute potassium toxicity test data (over a range of potassium
concentrations) for two mussel species.
a) A mussel species indigenous to the Atlantic Slope. Related to availability
and culture suitability. Lampsilis radiata (Eastern Lampmussel) was
selected as a representative Atlantic Slope indigenous test species.
b) For comparative purposes, the second species selected was Lampsilis
siliquoidea (Fatmucket) mussel. The most commonly tested species in
North America.
2) Generate data at a nominal hardness of 25 mg/L and 75 mg/L to:
a) Test at the floor hardness of 25 mg/L presented in North Carolina
regulations for hardness-based metal criteria.
1/4

RAMB LI-
b)
lb) Test at 75 mg/L hardness to serve as another comparison point between the two species and
further expand the dataset of potassium toxicity in low to moderate hardness (<100 mg/L)
waters.
c) Re-evaluate the predicted toxicity results based on the established hardness/potassium toxicity
relationship for the Fatmucket mussel in waters with hardness from 100 to 400 mg/L as CaCO3,
and determine if the relationship is appropriate for Atlantic Slope mussels such as the Eastern
Lampmussel.
The results of the acute testing with the Eastern Lampmussel and Fatmucket in reduced hardness
waters indicated that mussel species of the Atlantic Slope assemblage are more tolerant of potassium
than common species in the Mississippi River drainage at equivalent hardness concentrations. Applying
this finding to derivation of chronic (sublethal) potassium limits is the focus of this memo.
ACUTE TOXICITY RESULTS FOR 25 MG/L AND 75 MG/L HARDNESS WATERS
The main observations and conclusions from the toxicity testing conducted in August 2017 are as
follows:
• The Eastern Lampmussel is less sensitive (as indicated by LC50) to potassium than the Fatmucket
mussel at both the 25 mg/L and 75 mg/L hardness (as CaCO3) levels.
o 25 mg/L Hardness Results
- Eastern Lampmussel measured LC50: 37.2 mg/L K
- Fatmucket measured LC50: 22.4 mg/L K
o 75 mg/L Hardness Results
- Eastern Lampmussel measured LC50: 60.8 mg/L K
- Fatmucket measured LC50: 28.1 mg/L K
• For the Eastern Lampmussel, actual LC50 values were higher than predicted valuesl.
• For the Fatmucket mussel, actual LC50 values were equal or lower than predicted values.
• For both species, the 95 percent Confidence Intervals around the measured LC50 values are small,
for example the single test percent span confidence interval compared to the LC50 values range
from 14 to 32 (calculation not shown). These results indicate good quality data and a high level of
certainty associated with the measured LC50 values.
The predicted LC50 values based on the Fatmucket derived models for a hardness 25 mg/L as CaCO3
are 31mg/L K for the Ramboll model and 30 mg/L K for the Wang model. The Eastern Lamp mussel
demonstrated 20 - 23 percent less sensitivity to K compared to model predictions at hardness 25. The
predicted LC50 values based on the Fatmucket derived models for a hardness 75 mg/L as CaCO3 are 40
mg/L K for the Ramboll model and 38 mg/L K for the Wang model. The Eastern Lamp mussel
demonstrated 52 - 60 percent less sensitivity to K compared to model predictions at hardness 75.
MUSSEL CHRONIC TOXICITY DATA
A recent publication (accepted for publication Wang et al, 7/30/2018) details two chronic toxicity tests
conducted with mussels exposed to potassium chloride. It should be noted that both tests were
' A hardness/potassium toxicity relationship was developed for the Fatmucket mussel in waters with hardness from 100 to 400 mg/L
as CaCO3. This relationship is defined as: LC50(mg/L of potassium) = 0.1609(hardness)+26.872. Wang 2017 developed a similar
function LC50 (mg/L of potassium) = 0.146(hardness)+26.7
2/4

MEM
conducted under general guidance of ASTM E2455-06 (2013) which are under development and have
not been subjected to extensive interlaboratory testing and review. Both were conducted by USGS in
2013 (Wang et al, 2018), and used Fatmucket mussels. The results are summarized below:
• A 28-day study (2013) conducted in hardness 100 laboratory water with no refugia substrate (no-
sand or water only) and,
• A 28-day study (2013) conducted in hardness 100 laboratory water with refugia substrate (sand).
The significant difference between the two side by side tests introduces a large degree of uncertainty for
interpretation. The control performance for both tests (with and without sand) differs by less than 1
percent indicating that the sand substrate compounded the potassium toxicity in these exposures. This
would suggest that the water only results are more valid with fewer uncontrolled variables in the study,
and the results from the sand substrate test should not be used solely as the basis for determining the
chronic toxicity of potassium to mussels.
• ACR calculations are based on the corresponding Fatmucket hardness 100 database 96-hour LC50 =
44 mg/L K.
The chronic values (ChV) and EC20 values for the water only 28-day test at hardness 100 without sand
are:
• Biomass ChV = 32 mg/L K (ACR = 1.38)
• Biomass EC20 = 23 mg/L K (ACR = 1.91)
These results can be adjusted to hardness of 25 mg/L using same equation as for in footnote 1 above:
• ACR calculations are based on the corresponding Fatmucket hardness 25 adjustment of the database
96-hour LC50 = 31.7 mg/L K
The adjusted chronic values (ChV) or EC20 values for the water only 28-day test at hardness 25 without
sand are:
• Biomass ChV = 23.1 mg/L K (ACR = 1.37)
• Biomass EC20 = 16.6 mg/L K (ACR = 1.91)
Chronic Criteria Derivations and Use of Indigenous Species and Ambient Site
Conditions
The hardness based acute sensitivity to potassium demonstrated by the indigenous Eastern Lampmussel
is significantly less than for surrogate mussel species in the data base. Therefore, it is appropriate to
assume that chronic tolerance will also be greater, especially since ambient potassium levels in Atlantic
slope streams are comparable to streams supporting mussels in other parts of the US where hardness is
greater. Furthermore, there is precedent for using resident or locally indigenous species for deriving
water quality criteria.
Given the level of uncertainty for the present database of chronic potassium toxicity to mussels, use of
the water only 28-day biomass results is considered the best available data for development of a
chronic potassium criteria for surface waters in Franklin County, NC. However, because of the
3/4