### 31682 Federal Register / Vol. 65, No. 97 / Thursday, May 18, 2000 / Rules and Regulations

ENVIRONMENTAL PROTECTION
AGENCY

40 CFR Part 131

[FRL–6587–9]

RIN 2040–AC44

Water Quality Standards;
Establishment of Numeric Criteria for Priority Toxic Pollutants for the State
of California

AGENCY : Environmental Protection Agency.

ACTION : Final rule.

SUMMARY : This final rule promulgates: numeric aquatic life criteria for 23 priority toxic pollutants; numeric human health criteria for 57 priority toxic pollutants; and a compliance schedule provision which authorizes
the State to issue schedules of compliance for new or revised National Pollutant Discharge Elimination System permit limits based on the federal
criteria when certain conditions are met.

EPA is promulgating this rule based
on the Administrator’s determination that numeric criteria are necessary in the State of California to protect human
health and the environment. The Clean Water Act requires States to adopt numeric water quality criteria for priority toxic pollutants for which EPA has issued criteria guidance, the presence or discharge of which could reasonably be expected to interfere with maintaining designated uses.

EPA is promulgating this rule to fill a gap in California water quality
standards that was created in 1994
when a State court overturned the State’s water quality control plans which contained water quality criteria for priority toxic pollutants. Thus, the
State of California has been without numeric water quality criteria for many priority toxic pollutants as required by the Clean Water Act, necessitating this action by EPA. These Federal criteria are legally applicable in the State of California for inland surface waters, enclosed bays and estuaries for all purposes and programs under the Clean

Water Act.

EFFECTIVE DATE : This rule shall be effective May 18, 2000.

ADDRESSES : The administrative record for today’s final rule is available for public inspection at the U.S. Environmental Protection Agency, Region 9, Water Division, 75 Hawthorne Street, San Francisco, California 94105,
between the hours of 8:00 a.m. and 4:30 p.m. For access to the administrative record, call Diane E. Fleck, P.E., Esq. at 415 744–1984 for an appointment. A reasonable fee will be charged for photocopies.

FOR FURTHER INFORMATION CONTACT : Diane E. Fleck, P.E., Esq. or Philip Woods, U.S. Environmental Protection Agency, Region 9, Water Division, 75 Hawthorne Street, San Francisco, California 94105, 415–744–1984 or 415– 744–1997, respectively.

SUPPLEMENTARY INFORMATION : This preamble is organized according to the following outline: A. Potentially Affected Entities

B. Introduction and Overview

1. Introduction

2. Overview C. Statutory and Regulatory Background D. California Water Quality Standards

Actions 1. California Regional Water Quality Control Board Basin Plans, and the Inland Surface Waters Plan (ISWP) and the Enclosed Bays and Estuaries Plan (EBEP) of April 1991 2. EPA’s Review of California Water Quality Standards for Priority Toxic Pollutants in the ISWP and EBEP, and the National

Toxics Rule 3. Status of Implementation of CWA Section 303(c)(2)(B) 4. State-Adopted, Site-Specific Criteria for Priority Toxic Pollutants a. State-Adopted Site-Specific Criteria Under

EPA Review b. State-Adopted Site-Specific Criteria With EPA Approval E. Rationale and Approach For Developing

the Final Rule 1. Legal Basis 2. Approach for Developing this Rule F. Derivation of Criteria 1. Section 304(a) Criteria Guidance Process 2. Aquatic Life Criteria

a. Freshwater Acute Selenium Criterion

b. Dissolved Metals Criteria c. Application of Metals Criteria d. Saltwater Copper Criteria e. Chronic Averaging Period

f. Hardness

3. Human Health Criteria a. 2,3,7,8–TCDD (Dioxin) Criteria

b. Arsenic Criteria c. Mercury Criteria d. Polychlorinated Biphenyls (PCBs) Criteria e. Excluded Section 304(a) Human Health

Criteria
f. Cancer Risk Level G. Description of Final Rule 1. Scope 2. EPA Criteria for Priority Toxic Pollutants 3. Implementation

4. Wet Weather Flows 5. Schedules of Compliance 6. Changes from Proposed Rule H. Economic Analysis

1. Costs
2. Benefits I. Executive Order 12866, Regulatory Planning and Review J. Unfunded Mandates Reform Act of 1995 K. Regulatory Flexibility Act L. Paperwork Reduction Act M. Endangered Species Act N. Congressional Review Act O. Executive Order 13084, Consultation and

Coordination With Indian Tribal

Governments P. National Technology Transfer and

Advancement Act Q. Executive Order 13132 on Federalism

R. Executive Order 13045 on Protection of

Children From Environmental Health Risks and Safety Risks

A. Potentially Affected Entities

Citizens concerned with water quality in California may be interested in this rulemaking. Entities discharging pollutants to waters of the United States in California could be affected by this rulemaking since water quality criteria are used by the State in developing National Pollutant Discharge Elimination System (NPDES) permit limits. Categories and entities that ultimately may be affected include:

Category Examples of potentially affected entities

Industry ............................................................... Industries discharging pollutants to surface waters in California or to publicly-owned treatment

works. Municipalities ...................................................... Publicly-owned treatment works discharging pollutants to su rface waters in California

This table is not intended to be exhaustive, but rather provides a guide for readers regarding entities likely to be affected by this action. This table lists the types of entities that EPA is now aware could potentially be affected by this action. Other types of entities not listed in the table could also be affected. To determine whether your facility might be affected by this action, you should carefully examine the applicability criteria in § 131.38(c). If you have questions regarding the applicability of this action to a particular entity, consult the persons listed in the preceding FOR FURTHER

INFORMATION CONTACT section.


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B. Introduction and Overview

1. Introduction

This section introduces the topics which are addressed in the preamble and provides a brief overview of EPA’s basis and rationale for promulgating
Federal criteria for the State of California. Section C briefly describes
the evolution of the efforts to control toxic pollutants; these efforts include the changes enacted in the 1987 CWA Amendments, which are the basis for
this rule. Section D summarizes
California’s efforts since 1987 to implement the requirements of CWA section 303(c)(2)(B) and describes EPA’s procedure and actions for determining whether California has fully implemented CWA section 303(c)(2)(B). Section E provides the rationale and approach for developing this final rule, including a discussion of EPA’s legal
basis for this final rule. Section F describes the development of the
criteria included in this rule. Section G summarizes the provisions of the final rule and discusses implementation issues. Sections H, I, J, K , L, M, N, O, P, and Q briefly address the requirements of Executive Order 12866,
the Unfunded Mandates Reform Act of 1995, the Regulatory Flexibility Act, the Paperwork Reduction Act, the Endangered Species Act, the Congressional Review Act, Executive Order 13084, Consultation and
Coordination with Indian Tribal Governments, the National Technology Transfer and Advancement Act, and Executive Order 13132, Federalism, respectively.

The proposal for this rulemaking was published in the Federal Register on August 5, 1997. Changes from the proposal are generally addressed in the body of this preamble and specifically addressed in the response to comments
document included in the
administrative record for this rulemaking. EPA responded to all comments on the proposed rule, including comments received after the September 26, 1997, deadline. Although EPA is under no legal obligation to respond to late comments, EPA made a policy decision to respond to all

comments.

Since detailed information concerning many of the topics in this preamble was published previously in the Federal Register in preambles for this and other rulemakings, references are frequently made to those preambles. Those rulemakings include: Water Quality Standards; Establishment of Numeric Criteria for Priority Toxic Pollutants for the State of California; Proposed Rule, 62 FR 42159, August 5, 1997 (referred to as the ‘‘proposed CTR’’); Water Quality Standards; Establishment of Numeric Criteria for Priority Toxic Pollutants, 57 FR 60848, December 22, 1992 (referred to as the ‘‘National Toxics Rule’’ or ‘‘NTR’’); and the NTR as amended by Administrative Stay of Federal Water Quality Criteria for Metals and Interim Final Rule, Water Quality Standards; Establishment of Numeric Criteria for Priority Toxic Pollutants; States’ Compliance— Revision of Metals Criteria, 60 FR 22228, May 4, 1995 (referred to as the ‘‘National Toxics Rule [NTR], as amended’’). The NTR, as amended, is codified at 40 CFR 131.36. A copy of the proposed CTR and its preamble, and the NTR, as amended, and its preambles are
contained in the administrative record for this rulemaking.

EPA is making this final rule effective upon publication. Under the Administrative Procedure Act, 5 U.S.C. 553(d)(3), agencies must generally publish a rule no more than 30 days prior to the effective date of the rule except as otherwise provided for by the Agency for good cause. The purpose of the 30-day waiting period is to give affected parties a reasonable time to adjust their behavior before the final
rule takes effect. See Omnipoint Corp. v. F.C.C., 78 F.3d 620, 630–631 (D.C. Cir. 1996); Riverbend Farms, Inc. v. Madigan , 958 F.2d 1479, 1485 (9th Cir. 1992).

In this instance, EPA finds good cause to make the final rule effective upon publication. In order to find good cause, an Agency needs to find that the 30-day period would be: (1) Impracticable, (2) unnecessary, or (3) contrary to the public interest. Here EPA is relying on the second reason to support its finding of good cause. EPA also notes that the State has requested EPA to make the rule immediately effective.

EPA finds that in this instance, waiting 30 days to make the rule effective is unnecessary. As explained
in further detail elsewhere in this preamble, this rule is not self implementing; rather it establishes
ambient conditions that the State of California will implement in future permit proceedings. These permit proceedings will, by regulation, take longer than 30 days to complete. This means that although the rule is immediately effective, no discharger’s
conduct would be altered under the rule in less than 30 days, and therefore the 30-day period is unnecessary.

2. Overview

This final rule establishes ambient water quality criteria for priority toxic pollutants in the State of California. The criteria in this final rule will supplement the water quality criteria promulgated for California in the NTR, as amended. In 1991, EPA approved a number of water quality criteria (discussed in section D), for the State of California. Since EPA had approved these criteria, it was not necessary to
include them in the 1992 NTR for these criteria. However, the EPA-approved criteria were subsequently invalidated in State litigation. Thus, this final rule contains criteria to fill the gap created by the State litigation.

This final rule does not change or supersede any criteria previously promulgated for the State of California in the NTR, as amended. Criteria which EPA promulgated for California in the NTR, as amended, are footnoted in the final table at 131.38(b)(1), so that readers may see the criteria promulgated in the NTR, as amended, for California and the criteria promulgated through this rulemaking for California in the
same table. This final rule is not intended to apply to waters within Indian Country. EPA recognizes that there are possibly waters located wholly or partly in Indian Country that are included in the State’s basin plans. EPA
will work with the State and Tribes to identify any such waters and determine whether further action to protect water quality in Indian Country is necessary.

This rule is important for several environmental, programmatic and legal reasons. Control of toxic pollutants in surface waters is necessary to achieve the CWA’s goals and objectives. Many of California’s monitored river miles, lake acres, and estuarine waters have elevated levels of toxic pollutants.
Recent studies on California water
bodies indicate that elevated levels of toxic pollutants exist in fish tissue which result in fishing advisories or bans. These toxic pollutants can be attributed to, among other sources, industrial and municipal discharges.

Water quality standards for toxic pollutants are important to State and EPA efforts to address water quality problems. Clearly established water quality goals enhance the effectiveness of many of the State’s and EPA’s water programs including permitting, coastal water quality improvement, fish tissue quality protection, nonpoint source controls, drinking water quality protection, and ecological protection. Numeric criteria for toxic pollutants
allow the State and EPA to evaluate the adequacy of existing and potential control measures to protect aquatic ecosystems and human health. Numeric criteria also provide a more precise basis for deriving water quality-based effluent limitations (WQBELs) in


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National Pollutant Discharge Elimination System (NPDES) permits
and wasteload allocations for total maximum daily loads (TMDLs) to control toxic pollutant discharges. Congress recognized these issues when it enacted section 303(c)(2)(B) to the

CWA.

While California recognizes the need for applicable water quality standards for toxic pollutants, its adoption efforts have been stymied by a variety of
factors. The Administrator has decided
to exercise her CWA authorities to move forward the toxic control program,
consistent with the CWA and with the State of California’s water quality standards program.

Today’s action will also help restore equity among the States. The CWA is designed to ensure all waters are sufficiently clean to protect public
health and/or the environment. The CWA allows some flexibility and differences among States in their adopted and approved water quality standards, but it should be implemented in a manner that ensures a level playing field among States. Although California has made important progress toward satisfying CWA requirements, it has not satisfied CWA section 303(c)(2)(B) by adopting numeric water quality criteria for toxic pollutants. This section was added to the CWA by Congress in 1987. Prior to today, the State of California had been the only State in the Nation for which CWA section 303(c)(2)(B) had remained substantially unimplemented after EPA’s promulgation of the NTR in December of 1992. Section 303(c)(4) of
the CWA authorizes the EPA Administrator to promulgate standards where necessary to meet the requirements of the Act. The
Administrator determined that this rule was a necessary and important component for the implementation of CWA section 303(c)(2)(B) in California.

EPA acknowledges that the State of California is working to satisfy CWA section 303(c)(2)(B). When the State formally adopts, and EPA approves, criteria consistent with statutory requirements, as envisioned by Congress in the CWA, EPA intends to stay this rule. If within the applicable time frame for judicial review, the States’ standards are challenged, EPA will withdraw this rule after such judicial review is complete and the State standards are
sustained.

C. Statutory and Regulatory Background

The preamble to the August 5, 1997, proposed rule provided a general discussion of EPA’s statutory and regulatory authority to promulgate water quality criteria for the State of
California. See 62 FR 42160–42163. EPA is including that discussion in the
record for the final rule. Commenters questioned EPA’s authority to promulgate certain aspects of the proposal. EPA is responding to those comments in the appropriate sections of this preamble, and in the response to
comments document included in the
administrative record for this rulemaking. Where appropriate, EPA’s responses expand upon the discussion of statutory and regulatory authority found in the proposal.

D. California Water Quality Standards

Actions

1. California Regional Water Quality Control Board Basin Plans, and the Inland Surface Waters Plan (ISWP) and the Enclosed Bays and Estuaries Plan (EBEP) of April 1991

The State of California regulates water quality through its State Water Resources Control Board (SWRCB) and through nine Regional Water Quality Control Boards (RWQCBs). Each of the nine RWQCBs represents a different geographic area; area boundaries are generally along watershed boundaries. Each RWQCB maintains a Basin Plan which contains the designated uses of the water bodies within its respective geographic area within California. These designated uses (or ‘‘beneficial uses’’under State law) together with legallyadopted criteria (or ‘‘objectives’’ under State law), comprise water quality
standards for the water bodies within
each of the Basin areas. Each of the nine RWQCBs undergoes a triennial basin planning review process, in compliance
with CWA section 303. The SWRCB provides assistance to the RWQCBs.

Most of the Basin Plans contain conventional pollutant objectives such as dissolved oxygen. None of the Basin Plans contains a comprehensive list of priority toxic pollutant criteria to satisfy CWA section 303(c)(2)(B). The nine RWQCBs and the SWRCB had intended that the priority toxic pollutant criteria
contained in the three SWRCB statewide plans, the Inland Surface Waters Plan (ISWP), the Enclosed Bays and Estuaries Plan (EBEP), and the Ocean Plan, apply to all basins and satisfy CWA section 303(c)(2)(B).

On April 11, 1991, the SWRCB adopted two statewide water quality control plans, the ISWP and the EBEP. These statewide plans contained narrative and numeric water quality criteria for toxic pollutants, in part to satisfy CWA section 303(c)(2)(B). The water quality criteria contained in the SWRCB statewide plans, together with the designated uses in each of the Basin Plans, created a set of water quality
standards for waters within the State of
California.

Specifically, the two plans established water quality criteria or objectives for all fresh waters, bays and estuaries in the State. The plans contained water quality criteria for some priority toxic pollutants, provisions relating to whole effluent toxicity, implementation procedures for point and nonpoint sources, and authorizing compliance schedule provisions. The plans also included special provisions affecting waters dominated by reclaimed water (labeled as Category (a) waters), and waters dominated by agricultural drainage and constructed agricultural drains (labeled as Category (b) and (c) waters, respectively).

2. EPA’s Review of California Water Quality Standards for Priority Toxic Pollutants in the ISWP and EBEP, and
the National Toxics Rule

The EPA Administrator has delegated the responsibility and authority for review and approval or disapproval of all new or revised State water quality standards to the EPA Regional Administrators (see 40 CFR 131.21). Thus, State actions under CWA section 303(c)(2)(B) are submitted to the appropriate EPA Regional Administrator for review and approval.

In mid-April 1991, the SWRCB
submitted to EPA for review and approval the two statewide water quality control plans, the ISWP and the EBEP. On November 6, 1991, EPA Region 9 formally concluded its review of the SWRCB’s plans. EPA approved the narrative water quality criterion and the toxicity criterion in each of the plans. EPA also approved the numeric water quality criteria contained in both plans, finding them to be consistent with the requirements of section 303(c)(2)(B) of the CWA and with EPA’s national criteria guidance published pursuant to section 304(a) of the CWA.

EPA noted the lack of criteria for some pollutants, and found that, because of the omissions, the plans did not fully satisfy CWA section 303(c)(2)(B). The plans did not contain criteria for all listed pollutants for which EPA had published national criteria guidance. The ISWP contained human health criteria for only 65 pollutants, and the EBEP contained human health criteria for only 61 pollutants for which EPA had issued section 304(a) guidance criteria. Both the ISWP and EBEP contained aquatic life criteria for all pollutants except cyanide and chromium III (freshwater only) for which EPA has CWA section


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304(a) criteria guidance. The SWRCB’s
administrative record stated that all priority pollutants with EPA criteria guidance were likely to be present in California waters. However, the
SWRCB’s record contained insufficient information to support a finding that the excluded pollutants were not reasonably expected to interfere with designated
uses of the waters of the State.

Although EPA approved the statewide selenium objective in the ISWP and EBEP, EPA disapproved the objective for the San Francisco Bay and Delta,
because there was clear evidence that the objective would not protect the designated fish and wildlife uses (the California Department of Health
Services had issued waterfowl consumption advisories due to selenium concentrations, and scientific studies had documented selenium toxicity to fish and wildlife). EPA restated its commitment to object to National Pollutant Discharge Elimination System (NPDES) permits issued for San Francisco Bay that contained effluent limits based on an objective greater than 5 parts per billion (ppb) (four day average) and 20 ppb (1 hour average),
the freshwater criteria. EPA reaffirmedits disapproval of Californias’ sitespecific selenium objective for portions of the San Joaquin River, Salt Slough, and Mud Slough. EPA also disapproved of the categorical deferrals and exemptions. These disapprovals included the disapproval of the State’s deferral of water quality objectives to effluent dominated streams (Category a) and to streams dominated by agricultural drainage (Category b), and the disapproval of the exemption of water quality objectives to constructed agricultural drains (Category c). EPA found the definitions of the categories imprecise and overly broad which could have led to an incorrect interpretation.

Since EPA had disapproved portions of each of the California statewide plans which were necessary to satisfy CWA section 303(c)(2)(B), certain disapproved aspects of California’s water quality
standards were included in EPA’s promulgation of the National Toxics Rule (NTR) (40 CFR 131.36, 57 FR 60848). EPA promulgated specific
criteria for certain water bodies in
California.

The NTR was amended, effective April 14, 1995, to stay certain metals criteria which had been promulgated as total recoverable. Effective April 15, 1995, EPA promulgated interim final
metals criteria as dissolved
concentrations for those metals which had been stayed (Administrative Stay of Federal Water Quality Criteria for Metals and Interim Final Rule, Water Quality Standards; Establishment of Numeric Criteria for Priority Toxic Pollutants; States’ Compliance— Revision of Metals Criteria; 60 FR 22228, 22229, May 4, 1995 [the NTR, as amended]). The stay was in response to a lawsuit against EPA challenging, among other issues, metals criteria expressed as total recoverable concentrations. A partial Settlement Agreement required EPA to stay specific
metals criteria in the NTR. EPA then promulgated certain metals criteria in the dissolved form through the use of
conversion factors. These factors are listed in the NTR, as amended. A
scientific discussion of these criteria is found in a subsequent section of this preamble.

Since certain criteria have already been promulgated for specific water
bodies in the State of California in the NTR, as amended, they are not within the scope of today’s final rule. However, for clarity in reading a comprehensive rule for the State of California, these criteria are incorporated into 40 CFR 131.38(d)(2). Footnotes to the Table in 40 CFR 131.38(b)(1) and 40 CFR 131.38(d)(3) clarify which criteria (and for which specific water bodies) were promulgated by the NTR, as amended,
and are therefore excluded from this final rule. The appropriate (freshwater or saltwater) aquatic life criteria which were promulgated in the NTR, as amended, for all inland surface waters and enclosed bays and estuaries include: chromium III and cyanide. The appropriate (water and organism or organism only) human health criteria which were promulgated in the NTR, as amended, for all inland surface waters and enclosed bays and estuaries
include:

antimony
thallium
asbestos
acrolein acrylonitrile
carbon tetrachloride
chlorobenzene 1,2-dichloroethane 1,1-dichloroethylene 1,3-dichloropropylene ethylbenzene 1,1,2,2-tetrachloroethane tetrachloroethylene 1,1,2-trichloroethane trichloroethylene vinyl chloride 2,4-dichlorophenol 2-methyl-4,6-dinitrophenol 2,4-dinitrophenol
benzidine bis(2-chloroethyl)ether bis(2-ethylhexyl)phthalate 3,3-dichlorobenzidine diethyl phthalate dimethyl phthalate di-n-butyl phthalate 2,4-dinitrotoluene 1,2-diphenylhydrazine

hexachlorobutadiene hexachlorocyclopentadiene

hexachloroethane isophorone

nitrobenzene n-nitrosodimethylamine n-nitrosodiphenylamine

Other pollutant criteria were promulgated in the NTR, as amended, for specific water bodies, but not all inland surface waters and enclosed bays
and estuaries.

3. Status of Implementation of CWA Section 303(c)(2)(B)

Shortly after the SWRCB adopted the ISWP and EBEP, several dischargers filed suit against the State alleging that it had not adopted the two plans in compliance with State law. The plaintiffs in a consolidated case included: the County of Sacramento, Sacramento County Water Agency; Sacramento Regional County Sanitation District; the City of Sacramento; the City of Sunnyvale; the City of San Jose; the City of Stockton; and Simpson Paper Company.

The dischargers alleged that the State had not adopted the ISWP and EBEP in compliance with the California Administrative Procedures Act (Gov Code. Section 11340, et seq. ), the California Environmental Quality Act (Pub. Re Code, Section 21000, et seq. ), and the Porter-Cologne Act (Wat. Code,
Section 13200, et seq. ). The allegation that the State did not sufficiently consider economics when adopting water quality objectives, as allegedly required by Section 13241 of the Porter Cologne Act, was an important issue in the litigation.

In October of 1993, the Superior Court of California, County of Sacramento,
issued a tentative decision in favor of the dischargers. In March of 1994, the Court issued a substantively similar
final decision in favor of the dischargers. Final judgments from the Court in July of 1994 ordered the
SWRCB to rescind the ISWP and EBEP. On September 22, 1994, the SWRCB formally rescinded the two statewide water quality control plans. The State is currently in the process of readopting water quality control plans for inland surface waters, enclosed bays and

estuaries.

CWA section 303(c)(2)(B) was fully implemented in the State of California from December of 1992, when the NTR was promulgated, until September of 1994, when the SWRCB was required to
rescind the ISWP and EBEP. The provisions for California in EPA’s NTR together with the approved portions of


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California’s ISWP and EBEP implemented the requirements of CWA section 303(c)(2)(B). However, since September of 1994, when the SWRCB rescinded the ISWP and EBEP, the requirements of section 303(c)(2)(B) have not been fully implemented in
California.

The scope of today’s rule is to reestablish criteria for the remaining priority toxic pollutants to meet the requirements of section 303(c)(2)(B) of the CWA. Pursuant to section 303(c)(4),
the Administrator has determined that it is necessary to include in today’s action criteria for priority toxic pollutants, which are not covered by the NTR, asamended, or by the State through EPAapproved site-specific criteria, for
waters of the United States in the State
of California.

4. State-Adopted, Site-Specific Criteria for Priority Toxic Pollutants

The State has the discretion to develop site-specific criteria when appropriate e.g., when statewide criteria appear over-or under-protective of designated uses. Periodically, the Statethrough its RWQCBs will adopt sitespecific criteria for priority toxic pollutants within respective Basin
Plans. These criteria are intended to be effective throughout the Basin or throughout a designated water body. Under California law, these criteria must be publicly reviewed and approved by the RWQCB, the SWRCB,
and the State’s Office of Administrative Law (OAL). Once this adoption process is complete, the criteria become State
law.

These criteria must be submitted to the EPA Regional Administrator for review and approval under CWA section 303. These criteria are usually submitted to EPA as part of a RWQCB Basin Plan Amendment, after the Amendment has been adopted under the State’s process and has become State
law.

a. State-Adopted Site-Specific Criteria
Under EPA Review

The State of California has recently reviewed and updated all of its RWQCB
Basin Plans. All of the Basin Plans have completed the State review and adoption process and have been
submitted to EPA for review and approval. Some of the Basin Plans contain site-specific criteria. In these cases, the State-adopted site-specific criteria are used for water quality

programs.

EPA has not yet concluded consultation under the Endangered Species Act with the U.S. Department of Interior, Fish and Wildlife Service, and the U.S. Department of Commerce, National Marine Fisheries Service, on EPA’s tentative approval/disapproval actions on the RWQCB Basin Plans. In this situation, the more stringent of thetwo criteria (the State-adopted sitespecific criteria in the RWQCB Basin Plans, or the Federal criteria in this final rule), would be used for water quality programs including the calculation of water quality-based effluent criteria in National Pollutant Discharge Elimination System (NPDES) permits.

b. State-Adopted Site-Specific Criteria With EPA Approval

In several cases, the EPA Regional Administrator has already reviewed and approved State-adopted site-specific
criteria within the State of California.
Several of these cases are discussed in this section. All of the EPA approval letters referenced in today’s preamble
are contained in the administrative record for today’s rule.

Sacramento River: EPA has approved site-specific acute criteria for copper,
cadmium and zinc in the Sacramento River, upstream of Hamilton City, in the Central Valley Region (RWQCB for the Central Valley Region) of the State ofCalifornia. EPA approved these sitespecific criteria by letter dated August 7, 1985. Specifically, EPA approved for the Sacramento River (and tributaries) above Hamilton City, a copper criterion
of 5.6 μg/l (maximum), a zinc criterion
of 16 μg/l (maximum) and a cadmium
criterion of 0.22 μg/l (maximum), all in the dissolved form using a hardness of 40 mg/l as CaCO3. (These criteria were actually adopted by the State and approved by EPA as equations which vary with hardness.) These ‘‘maximum’’ criteria correspond to acute criteria in today’s final rule. Therefore, Federal acute criteria for copper, cadmium, and zinc for the Sacramento River (and tributaries) above Hamilton City are not necessary to protect the designated uses
and are not included in the final rule. However, the EPA Administrator is making a finding that it is necessary to include chronic criteria for copper,
cadmium and zinc for the Sacramento River (and tributaries) above Hamilton City, as part of the statewide criteria promulgated in today’s final rule.

San Joaquin River: The selenium criteria in this rule are not applicable to portions of the San Joaquin River, in the Central Valley Region, because selenium criteria have been either previously approved by EPA or previously promulgated by EPA as part of the NTR.EPA approved and disapproved Stateadopted site-specific selenium criteria in portions of the San Joaquin River, in the Central Valley Region of the State of California (RWQCB for the Central Valley Region). EPA’s determination on these site-specific criteria is contained in a letter dated April 13, 1990.

Specifically, EPA approved for the San Joaquin River, mouth of Merced River to Vernalis, an aquatic life
selenium criterion of 12 μg/l (maximum with the understanding that the

instantaneous maximum concentration may not exceed the objective more than once every three years). Today’s finalrule does not affect this Federallyapproved, State-adopted site-specific acute criterion, and it remains in effect for the San Joaquin River, mouth of Merced River to Vernalis. Therefore, an
acute criterion for selenium in the San Joaquin River, mouth of Merced River to Vernalis is not necessary to protect the designated use and thus is not included
in this final rule.

By letter dated April 13, 1990, EPA also approved for the San Joaquin River, mouth of Merced River to Vernalis, a State-adopted site-specific aquatic life
selenium criterion of 5 μg/l (monthly mean); however, EPA disapproved a State-adopted site-specific selenium
criterion of 8 μg/l (monthly mean— critical year only) for these waters. Subsequently, EPA promulgated a
chronic selenium criterion of 5 μg/l (4 day average) for waters of the San Joaquin River from the mouth of the
Merced River to Vernalis in the NTR. This chronic criterion applies to all water quality programs concerning the San Joaquin River, mouth of Merced River to Vernalis. Today’s final ruledoes not affect the Federallypromulgated chronic selenium criterion
of 5 μg/l (4 day average) set forth in theNTR. This previously Federallypromulgated criterion remains in effect for the San Joaquin River, mouth of
Merced River to Vernalis.

Grassland Water District, San Luis National Wildlife Refuge, and Los Banos State Wildlife Refuge: EPA approved for the Grassland Water District, San Luis National Wildlife Refuge, and Los Banos State Wildlife Refuge, a State-adopted site-specific aquatic life selenium
criterion of 2 μg/l (monthly mean) by letter dated April 13, 1990. ThisFederally-approved, State-adopted sitespecific chronic criterion remains in effect for the Grassland Water District, San Luis National Wildlife Refuge and Los Banos State Wildlife Refuge. Therefore it is not necessary to include in today’s final rule, a chronic criterion
for selenium for the Grassland Water District, San Luis National Wildlife Refuge and Los Banos State Wildlife Refuge, and thus, it is not included in
this final rule.


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San Francisco Regional Board Basin Plan of 1986: EPA approved several priority toxic pollutant objectives (CWA criteria) that were contained in the1986 San Francisco Regional Board Basin Plan, as amended by SWRCB Resolution Numbers 87–49, 87–82 and 87–92, by letters dated September 2, 1987 and December 24, 1987. This Basin Plan, the SWRCB Resolutions, and the EPA approval letters are contained in the
administrative record for this rulemaking. It is not necessary to include these criteria for priority toxic pollutants that are contained in the San Francisco Regional Board’s 1986 Basin Plan as amended, and approved by EPA. Priority pollutants in this situation are footnoted in the matrix at 131.38(b)(1) with footnote ‘‘b.’’ Where gaps exist in the State adoption and EPA approval of priority toxic pollutant objectives, the criteria in today’s rule apply.

EPA is assigning ‘‘human health, water and organism consumption’’
criteria to waters with the States’ municipal or ‘‘MUN’’ beneficial use designation in the Basin Plan. Also, some pollutants regulated through the Basin Plan have different averaging periods, e.g., one hour as compared with the rule’s ‘‘short-term.’’ However, where classes of chemicals, such as polynuclear aromatic hydrocarbons, or PAHs, and phenols, are regulated through the Basin Plan, but not specific chemicals within the category, specific chemicals within the category are regulated by today’s rule.

E. Rationale and Approach for Developing the Final Rule

This section explains EPA’s legal basis for today’s final rule, and discusses EPA’s general approach for developing the specific requirements for
the State of California.

1. Legal Basis

CWA section 303(c) specifies that adoption of water quality standards is primarily the responsibility of the States. However, CWA section 303(c)
also describes a role for the Federal government to oversee State actions to ensure compliance with CWA requirements. If EPA’s review of the
States’ standards finds flaws or omissions, then the CWA authorizes EPA to correct the deficiencies (see CWA section 303(c)(4)). This water quality standards promulgation authority has been used by EPA to issue final rules on several separate occasions, including the NTR, as amended, which promulgated criteria similar to those
included here for a number of States.
These actions have addressed both insufficiently protective State criteria and/or designated uses and failure to adopt needed criteria. Thus, today’s action is not unique.

The CWA in section 303(c)(4) provides two bases for promulgation of Federal water quality standards. The first basis, in paragraph (A), applies
when a State submits new or revised
standards that EPA determines are not consistent with the applicable requirements of the CWA. If, after EPA’s disapproval, the State does not amend
its rules so as to be consistent with the CWA, EPA is to promptly propose appropriate Federal water quality
standards for that State. The second basis for an EPA action is in paragraph (B), which provides that EPA shall promptly initiate promulgation ‘‘* * * in any case where the Administrator
determines that a revised or new standard is necessary to meet the requirements of this Act.’’ EPA is using section 303(c)(4)(B) as the legal basis for today’s final rule.

As discussed in the preamble to the NTR, the Administrator’s determination under CWA section 303(c)(4) that criteria are necessary to meet the requirements of the Act could be supported in several ways. Consistent with EPA’s approach in the NTR, EPA interprets section 303(c)(2)(B) of the
CWA to allow EPA to act where the State has not succeeded in establishing numeric water quality standards for toxic pollutants. This inaction can be
the basis for the Administrator’s determination under section 303(c)(4)
that new or revised criteria are necessary to ensure designated uses are protected.

EPA does not believe that it is necessary to support the criteria in today’s rule on a pollutant-specific, water body-by-water-body basis. For
EPA to undertake an effort to conduct
research and studies of each stream segment or water body across the State
of California to demonstrate that for each toxic pollutant for which EPA has issued CWA section 304(a) criteria guidance there is a ‘‘discharge or presence’’ of that pollutant which could reasonably ‘‘be expected to interfere with’’ the designated use would impose
an enormous administrative burden and would be contrary to the statutory directive for swift action manifested by the 1987 addition of section 303(c)(2)(B) to the CWA. Moreover, because these
criteria are ambient criteria that define attainment of the designated uses, their application to all water bodies will
result in additional controls on dischargers only where necessary to protect the designated uses.

EPA’s interpretation of section 303(c)(2)(B) is supported by the language of the provision, the statutory framework and purpose of section 303, and the legislative history. In adding section 303(c)(2)(B) to the CWA, Congress understood the existing requirements in section 303(c)(1) for
States to conduct triennial reviews of their water quality standards and submit
the results of those reviews to EPA and in section 303(c)(4)(B) for promulgation. CWA section 303(c) includes numerous deadlines and section 303(c)(4) directs the Administrator to act ‘‘promptly’’
where the Administrator determines
that a revised or new standard is necessary to meet the requirements of the Act. Congress, by linking section 303(c)(2)(B) to the section 303(c)(1) three-year review period, gave States a last chance to correct this deficiency on their own. The legislative history of the provision demonstrates that chief Senate sponsors, including Senators Stafford, Chaffee and others wanted the provision to eliminate State and EPA delays and force quick action. Thus, to interpret CWA section 303(c)(2)(B) and (c)(4) to require such a cumbersome pollutant specific effort on each stream segment would essentially render section 303(c)(2)(B) meaningless. The provision and its legislative background
indicate that the Administrator’s
determination to invoke section 303(c)(4)(B) authority can be met by the Administrator making a generic finding of inaction by the State without the need to develop pollutant specific data for individual stream segments. Finally, the reference in section 303(c)(2)(B) to section 304(a) criteria suggests that section 304(a) criteria serve as default criteria; that once EPA has issued them, States were to adopt numeric criteria for those pollutants based on the 304(a) criteria, unless they had other scientifically defensible criteria. EPA
also notes that this rule follows the approach EPA took nationally in promulgating the NTR for States that failed to comply with CWA section 303(c)(2)(B). 57 FR 60848, December 22, 1992. EPA incorporates the discussion in the NTR preamble as part of this rulemaking record.

This determination is supported by information in the rulemaking record showing the discharge or presence of priority toxic pollutants throughout the State. While this data is not necessarily complete, it constitutes a strong record supporting the need for numeric criteria for priority toxic pollutants with section 304(a) criteria guidance where the State
does not have numeric criteria.

Today’s final rule would not impose any undue or inappropriate burden on the State of California or its dischargers. It merely puts in place numeric criteria


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for toxic pollutants that are already used in other States in implementing CWA programs. Under this rulemaking, the State of California retains the ability to adopt alternative water quality criteria simply by completing its criteria adoption process. Upon EPA approval of those criteria, EPA will initiate action to stay the Federally-promulgated criteria and subsequently withdraw
them.

2. Approach for Developing This Rule

In summary, EPA developed the criteria promulgated in today’s final rule as follows. Where EPA promulgated criteria for California in the NTR, EPA
has not acted to amend the criteria in
the NTR. Where criteria for California were not included in the NTR, EPA used section 304(a) National criteria guidance documents as a starting point for the criteria promulgated in this rule.
EPA then determined whether new information since the development of the national criteria guidance documents warranted any changes. New information came primarily from two sources. For human health criteria, new
or revised risk reference doses and cancer potency factors on EPA’s Integrated Risk Information System (IRIS) as of October 1996 form the basis for criteria values (see also 63 FR 68354). For aquatic life criteria, updated data sets resulting in revised criteria maximum concentrations (CMCs) and

criteria continuous concentrations (CCCs) formed the basis for differences from the national criteria guidance documents. Both of these types of changes are discussed in more detail in the following sections. This revised information was used to develop the water quality criteria promulgated here
for the State of California.

F. Derivation of Criteria

1. Section 304(a) Criteria Guidance

Process

Under CWA section 304(a), EPA has developed methodologies and specific criteria guidance to protect aquatic life and human health. These methodologies are intended to provide protection for
all surface waters on a national basis. The methodologies have been subject to public review, as have the individual criteria guidance documents. Additionally, the methodologies have been reviewed by EPA’s Science Advisory Board (SAB) of external
experts.

EPA has included in the record of this rule the aquatic life methodology as described in ‘‘Appendix B—Guidelines for Deriving Water Quality Criteria for the Protection of Aquatic Life and Its Uses’’ to the ‘‘Water Quality Criteria Documents; Availability’’ (45 FR 79341, November 28, 1980) as amended by the ‘‘Summary of Revisions to Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses’’ (50 FR 30792, July 29, 1985). (Note: Throughout the remainder of this preamble, this reference is described as the 1985 Guidelines. Any page number references are to the actual guidance document, not the notice of availability
in the Federal Register . A copy of the 1985 Guidelines is available through the
National Technical Information Service (PB85–227049), is in the administrative record for this rule, and is abstracted in Appendix A of Quality Criteria for
Water, 1986.) EPA has also included in
the administrative record of this rule the human health methodology as described in ‘‘Appendix C—Guidelines and Methodology Used in the Preparation of Health Effects Assessment Chapters of
the Consent Decree Water Criteria Documents’’ (45 FR 79347, November 28, 1980). (Note: Throughout the remainder of this preamble, this
reference is described as the Human
Health Guidelines or the 1980 Guidelines.) EPA also recommends that the following be reviewed: ‘‘Appendix D—Response to Comments on Guidelines for Deriving Water Quality Criteria for the Protection of Aquatic Life and Its Uses,’’ (45 FR 79357, November 28, 1980); ‘‘Appendix E— Responses to Public Comments on the Human Health Effects Methodology for Deriving Ambient Water Quality Criteria’’ (45 FR 79368, November 28, 1980); and ‘‘Appendix B—Response to Comments on Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses’’ (50 FR 30793, July 29, 1985). EPA placed into
the administrative record for this rulemaking the most current individual criteria guidance for the priority toxic pollutants included in today’s rule. (Note: All references to appendices are
to the associated Federal Register publication.)

EPA received many comments related
to the issue of what criteria should apply in the CTR if the CWA section 304(a) criteria guidance is undergoing re-evaluation, or if new data are developed that may affect a
recommended criterion. As science is always evolving, EPA is faced with the challenge of promulgating criteria that
reflect the best science and sound science. EPA addressed this challenge
in some detail in its Federal Register notice that contained the Agency’s current section 304(a) criteria guidance (63 FR 68335, December 10, 1998). There, EPA articulated its policy, reiterated here, that the existing criteria guidance represent the Agency’s best
assessment until such time as EPA’s reevaluation of a criteria guidance value for a particular chemical is complete.
The reason for this is that both EPA’s human health criteria guidance and aquatic life criteria guidance are developed taking into account numerous variables. For example, for human health criteria guidance, EPA evaluates many diverse toxicity studies,
whose results feed into a reference dose or cancer potency estimate that, along with a number of exposure factors and determination of risk level, results in a guidance criterion. For aquatic life, EPA evaluates many diverse aquatic toxicity
studies to determine chronic and acute toxicity taking into account how other factors (such as pH, temperature or hardness) affect toxicity. EPA also, to the extent possible, addresses
bioaccumulation or bioconcentration. EPA then uses this toxicity information along with exposure information to determine the guidance criterion. Importantly, EPA subjects such evaluation to peer review and/or public

comment.

For these reasons, EPA generally does not make a change to the 304(a) criteria guidance based on a partial picture of the evolving science. This makes sense, because to address one piece of new data without looking at all relevant data is less efficient and results in regulatory impacts that may go back and forth, when in the end, the criteria guidance value does not change that much. Certain new changes, however, do warrant change in criteria guidance, such as a change in a value in EPA’s Integrated Risk Information System (IRIS) because it represents the Agency consensus about human health impacts. These changes are sufficiently examined across the Agency such that EPA believes they can be incorporated into EPA’s water quality criteria guidance. EPA has followed this approach in the
CTR. Included in the administrative record for today’s rule is a document
entitled ‘‘Status of Clean Water Act Section 304(a) Criteria’’ which further explains EPA’s policy on managing change to criteria guidance.

2. Aquatic Life Criteria

Aquatic life criteria may be expressed
in numeric or narrative form. EPA’s 1985 Guidelines describe an objective, internally consistent and appropriate way of deriving chemical-specific, numeric water quality criteria for the protection of the presence of, as well as


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the uses of, both fresh and salt water aquatic organisms.

An aquatic life criterion derived using EPA’s CWA section 304(a) method ‘‘might be thought of as an estimate of the highest concentration of a substance in water which does not present a significant risk to the aquatic organisms in the water and their uses.’’ (45 FR 79341.) EPA’s guidelines are designed to derive criteria that protect aquatic
communities. EPA’s 1985 Guidelines attempt to provide a reasonable and adequate amount of protection with only a small possibility of substantial overprotection or underprotection. As discussed in detail below, there are several individual factors which may
make the criteria somewhat overprotective or underprotective. The approach EPA is using is believed to be as well balanced as possible, given the
state of the science.

Numerical aquatic life criteria derived using EPA’s 1985 Guidelines are expressed as short-term and long-term averages, rather than one number, in order that the criterion more accurately reflect toxicological and practical
realities. The combination of a criterionmaximum concentration (CMC), a shortterm concentration limit, and a criterioncontinuous concentration (CCC), a fourday average concentration limit, are designed to provide protection of aquatic life and its uses from acute and chronic toxicity to animals and plants,without being as restrictive as a onenumber criterion would have to be (1985 Guidelines, pages 4 & 5). The
terms CMC and CCC are the formal names for the two (acute and chronic) values of a criterion for a pollutant; however, this document will also use the informal synonyms acute criterion
and chronic criterion.

The two-number criteria are intended to identify average pollutant concentrations which will produce water quality generally suited to maintenance of aquatic life and designated uses while restricting the duration of excursions over the average so that total exposures will not cause unacceptable adverse effects. Merely specifying an average value over a time period may be insufficient unless the time period is short, because excursions higher than the average may kill or cause substantial damage in short periods.

A minimum data set of eight specified
families is recommended for criteria development (details are given in the 1985 Guidelines, page 22). The eight specific families are intended to be representative of a wide spectrum of aquatic life. For this reason it is not necessary that the specific organisms tested be actually present in the water body. EPA’s application of its guidelines to develop the criteria matrix in this rule is judged by the Agency to be appropriate for all waters of the United States (U.S.), and to all ecosystems (1985 Guidelines, page 4) including those waters of the U.S. and ecosystems
in the State of California.

Fresh water and salt water (including both estuarine and marine waters) have different chemical compositions, and freshwater and saltwater species often
do not inhabit the same water. To provide additional accuracy, criteria are developed for fresh water and for salt

water.

For this rule, EPA updated freshwater aquatic life criteria contained in CWA section 304(a) criteria guidance first published in the early 1980’s and later modified in the NTR, as amended, for the following ten pollutants: arsenic, cadmium, chromium (VI), copper, dieldrin, endrin, lindane (gamma BHC), nickel, pentachlorophenol, and zinc. The updates used as the basis for this rule are explained in a technical support document entitled, 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient

Water (U.S. EPA–820–B–96–001, September 1996), available in the
administrative record to this rulemaking; this document presents the
derivation of each of the final CMCs and CCCs and the toxicity studies from which the updated freshwater criteria for the ten pollutants were derived.

The polychlorinated biphenyls (PCB)
criteria in the criteria matrix for this rule differs from that in the NTR, as amended; for this rule, the criteria are expressed as the sum of seven aroclors, while for the NTR, as amended, the criteria are expressed for each of seven aroclors. The aquatic life criteria for
PCBs in the CTR are based on the
criteria contained in the 1980 criteria guidance document for PCBs which is
included in the administrative record
for this rule. This criteria document explains the derivation of aquatic life
criteria based on total PCBs. For more information see the Response to
Comments document for this rule. Today’s chronic aquatic life criteria for
PCBs are based on a final residue value (FRV). In EPA’s guidelines for deriving aquatic life criteria, an FRV-based criterion is intended to prevent concentrations of pollutants in commercially or recreationally important aquatic species from affecting the marketability of those species or affecting the wildlife that consume aquatic life.

The proposed CTR included an updated freshwater and saltwater aquatic life criteria for mercury. In today’s final rule, EPA has reserved the mercury criteria for freshwater and saltwater aquatic life, but is promulgating human health criteria for mercury for all surface waters in California. In some instances, the human health mercury criteria included in today’s final rule may not protect some aquatic species or threatened or endangered species. In such instances, more stringent mercury limits may be determined and implemented through
use of the State’s narrative criterion. The reasons for reserving the mercury aquatic life numbers are explained in further detail in Section L, Endangered Species Act.

a. Freshwater Acute Selenium Criterion

EPA proposed a different freshwater acute aquatic life criterion for selenium for this rule than was promulgated in the NTR, as amended. EPA’s proposed
action was consistent with EPA’s proposed selenium criterion maximum concentration for the Water Quality Guidance for the Great Lakes System (61 FR 58444, November 14, 1996). This proposal took into account data showing that selenium’s two most prevalent oxidation states, selenite and selenate, present differing potentials for aquatic toxicity, as well as new data which
indicated that various forms of selenium are additive. Additivity increases the toxicity of mixtures of different forms of the pollutant. The proposed approach produces a different selenium acute
criterion concentration, or CMC, depending upon the relative proportions of selenite, selenate, and other forms of selenium that are present.

The preamble to the August 5, 1997, proposed rule provided a lengthy discussion of this proposed criterion for
the State of California. See 62 FR 42160–42208. EPA incorporates that discussion here as part of this rulemaking record. In 1996, a similar
discussion was included in the proposed rule for the Great Lakes System. Commenters questioned several aspects of the Great Lakes proposal. EPA is continuing to respond to those comments, and to follow up with additional literature review and toxicity testing. In addition, the U.S. FWS and U.S. NMFS (collectively, the Services) are concerned that EPA’s proposed criterion may not be sufficiently protective of certain threatened and endangered species in California.
Because the Services believe there is a
lack of data to show for certain that the proposed criterion would not affect threatened and endangered species, the Services prefer that EPA further investigate the protectiveness of the


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criterion before finalizing the proposed criterion. Therefore, EPA is not promulgating a final acute freshwater
selenium criterion at this time.

b. Dissolved Metals Criteria

In December of 1992, in the NTR, EPA promulgated water quality criteria for
several States that had failed to meet the requirements of CWA section 303(c)(2)(B). Included among the water quality criteria promulgated were numeric criteria for the protection of aquatic life for 11 metals: arsenic, cadmium, chromium (III), chromium (VI), copper, lead, mercury, nickel, selenium, silver and zinc. Criteria for two metals applied to the State of
California: chromium III and selenium.

The Agency received extensive public comment during the development of the NTR regarding the most appropriate approach for expressing the aquatic life metals criteria. The principal issue was
the correlation between metals that are
measured and metals that are bioavailable and toxic to aquatic life. It is now the Agency’s policy that the use
of dissolved metal to set and measure compliance with aquatic life water quality standards is the recommended approach, because dissolved metal more closely approximates the bioavailable
fraction of the metal in the water
column than does total recoverable
metal.

Since EPA’s previous aquatic life criteria guidance had been expressed as total recoverable metal, to express the criteria as dissolved, conversion factors were developed to account for the possible presence of particulate metal in the laboratory toxicity tests used to develop the total recoverable criteria.
EPA included a set of recommended
freshwater conversion factors with its Metals Policy (see Office of Water Policy
and Technical Guidance on Interpretation and Implementation of Aquatic Life Metals Criteria, Martha G. Prothro, Acting Assistant Administrator for Water, October 1, 1993). Based on additional laboratory evaluations that simulated the original toxicity tests, EPA refined the procedures used to develop freshwater conversion factors for aquatic life criteria. These new
conversion factors were made available for public review and comment in the amendments to the NTR on May 4, 1995, at 60 FR 22229. They are also contained in today’s rule at 40 CFR 131.38(b)(2).

The preamble to the August 5, 1997, proposed rule provided a more detailed discussion of EPA’s metals policy concerning the aquatic life water quality
criteria for the State of California. See 62 FR 42160–42208. EPA incorporates that discussion here as part of this rulemaking record. Many commenters strongly supported the Agency’s policy on dissolved metals aquatic life criteria. A few commenters expressed an opinion that the metals policy may not provide criteria that are adequately protective of aquatic or other species. Responses to those comments are
contained in a memo to the CTR record
entitled ‘‘Discussion of the Use of Dissolved Metals in the CTR’’ (February 1, 2000, Jeanette Wiltse) and EPA’s response to comments document which
are both contained in the administrative
record for the final rule.

Calculation of Aquatic Life Dissolved
Metals Criteria: Metals criteria values for aquatic life in today’s rule in the matrix at 131.38(b)(1) are shown as
dissolved metal. These criteria have been calculated in one of two ways. For
freshwater metals criteria that are hardness-dependent, the metals criteria value is calculated separately for each hardness using the table at 40 CFR 131.38(b)(2). (The hardness-dependent freshwater values presented in the matrix at 40 CFR 131.38(b)(1) have been calculated using a hardness of 100 mg/ l as CaCO3 for illustrative purposes only.) The hardness-dependent criteria are then multiplied by the appropriate
conversion factors in the table at 40 CFR 131.38(b)(2). Saltwater and freshwater
metals criteria that are not hardnessdependent are calculated by taking the total recoverable criteria values (from EPA’s national section 304(a) criteria guidance, as updated and described in section F.2.a.) before rounding, and multiplying them by the appropriate
conversion factors. The final dissolved metals criteria values, as they appear in the matrix at 40 CFR 131.38(b)(1), are rounded to two significant figures.

Translators for Dissolved to Total
Recoverable Metals Limits: EPA’s National Pollutant Discharge Elimination System (NPDES) regulations require that limits for metals in permits be stated as total recoverable in most cases (see 40 CFR 122.45(c)) except when an effluent guideline specifies the limitation in another form of the metal, the approved analytical methods measure only dissolved metal, or the permit writer expresses a metal’s limit in another form ( e.g., dissolved, specific valence, or total) when required to carry out provisions of the CWA. This
is because the chemical conditions in ambient waters frequently differ substantially from those in the effluent and these differences result in changes in the partitioning between dissolved
and absorbed forms of the metal. This
means that if effluent limits were expressed in the dissolved form, additional particulate metal could dissolve in the receiving water causing the criteria to be exceeded. Expressing criteria as dissolved metal requires
translation between different metal forms in the calculation of the permit limit so that a total recoverable permit
limit can be established that will achieve water quality standards. Thus, it is important that permitting authorities and other authorities have the ability to
translate between dissolved metal in
ambient waters and total recoverable
metal in effluent.

EPA has completed guidance on the
use of translators to convert from
dissolved metals criteria to total recoverable permit limits. The document, The Metals Translator: Guidance for Calculating a Total
Recoverable Permit Limit From a
Dissolved Criterion (EPA 823–B–96– 007, June 1996), is included in the administrative record for today’s rule. This technical guidance examines how to develop a metals translator which is
defined as the fraction of total
recoverable metal in the downstream water that is dissolved, i.e., the
dissolved metal concentration divided by the total recoverable metal concentration. A translator may take one of three forms: (1) It may be assumed to be equivalent to the criteria guidance conversion factors; (2) it may be developed directly as the ratio of dissolved to total recoverable metal; and (3) it may be developed through the use of a partition coefficient that is functionally related to the number of metal binding sites on the adsorbent in the water column ( e.g., concentrations of total suspended solids or TSS). This guidance document discusses these three forms of translators, as well as field study designs, data generation and analysis, and site-specific study plans to generate site-specific translators.

California Regional Water Quality Control Boards may use any of thesemethods in developing water qualitybased permit limits to meet water quality standards based on dissolved metals criteria. EPA encourages the State to adopt a statewide policy on the
use of translators so that the most appropriate method or methods are used consistently within California.

c. Application of Metals Criteria

In selecting an approach for implementing the metals criteria, the principal issue is the correlation
between metals that are measured and metals that are biologically available
and toxic. In order to assure that the metals criteria are appropriate for the chemical conditions under which they are applied, EPA is providing for the


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adjustment of the criteria through application of the ‘‘water-effect ratio’’ procedure. EPA notes that performingthe testing to use a site-specific watereffect ratio is optional on the part of the

State.

In the NTR, as amended, EPA identified the water-effect ratio (WER)procedure as a method for optional sitespecific criteria development for certain metals. The WER approach compares bioavailability and toxicity of a specific pollutant in receiving waters and in laboratory waters. A WER is an appropriate measure of the toxicity of a
material obtained in a site water divided by the same measure of the toxicity of
the same material obtained simultaneously in a laboratory dilution

water.

On February 22, 1994, EPA issued
Interim Guidance on the Determination and Use of the Water-Effect Ratios for
Metals (EPA 823-B–94–001) now incorporated into the updated Second Edition of the Water Quality Standards Handbook, Appendix L. A copy of the
Handbook is contained in the administrative record for today’s rule. In accordance with the WER guidance and where application of the WER is deemed appropriate, EPA strongly encourages the application of the WER on a watershed or water body basis as part of a water quality criteria in California as opposed to the application on a discharger-by-discharger basis through individual NPDES permits. This approach is technically sound and an efficient use of resources. However, discharger specific WERs for individual NPDES permit limits are possible and potentially efficient where the NPDES discharger is the only point source discharger to a specific water body.

The rule requires a default WER valueof 1.0 which will be assumed, if no sitespecific WER is determined. To use a WER other than the default of 1.0, the rule requires that the WER must be
determined as set forth in EPA’s WER guidance or by another scientifically
defensible method that has been adopted by the State as part of its water quality standards program and approved by EPA.

The WER is a more comprehensive mechanism for addressing bioavailability issues than simply expressing the criteria in terms of dissolved metal. Consequently, expressing the criteria in terms of dissolved metal, as done in today’s rule for California, does not completely eliminate the utility of the WER. This is particularly true for copper, a metal that forms reduced-toxicity complexes with dissolved organic matter. The Interim Guidance on Determination and Use of Water-Effect Ratios for Metals explains the relationship between WERs for
dissolved criteria and WERs for total
recoverable criteria. Dissolved
measurements are to be used in the sitespecific toxicity testing underlying the
WERs for dissolved criteria. Because WERs for dissolved criteria generally are little affected by elevated particulate concentrations, EPA expects those
WERs to be somewhat less than WERs
for total recoverable criteria in suchsituations. Nevertheless, after the sitespecific ratio of dissolved to total metal has been taken into account, EPA expects a permit limit derived using a
WER for a dissolved criterion to be similar to the permit limit that would be
derived from the WER for the corresponding total recoverable

criterion.

d. Saltwater Copper Criteria

The saltwater copper criteria for aquatic life in today’s rule are 4.8 μg/l (CMC) and 3.1 μg/l (CCC) in the
dissolved form. These criteria reflect new data including data collected from studies for the New York/New Jersey Harbor and the San Francisco Bay indicating a need to revise the former copper 304(a) criteria guidance document to reflect a change in the saltwater CMC and CCC aquatic life
values. These data also reflect a comprehensive literature search resulting in added toxicity test data for seven new species to the database for the saltwater copper criteria. EPA
believes these new data have national implications and the national criteria guidance now contains a CMC of 4.8 μg/
l dissolved and a CCC of 3.1 μg/l
dissolved. In the amendments to the NTR, EPA noticed the availability of data to support these changes to the NTR, and solicited comments. The data
can be found in the draft document entitled, Ambient Water Quality Criteria—Copper, Addendum 1995. This
document is available from the Office of
Water Resource Center and is available
for review in the administrative record for today’s rule.

e. Chronic Averaging Period

In establishing water quality criteria, EPA generally recommends an ‘‘averaging period’’ which reflects the duration of exposure required to elicit effects in individual organisms (TSD, Appendix D–2). The criteria continuous concentration, or CCC, is intended to be the highest concentration that could be maintained indefinitely in a water body without causing an unacceptable effect on the aquatic community or its uses (TSD, Appendix D–1). As aquatic organisms do not generally experience steady exposure, but rather fluctuating exposures to pollutants, and because aquatic organisms can generally tolerate higher concentrations of pollutants over a shorter periods of time, EPA expects that the concentration of a pollutant can exceed the CCC without causing an unacceptable effect if (a) the magnitude
and duration of exceedences are appropriately limited and (b) there are compensating periods of time during
which the concentration is below the CCC. This is done by specifying a duration of an ‘‘averaging period’’ over which the average concentration should
not exceed the CCC more often than specified by the frequency (TSD, Appendix D–1).

EPA is promulgating a 4-day averaging period for chronic criteria,
which means that measured or predicted ambient pollutant concentrations should be averaged over a 4-day period to determine attainment of chronic criteria. The State may apply to EPA for approval of an alternative averaging period. To do so, the State
must submit to EPA the basis for such alternative averaging period.

The most important consideration for setting an appropriate averaging period is the length of time that sensitive organisms can tolerate exposure to a pollutant at levels exceeding a criterion without showing adverse effects on survival, growth, or reproduction. EPA believes that the chronic averaging period must be shorter than the duration
of the chronic tests on which the CCC is based, since, in some cases, effects are elicited before exposure of the entire duration. Most of the toxicity tests used
to establish the chronic criteria are conducted using steady exposure to toxicants for a least 28 days (TSD, page 35). Some chronic tests, however, are much shorter than this (TSD, Appendix D–2). EPA selected the 4-day averaging period based on the shortest duration in
which chronic test effects are sometimes observed for certain species and toxicants. In addition, EPA believes that
the results of some chronic tests are due to an acute effect on a sensitive life stage that occurs some time during the test, rather than being caused by long-term stress or long-term accumulation of the test material in the organisms.

Additional discussion of the rationale for the 4-day averaging period is contained in Appendix D of the TSD. Balancing all of the above factors and data, EPA believes that the 4-day averaging period falls within the scientifically reasonable range of values for choice of the averaging period, and is an appropriate length of time of


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pollutant exposure to ensure protection of sensitive organisms.

EPA established a 4-day averaging period in the NTR. In settlement of litigation on the NTR, EPA stated that it was ‘‘in the midst of conducting, sponsoring, or planning research related to the basis for and application of’’ water quality criteria and mentioned the issue of averaging period. See Partial Settlement Agreement in American Forest and Paper Ass’n, Inc. et al. v. U.S. EPA (Consolidated Case No. 93–0694 (RMU), D.D.C.). EPA is reevaluating issues raised about averaging periods and will, if appropriate, revise
the 1985 Guidelines.

EPA received public comment relevant to the averaging period during the comment period for the 1995 Amendments to the NTR (60 FR 22228, May 4, 1995), although these public
comments did not address the chronic averaging period separately from the allowable excursion frequency and the design flow. Comments recommended that EPA use the 30Q5 design flow for
chronic criteria.

While EPA is undertaking analysis of the chronic design conditions as part of the revisions to the 1985 Guidelines, EPA has not yet completed this work. Until this work is complete, for the reasons set forth in the TSD, EPA continues to believe that the 4-day chronic averaging period represents a reasonable, defensible value for this
parameter.

EPA added language to the final rule which will enable the State to adopt alternative averaging periods and frequencies and associated design flows where appropriate. The State may apply to EPA for approval of alternative averaging periods and frequencies and related design flows; the State must submit the bases for any changes. Before approving any change, EPA will publish for public comment, a notice proposing the changes.

f. Hardness

Freshwater aquatic life criteria for certain metals are expressed as a
function of hardness because hardness and/or water quality characteristics that are usually correlated with hardness can
reduce or increase the toxicities of some metals. Hardness is used as a surrogate for a number of water quality characteristics which affect the toxicity of metals in a variety of ways. Increasing hardness has the effect of decreasing the toxicity of metals. Water quality criteria to protect aquatic life may be calculated
at different concentrations of hardnesses measured in milligrams per liter (mg/l) as calcium carbonate (CaCO 3 ). Section 131.38(b)(2) of the final rule presents the hardness-dependent equations for freshwater metals criteria. For example, using the equation for zinc, the total recoverable CMCs at a hardness of 10, 50, 100 or 200 mg/l as

CaCO 3 are 17, 67, 120 and 220 micrograms per liter (μg/l), respectively. Thus, the specific value in the table in the regulatory text is for illustrative purposes only. Most of the data used to develop these hardness equations for deriving aquatic life criteria for metals were in the range of 25 mg/l to 400 mg/
l as CaCO 3 , and the formulas are therefore most accurate in this range. The majority of surface waters
nationwide and in California have a hardness of less than 400 mg/l as

CaCO 3

.

In the past, EPA generally recommended that 25 mg/l as CaCO 3 be
used as a default hardness value in deriving freshwater aquatic life criteria for metals when the ambient (or actual) hardness value is below 25 mg/l as

CaCO 3 . However, use of the approach results in criteria that may not be fully protective. Therefore, for waters with a hardness of less than 25 mg/l as CaCO 3 , criteria should be calculated using the
actual ambient hardness of the surface

water.

In the past, EPA generally
recommended that if the hardness was over 400 mg/l, two options were available: (1) Calculate the criterion using a default WER of 1.0 and using a hardness of 400 mg/l in the hardness equation; or (2) calculate the criterion using a WER and the actual ambient
hardness of the surface water in the equation. Use of the second option is expected to result in the level of protection intended in the 1985
Guidelines whereas use of the first option is thought to result in an even more protective aquatic life criterion. At high hardness there is an indication that hardness and related inorganic water quality characteristics do not have as much of an effect on toxicity of metals as they do at lower hardnesses. Related water quality characteristics do not correlate as well at higher hardnesses as they do at lower hardnesses. Therefore, if hardness is over 400 mg/l as CaCO 3 , a hardness of 400 mg/l as CaCO 3 should be used with a default WER of 1.0; alternatively, the WER and actual hardness of the surface water may be
used.

EPA requested comments in the NTR
amendments on the use of actual ambient hardness for calculating criteria when the hardness is below 25 mg/l as

CaCO 3 , and when hardness is greater than 400 mg/l as CaCO 3 . Most of the
comments received were in favor of using the actual hardness with the use of the water-effect ratio (1.0 unless otherwise specified by the permitting authority) when the hardness is greater than 400 mg/l as CaCO 3 . A few
commenters did not want the watereffect ratio to be mandatory in calculating hardness, and other commenters had concerns about being responsible for deriving an appropriate water-effect ratio. Overall, the commenters were in favor of using the actual hardness when calculating hardness-dependent freshwater metals criteria for hardness between 0–400 mg/
l as CaCO 3 . EPA took those comments into account in promulgating today’s
rule.

A hardness equation is most accurate when the relationships between hardness and the other important inorganic constituents, notably alkalinity and pH, are nearly identical
in all of the dilution waters used in the toxicity tests and in the surface waters to which the equation is to be applied.
If an effluent raises hardness but not alkalinity and/or pH, using the hardness of the downstream water might provide a lower level of protection than intended by the 1985 guidelines. If it appears that an effluent causes hardness to be inconsistent with alkalinity and/or pH, the intended level of protection will usually be maintained or exceeded if either (1) data are available to demonstrate that alkalinity and/or pH do not affect the toxicity of the metal, or (2) the hardness used in the hardness equation is the hardness of upstream
water that does not contain the effluent. The level of protection intended by the 1985 guidelines can also be provided by using the WER procedure.

In some cases, capping hardness at 400 mg/l might result in a level of protection that is higher than that intended by the 1985 guidelines, but any such increase in the level of protection can be overcome by use of the WER procedure. For metals whose criteria are expressed as hardness equations, use of the WER procedure will generally be intended to account for effects of such water quality characteristics as total organic carbon on
the toxicities of metals. The WER procedure is equally useful for accounting for any deviation from a hardness equation in a site water.

3. Human Health Criteria

EPA’s CWA section 304(a) human health criteria guidance provides
criteria recommendations to minimize
adverse human effects due to substances
in ambient water. EPA’s CWA section 304(a) criteria guidance for human health are based on two types of


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toxicological endpoints: (1) carcinogenicity and (2) systemic toxicity (i.e., all other adverse effects other than cancer). Thus, there are two procedures for assessing these health effects: one forcarcinogens and one for noncarcinogens.

If there are no data on how a chemical agent causes cancer, EPA’s existing human health guidelines assume that carcinogenicity is a ‘‘non-threshold phenomenon,’’ that is, there are no
‘‘safe’’ or ‘‘no-effect levels’’ because even extremely small doses are assumed
to cause a finite increase in the incidence of the effect (i.e., cancer). Therefore, EPA’s water quality criteria guidance for carcinogens are presented as pollutant concentrations corresponding to increases in the risk of developing cancer. See Human Health
Guidelines at 45 FR 79347.

With existing criteria, pollutants that do not manifest any apparent carcinogenic effect in animal studies (i.e., systemic toxicants), EPA assumes that the pollutant has a threshold below
which no effect will be observed. This assumption is based on the premise that a physiological mechanism exists within living organisms to avoid or
overcome the adverse effect of the pollutant below the threshold

concentration.

Note: Recent changes in the Agency’s cancer guidelines addressing these assumptions are described in the Draft Water Quality Criteria Methodology: Human Health, 63 FR 43756, August 14, 1998.

The human health risks of a substance cannot be determined with any degree of confidence unless dose-response relationships are quantified. Therefore, a dose-response assessment is required
before a criterion can be calculated. The dose-response assessment determines the quantitative relationships between the amount of exposure to a substance and the onset of toxic injury or disease. Data for determining dose-response relationships are typically derived from animal studies, or less frequently, from epidemiological studies in exposed populations.

The dose-response information needed for carcinogens is an estimate of the carcinogenic potency of the compound. Carcinogenic potency is defined here as a general term for a chemical’s human cancer-causing potential. This term is often used loosely to refer to the more specific carcinogenic or cancer slope factor
which is defined as an estimate of carcinogenic potency derived from animal studies or epidemiological data of human exposure. It is based on extrapolation from test exposures of high doses over relatively short periods of time to more realistic low doses over a lifetime exposure period by use of linear extrapolation models. The cancer slope factor, q1*, is EPA’s estimate of carcinogenic potency and is intended to be a conservative upper bound estimate (e.g. 95% upper bound confidence limit).

For non-carcinogens, EPA uses thereference dose (RfD) as the doseresponse parameter in calculating the criteria. For non-carcinogens, oral RfD assessments (hereinafter simply ‘‘RfDs’’) are developed based on pollutant
concentrations that cause threshold effects. The RfD is an estimate (with uncertainty spanning perhaps an order of magnitude) of a daily exposure to the human population (including sensitive subgroups) that is likely to be without appreciable risk of deleterious effects during a lifetime. See Human Health Guidelines. The RfD was formerly referred to as an ‘‘Acceptable Daily
Intake’’ or ADI. The RfD is useful as a reference point for gauging the potential
effect of other doses. Doses that are less than the RfD are not likely to be associated with any health risks, and are therefore less likely to be of regulatory concern. As the frequency of exposures exceeding the RfD increases and as the size of the excess increases, the probability increases that adverse effect may be observed in a human population. Nonetheless, a clear conclusion cannot be categorically
drawn that all doses below the RfD are ‘‘acceptable’’ and that all doses in excess of the RfD are ‘‘unacceptable.’’ In extrapolating non-carcinogen animal test data to humans to derive an RfD,
EPA divides either a No ObservedAdverse Effect Level (NOAEL), Lowest Observed Adverse Effect Level (LOAEL),
or other benchmark dose observed in animal studies by an ‘‘uncertainty factor’’ which is based on professional judgment of toxicologists and typically ranges from 10 to 10,000.

For CWA section 304(a) human health criteria development, EPA typically considers only exposures to a pollutant that occur through the ingestion of
water and contaminated fish and shellfish. Thus, the criteria are based on
an assessment of risks related to the surface water exposure route only where designated uses are drinking water and fish and shellfish consumption.

The assumed exposure pathways in calculating the criteria are the consumption of 2 liters per day of water
at the criteria concentration and the consumption of 6.5 grams per day of
fish and shellfish contaminated at a level equal to the criteria concentration but multiplied by a ‘‘bioconcentration
factor.’’ The use of fish and shellfish consumption as an exposure factor requires the quantification of pollutant residues in the edible portions of the ingested species.

Bioconcentration factors (BCFs) are used to relate pollutant residues in aquatic organisms to the pollutant
concentration in ambient waters. BCFs are quantified by various procedures depending on the lipid solubility of the pollutant. For lipid soluble pollutants, the average BCF is calculated from the weighted average percent lipids in the edible portions of fish and shellfish, which is about 3%; or it is calculated from theoretical considerations using the octanol/water partition coefficient. For non-lipid soluble compounds, the BCF is determined empirically. The assumed water consumption is taken from the National Academy of Sciences publication Drinking Water and Health (1977). (Referenced in the Human Health Guidelines.) This value is appropriate as it includes a margin of safety so that the general population is protected. See also EPA’s discussion of the 2.0 liters/day assumption at 61 FR 65183 (Dec. 11, 1996). The 6.5 grams per day contaminated fish and shellfish consumption value was equivalent to the average per-capita consumption rateof all (contaminated and noncontaminated) freshwater and estuarine
fish and shellfish for the U.S. population. See Human Health
Guidelines.

EPA assumes in calculating water quality criteria that the exposed individual is an average adult with body weight of 70 kilograms. EPA assumes 6.5 grams per day of contaminated fish and shellfish consumption and 2.0 liters per day of contaminated drinking water consumption for a 70 kilogram person in calculating the criteria. Regarding issues concerning criteria development and differences in dose per kilogram of body weight, RfDs are always derived
based on the most sensitive health effect endpoint. Therefore, when that basis is
due to a chronic or lifetime health effect, the exposure parameters assume the exposed individual to be the average adult, as indicated above.

In the absence of this final rule, there may be particular risks to children. EPA believes that children are protected by
the human health criteria contained in this final rule. Children are protected against other less sensitive adverse health endpoints due to the conservative way that the RfDs are derived. An RfD is a public health protective endpoint. It is an amount of
a chemical that can be consumed on a daily basis for a lifetime without expecting an adverse effect. RfDs are based on sensitive health endpoints and


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are calculated to be protective for sensitive human sub-populations including children. If the basis of the
RfD was due to an acute or shorter-term developmental effect, EPA uses exposure parameters other than those indicated above. Specifically, EPA uses parameters most representative of the population of concern ( e.g., the health
criteria for nitrates based on infant exposure parameters). For carcinogens, the risk assessments are upper bound one in a million (10

¥ 6) lifetime risk
numbers. The risk to children is not likely to exceed these upper bounds estimates and may be zero at low doses. The exposure assumptions for drinking water and fish protect children because they are conservative for infants and
children. EPA assumes 2 liters of untreated surface water and 6.5 grams of
freshwater and estuarine fish are consumed each day. EPA believes the adult fish consumption assumption is
conservative for children because children generally consume marine fish
not freshwater and estuarine.

EPA has a process to develop a
scientific consensus on oral reference dose assessments and carcinogenicity assessments (hereinafter simply cancer slope factors or slope factors or q1*s). Through this process, EPA develops a consensus of Agency opinion which is then used throughout EPA in risk management decision-making. EPA
maintains an electronic data base which contains the official Agency consensus
for oral RfD assessments and carcinogenicity assessments which is known as the Integrated Risk Information System (IRIS). It is available for use by the public on the National Institutes of Health’s National Library of Medicine’s TOXNET system, and through diskettes from the National Technical Information Service (NTIS). (NTIS access number is PB 90–591330.)

Section 304(a)(1) of the CWA requires EPA to periodically revise its criteria guidance to reflect the latest scientific knowledge: ‘‘(A) On the kind and extent
of all identifiable effects on health and welfare * * *; (B) on the concentration and dispersal of pollutants, or their byproducts, through biological, physical, and chemical processes; and (C) on the effects of pollutants on the biological community diversity, productivity, and stability, including information on the factors affecting eutrophication rates of organic and inorganic sedimentation for varying types of receiving waters.’’ In developing up-to-date water quality criteria for the protection of human health, EPA uses the most recent IRIS values (RfDs and q1*s) as the toxicological basis in the criterion calculation. IRIS reflects EPA’s most current consensus on the toxicological
assessment for a chemical. In developing the criteria in today’s rule,
the IRIS values as of October 1996 were used together with currently accepted exposure parameters for bioconcentration, fish and shellfish and water consumption, and body weight. The IRIS cover sheet for each pollutant criteria included in today’s rule is
contained in the administrative record.

For the human health criteria included in today’s rule, EPA used the
Human Health Guidelines on which
criteria recommendations from the appropriate CWA section 304(a) criteria guidance document were based. (These documents are also placed in the administrative record for today’s rule.) Where EPA has changed any parameters
in IRIS used in criteria derivation since issuance of the criteria guidance document, EPA recalculated the criteria
recommendation with the latest IRIS information. Thus, there are differences between the original 1980 criteria guidance document recommendations, and those in this rule, but this rule presents EPA’s most current CWA section 304(a) criteria recommendation. The basis (q1* or RfD) and BCF for each pollutant criterion in today’s rule is
contained in the rule’s Administrative
Record Matrix which is included in the
administrative record for the rule. In addition, all recalculated human health numbers are denoted by an ‘‘a’’ in the criteria matrix in 40 CFR 131.38(b)(1) of the rule. The pollutants for which a
revised human health criterion has been
calculated since the December 1992
NTR include:

mercury dichlorobromomethane 1,2-dichloropropane 1,2-trans-dichloroethylene 2,4-dimethylphenol acenaphthene benzo(a)anthracene benzo(a)pyrene benzo(b)flouranthene benzo(k)flouranthene 2-chloronaphthalene chrysene dibenzo(a,h)anthracene indeno(1,2,3-cd)pyrene N-nitrosodi-n-propylamine alpha-endosulfan

beta-endosulfan

endosulfan sulfate 2-chlorophenol butylbenzyl phthalate polychlorinated biphenyls.

In November of 1991, the proposed NTR presented criteria for several pollutants in parentheses. These were pollutants for which, in 1980,
insufficient information existed to develop human health water quality criteria, but for which, in 1991,
sufficient information existed. Since these criteria did not undergo the public
review and comment in a manner similar to the other water quality criteria presented in the NTR (for which
sufficient information was available in 1980 to develop a criterion, as presented in the 1980 criteria guidance documents), they were not proposed for adoption into the water quality criteria, but were presented to serve as notice for
inclusion in future State triennial reviews. Today’s rule promulgates criteria for these nine pollutants:

copper 1, 2-dichloropropane 1,2-trans-dichloroethylene 2,4-dimethylphenol acenaphthene 2-chloronaphthalene N-nitrosodi-n-propylamine 2-chlorophenol butylbenzene phthalate

All the criteria are based on IRIS values—either an RfD or q1*—which
were listed on IRIS as of November 1991, the date of the proposed NTR. These values have not changed since the final NTR was published in December of
1992. The rule’s Administrative Record
Matrix in the administrative record of today’s rule contains the specific RfDs, q1*s, and BCFs used in calculating
these criteria.

Proposed Changes to the Human Health Criteria Methodology: EPA recently proposed revisions to the 1980 ambient water quality criteria derivation guidelines (the Human Health Guidelines). See Draft Water Quality Criteria Methodology: Human Health, 63 FR 43756, August 14, 1998; see also Draft Water Quality Criteria Methodology: Human Health, U.S. EPA Office of Water, EPA 822–Z–98–001.
The EPA revisions consist of five
documents: Draft Water Quality Criteria Methodology: Human Health, EPA 822–
Z–98–001; Ambient Water Quality Criteria Derivation Methodology Human Health, Technical Support Document, Final Draft, EPA–822–B–98–005; and three Ambient Water Quality Criteria for the Protection of Human Health, Drafts—one each for Acrylonitrile, 1,3- Dichloropropene (1,3-DCP), and Hexachlorobutadiene (HCBD), respectively, EPA–822–R–98–006, –005,
and –004. All five documents are
contained in the administrative record for today’s rule.

The proposed methodology revisions reflect significant scientific advances that have occurred during the past nineteen years in such key areas as cancer and noncancer risk assessments, exposure assessments and bioaccumulation. For specific details on


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these proposed changes and others, please refer to the Federal Register
notice or the EPA document.

It should be noted that some of the proposed changes may result in significant numeric changes in the ambient water quality criteria. However, EPA will continue to rely on existing criteria as the basis for regulatory and non-regulatory decisions, until EPA revises and reissues a 304(a) criteria guidance using the revised final human health criteria methodology. The existing criteria are still viewed as scientifically acceptable by EPA. The intention of the proposed methodology revisions is to present the latest
scientific advancements in the areas of risk and exposure assessment in order to incrementally improve the already sound toxicological and exposure bases
for these criteria. As EPA’s current human health criteria are the product of many years worth of development and peer review, it is reasonable to assume that revisiting all existing criteria, and incorporating peer review into such review, could require comparable
amounts of time and resources. Given these circumstances, EPA proposed a process for revisiting these criteria as part of the overall revisions to the methodology for deriving human health criteria. This process is discussed in the Implementation Section of the Notice of Draft Revisions to the Methodology for Deriving Ambient Water Quality Criteria for the Protection of Human Health (see 63 FR 43771–43776, August 14, 1998).

The State of California in its Ocean Plan, adopted in 1990 and approved by EPA in 1991, established numeric water quality criteria using an average fish and shellfish consumption rate of 23 grams per day. This value is based on an earlier California Department of Health Services estimate. The State is currently in the process of readopting its water quality control plans for inland surface waters, enclosed bays, and estuaries.
The State intends to consider
information on fish and shellfish consumption rates evaluated and summarized in a report prepared by the
State’s Pesticide and Environmental Toxicology Section of the Office of
Environmental Health Hazard
Assessment of the California Environmental Protection Agency. The report, entitled, Chemicals in Fish Report No. 1: Consumption of Fish and Shellfish in California and the United States, was published in final draft form in July of 1997, and released to the public on September 16, 1997. The report is currently undergoing final evaluation, and is expected to published
in final form in the near future. This final draft report is contained in the administrative record for today’s rule. Although EPA has not used this fish consumption value here because this information has not yet been finalized, the State may use any appropriate higher state-specific fish and shellfish consumption rates in its readoption of criteria in its statewide plans.

a. 2,3,7,8-TCDD (Dioxin) Criteria

In today’s action, EPA is promulgating human health water quality criteria for 2,3,7,8-tetrachlorodibenzo-p-dioxin (‘‘dioxin’’) at the same levels as promulgated in the NTR, as amended.
These criteria are derived from EPA’s 1984 CWA section 304(a) criteria guidance document for dioxin.

For National Pollutant Discharge Elimination System (NPDES) purposes, EPA supports the regulation of other dioxin and dioxin-like compounds through the use of toxicity equivalencies or TEQs in NPDES permits (see discussion below). For California waters, if the discharge of dioxin or dioxin-like compounds has reasonable potential to cause or contribute to a violation of a narrative criterion, numeric water quality-based effluent
limits for dioxin or dioxin-like compounds should be included in NPDES permits and should be expressed using a TEQ scheme.

EPA has been evaluating the health threat posed by dioxin nearly continuously for over two decades. Following issuance of the 1984 criteria guidance document, evaluating the
health effects of dioxin and recommending human health criteria for dioxin, EPA prepared draft reassessments reviewing new scientific information relating to dioxin in 1985 and 1988. EPA’s Science Advisory Board (SAB), reviewing the 1988 draft reassessment, concluded that while the risk assessment approach used in 1984 criteria guidance document had inadequacies, a better alternative was unavailable (see SAB’s Dioxin Panel Review of Documents from the Office or Research and Development relating to the Risk and Exposure Assessment of
2,3,7,8-TCDD (EPA–SAB–EC–90–003, November 28, 1989) included in the administrative record for today’s rule). Between 1988 and 1990, EPA issued numerous reports and guidances relating to the control of dioxin discharges from pulp and paper mills. See e.g., EPA Memorandum, ‘‘Strategy for the Regulation of Discharges of PHDDs & PHDFs from Pulp and Paper
Mills to the Waters of the United States,’’ from Assistant Administrator for Water to Regional Water Management Division Directors and NPDES State Directors, dated May 21, 1990 (AR NL–16); EPA Memorandum, ‘‘State Policies, Water Quality Standards, and Permit Limitations Related to 2,3,7,8-TCDD in Surface Water,’’ from the Assistant Administrator for Water to Regional Water Management Division Directors, dated January 5, 1990 (AR VA–66).
These documents are available in the administrative record for today’s rule.

In 1991, EPA’s Administrator
announced another scientific reassessment of the risks of exposure to dioxin (see Memorandum from Administrator William K. Reilly to Erich W. Bretthauer, Assistant Administrator for Research and Development and E. Donald Elliott, General Counsel, entitled Dioxin: Follow-Up to Briefing on Scientific Developments, April 8, 1991,
included in the administrative record for today’s rule). At that time, the
Administrator made clear that while the reassessment was underway, EPA would continue to regulate dioxin in accordance with existing Agency policy. Thereafter, the Agency proceeded to regulate dioxin in a number of environmental programs, including standards under the Safe Drinking
Water Act and the CWA.

The Administrator’s promulgation of
the dioxin human health criteria in the 1992 NTR affirmed the Agency’s decision that the ongoing reassessment should not defer or delay regulating this potent contaminant, and further, that
the risk assessment in the 1984 criteria guidance document for dioxin continued to be scientifically defensible. Until the reassessment process was completed, the Agency could not ‘‘say with any certainty what the degree or directions of any changes in the risk estimates might be’’ (57 FR 60863–64).

The basis for the dioxin criteria as
well as the decision to include the dioxin criteria in the 1992 NTR pending
the results of the reassessment were challenged. See American Forest and Paper Ass’n, Inc. et al. v. U.S. EPA (Consolidated Case No. 93–0694 (RMU) D.D.C.). By order dated September 4, 1996, the Court upheld EPA’s decision.
EPA’s brief and the Court’s decision are
included in the administrative record for today’s rule.

EPA has undertaken significant effort toward completion of the dioxin reassessment. On September 13, 1994, EPA released for public review and
comment a draft reassessment of toxicity and exposure to dioxin. See Health Assessment Document for 2,3,7,8-Tetrachlorobenzo-p-Dioxin (TCDD) and Related Compounds, U.S. EPA, 1994. EPA is currently addressing comments made by the public and the SAB and anticipates that the final


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revised reassessment will go to the SAB in the near future. With today’s rule, the Agency reaffirms that, notwithstanding the on-going risk reassessment, EPA intends to continue to regulate dioxin to avoid further harm to public health, and the basis for the dioxin criteria, both in terms of the cancer potency and the exposure estimates, remains scientifically defensible. The fact that EPA is reassessing the risk of dioxin, virtually a continuous process to evaluate new scientific information,
does not mean that the current risk assessment is ‘‘wrong’’. It continues to be EPA’s position that until the risk assessment for dioxin is revised, EPA supports and will continue to use the existing risk assessment for the regulation of dioxin in the environment. Accordingly, EPA today promulgates
dioxin criteria based on the 1984 criteria guidance document for dioxin and promulgated in the NTR in 1992.

Toxicity Equivalency: The State of California, in its 1991 water quality control plans, adopted human health
criteria for dioxin and dioxin-like compounds based on the concept of toxicity equivalency (TEQ) using toxicity equivalency factors (TEFs). EPA Region 9 reviewed and approved the State’s use of the TEQ concept and TEFs in setting the State’s human health water quality criteria for dioxin and dioxin-like compounds.

In 1987, EPA formally embraced the TEQ concept as an interim procedure to
estimate the risks associated withexposures to 210 chlorinated dibenzo-pdioxin and chlorinated dibenzofuran (CDD/CDF) congeners, including 2,3,7,8-TCDD. This procedure uses a set
of derived TEFs to convert the concentration of any CDD/CDF congener into an equivalent concentration of 2,3,7,8-TCDD. In 1989, EPA updated its
TEFs based on an examination of
relevant scientific evidence and a recognition of the value of international consistency. This updated information
can be found in EPA’s 1989 Update to the Interim Procedures for Estimating Risks Associated with Exposures toMixtures of Chlorinated Dibenzo-pdioxins and -dibenzofurans (CDDs and CDFs) (EPA/625/3–89/016, March 1989). EPA had been active in an international effort aimed at adopting a common set of TEFs (International TEFs/89 or I–TEFs/89), to facilitate information exchange on environmental
contamination of CDD/CDF. This document reflects EPA’s support of an internationally consistent set of TEFs,
the I–TEFs/89. EPA uses I–TEFs/89 in many of its regulatory programs.

In 1994, the World Health Organization (WHO) revised the TEF scheme for dioxins and furans to include toxicity from dioxin-like compounds (Ahlborg et al., 1994). However, no changes were made to the TEFs for dioxins and furans. In 1998,
the WHO re-evaluated and revised the previously established TEFs for dioxins (Ds), furans (Fs) and dioxin-like compounds (Vanden Bers, 1998). The
nomenclature for this TEF scheme is TEQDFP–WHO98, where TEQ represents the 2,3,7,8-TCDD Toxic Equivalence of the mixture, and the subscript DFP indicates that dioxins (Ds) furans (Fs) and dioxin-like compounds (P) are included in the TEF scheme. The subscript 98 following WHO displays the year changes were
made to the TEF scheme.

EPA intends to use the 1998 WHO
TEF scheme in the near future. At this point however, EPA will support the
use of either the 1989 interim procedures or the 1998 WHO TEF scheme but encourages the use of the
1998 WHO TEF scheme in State programs. EPA expects California to use a TEF scheme in implementing the 2,3,7,8-TCDD water quality criteria contained in today’s rule. The TEQ and TEF approach provide a methodology for setting NPDES water quality-based permit limits that are protective of
human health for dioxin and dioxin-like compounds.

Several commenters requested EPA to promulgate criteria for other forms of dioxin, in addition to 2,3,7,8-TCDD.
EPA’s draft reassessment for dioxin examines toxicity based on the TEQ concept and I–TEFs/89. When EPA completes the dioxin reassessment, the Agency intends to adopt revised 304(a) water quality criteria guidance based on
the reassessment for dioxin. If necessary, EPA will then act to amend
the NTR and CTR to reflect the revised 304(a) water quality criteria guidance.

b. Arsenic Criteria

EPA is not promulgating human health criteria for arsenic in today’s rule. EPA recognizes that it promulgated human health water quality criteria for arsenic for a number of States in 1992, in the NTR, based on EPA’s 1980 section 304(a) criteria guidance for arsenic established, in part, from IRIS values current at that time. However, a
number of issues and uncertainties existed at the time of the CTR proposal concerning the health effects of arsenic.
These issues and uncertainties were
summarized in ‘‘Issues Related to
Health Risk of Arsenic’’ which is
contained in the administrative record for today’s rule. During the period of this rulemaking action, EPA commissioned a study of arsenic health effects by the National Research Council (NRC) arm of the National Academy of Sciences. EPA received the NRC report
in March of 1999. EPA scientists reviewed the report, which
recommended that EPA lower the Safe Drinking Water Act arsenic maximum contaminant level (MCL) as soon as possible (The arsenic MCL is currently

50 μg/l.) The bladder cancer analysis in the NRC report will provide part of the
basis for the risk assessment of a proposed revised arsenic MCL in the near future. After promulgating a revised MCL for drinking water, the Agency plans to revise the CWA 304(a)
human health criteria for arsenic in
order to harmonize the two standards. Today’s rule defers promulgating arsenic criteria based on the Agency’s previous risk assessment of skin cancer. In the meantime, permitting authorities in California should rely on existing narrative water quality criteria to
establish effluent limitations as necessary for arsenic. California has previously expressed its science and policy position by establishing a
criterion level of 5 μg/l for arsenic. Permitting authorities may, among other considerations, consider that value when evaluating and interpreting narrative water quality criteria.

c. Mercury Criteria

The human health criteria promulgated here use the latest RfD in EPA’s Integrated Risk Information System (IRIS) and the weighted average practical bioconcentration factor (PBCF) from the 1980 section 304(a) criteria guidance document for mercury. EPA considered the approach used in the Great Lakes Water Quality Guidance (‘‘Guidance’’) incorporating Bioaccumulation Factors (BAFs), but rejected this approach for reasons outlined below. The equation used here to derive an ambient water quality criterion for mercury from exposure to organisms and water is:



### HHC RfD BW

WC FC PBCF = ×

+ ×

( )

Where:

RfD = Reference Dose BW = Body Weight WC = Water Consumption FC = Total Fish and Shellfish Consumption per Day PBCF = Practical Bioconcentration Factor (weighted average) For mercury, the most current RfD
from IRIS is 1 x 10 -4 mg/kg/day. The RfD
used a benchmark dose as an estimate
of a No Observed Adverse Effect Level (NOAEL). The benchmark dose was calculated by applying a Weibel model


### 31697 Federal Register / Vol. 65, No. 97 / Thursday, May 18, 2000 / Rules and Regulations

for extra risk to all neurological effects observed in 81 Iraqi children exposed in utero as reported in Marsh, et. al. (1987). Maternal hair mercury was the measure of exposure. Extra risk refers to an adjustment for background incidence of a given health effect. Specifically, the
extra risk is the added incidence of observing an effect above the background rate relative to the proportion of the population of interest that is not expected to exhibit such as effect. The resulting estimate was the lower 95% statistical bound on the 10% extra risk; this was 11 ppm mercury in
maternal hair. This dose in hair was converted to an equivalent ingested amount by applying a model based on data from human studies; the resulting
benchmark dose was 1 x 10 -3 mg/kg body weight /day. The RfD was calculated by dividing the benchmark dose by a composite uncertainty factor of 10. The uncertainty factor was used to account for variability in the human population, in particular the wide variation in biological half-life of methylmercury and the variation that is observed in the ration of hair mercury to mercury in the blood. In addition the uncertainty factor accounts for lack of a two-generation reproductive study and the lack of data on long term effects of childhood mercury exposures. The RfD
thus calculated is 1 x 10 -4 mg/kg body weight/day or 0.1 μg/kg/day. The body weight used in the equation for the mercury criteria, as discussed in the Human Health Guidelines, is a mean adult human body weight of 70 kg. The drinking water consumption rate, as
discussed in the Human Health Guidelines, is 2.0 liters per day.

The bioconcentration factor or BCF is
defined as the ratio of chemical concentration in the organism to that in surrounding water. Bioconcentration occurs through uptake and retention of a substance from water only, through gill membranes or other external body surfaces. In the context of setting exposure criteria it is generally

understood that the terms ‘‘BCF’’ and ‘‘steady-state BCF’’ are synonymous. A steady-state condition occurs when the organism is exposed for a sufficient length of time that the ratio does not change substantially.

The BCFs that were used herein are

the ‘‘Practical Bioconcentration Factors (PBCFs)’’ that were derived in 1980: 5500 for fresh water, 3765 for estuarine coastal waters, and 9000 for open oceans. See pages C–100–1 of Ambient Water Quality Criteria for Mercury (EPA 440/5–80–058) for a complete

discussion on the PBCF. Because of the way they were derived, these PBCFs take into account uptake from food as well as uptake from water. A weighted average PBCF was calculated to take into account the average consumption from the three waters using the following equation:



### Weighted Average Practical BCF = (FC PBCF)

(FC) ×

= + +

+ + = = 

# ∑ ∑ ( . )( ) ( . )( ) ( . )( )

... .

. . 0 00172 5500 0 00478 3765 0 0122 9000

0 00172 0 00478 0 0122 137 3

0 0187 7342 6

Given the large value for the weighted average PBCF, the contribution of drinking water to total daily intake is negligible so that assumptions concerning the chemical form of mercury in drinking water become less important. The human health mercury criteria promulgated for this rule are
based on the latest RfD as listed in IRIS and a weighted PBCF from the 1980 § 304(a) criteria guidance document for

mercury.

On March 23, 1995 (60 FR 15366), EPA promulgated the Great Lakes Water Quality Guidance (‘‘Guidance’’). The Guidance incorporated bioaccumulation factors (BAFs) in the derivation of criteria to protect human health because
it is believed that BAFs are a better predictor than BCFs of the
concentration of a chemical within fish
tissue since BAFs include consideration of the uptake of contaminants from all routes of exposure. A bioaccumulation factor is defined as the ratio (in L/kg) of
a substance’s concentration in tissue to the concentration in the ambient water, in situations where both the organism and its food are exposed and the ratio does not change substantially over time.
The final Great Lakes Guidance establishes a hierarchy of four methods for deriving BAFs for non-polar organic chemicals: (1) Field-measured BAFs; (2)predicted BAFs derived using a fieldmeasured biota-sediment accumulation factor; (3) predicted BAFs derived by multiplying a laboratory-measured BCF by a food chain multiplier; and (4) predicted BAFs derived by multiplying a BCF calculated from the log Kow by a food-chain multiplier. The final Great Lakes Guidance developed BAFs for trophic levels three and four fish of the Great Lakes Basin. Respectively, the BAFs for mercury for trophic level 3 and 4 fish were: 27,900 and 140,000.

The BAF promulgated in the GLI was developed specifically for the Great Lakes System. It is uncertain whether the BAFs of 27,900 and 140,000 are appropriate for use in California at this time; therefore, today’s final rule does not use the GLI BAF in establishing human health criteria for mercury in California. The magnitude of the BAF for mercury in a given system depends on how much of the total mercury is present in the methylated form. Methylation rates vary widely from one water body to another for reasons that are not fully understood. Lacking the data, it is difficult to determine if the BAF used in the GLI represents the true potential for mercury to bioaccumulate in California surface waters. The true, average BAF for California could be higher or lower. For more information see EPA’s Response to Comments
document in the administrative record for this rule (specifically comments CTR–002–007(b) and CTR–016–007).

EPA is developing a national BAF for mercury as part of revisions to its 304(a) criteria for human health; however, the BAF methodology that will be used is currently under evaluation as part of
EPA’s revisions to its National Human Health Methodology (see section F.3 above). EPA applied a similar methodology in its Mercury Study Report to Congress (MSRC) to derive a BAF for methylmercury. The MSRC is available through NTIS (EPA–452/R– 97–003). Although a BAF was derived in the MSRC, EPA does not intend to use this BAF for National application. EPA is engaged in a separate effort to incorporate additional mercury
bioaccumulation data that was not considered in the MSRC, and to assess uncertainties with using a National BAF approach for mercury. Once the proposed revised human health methodology, including the BAF component, is finalized, EPA will revise its 304(a) criteria for mercury to reflect changes in the underlying methodology,
recommendations contained in the MSRC, and recommendations in a National Academy of Science report on
human health assessment of methylmercury. When EPA changes its 304(a) criteria recommendation for mercury, States and Tribes will be expected to review their water quality standards for mercury and make any revisions necessary to ensure their standards are scientifically defensible.

New information may become available regarding the bioaccumulation


### 31698 Federal Register / Vol. 65, No. 97 / Thursday, May 18, 2000 / Rules and Regulations

of mercury in certain water bodies in California. EPA supports the use of this information to develop site-specific criteria for mercury. Further, if a California water body is impaired due to mercury fish tissue or sediment contamination, loadings of mercury
could contribute to or exacerbate the impairment. Therefore, one option regulatory authorities should consider is to include water quality-based effluent limits (WQBELs) in permits based on mass for discharges to the impaired water body. Such WQBELs must be derived from and comply with applicable State water quality standards (including both numeric and narrative criteria) and assure that the discharge
does not cause or contribute to a violation of water quality standards.

d. Polychlorinated Biphenyls (PCBs)

Criteria

The NTR, as amended, calculated human health criteria for PCBs using acancer potency factor of 7.7 per mg/kgday from the Agency’s IRIS. This cancer potency factor was derived from the Norback and Weltman (1985) study
which looked at rats that were fed Aroclor 1260. The study used the linearized multistage model with a default cross-species scaling factor (body weight ratio to the 2 ⁄ 3 power). Although it is known that PCB mixtures vary greatly as to their potency in producing biological effects, for purposes of its carcinogenicity assessment, EPA considered Aroclor 1260 to be representative of all PCB mixtures. The Agency did not pool data from all available congener studies or generate a geometric mean from these studies, since the Norback and Weltman study was judged by EPA as acceptable, and not of marginal quality, in design or conduct as compared with other studies. Thereafter, the Institute for Evaluating Health Risks (IEHR, 1991) reviewed the pathological slides from the Norback and Weltman study, and concluded that some of the malignant liver tumors should have been interpreted as nonmalignant lesions, and that the cancer potency factor should be 5.1 per mg/kg-day as compared with EPA’s 7.7 per mg/kg-day.

The Agency’s peer-reviewed reassessment of the cancer potency of PCBs published in a final report, PCBs: Cancer Dose-Response Assessment and Applications to Environmental Mixtures (EPA/600/P–96/001F), adopts a different approach that distinguishes among PCB mixtures by using information on environmental processes. (The report is
included in the administrative record of today’s rule.) The report considers all cancer studies (which used commercial mixtures only) to develop a range of cancer potency factors, then uses information on environmental processes to provide guidance on choosing an appropriate potency factor for representative classes of environmental mixtures and different pathways. The reassessment provides that, depending on the specific application, either central estimates or upper bounds can be appropriate. Central estimates describe a typical individual’s risk, while upper bounds provide assurance (i.e., 95% confidence) that this risk is not likely to be underestimated if the underlying model is correct. Central estimates are used for comparing or ranking environmental hazards, while upper bounds provide information about the precision of the comparison or ranking. In the reassessment, the use of the upper bound values were found to increase cancer potency estimates by two or three-fold over those using central tendency. Upper bounds are useful for estimating risks or setting exposure-related standards to protect public health, and are used by EPA in quantitative cancer risk assessment. Thus, the cancer potency of PCB mixtures is determined using a tiered approach based on environmental exposure routes with upper-bound potency factors (using a body weight
ratio to the 3 ⁄ 4 power) ranging from 0.07 (lowest risk and persistence) to 2 (high risk and persistence) per mg/kg-day for average lifetime exposures to PCBs. It is noteworthy that bioaccumulated PCBs appear to be more toxic than commercial PCBs and appear to be more persistent in the body. For exposure through the food chain, risks can be higher than other exposures.

EPA issued the final reassessment report on September 27, 1996, and updated IRIS to include the reassessment on October 1, 1996. EPA updated the human health criteria for
PCBs in the National Toxics Rule on September 27, 1999. For today’s rule,
EPA derived the human health criteria for PCBs using a cancer potency factor of 2 per mg/kg-day, an upper bound potency factor reflecting high risk and persistence. This decision is based on recent multimedia studies indicating that the major pathway of exposure to persistent toxic substances such as PCBs is via dietary exposure (i.e.,
contaminated fish and shellfish consumption).

Following is the calculation of the human health criterion (HHC) for organism and water consumption:



### HHC RF BW

= × ×

× × ( , 1 000 g/mg)

q1* [WC + (FC BCF)] μ Where:

RF = Risk Factor = 1 x 10

¥ 6 BW = Body Weight = 70 kg q1* = Cancer slope factor = 2 per mg/ kg-day WC = Water Consumption = 2 l/day FC = Fish and Shellfish Consumption = 0.0065 kg/day
BCF = Bioconcentration Factor = 31,200
the HHC (μg/l) = 0.00017 μg/l (rounded to two significant digits).

Following is the calculation of the human health criterion for organism only consumption:



### HHC RF BW

= × ×

× × ( , 1 000 g/mg)

q1* FC BCF μ

Where:

RF = Risk Factor = 1 x 10

¥ 6 BW = Body Weight = 70 kg q1* = Cancer slope factor = 2 per mg/ kg-day
FC = Total Fish and Shellfish Consumption per Day = 0.0065 kg/ day
BCF = Bioconcentration Factor = 31,200
the HHC (μg/l) = 0.00017 μg/l (rounded to two significant digits).

The criteria are both equal to 0.00017

μg/l and apply to total PCBs. See PCBs: Cancer Dose Response Assessment and Application to Environmental Mixtures (EPA/600/9–96–001F). For a discussion of the body weight, water consumption, and fish and shellfish consumption factors, see the Human Health Guidelines. For a discussion of the BCF, see the 304(a) criteria guidance document for PCBs (included in the administrative record for today’s rule).

e. Excluded Section 304(a) Human
Health Criteria

As is the case in the NTR, as amended, today’s rule does not promulgate criteria for certain priority pollutants for which CWA section 304(a) criteria guidance exists because those criteria were not based on toxicity to humans or aquatic organisms. The basis for those particular criteria is organoleptic effects ( e.g., taste and odor)
which would make water and edible aquatic life unpalatable but not toxic.
Because the basis for this rule is to protect the public health and aquatic life from toxicity consistent with the language and intent in CWA section 303(c)(2)(B), EPA is promulgating criteria only for those priority toxic pollutants whose criteria recommendations are based on toxicity. The CWA section 304(a) human health criteria based on organoleptic effects for zinc and 3-methyl-4-chlorophenol are
excluded for this reason. See the 1992
NTR discussion at 57 FR 60864.


### 31699 Federal Register / Vol. 65, No. 97 / Thursday, May 18, 2000 / Rules and Regulations

f. Cancer Risk Level

EPA’s CWA section 304(a) criteria guidance documents for priority toxic pollutants that are based on carcinogenicity present concentrations for upper bound risk levels of 1 excess cancer case per 100,000 people (10

¥ 5 ), per 1,000,000 people (10

¥ 6), and per 10,000,000 people (10

¥ 7). However, the
criteria documents do not recommend a particular risk level as EPA policy.

As part of the proposed rule, EPA requested and received comment on the adoption of a 10

¥ 5 risk level for carcinogenic pollutants. The effect of a

10

¥ 5 risk level would have been to increase (i.e., make less stringent) carcinogenic pollutant criteria values (noted in the matrix by footnote c) that are not already promulgated in the NTR, by one order of magnitude. For example, the organism-only criterion for gamma BHC (pollutant number 105 in the matrix) is 0.013 μg/l; the criterion based

on a 10

¥ 5 risk level would have been

0.13 μg/l. EPA received several comments that indicated a preference for a higher (10

¥ 4 and 10

¥ 5 ) risk level for effluent dependent waters or other types of special circumstances.

In today’s rule, EPA is promulgating criteria that protect the general population at an incremental cancer risk level of one in a million (10

¥ 6) for all priority toxic pollutants regulated as carcinogens, consistent with the criteria promulgated in the NTR for the State of California. Standards adopted by the State contained in the Enclosed Bays and Estuaries Plan (EBEP), and the Inland Surface Waters Plan (ISWP), partially approved by EPA on November 6, 1991, and the Ocean Plan approved by EPA on June 28, 1990, contained a
risk level of 10

¥ 6 for most carcinogens. The State has historically protected at a

10

¥ 6 risk level for carcinogenic pollutants.

EPA, in its recent human health methodology revisions, proposed acceptable lifetime cancer risk for the general population in the range of 10

¥ 5

to 10

¥ 6 . EPA also proposed that States and Tribes ensure the most highly exposed populations do not exceed a

10

¥ 4 risk level. However, EPA’s draft methodology revisions also stated that it will derive 304(a) criteria at a 10

¥ 6 risk level, which the Agency believes reflects the appropriate risk for the general population and which applies a risk management policy which ensures protection for all exposed population groups. (Draft Water Quality Criteria Methodology: Human Health, EPA 822– Z–98–001, August 1998, Appendix II, page 72). Subpopulations within a State may exist, such as recreational and subsistence anglers, who as a result of greater exposure to a contaminant are at greater risk than the standard 70 kilogram person eating 6.5 grams per day of fish and shellfish and drinking 2.0 liters per day of drinking water with pollutant levels meeting the water quality criteria. EPA acknowledges that at any given risk level for the general population, those segments of the population that are more highly exposed face a higher relative risk. For example,
if fish are contaminated at a level permitted by criteria derived on the
basis of a risk level of 10

¥ 6 , individuals consuming up to 10 times the assumed fish consumption rate would still be protected at a 10

¥ 5 risk level. Similarly, individuals consuming 100 times the general population rate would be protected at a 10

¥ 4 risk level. EPA, therefore, believes that derivation of
criteria at the 10

¥ 6 risk level is a reasonable risk management decision protective of designated uses under the CWA. While outside the scope of this rule, EPA notes that States and Tribes, however, have the discretion to adopt water quality criteria that result in a higher risk level ( e.g., 10

¥ 5 ). EPA expects to approve such criteria if the
State or Tribe has identified the most highly exposed subpopulation within the State or Tribe, demonstrates the chosen risk level is adequately protective of the most highly exposed subpopulation, and has completed all necessary public participation.

This demonstration has not happened in California. Further, the information that is available on highly exposed subpopulations in California supports the need to protect the general population at the 10

¥ 6 level. California has cited the Santa Monica Bay Seafood Consumption Study as providing the best available data set for estimating consumption of sport fish and shellfish
in California for both marine or freshwater sources (Chemicals in Fish Report No. 1: Consumption of Fish and
Shellfish in California and the United States, Final Draft Report, July 1997). Consumption rates of sport fish and shellfish of 21g/day, 50 g/day, 107 g/ day, and 161 g/day for the median, mean, 90th, and 95th percentile rates, respectively, were determined from this study. Additional consumption of commercial species in the range of approximately 8 to 42 g/day would further increase these values. Clearly the consumption rates for the most highly exposed subpopulation within the State exceeds 10 times the 6.5 g/day rates used in the CTR. Therefore, use of a risk level of 10

¥ 5 for the general population would not be sufficient to protect the most highly exposed population in
California at a 10

¥ 4 risk level. On the other hand, even the most highly exposed subpopulations cited in the California study do not have consumption rates approaching 100 times the 6.5 g/day rates used in the
CTR. The use of the 10

¥ 6 risk level to protect average level consumers does not subject these subpopulations to risk levels as high as 10

¥ 4

.

EPA believes its decision to establish

a 10

¥ 6 risk level for the CTR is also consistent with EPA’s policy in the NTR
to select the risk level that reflect the policies or preferences of CWA programs in the affected States. California adopted standards for priority toxic pollutants for its ocean waters in 1990 using a 10

¥ 6 risk level to protect human health (California Ocean Plan, 1990). In April 1991, and again in November 1992, California adopted
standards for its inland surface waters and enclosed bays and estuaries in its Inland Surface Waters Plan (ISWP) and its Enclosed Bays and Estuaries Plan (EBEP) using a 10

¥ 6 risk level. To be consistent with the State’s water quality standards, EPA used a 10

¥ 6 risk level
for California in the NTR at 57 FR 60867. The State has continued using a

10

¥ 6 risk level to protect human health
for its standards that were not
withdrawn with the ISWP and EBEP. The most recent expression of risk level preference is contained in the Draft Functional Equivalent Document, Amendment of the Water Quality
Control Plan for Ocean Waters of California, October 1998, where the State recommended maintaining a
consistent risk level of 10

¥ 6 for the
human health standards that it was proposing to revise.

EPA received several comments requesting a 10

¥ 5 risk level based on the
risk level chosen for the Great Lakes Water Quality Guidance (the Guidance).
There are several differences between the guidelines for the derivation of
human health criteria contained in the
Guidance and the California Toxics Rule (CTR) that make a 10

¥ 5 risk factor appropriate for the Guidance, but not for
the CTR. These differences result in criteria developed using the 10

¥ 5 risk factor in the Guidance being at least as stringent as criteria derived under the CTR using a 10

¥ 6 risk factor. The relevant aspects of the Guidance
include:

• Use of fish consumption rates that are considerably higher than fish consumption rates for the CTR.

• Use of bioaccumulation factors
rather than bioconcentration factors in


### 31700 Federal Register / Vol. 65, No. 97 / Thursday, May 18, 2000 / Rules and Regulations

estimating exposure, considerably increasing the dose of carcinogens to sensitive subgroups.

• Consideration of additivity of effects of mixtures for both carcinogenic and noncarcinogenic pollutants.

This combination of factors increase the calculated carcinogenic risk substantially under the Guidance (the combination would generally be more than one order of magnitude), making a lower overall risk factor acceptable. The Guidance risk factor provides, in fact,
criteria with at least the same level of protection against carcinogens as criteria derived with a higher risk factor using the CTR. A lower risk factor for the CTR would not be appropriate absent concomitant changes in the derivation procedures that provide equivalent risk protection.

G. Description of Final Rule

1. Scope

Paragraph (a) in 40 CFR 131.38, entitled ‘‘Scope,’’ states that this rule is a promulgation of criteria for priority toxic pollutants in the State of California for inland surface waters, enclosed bays, and estuaries. Paragraph (a) in 40 CFR 131.38 also states that this rule contains an authorizing compliance schedule provision.

2. EPA Criteria for Priority Toxic
Pollutants

EPA’s criteria for California are presented in tabular form at 40 CFR 131.38. For ease of presentation, the table that appears combines water quality criteria promulgated in the NTR, as amended, that are outside the scope of this rulemaking, with the criteria that are within the scope of today’s rule. This is intended to help readers determine applicable water quality
criteria for the State of California. The
table contains footnotes for clarification.

Paragraph (b) in 40 CFR 131.38 presents a matrix of the applicable EPA aquatic life and/or human health criteria for priority toxic pollutants in California. Section 303(c)(2)(B) of the CWA addresses only pollutants listed as ‘‘toxic’’ pursuant to section 307(a) of the CWA for which EPA has developed section 304(a) criteria guidance. As discussed earlier in this preamble, the section 307(a) list of toxics contains 65 compounds and families of compounds, which potentially include thousands of specific compounds. Of these, the Agency identified a list of 126 ‘‘priority toxic pollutants’’ to implement the CWA (see 40 CFR 131.36(b)). Reference in this rule to priority toxic pollutants, toxic pollutants, or toxics refers to the 126 priority toxic pollutants. EPA has not developed both aquatic
life and human health CWA section 304(a) criterion guidance for all of the priority toxic pollutants. The matrix in 40 CFR 131.38(b) contains human
health criteria in Column D for 92 priority toxic pollutants which are
divided into Column 1: criteria for water consumption (i.e., 2.0 liters per day) and aquatic organism consumption (i.e., 6.5 grams per day of aquatic organisms); and Column 2: criteria for aquatic organism consumption only. The term aquatic organism includes fish and shellfish such as shrimp, clams, oysters
and mussels. One reason the total number of priority toxic pollutants with criteria today differs from the total number of priority toxic pollutants contained in earlier published CWA section 304(a) criteria guidance is because EPA has developed and is promulgating chromium criteria for two valence states with respect to aquatic life criteria. Thus, although chromium is a single priority toxic pollutant, there
are two criteria for chromium for aquatic life protection. See pollutant 5 in today’s rule at 40 CFR 131.38(b).
Another reason is that EPA is promulgating human health criteria for nine priority pollutants for which
health-based national criteria have been
calculated based on information obtained from EPA’s IRIS database (EPA provided notice of these nine criteria in
the NTR for inclusion in future State triennial reviews. See 57 FR 60848, 60890).

The matrix contains aquatic life criteria for 23 priority pollutants. These
are divided into freshwater criteria (Column B) and saltwater criteria (Column C). These columns are further
divided into acute and chronic criteria. The aquatic life criteria are considered by EPA to be protective when applied
under the conditions described in the section 304(a) criteria documents and in the TSD. For example, water body uses should be protected if the criteria are not exceeded, on average, once every three year period. It should be noted
that the criteria maximum concentrations (the acute criteria) are
short-term concentrations and that the criteria continuous concentrations (the chronic criteria) are four-day averages. It
should also be noted that for certain metals, the actual criteria are equations
which are included as footnotes to the matrix. The toxicity of these metals is water hardness dependent and may be adjusted. The values shown in the table are illustrative only, based on a hardness expressed as calcium carbonate of 100 mg/l. Finally, the criterion for pentachlorophenol is pH dependent. The equation is the actual
criterion and is included as a footnote.
The value shown in the matrix is for a pH of 7.8. Several of the freshwater aquatic life criteria are incorporated into
the matrix in the format used in the 1980 criteria methodology which uses a
final acute value instead of a continuous
maximum concentration. This distinction is noted in footnote g of the
table.

The final rule at 40 CFR 131.38(c) establishes the applicability of the
criteria to the State of California. 40 CFR 131.38(d) is described later in Section F, of this preamble. EPA has included in this rule provisions necessary to implement numeric criteria in a way that maintains the level of protection intended. These provisions are included in 40 CFR 131.38(c) of today’s rule. For example, in order to do steady state waste load allocation analyses, most
States have low flow values for streams
and rivers which establish flow rates for various purposes. These low flow values become design flows for sizing treatment plants and developing water quality-based effluent limits and/or TMDLs. Historically, these design flows were selected for the purposes of waste load allocation analyses which focused on instream dissolved oxygen concentrations and protection of aquatic life. With the publication of the 1985 TSD, EPA introduced hydrologically and biologically based analyses for the protection of aquatic life and human health. (These concepts have been expanded subsequently in EPA’s Technical Guidance Manual for Performing Wasteload Allocations, Book 6, Design Conditions, U.S. EPA, 1986. These analyses are included in Appendix D of the revised TSD. The discussion here is greatly simplified and is provided to support EPA’s decision to promulgate design flows for instream flows and thereby maintain the adequacy of the criteria for priority toxic pollutants.) EPA recommended either of two methods for calculating acceptable low flows, the traditional hydrologic method developed by the U.S. Geological Survey or a biological based method developed by EPA. Other methods for evaluating the instream flow record may be available; use of these methods may result in TMDLs and/or water quality-based effluent limitations which adequately protect human health and/or aquatic life. The results of either of these two methods, or an equally protective alternative method, may be used.

The State of California may adopt specific design flows for streams and rivers to protect designated uses against
the effects of toxics. EPA believes it is


### 31701 Federal Register / Vol. 65, No. 97 / Thursday, May 18, 2000 / Rules and Regulations

important to specify design flows in today’s rule so that, in the absence of state design flows, the criteria promulgated today would be implemented appropriately. The TSD
also recommends the use of three dynamic models to perform wasteload allocations. Dynamic wasteload models do not generally use specific steady state design flows but accomplish the same effect by factoring in the probability of occurrence of stream
flows based on the historical flow
record.

The low flows specified in the rule explicitly contain duration and frequency of occurrence which represent certain probabilities of occurrence. Likewise, the criteria for priority toxic pollutants are defined with duration and frequency components. Dynamic modeling techniques explicitly predict the effects of variability in receiving water, effluent flow, and pollution variation. Dynamic modeling techniques, as described in the TSD, allow for calculating wasteload
allocations that meet the criteria for priority toxic pollutants without using a single, worst-case concentration based on a critical condition. Either dynamic modeling or steady state modeling can be used to implement the criteria promulgated today. For simplicity, only steady state conditions are discussed here. Clearly, if the criteria were implemented using design flows that are too high, the resulting toxic controls would not be adequate, because the resulting ambient concentrations would
exceed EPA’s criteria.

In the case of aquatic life, assuming exceedences occur more frequently than once in three years on the average,
exceedences would result in diminished vitality of stream ecosystems characterized by the loss of desired species. Numeric water quality criteria should apply at all flows that are equal to or greater than flows specified below.
The low flow values are:

Type of criteria Design flow

Acute Aquatic Life

(CMC). 1 Q 10 or 1 B 3

Chronic Aquatic Life

(CCC). 7 Q 10 or 4 B 3

Human Health ........... harmonic mean flow

Where:

1 Q 10 is the lowest one day flow with

an average recurrence frequency of once in 10 years determined hydrologically; 1 B 3 is biologically based and indicates

an allowable exceedence of once every 3 years. It is determined by EPA’s computerized method (DFLOW model); 7 Q 10 is the lowest average 7

consecutive day low flow with an average recurrence frequency of once in 10 years determined hydrologically; 4 B 3 is biologically based and indicates

an allowable exceedences for 4 consecutive days once every 3 years. It is determined by EPA’s computerized method (DFLOW model); EPA is requiring that the harmonic mean flow be applied with human
health criteria. The harmonic mean is a
standard calculated statistical value.
EPA’s model for human health effects
assumes that such effects occur because of a long-term exposure to low concentration of a toxic pollutant, for example, two liters of water per day for seventy years. To estimate the concentrations of the toxic pollutant in those two liters per day by withdrawal from streams with a high daily variation in flow, EPA believes the harmonic
mean flow is the correct statistic to use in computing such design flows rather than other averaging techniques. (For a description of harmonic means see ‘‘Design Stream Flows Based on
Harmonic Means,’’ Lewis A. Rossman, Jr. of Hydraulics Engineering, Vol. 116, No. 7, July, 1990.)

All waters (including lakes, estuaries, and marine waters), whether or not suitable for such hydrologic calculations, are subject to the criteria promulgated today. Such criteria will
need to be attained at the end of the discharge pipe, unless the State authorizes a mixing zone. Where the State plans to authorize a mixing zone, the criteria would apply at the locations allowed by the mixing zone. For example, the chronic criteria (CCC) would apply at the defined boundary of the chronic mixing zone. Discussion of and guidance on these factors are included in the revised TSD in Chapter

4. EPA is aware that the criteria promulgated today for some of the priority toxic pollutants are at
concentrations less than EPA’s current analytical detection limits. Analytical
detection limits have never been an acceptable basis for setting water quality criteria since they are not related to actual environmental impacts. The environmental impact of a pollutant is based on a scientific determination, not a measuring technique which is subject to change. Setting the criteria at levels that reflect adequate protection tends to be a forcing mechanism to improve analytical detection methods. See 1985 Guidelines, page 21. As the methods improve, limits based on the actual criteria necessary to protect aquatic life
and human health become measurable. The Agency does not believe it is appropriate to promulgate criteria that are not sufficiently protective. EPA
discusses this issue further in its Response to Comment Document for today’s final rule.

EPA does believe, however, that the use of analytical detection limits are appropriate for assessing compliance with National Pollutant Discharge Elimination System (NPDES) permit
limits. This view of the role of detection limits was first articulated in guidance for translating dioxin criteria into NPDES permit limits. See ‘‘Strategy for the Regulation of Discharges of PHDDs and PHDFs from Pulp and Paper Mills
to Waters of the U.S.’’ Memorandum
from the Assistant Administrator for Water to the Regional Water Management Division Directors, May 21, 1990. This guidance presented a model for addressing toxic pollutants
which have criteria less than current detection limits. EPA, in more recent guidance, recommends the use of the ‘‘minimum level’’ or ML for reporting sample results to assess compliance with WQBELs (TSD page 111). The ML, also called the ‘‘quantification level,’’ is the level at which the entire analytical system gives recognizable mass spectra and acceptable calibration points, i.e., the point at which the method can reliably quantify the amount of pollutant in the sample. States can use their own procedures to average and otherwise account for monitoring data,

e.g., quantifying results below the ML.
These results can then be used to assess compliance with WQBELs. (See 40 CFR part 132, Appendix F, Procedure 8.B.) This approach is applicable to priority toxic pollutants with criteria less than current detection limits. EPA’s guidance explains that standard analytical methods may be used for purposes of assessing compliance with permit limits, but not for purposes of establishing water quality criteria or permit limits. Under the CWA, analytical methods are appropriately used in connection with NPDES permit limit compliance assessments. Because of the function of water quality criteria, EPA has not considered the sensitivity of analytical methods in deriving the criteria promulgated today.

EPA has promulgated 40 CFR 131.38(c)(3) to determine when freshwater or saltwater aquatic life criteria apply. This provision incorporates a time parameter to better
define the critical condition. The structure of the paragraph is to establish


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applicable rules and to allow for sitespecific exceptions where the rules are
not consistent with actual field
conditions. Because a distinct separation generally does not exist
between freshwater and saltwater aquatic communities, EPA is establishing the following: (1) The freshwater criteria apply at salinities of 1 part per thousand and below at locations where this occurs 95% or more of the time; (2) saltwater criteria apply at salinities of 10 parts per
thousand and above at locations where this occurs 95% more of the time; and (3) at salinities between 1 and 10 parts per thousand the more stringent of the two apply unless EPA approves the application of the freshwater or
saltwater criteria based on an appropriate biological assessment. The percentiles included here were selected to minimize the chance of overlap, that is, one site meeting both criteria. Determination of these percentiles can be done by any reasonable means such as interpolation between points with measured data or by the application of
calibrated and verified mathematical models (or hydraulic models). It is not EPA’s intent to require actual data collection at particular locations.

In the brackish water transition zones of estuaries with varying salinities, there generally will be a mix of freshwater and saltwater species. Generally, therefore, it is reasonable for the more stringent of the freshwater or saltwater criteria to apply. In evaluating appropriate data supporting the alternative set of criteria, EPA will focus on the species composition as its preferred method. This assignment of criteria for fresh, brackish and salt waters was developed in consultation
with EPA’s research laboratories at Duluth, Minnesota and Narragansett, Rhode Island. The Agency believes such an approach is consistent with field experience.

Paragraph (d) in 40 CFR 131.38 lists the designated water and use
classifications for which the criteria apply. The criteria are applied to the beneficial use designations adopted by the State of California; EPA has not promulgated any new use classifications
in this rule.

Exceedences Frequency: In a water quality criterion for aquatic life, EPA recommends an allowable frequency for
excursions of the criteria. See 1985 Guidelines, pages 11–13. This allowable frequency provides an appropriate period of time during which the aquatic community can recover from the effect
of an excursion and then function normally for a period of time before the
next excursion. An excursion is defined as an occurrence of when the average
concentration over the duration of the averaging period is above the CCC or the CMC. As ecological communities are naturally subjected to a series of stresses, the allowable frequency of pollutant stress may be set at a value that does not significantly increase the frequency or severity of all stresses combined. See also TSD, Appendix D. In addition, providing an allowable frequency for exceeding the criterion recognizes that it is not generally possible to assure that criteria are never exceeded. (TSD, page 36.)

Based on the available data, today’s rule requires that the acute criterion for a pollutant be exceeded no more than once in three years on the average. EPA is also requiring that the chronic criterion for a pollutant be exceeded no more than once in three years on the average. EPA acknowledges that States may develop allowable frequencies that differ from these allowable frequencies, so long as they are scientifically supportable, but believes that these allowable frequencies are protective of the designated uses where EPA is promulgating criteria.

The use of aquatic life criteria for developing water quality-based effluent limits in permits requires the permitting official to use an appropriate wasteload allocation model. (TSD, Appendix D–6.) As discussed above, there are generally two methods for determining design flows, the hydrologically-based method and the biologically-based method.

The biologically-based method directly uses the averaging periods and frequencies specified in the aquatic life criteria for determining design flows. (TSD, Appendix. D–8.) Because the biologically-based method calculates the design flow directly from the duration and allowable frequency, it most accurately provides the allowed number of excursions. The hydrologically based method applies the CMC at a design flow equal to or equivalent to the 1Q10 design flow (i.e., the lowest one-day flow with an average recurrence frequency of once in ten years), and applies the CCC at the 7Q10 design flow (i.e., the lowest average seven consecutive day flow with a recurrence frequency of once in ten years).

EPA established a three year allowable frequency in the NTR. In settlement of the litigation on the NTR,
EPA stated that it was in the midst of conducting, sponsoring, or planning research aimed at addressing scientific
issues related to the basis for and application of water quality criteria and
mentioned the issue of allowable frequency. See Partial Settlement Agreement in American Forest and Paper Ass’n, Inc. et al. v. U.S. EPA (Consolidated Case No. 93–0694 (RMU) D.D.C. To that end, EPA is reevaluating issues raised about allowable frequency as part of its work in revising the 1985
Guidelines.

EPA recognizes that additional data concerning (a) the probable frequency of lethal events for an assemblage of taxa covering a range of sensitivities to pollutants, (b) the probable frequency of sublethal effects for such taxa, (c) the differing effects of lethal and sublethal events in reducing populations of such taxa, and (d) the time needed to replace organisms lost as a result of toxicity, may lead to further refinement of the allowable frequency value. EPA has not yet completed this work. Until this work is complete, EPA believes that where EPA promulgates criteria, the three year allowable frequency represents a value in the reasonable range for this
parameter.

3. Implementation

Once the applicable designated uses and water quality criteria for a water body are determined, under the National Pollutant Discharge Elimination System (NPDES) program discharges to the water body must be characterized and the permitting authority must determine the need for permit limits. If a discharge causes, has the reasonable potential to cause, or
contributes to an excursion of a numeric or narrative water quality criteria, the permitting authority must develop permit limits as necessary to meet water quality standards. These permit limits are water quality-based effluent limitations or WQBELs. The terms ‘‘cause,’’ ‘‘reasonable potential to cause,’’ and ‘‘contribute to’’ are the terms in the NPDES regulations forconditions under which water qualitybased permit limits are required. See 40 CFR 122.44(d)(1).

Since the publication of the proposed CTR, the State of California adopted procedures which detail how water quality criteria will be implemented through NPDES permits, waste discharge requirements, and other regulatory approaches. These procedures entitled, Policy for Implementation of Toxics Standards for Inland Surface Waters, Enclosed Bays, and Estuaries of California were adopted on March 2, 2000. Once these procedures are submitted for review under CWA section 303(c), EPA will review them as they relate to water quality standards, and approve or disapprove them.

Several commenters understood the language in the preamble to the proposed rule regarding implementation


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to mean that site-specific criteria, variances, and other actions would be prohibited or severely limited by the CTR. Site-specific criteria, variances and other actions modifying criteria are neither prohibited nor limited by the CTR. The State, if it so chooses, still can make these changes to its water quality standards, subject to EPA approval. However, with this Federal rule in effect, the State cannot implement any modifications that are less stringent
than the CTR without an amendment to
the CTR to reflect these modifications. EPA will make every effort to expeditiously accommodate Federal rulemaking of appropriate modifications to California’s water quality standards. In the preamble to the proposed CTR, and here today, EPA is emphasizing that
these efforts to amend the CTR on a case-by-case basis will generally
increase the time before a modification can be implemented.

4. Wet Weather Flows

EPA has for a longtime maintained that CWA section 301(b)(1)(C) applies to NPDES permits for discharges from municipal separate storm sewer systems. Recently, the U.S. Court of Appeals for the Ninth Circuit upheld NPDES permits issued by EPA for five Arizona municipal separate storm sewer systems and addressed this issue specifically. Defenders of Wildlife, et al.

v. Browner, No. 98–71080 (9th Cir., October 1999). The Court held that the CWA does not require ‘‘strict compliance’’ with State water quality standards for municipal storm sewer permits under section 301(b)(1)(C), but that at the same time, the CWA does give EPA discretion to incorporate appropriate water quality-based effluent limitations under another provision, CWA section 402(p)(3)(B)(iii).

The Court based its decision on the structure of section 402(p)(3), which contains distinct language for discharges of industrial storm water and municipal storm water. In section 402(p)(3)(A), Congress requires that ‘‘dischargers associated with industrial activity shall meet all applicable provisions of [section 402] and section [301].’’ 33 U.S.C. section 1342(p)(3)(A). The Court noted, therefore, that by incorporation, industrial storm water discharges need to achieve ‘‘any more stringent limitation, including those necessary to meet water quality standards * * *’’ The Court explained that industrial storm water discharges ‘‘must comply strictly with State water quality standards’’ but that Congress chose not to include a similar provision for municipal storm sewer discharges, including instead a requirement for controls to reduce pollutants to the maximum extent practicable or MEP standard in section 402(p)(3)(B). Reading the two related sections together, the Court concluded that section 402(p)(3)(B)(iii) does not require ‘‘strict compliance’’ by municipal storm sewer discharges according to section 301(b)(1)(C). At the same time, however, the Court found that the language in CWA section 402(p)(3)(B)(iii) which states that permits for discharges from municipal storm sewers shall require ‘‘such other provisions as the

Administrator of the state determines appropriate for the control of such pollutants’’ provides EPA with discretion to incorporate provisions lending to ultimate compliance with water quality standards.

EPA believes that compliance with water quality standards through the use of Best Management Practices (BMPs) is appropriate. EPA articulated its position

on the use of BMPs in storm water permits in the policy memorandum entitled, ‘‘Interim Permitting Approach for Water Quality-Based Effluent

Limitations In Storm Water Permits’’ which was signed by the Assistant Administrator for Water, Robert Perciasepe on August 1, 1996 (61 FR 43761, August 9, 1996). A copy of this
memorandum is contained in the administrative record for today’s rule. The policy affirms the use of BMPs as a means to attain water quality standards in municipal storm water permits, and embraces BMPs as an interim permitting approach.

The interim permitting approach uses
BMPs in first-round storm water permits, and expanded or better-tailored BMPs in subsequent permits, where necessary, to provide for the attainment of water quality standards. In cases where adequate information exists to develop more specific conditions or limitations to meet water quality standards, these conditions or limitations are to be incorporated into storm water permits, as necessary and appropriate.

This interim permitting approach, however, only applies to EPA. EPA encourages the State to adopt a similar policy for municipal storm water permits. This interim permitting approach provides time, where necessary, to more fully assess the range of issues and possible options for the control of storm water discharges for the protection of water quality. More
information on this issue is included in the response to comment document in response to specific storm water issues raised by commenters. 5. Schedules of Compliance

A compliance schedule refers to an enforceable sequence of interim requirements in a permit leading toultimate compliance with water qualitybased effluent limitations or WQBELs in
accordance with the CWA. The authorizing compliance schedule provision authorizes, but does not require, the permit issuing authority in
the State of California to include such compliance schedules in permits under appropriate circumstances. The State of
California is authorized to administer the National Pollutant Discharge Elimination System (NPDES) program and may exercise its discretion when deciding if a compliance schedule is justified because of the technical or financial (or other) infeasibility of immediate compliance. An authorizing compliance schedule provision is included in today’s rule because of the potential for existing dischargers to have new or more stringent effluent
limitations for which immediate compliance would not be possible or practicable.

New and Existing Dischargers: The provision allows compliance schedules only for an ‘‘existing discharger’’ which is defined as any discharger which is not a ‘‘new California discharger.’’ A ‘‘new California discharger’’ includes ‘‘any building, structure, facility, or installation from which there is, or may be, a ‘discharge of pollutants’, the
construction of which commences after the effective date of this regulation.’’
These definitions are modeled after the existing 40 CFR 122.2 definitions for parallel terms, but with a cut-off date modified to reflect this rule. Only ‘‘new California dischargers’’ are required to comply immediately upon commencement of discharge with
effluent limitations derived from the criteria in this rule. For ‘‘existing dischargers’’ whose permits are reissued
or modified to contain new or more stringent limitations based upon certain water quality requirements, the permit could allow up to five years, or up to the length of a permit, to comply with such limitations. The provision applies to new or more stringent effluent
limitations based on the criteria in this
EPA rule.

EPA has included ‘‘increasing dischargers’’ within the category of ‘‘existing dischargers’’ since ‘‘increasing dischargers’’ are existing facilities with a change—an increase—in their discharge. Such facilities may include
those with seasonal variations. ‘‘Increasing dischargers’’ will already have treatment systems in place for their current discharge, thus, they have less


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opportunity than a new discharger does to design and build a new treatment system which will meet new water quality-based requirements for their changed discharge. Allowing existing facilities with an increasing discharge a compliance schedule will avoid placing the discharger at a competitive disadvantage vis-a-vis other existing dischargers who are eligible for compliance schedules.

Today’s rule does not prohibit the use of a short-term ‘‘shake down period’’ for new California dischargers as is provided for new sources or new dischargers in 40 CFR 122.29(d)(4). These regulations require that the owner or operator of (1) a new source; (2) a new discharger (as defined in 40 CFR 122.2) which commenced discharge after August 13, 1979; or (3) a recommencing discharger shall install and implement all pollution control equipment to meet the conditions of the permit before discharging. The facility must also meet all permit conditions in the shortest feasible time (not to exceed 90 days). This shake-down period is not a compliance schedule. This approach may be used to address violations whichmay occur during a new facility’s startup, especially where permit limits are water quality-based and biological
treatment is involved.

The burden of proof to show the necessity of a compliance schedule is on the discharger, and the discharger must request approval from the permit issuing authority for a schedule of compliance. The discharger should submit a description of the minimum required actions or evaluations that must be undertaken in order to comply
with the new or more restrictive discharge limits. Dates of completion for the required actions or evaluations should be included, and the proposed
schedule should reflect the shortest practicable time to complete all minimum required actions.

Duration of Compliance Schedules: Today’s rule provides that compliance schedules may provide for up to five years to meet new or more stringent
effluent limitations in those limited circumstances where the permittee can demonstrate to the permit authority that
an extended schedule is warranted. EPA’s regulations at 122.47 require compliance with standards as soon as possible. This means that permit authorities should not allow compliance schedules where the permittee fails to demonstrate their necessity. This provision should not be considered a default compliance schedule duration for existing facilities.

In instances where dischargers wish to conduct toxicological studies, analyze results, and adopt and implement new or revised water quality-based effluent limitations, EPA believes that five years
is sufficient time within which to complete this process. See the preamble to the proposed rule.

Under this rule, where a schedule of compliance exceeds one year, interim requirements are to be specified and interim progress reports are to be submitted at least annually to the permit issuing authority, in at least one-year
time intervals.

The rule allows all compliance schedules to extend up to a maximum duration of five years, which is the maximum term of any NPDES permit. See 40 CFR 122.46. The discharger’s opportunity to obtain a compliance schedule occurs when the existing permit for that discharge is issued,
reissued or modified to contain more stringent limits based on the water quality criteria in today’s rule. Such compliance schedules, however, cannot be extended to any indefinite point of
time in the future because the compliance schedule provision in this rule will sunset on May 18, 2005. The sunset applies to the authorizing provision in today’s rule (40 CFR 131.38(e)), not to individual schedules of compliance included in specific NPDES permits. Delays in reissuing expired permits (including those which continue in effect under applicable NPDES regulations) cannot indefinitely extend the period of time during which a compliance schedule is in effect. This would occur where the permit authority includes the single maximum five-year compliance schedule in a permit that is reissued just before the compliance schedule provision sunsets (having been previously issued without WQBELS using the rule’s criteria on the eve of the effective date of this rule). Instead, the effect of the sunset provision is to limit the longest time period for compliance to ten years after the effective date of
this rule.

EPA recognizes that where a permit is modified during the permit term, and the permittee needs the full five years to comply, the five-year schedule may extend beyond the term of the modified permit. In such cases, the rule allows for the modified permit to contain a compliance schedule with an interim limit by the end of the permit term. When the permit is reissued, the permit authority may extend the compliance schedule in the next permit, provided that, taking into account the amount of time allowed under the previous permit, the entire compliance schedule contained in the permit shall not exceed five years. Final permit limits and compliance dates will be included in the record for the permit. Final compliance dates must occur within five years from the date of permit issuance, reissuance, or modification,
unless additional or less time is provided for by law.

EPA would prefer that the State adopt an authorizing compliance schedule provision but recognizes that the State may not be able to complete this action for some time after promulgation of the CTR. Thus, EPA has chosen to promulgate the rule with a sunset provision which states that the authorizing compliance schedule provision will cease or sunset on May 18, 2005. However, if the State Board adopts, and EPA approves, a statewide authorizing compliance schedule provision significantly prior to May 18, 2005, EPA will act to stay the authorizing compliance schedule provision in today’s rule. Additionally, if a Regional Board adopts, and the State Board adopts and EPA approves, a Regional Board authorizing compliance schedule provision, EPA will act to stay today’s provision for the appropriate or corresponding geographic region in California. At that time, the State Board’s or Regional Board’s authorizing compliance schedule provision will govern the ability of the State regulatory entity to allow a discharger to include a compliance schedule in a discharger’s NPDES permit.

Antibacksliding: EPA wishes to address the potential concern over antibacksliding where revised permit
limits based on new information are the result of the completion of additional studies. The Agency’s interpretation of the CWA is that the antibacksliding requirements of section 402(o) of the CWA do not apply to revisions to
effluent limitations made before the scheduled date of compliance for those
limitations.

State Compliance Schedule

Provisions: EPA supports the State in adopting a statewide provision independent of or as part of the effort to readopt statewide water quality controlplans, or in adopting individual basinwide compliance schedule provisions through its nine Regional Water Quality Control Boards (RWQCBs). The State and RWQCBs have broad discretion to adopt a provision, including discretion on reasonable lengths of time for final compliance with WQBELs. EPA recognizes that practical time frames within which to set interim goals may be necessary to achieve meaningful, long-term improvements in water quality in California.

At this time, two RWQCBs have adopted an authorizing compliance schedule provision as an amendment to


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their respective Basin Plans during the Boards’ last triennial review process. The Basin Plans have been adopted by
the State and have come to EPA for approval. Thus, the Basin Plans’ provisions are effective for the respective Basins. If and when EPA approves of either Regional Basin Plan, EPA will expeditiously act to amend the CTR, staying its compliance schedule provision, for the appropriate geographic region.

6. Changes From Proposed Rule

A few changes were made in the final rule from the proposal both as a result of the Agency’s consideration of issues raised in public comments and Endangered Species Act consultation
with the U.S. Fish and Wildlife Service (FWS) and U.S. National Marine Fisheries Service (NMFS). The important changes include: reserving the mercury aquatic life criteria; reserving the selenium freshwater acute aquatic life criterion; reserving the chloroform human health criteria; and adding a sunset provision to the authorizing compliance schedule provision. EPA also clarified that the CTR will not replace priority toxic pollutant criteria which were adopted by the San Francisco Regional Water Quality Control Board in its 1986 Basin Plan, adopted by the State Board, and approved by EPA; specifying the
harmonic mean for human health criteria for non-carcinogens and adding a provision which explicitly allows the State to adopt and implement an alternative averaging period, frequency, and design flow for a criterion after opportunity for public comment.

The first two changes, the reservation of mercury criteria and selenium criterion, are discussed in more detail below in Section L., The Endangered Species Act (ESA). The selenium
criterion is also discussed in more detail above in Section E., Derivation of Criteria, in subsection 2.b., Freshwater
Acute Selenium Criterion. EPA has also
decided to reserve a decision on
numeric criteria for chloroform and therefore not promulgate chloroform criteria in the final rule. As part of a large-scale regulation promulgated in December l998 under the Safe DrinkingWater Act, EPA published a healthbased goal for chloroform (the maximum contaminant level goal or MCLG) of zero, see 63 FR 69390, Dec. 16, 1998. EPA provided new data and analyses concerning chloroform for public review and comment, including a different, mode of action approach for estimating the cancer risk, 63 FR 15674, March 31, 1998, but did not reach a
conclusion on how to use that new information in establishing the final MCLG, pending further review by the Science Advisory Board. EPA has now concluded that any further actions on water quality criteria should take into account the new data and analysis as reviewed by the SAB. This decision is
consistent with a recent federal court decision vacating the MCLG for chloroform ( Chlorine Chemistry Council

v. EPA, No. 98–1627 (DC Cir., Mar. 31,2000)). EPA intends to reassess the human health 304(a) criteria
recommendation for chloroform. For these reasons, EPA has decided to
reserve a decision on numeric criteria
for chloroform in the CTR and not promulgate water quality criteria as proposed. Permitting authorities in California should continue to rely on existing narrative criteria to establish effluent limitations as necessary for
chloroform.

The sunset provision for the authorizing compliance schedule provision has been added to ease the transition from a Federal provision to the State’s provision that was adopted in March 2000 as part of its’ new statewide implementation plan. The sunset provision is discussed in more detail in Section G.5 of today’s preamble. The CTR matrix at 40 CFR 131.38(b)(1) makes it explicit that the rule does not supplant priority toxic pollutant criteria which were adopted by the San Francisco Regional Water Quality Control Board in its 1986 Basin Plan, adopted by the State Board, and approved by EPA. This change is discussed more fully in Section D.4. of today’s preamble. EPA modified the design flow for implementing human health criteria for non-carcinogens from a 30Q5 to a harmonic mean. Human health criteria for non-carcinogens are based on an RfD, which is an acceptable daily exposure over a lifetime. EPA matched the criteria for protection over a human lifetime with the longest stream flow averaging period, i.e., the harmonic mean. Lastly, the CTR now contains language which is intended to make it easier for the State to adopt and implement an alternative averaging period, frequency and related design flow, for situations where the default parameters are inappropriate. This language is found at 40 CFR 131.38(c)(2)(iv).

H. Economic Analysis

This final rule establishes ambient water quality criteria which, by themselves, do not directly impose economic impacts (see section K). These
criteria combined with the Stateadopted designated uses for inland surface waters, enclosed bays and estuaries, and implementation policies, will establish water quality standards. Until the State implements these water quality standards, there will be no effect of this rule on any entity. The State will implement these criteria by ensuring that NPDES permits result in discharges that will meet these criteria. In so doing,
the State will have considerable
discretion.

EPA has analyzed the indirect potential costs and benefits of this rule.
In order to estimate the indirect costs and benefits of the rule, an appropriate
baseline must be established. The baseline is the starting point for measuring incremental costs and benefits of a regulation. The baseline is established by assessing what would occur in the absence of the regulation. At present, State Basin Plans contain a narrative water quality criterion stating
that all waters shall be maintained free
of toxic substances in concentrations that produce detrimental physiological responses in human, plant, animal, or aquatic life. EPA’s regulation at 40 CFR 122.44(d)(1)(vi) requires that where a discharge causes or has the reasonable potential to cause an excursion above a
narrative criterion within a State water quality standard, the permitting authority must establish effluent limits but may determine limits using a number of options. These options include establishing ‘‘effluent limits on a case-by-case basis, using EPA’s water quality criteria published under section 304(a) of the CWA, supplemented where necessary by other relevant information’’ (40 CFR 122.44(d)(1)(vi)(B)). Thus, to the extent that the State is implementing its narrative criteria by applying the CWA section 304(a) criteria, this rule does not impose any incremental costs because
the criteria in this rule are identical to the CWA section 304(a) criteria. Alternatively, to the extent that the State is implementing its narrative criteria on a ‘‘case-by-case basis’’ using ‘‘other relevant information’’ in its permits this rule may impose incremental indirect
costs because the criteria in these permits may not be based on CWA 304(a) criteria. Both of these approaches to establishing effluent limits are in full compliance with the CWA.

Because a specific basis for effluent limits in all existing permits in California is not known, it is not possible to determine a precise estimate
of the indirect costs of this rule. The incremental costs of the rule may be as low as zero, or as high as $61 million. The high estimate of costs is based on the possibility that most of the effluent
limits now in effect are not based on 304(a) criteria. EPA evaluated these


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indirect costs using two different approaches. The first approach uses existing discharge data and makes assumptions about future State NPDES permit limits. Actual discharge levels are usually lower than the level set by current NPDES permit limits. This approach, representing the low-end scenario, also assumes that some of the discretionary mechanisms that would enhance flexibility ( e.g., site specific criteria, mixing zones) would be granted by the State. The second approach uses a sample of existing permit limits and assumes that dischargers are actually discharging at the levels contained in their permits and makes assumptions
about limits statewide that would be required under the rule. This approach, representing the high-end scenario, also assumes that none of the discretionary
mechanisms that would enhance flexibility ( e.g., site specific criteria, mixing zones) would be granted by the State. These two approaches recognize that the State has significant flexibility
and discretion in how it chooses to implement standards within the NPDES permit program, the EA by necessity includes many assumptions about how the State will implement the water quality standards. These assumptions
are based on a combination of EPA guidance and current permit conditions
for the facilities examined in this analysis. To account for the uncertainty of EPA’s implementation assumptions, this analysis estimates a wide range of costs and benefits. By completing the EA, EPA intends to inform the public about how entities might be potentially affected by State implementation of water quality standards in the NPDES permit program. The costs and benefits
sections that follow summarize the methodology and results of the analysis.

1. Costs

EPA assessed the potential compliance costs that facilities may incur to meet permit limits based on the criteria in today’s rule. The analysis focused on direct compliance costs such as capital costs and operation andmaintenance costs (O&M) for end-ofpipe pollution control, indirect source controls, pollution prevention, monitoring, and costs of pursuing alternative methods of compliance.

The population of facilities with NPDES permits that discharge into California’s enclosed bays, estuaries and
inland surface waters includes 184 major dischargers and 1,057 minor dischargers. Of the 184 major facilities, 128 are publicly owned treatment works (POTWs) and 56 are industrial facilities. Approximately 2,144 indirect dischargers designated as significant industrial users discharge wastewater to
those POTWs. In the EA for the proposed CTR, EPA used a three-phased process to select a sample of facilities to represent California dischargers potentially affected by the State’s implementation of permit limits based
on the criteria contained in this rule.

The first phase consisted of choosing three case study areas for which data was thought to exist. The three case
studies with a total of 5 facilities included: the South San Francisco Bay (the San Jose/Santa Clara Water Pollution Control Plant and Sunnyvale Water Pollution Control Plant); the Sacramento River (the Sacramento Regional Wastewater Treatment Plant); and the Santa Ana River (the City of Riverside Water Quality Control Plant and the City of Colton Municipal Wastewater Treatment Facility). The second phase consisted of selecting five additional major industrial dischargers to complement the case-study POTWs.

The third phase involved selecting 10 additional facilities to improve the basis for extrapolating the costs of the selected sample facilities to the entire population of potentially affected dischargers. The additional 10 facilities were selected such that the group examined: (1) Was divided between major POTWs and major industrial discharger categories in proportion to the numbers of facilities in the State; (2) gave greater proportionate representation to major facilities than minor facilities based on a presumption that the majority of compliance costs would be incurred by major facilities; (3) gave a proportionate representation to each of four principal conventional treatment processes typically used by facilities in specified industries in California; and (4) was representative of the proportionate facilities located within the different California Regional Water Quality Control Boards. Within these constraints, facilities were selected at random to complete the sample.

In the EA for today’s final rule, EPA primarily used the same sample as the EA for the proposed rule with some
modifications. EPA increased the
number of minor POTWs and minor industrial facilities in the sample. EPA randomly selected four new minor
POTW facilities and five new minor industrial facilities to add to the sample. The number of sample facilities selected in each area under the jurisdiction of a Regional Water Quality Control Board was roughly proportional to the
universe of facilities in each area.

For those facilities that were projected to exceed permit limits based on the criteria, EPA estimated the incremental costs of compliance. Using a decision matrix or flow chart, costs were developed for two different scenarios—a ‘‘low-end’’ cost scenario and a ‘‘highend’’ cost scenario—to account for a range of regulatory flexibility available to the State when implementing permit limits based on the water quality criteria. The assumptions for baseline loadings also vary over the two
scenarios. The low-end scenario generally assumed that facilities were discharging at the maximum effluent
concentrations taken from actual monitoring data, while the high-end scenario generally assumed that facilities were discharging at their
current effluent limits. The decision matrix specified assumptions used for selection of control options, such as optimization of existing treatment processes and operations, in-plant pollutant minimization and prevention, and end-of-pipe treatment.

The annualized potential costs that direct and indirect dischargers may incur as a result of State implementation of permit limits based on water quality standards using today’s criteria are estimated to be between $33.5 million and $61 million. EPA believes that the
costs incurred as a result of State implementation of these permit limits will approach the low-end of the cost range. Costs are unlikely to reach the high-end of the range because State authorities are likely to choose implementation options that provide some degree of flexibility or relief to point source dischargers. Furthermore, cost estimates for both scenarios, but especially for the high-end scenario, may be overstated because the analysis tended to use conservative assumptions in calculating these permit limits and in establishing baseline loadings. The baseline loadings for the high-end were
based on current effluent limits rather than actual pollutant discharge data. Most facilities discharge pollutants in
concentrations well below current effluent limits. In addition, both the high-end and low-end cost estimates in the EA may be slightly overstated since potential costs incurred to reduce chloroform discharges were included in
these estimates. EPA made a decision to
reserve the chloroform human health criteria after the EA was completed.

Under the low-end cost scenario, major industrial facilities and POTWs would incur about 27 percent of the potential costs, indirect dischargers would incur about 70 percent of the potential costs, while minor dischargers would incur about 3 percent. Of the major direct dischargers, POTWs would incur the largest share of projected costs (87 percent). However, distributed


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among 128 major POTWs in the State, the average cost per plant would be $61,000 per year. Chemical and petroleum industries would incur the highest cost of the industrial categories (5.6 percent of the annual costs, with an annual average of $25,200 per plant). About 57 percent of the low-end costs would be associated with pollution prevention activities, while nearly 38 percent would be associated with pursuing alternative methods of compliance under the regulations.

Under the high-end cost scenario, major industrial facilities and POTWs would incur about 94 percent of the potential costs, indirect dischargers would incur about 17 percent of the potential costs, while minor dischargers would incur about 5 percent. Among the major, direct dischargers, two categories would incur the majority of potential costs—major POTWs (82 percent), Chemical/Petroleum Products (9 percent). The average annual per plant cost for different industry categories would ranges from zero to $324,000. The two highest average cost categories would be major POTWs ($324,000 per year) and Chemical/Petroleum Products ($221,264 per year). The shift in proportion of potential costs between direct and indirect dischargers is due to the assumption that more direct dischargers would use end-of-pipe treatment under the high-end scenario. Thus, a smaller proportion of indirect dischargers would be impacted under the high-end scenario, since somemunicipalities are projected to add endof-pipe treatment which would reduce
the need for controls from indirect discharges. Over 91 percent of the
annual costs are for waste minimization and treatment optimization costs. Waste minimization would represent nearly 84% of the total annual costs. Capital and operation and maintenance costs would make up less than 9 percent of
annual costs.

Cost-Effectiveness: Cost-effectiveness
is estimated in terms of the cost of reducing the loadings of toxic pollutantsfrom point sources. The costeffectiveness is derived by dividing the projected annual costs of implementing permit limits based on water quality standards using today’s criteria by thetoxicity-weighted pounds (poundequivalents) of pollutants removed. Pound-equivalents are calculated by multiplying pounds of each pollutant removed by the toxic weight (based on the toxicity of copper) for that pollutant.

Based on this analysis, State implementation of permit limits based on today’s criteria would be responsible
for the reduction of about 1.1 million to 2.7 million toxic pound-equivalents per year, or 15 to 50 percent of the toxicweighted baseline loadings for the highand low-end scenarios, respectively.
The cost-effectiveness of the scenarios would range from $22 (high-end scenario) to $31 (low-end scenario) per pound-equivalent.

2. Benefits

The benefits analysis is intended to provide insight into both the types and potential magnitude of the economic benefits expected as a result of implementation of water quality standards based on today’s criteria. To the extent feasible, empirical estimates of the potential magnitude of the benefits were developed and then compared to the estimated costs of implementing water quality standards based on today’s criteria.

To perform a benefits analysis, the types or categories of benefits that apply
need to be defined. EPA relied on a set of benefits categories that typically apply to changes in the water resource environment. Benefits were categorized as either use benefits or passive (nonuse) benefits depending on whether or not they involve direct use of, or contact with, the resource. The most prominent use benefit categories are those related to recreational fishing, boating, and swimming. Another use benefit category of significance is
human health risk reduction. Human
health risk reductions can be realized through actions that reduce human exposure to contaminants such as exposure through the consumption of fish containing elevated levels of pollutants. Passive use benefits are those improvements in environmental quality that are valued by individuals apart from any use of the resource in question.

Benefits estimates were derived in this study using an approach in which benefits of discrete large-scale changes in water quality beyond present day
conditions were estimated wherever
feasible. A share of those benefits was then apportioned to implementation of water quality standards based on today’s criteria. The apportionment estimate was based on a three-stage process:

First, EPA assessed current total loadings from all sources that are contributing to the toxics-related water quality problems observed in the State. This defines the overall magnitude of loadings. Second, the share of total loadings that are attributable to sources that would be controlled through implementation of water quality standards based on today’s criteria was estimated. Since this analysis was designed to focus only on those controls imposed on point sources, this stage of the process entailed estimating the portion of total loadings originating from point sources. Third, the percentage reduction in loadings expected due to implementation of today’s criteria was estimated and then multiplied by the share of point source loadings to calculate the portion of
benefits that could be attributed to implementation of water quality standards based on today’s criteria.

Total monetized annual benefits were estimated in the range of $6.9 to $74.7 million. By category, annual benefits would be $1.3 to $4.6 million for avoided cancer risk, $2.2 to $15.2 million for recreational angling, and $3.4 to $54.9 million for passive use
benefits.

There are numerous categories of potential or likely benefits that have been omitted from the quantified and
monetized benefit estimates. In terms of potential magnitudes of benefit, the following are likely to be significant
contributors to the underestimation of the monetized values presented above:

• Improvements in water-related (instream and near stream) recreation apart from fishing. The omission of potential motorized and nonmotorized boating,swimming, picnicking, and related instream and stream-side recreational
activities from the benefits estimates could contribute to an appreciable
underestimation of total benefits. Such
recreational activities have been shown in empirical research to be highly valued, and even modest changes in participation and or user values could
lead to sizable benefits statewide. Some of these activities can be closely associated with water quality attributes (notably, swimming). Other recreational activities may be less directly related to the water quality improvements, but might nonetheless increase due to their association with fishing, swimming, or
other activities in which the participants might engage.

• Improvements in consumptive and nonconsumptive land-based recreation, such as hunting and wildlife observation. Improvements in aquatic habitats may lead (via food chain and related ecologic benefit mechanisms) to healthier, larger, and more diverse populations of avian and terrestrial species, such as waterfowl, eagles, and otters. Improvements in the populations for these species could manifest as improved hunting and wildlife viewing opportunities, which might in turn increase participation and user day values for such activities. Although the scope of the benefits analysis has not allowed a quantitative assessment of these values at either pre- or post-rule


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conditions, it is conceivable that these benefits could be appreciable.

• Improvements in human health resulting from reduction of non-cancer risk. EPA estimated that implementation of water quality standards based on the
criteria would result in a reduction of mercury concentrations in fish tissue and, thus, a reduction in the hazard from consumption of mercury contaminated fish. However, EPA was
unable to monetize benefits due to
reduced non-cancer health effects.

• Human health benefits for saltwater anglers outside of San Francisco Bay
were not estimated. The number of saltwater anglers outside of San Francisco Bay is estimated to be 673,000 (based on Huppert, 1989, and U.S. FWS, 1993). The omission of other saltwater anglers may cause human health
benefits to be underestimated. In addition, benefit estimates in the EA may be slightly overstated since potential benefits from reductions in chloroform discharges were included in
these estimates. EPA made a decision to
reserve the chloroform human health criteria after the EA was completed.

EPA received a number of comments which requested the Agency use the cost-benefit analysis in the EA as a factor in setting water quality criteria.
EPA does not use the EA as a basis in determining protective water quality criteria. EPA’s current regulations at 40
CFR 131.11 state that the criteria must
be based on sound scientific rationale and must protect the designated use. From the outset of the water quality standards program, EPA has explained that while economic factors may be considered in designating uses, they may not be used to justify criteria that are not protective of those uses. 44 FR 25223–226, April 30, 1979. See e.g. Mississippi Commission on Natural

Resources v. Costle, 625 F. 2d 1269, 1277 (5th Cir. 1980). EPA reiterated this interpretation of the CWA and its implementing regulations in discussing section 304(a) recommended criteria guidance stating that ‘‘they are based solely on data and scientific judgments on the relationship between pollutant
concentrations and environmental and
human health effects and do not reflect consideration of economic impacts or the technological feasibility of meeting
the chemical concentrations in ambient water.’’ 63 FR 36742 and 36762, July 7,

1998.

I. Executive Order 12866, Regulatory Planning and Review

Under Executive Order 12866 (58 FR 51735, October 4, 1993), the Agency must determine whether the regulatory action is ‘‘significant’’ and therefore subject to Office of Management and Budget (OMB) review and the requirements of the Executive Order. The Order defines ‘‘significant regulatory action’’ as one that is likely to result in a rule that may:

(1) Have an annual effect on the economy of $100 million or more or adversely affect in a material way the economy, a sector of the economy, productivity, competition, jobs, the environment, public health or safety, or State, local, or tribal governments or
communities;

(2) Create a serious inconsistency or
otherwise interfere with an action taken or planned by another Agency;

(3) Materially alter the budgetary impact of entitlements, grants, user fees, or loan programs or the rights and obligations of recipients thereof; or

(4) Raise novel legal or policy issues arising out of legal mandates, the President’s priorities, or the principles
set forth in the Executive Order.

It has been determined that this rule is not a ‘‘significant regulatory action’’
under the terms of Executive Order 12866 and is therefore not subject to

OMB review.

J. Unfunded Mandates Reform Act of

1995

Title II of the Unfunded Mandates Reform Act of 1995 (UMRA), Public Law 104–4, establishes requirements for Federal agencies to assess the effects of their regulatory actions on State, local, and tribal governments and the private sector. Under section 202 of the UMRA, EPA generally must prepare a written statement, including a cost-benefit analysis, for proposed and final rules with ‘‘Federal mandates’’ that may result in expenditures to State, local, and tribal governments, in the aggregate, or to the private sector, of $100 million or more in any one year. Before promulgating any regulation for which a written statement is needed, section 205 of the UMRA generally requires EPA to identify and consider a reasonable number of regulatory alternatives andadopt the least costly, most costeffective or least burdensome alternative that achieves the objectives of the rule. The provisions of section 205 do not apply when they are inconsistent with applicable law. Moreover, section 205 allows an Agency to adopt an alternative other than the least costly,
most cost-effective or least burdensome
alternative if the Administrator publishes with the final rule an explanation why that alternative was not adopted. Before EPA establishes any regulatory requirements that may significantly or uniquely affect small governments, including tribal governments, it must have developed
under section 203 of the UMRA a small government Agency plan. The plan must provide for notifying potentially affected small governments, enabling
officials of the affected small governments to have meaningful and timely input in the development of regulatory proposals with significant Federal intergovernmental mandates, and EPA informing, educating, and advising small governments on compliance with the regulatory requirements.

Today’s rule contains no Federal mandates (under the regulatory provisions of Title II of the Unfunded Mandates Reform Act (UMRA)) for State, local, or tribal governments or the private sector. Today’s rule imposes no enforceable duty on any State, local or Tribal governments or the private sector; rather, the CTR promulgates ambient water quality criteria which, when combined with State-adopted uses, will create water quality standards for those water bodies with adopted uses. The State will then use these resulting water quality standards in implementing its existing water quality control programs. Thus, today’s rule is not subject to the requirements of sections 202 and 205 of
the UMRA.

EPA has determined that this rule contains no regulatory requirements that might significantly or uniquely affect small governments. This rule establishes ambient water quality criteria which, by themselves do not directly impact any entity. The State will implement these criteria by ensuring that NPDES permits result in discharges that will meet these criteria. In so doing, the State will have
considerable discretion. Until the State implements these water quality standards, there will be no effect of this rule on any entity. Thus, today’s rule is not subject to the requirements of
section 203 of UMRA.

K. Regulatory Flexibility Act

The Regulatory Flexibility Act generally requires Federal agencies to prepare a regulatory flexibility analysis of any rule subject to notice and comment rulemaking requirements
under the Administrative Procedure Act or any other statute unless the Agency
certifies that the rule will not have a significant economic impact of a
substantial number of small entities. Small entities include small businesses, small organizations, and small governmental jurisdictions. For purposes of assessing the impacts of today’s rule on small entities, small entity is defined as: (1) A small business according to RFA default definitions for small businesses (based on SBA size


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standards); (2) a small governmental jurisdiction that is a government of a city, county, town, school district or special district with a population of less than 50,000; and (3) a small organization that is any not-for-profit enterprise which is independently owned and operated and is not
dominant in its field.

After considering the economic impacts of today’s final rule on small entities, I certify that this action will not have a significant economic impact on
a substantial number of small entities. This final rule will not impose any requirements on small entities.

Under the CWA water quality standards program, States must adopt water quality standards for their waters
that must be submitted to EPA for approval. If the Agency disapproves a
State standard and the State does not adopt appropriate revisions to address EPA’s disapproval, EPA must promulgate standards consistent with the statutory requirements. EPA has authority to promulgate criteria or standards in any case where the
Administrator determines that a revised or new standard is necessary to meet the requirements of the Act. These State standards (or EPA-promulgated standards) are implemented through various water quality control programs including the National Pollutant Discharge Elimination System (NPDES) program that limits discharges to navigable waters except in compliance with an EPA permit or permit issued under an approved State NPDES program. The CWA requires that all NPDES permits must include any limits on discharges that are necessary to meet State water quality standards.

Thus, under the CWA, EPA’s promulgation of water quality criteria or
standards establishes standards that the State, in turn, implements through the NPDES permit process. The State has considerable discretion in deciding how to meet the water quality standards and in developing discharge limits as
needed to meet the standards. In
circumstances where there is more than one discharger to a water body that is subject to water quality standards or criteria, a State also has discretion in deciding on the appropriate limits for the different dischargers. While theState’s implementation of federallypromulgated water quality criteria or standards may result indirectly in new or revised discharge limits for small entities, the criteria or standards themselves do not apply to any discharger, including small entities.

Today’s rule, as explained above, does not itself establish any requirements that are applicable to small entities. As a result of EPA’s action here, the State
of California will need to ensure that permits it issues include limits as necessary to meet the water quality standards established by the criteria in today’s rule. In so doing, the State will have a number of discretionary choices associated with permit writing. While California’s implementation of today’s rule may ultimately result in some new or revised permit conditions for some dischargers, including small entities, EPA’s action today does not impose any of these as yet unknown requirements
on small entities.

The RFA requires analysis of the economic impact of a rule only on the small entities subject to the rule’s requirements. Courts have consistently held that the RFA imposes no obligation on an Agency to prepare a small entity analysis of the effect of a rule on entities not regulated by the rule. Motor & Equip. Mrfrs. Ass’n v. Nichols, 142 F.3d 449, 467 & n.18 (D.C. Cir. 1998)(quoting United States Distribution Companies v. FERC, 88 F.3d 1105, 1170 (D.C. Cir. 1996); see also American Trucking
Association, Inc. v. EPA, 175 F.3d 1027 (D.C. Cir. 1999). This final rule will have a direct effect only on the State of California which is not a small entity under the RFA. Thus, individual dischargers, including small entities, are not directly subject to the requirements of the rule. Moreover, because of California’s discretion in implementing these standards, EPA cannot assess the extent to which the promulgation of this rule may subsequently affect any dischargers, including small entities. Consequently, certification under section 605(b) is appropriate. State of Michigan, et al. v. U.S. Environmental Protection Agency, No. 98–1497 (D.C. Cir. Mar. 3, 2000), slip op. at 41–42.

L. Paperwork Reduction Act

This action requires no new or additional information collection, reporting, or record keeping subject to the Paperwork Reduction Act, 44 U.S.C.

3501 et seq.

M. Endangered Species Act

Pursuant to section 7(a) of the Endangered Species Act (ESA), EPA has
consulted with the U.S. Fish and
Wildlife Service and the U.S. National Marine Fisheries Service (collectively, the Services) concerning EPA’s rulemaking action for the State of
California. EPA initiated informal consultation in early 1994, and completed formal consultation in April 2000. As a result of the consultation, EPA modified some of the provisions in
the final rule. As part of the consultation process,
EPA submitted to the Services a Biological Evaluation for their review in
October of 1997. This evaluation found that the proposed CTR was not likely to jeopardize the continued existence of any Federally listed species or result in
the destruction or adverse modification of designated critical habitat. In April of 1998, the Services sent EPA a draft Biological Opinion which tentatively found that EPA’s proposed rule would jeopardize the continued existence of several Federally listed species and
result in the destruction or have adverse effect on designated critical habitat. After lengthy discussions with the Services, EPA agreed to several changes
in the final rule and the Services in turn issued a final Biological Opinion finding that EPA’s action would not likely jeopardize the continued existence of any Federally listed species
or result in the destruction or adverse modification of designated critical habitat. EPA’s Biological Evaluation and the Services’ final Biological Opinion
are contained in the administrative record for today’s rule.

In order to ensure the continued protection of Federally listed threatened and endangered species and to protect their critical habitat, EPA agreed to reserve the aquatic life criteria for mercury and the acute freshwater aquatic life criterion for selenium. The Services believe that EPA’s proposed criteria are not sufficiently protective of Federally listed species and should not be promulgated. EPA agreed that it would reevaluate these criteria in light
of the Services concerns before promulgating them for the State of California. Other commitments made by
EPA are described in a letter to the Services dated December 16, 1999; this
letter is contained in the administrative record for today’s rule.

N. Congressional Review Act

The Congressional Review Act, 5

U.S.C. 801 et seq. , as added by the Small Business Regulatory Enforcement Fairness Act of 1996, generally provides that before a rule may take effect, the Agency promulgating the rule must submit a rule report, which includes a copy of the rule, to each House of the Congress and to the Comptroller General
of the United States. EPA will submit a report containing this rule and other required information to the U.S. Senate, the U.S. House of Representatives, and the Comptroller General of the United States prior to publication of the rule in
the Federal Register . A major rule cannot take effect until 60 days after it is published in the Federal Register

. This rule is not a major rule as defined


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by 5 U.S.C. 804(2). This rule will be effective May 18, 2000.

O. Executive Order 13084, Consultation
and Coordination With Indian Tribal

Governments

Under Executive Order 13084, EPA may not issue a regulation that is not required by statute, that significantly or uniquely affects the communities of Indian tribal governments, and that imposes substantial direct compliance costs on those communities, unless the Federal government provides the funds necessary to pay the direct compliance costs incurred by the tribal governments, or EPA consults with those governments. If EPA complies by consulting, Executive Order 13084 requires EPA to provide to the Office of Management and Budget, in a separately identified section of the preamble to the rule, a description of the extent of EPA’s prior consultation with representatives of affected tribal governments, a summary of the nature of their concerns, and a statement supporting the need to issue the regulation. In addition, Executive Order 13084 requires EPA to develop an effective process permitting
elected officials and other representatives of Indian tribal governments ‘‘to provide meaningful and timely input in the development of regulatory policies on matters that significantly or uniquely affect their

communities.’’

Today’s rule does not significantly or uniquely affect the communities of Indian tribal governments nor does it impose substantial direct compliance cots on them. Today’s rule will only address priority toxic pollutant water quality criteria for the State of California and does not apply to waters in Indian country. Accordingly, the requirements of section 3(b) of Executive Order 13084 do not apply to this rule.

P. National Technology Transfer and
Advancement Act

Section 12(d) of the National Technology Transfer and Advancement Act of 1995 (‘‘NTTAA’’), Public Law No. 104–113, section 12(d) (15 U.S.C. 272 note) directs EPA to use voluntary consensus standards in its regulatory
activities unless to do so would be inconsistent with applicable law or otherwise impractical. Voluntary
consensus standards are technical standards (e.g., materials specifications, test methods, sampling procedures, and business practices) that are developed or adopted by voluntary consensus
standards bodies. The NTTAA directs EPA to provide Congress, through OMB, explanations when the Agency decides not to use available and applicable voluntary consensus standards.

This final rule does not involve technical standards. Therefore, EPA did not consider the use of any voluntary
consensus standards.

Q. Executive Order 13132 on
Federalism

Executive Order 13132, entitled ‘‘Federalism’’ (64 FR 43255, August 10, 1999), requires EPA to develop an accountable process to ensure ‘‘meaningful and timely input by State and local officials in the development of regulatory policies that have federalism implications.’’ ‘‘Policies that have federalism implications’’ is defined in
the Executive Order to include regulations that have ‘‘substantial direct effects on the States, on the relationship between the national government and the States, or on the distribution of power and responsibilities among the various levels of government.’’

Under section 6 of Executive Order 13132, EPA may not issue a regulation that has federalism implications, that imposes substantial direct compliance costs, and that is not required by statute, unless the Federal government provides the funds necessary to pay the direct compliance costs incurred by State and local governments, or EPA consults with State and local officials early in the process of developing the proposed regulation. EPA also may not issue a regulation that has federalism implications and that preempts State law, unless the Agency consults with State and local officials early in the process of developing the proposed regulation.

This final rule does not have federalism implications. It will not have substantial direct effects on the States, on the relationship between the national government and the States, or on the distribution of power and responsibilities among the various levels of government, as specified in
Executive Order 13132. The rule does not affect the nature of the relationship between EPA and States generally, for the rule only applies to water bodies in California. Further, the rule will not substantially affect the relationship of EPA and the State of California, or the distribution of power or responsibilities
between EPA and the State. The rule does not alter the State’s authority to issue NPDES permits or the State’s considerable discretion in implementing these criteria. The rule simply implements Clean Water Act section 303(c)(2)(B) requiring numeric ambient water quality criteria for which EPA has issued section 304(a) recommended
criteria in a manner that is consistent with previous regulatory guidance that the Agency has issued to implement CWA section 303(c)(2)(B). Further, this rule does not preclude the State from adopting water quality standards that meet the requirements of the CWA. Thus, the requirements of section 6 of the Executive Order do not apply to this
rule.

Although section 6 of Executive Order 13132 does not apply to this rule, EPA
did consult with State and local government representatives in developing this rule. EPA and the State reached an agreement that to best utilize its respective resources, EPA would promulgate water quality criteria and the State would concurrently work on a plan to implement the criteria. Since the proposal of this rule, EPA has kept State officials fully informed of changes to the proposal. EPA has continued to invite
comment from the State on these changes. EPA believes that the final CTR incorporates comments from State
officials and staff.

R. Executive Order 13045 on Protection
of Children From Environmental Health Risks and Safety Risks

Executive Order 13045: ‘‘Protection of
Children from Environmental Health Risks and Safety Risks’’ (62 FR 19885, April 23, 1997) applies to any rule that: (1) Is determined to be ‘‘economically significant’’ as defined under Executive Order 12866, and (2) concerns an environmental health or safety risk that EPA has reason to believe may have a disproportionate effect on children. If the regulatory action meets both criteria, the Agency must evaluate the environmental health or safety effects of the planned rule on children, and explain why the planned regulation is preferable to other potentially effective and reasonably feasible alternatives considered by the Agency.

While this final rule is not subject to
the Executive Order because it is not economically significant as defined in Executive Order 12866, we nonetheless
have reason to believe that the environmental health or safety risk addressed by this action may have a disproportionate effect on children. As a matter of EPA policy, we therefore
have assessed the environmental health or safety effects of ambient water quality
criteria on children. The results of this assessment are contained in section F.3.,
Human Health Criteria.

List of Subjects in 40 CFR Part 131

Environmental protection, Indians— lands, Intergovernmental relations, Reporting and recordkeeping requirements, Water pollution control.


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Dated: April 27, 2000.

Carol Browner,

Administrator.

For the reasons set out in the preamble, part 131 of chapter I of title 40 of the Code of Federal Regulations is

amended as follows:

PART 131—WATER QUALITY

STANDARDS

1. The authority citation for part 131

continues to read as follows: Authority: 33 U.S.C. 1251 et seq.

Subpart D—[Amended]

2. Section 131.38 is added to subpart

D to read as follows:

§ 131.38 Establishment of Numeric Criteria for Priority Toxic Pollutants for the State of

California.

(a) Scope. This section promulgates criteria for priority toxic pollutants in

the State of California for inland surface waters and enclosed bays and estuaries. This section also contains a compliance schedule provision.

(b)(1) Criteria for Priority Toxic

Pollutants in the State of California as described in the following table:

BILLING CODE 6560–50–P


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BILLING CODE 6560–50–C


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Footnotes to Table in Parargraph (b)(1):

a. Criteria revised to reflect the Agency q1* or RfD, as contained in the Integrated Risk Information System (IRIS) as of October 1,

1996. The fish tissue bioconcentration factor (BCF) from the 1980 documents was retained

in each case.

b. Criteria apply to California waters except for those waters subject to objectives in

Tables III–2A and III–2B of the San Francisco Regional Water Quality Control Board’s (SFRWQCB) 1986 Basin Plan, that were adopted by the SFRWQCB and the State Water Resources Control Board, approved by EPA, and which continue to apply.

c. Criteria are based on carcinogenicity of 10 (-6) risk.

d. Criteria Maximum Concentration (CMC) equals the highest concentration of a pollutant to which aquatic life can be exposed for a short period of time without

deleterious effects. Criteria Continuous Concentration (CCC) equals the highest concentration of a pollutant to which aquatic life can be exposed for an extended period of time (4 days) without deleterious effects. ug/L equals micrograms per liter.

e. Freshwater aquatic life criteria for metals are expressed as a function of total hardness (mg/L) in the water body. The equations are provided in matrix at paragraph (b)(2) of this section. Values displayed above in the matrix correspond to a total hardness of 100 mg/l.

f. Freshwater aquatic life criteria for pentachlorophenol are expressed as a function of pH, and are calculated as follows: Values displayed above in the matrix correspond to a pH of 7.8. CMC = exp(1.005(pH)

¥ 4.869). CCC = exp(1.005(pH)

¥ 5.134).

g. This criterion is based on 304(a) aquatic life criterion issued in 1980, and was issued in one of the following documents: Aldrin/ Dieldrin (EPA 440/5–80–019), Chlordane (EPA 440/5–80–027), DDT (EPA 440/5–80– 038), Endosulfan (EPA 440/5–80–046), Endrin (EPA 440/5–80–047), Heptachlor (440/5–80–052), Hexachlorocyclohexane (EPA 440/5–80–054), Silver (EPA 440/5–80– 071). The Minimum Data Requirements and derivation procedures were different in the

1980 Guidelines than in the 1985 Guidelines. For example, a ‘‘CMC’’ derived using the

1980 Guidelines was derived to be used as

an instantaneous maximum. If assessment is to be done using an averaging period, the values given should be divided by 2 to obtain a value that is more comparable to a CMC derived using the 1985 Guidelines.

h. These totals simply sum the criteria in each column. For aquatic life, there are 23 priority toxic pollutants with some type of freshwater or saltwater, acute or chronic criteria. For human health, there are 92 priority toxic pollutants with either ‘‘water + organism’’ or ‘‘organism only’’ criteria. Note

that these totals count chromium as one pollutant even though EPA has developed

criteria based on two valence states. In the matrix, EPA has assigned numbers 5a and 5b

to the criteria for chromium to reflect the fact that the list of 126 priority pollutants includes only a single listing for chromium.

i. Criteria for these metals are expressed as a function of the water-effect ratio, WER, as defined in paragraph (c) of this section. CMC = column B1 or C1 value x WER; CCC =

column B2 or C2 value x WER.

j. No criterion for protection of human health from consumption of aquatic organisms (excluding water) was presented

in the 1980 criteria document or in the 1986 Quality Criteria for Water. Nevertheless, sufficient information was presented in the

1980 document to allow a calculation of a criterion, even though the results of such a

calculation were not shown in the document.

k. The CWA 304(a) criterion for asbestos is

the MCL.

l. [Reserved]

m. These freshwater and saltwater criteria for metals are expressed in terms of the

dissolved fraction of the metal in the water column. Criterion values were calculated by using EPA’s Clean Water Act 304(a) guidance values (described in the total recoverable fraction) and then applying the conversion factors in § 131.36(b)(1) and (2).

n. EPA is not promulgating human health criteria for these contaminants. However, permit authorities should address these contaminants in NPDES permit actions using the State’s existing narrative criteria for

toxics.

o. These criteria were promulgated for specific waters in California in the National Toxics Rule (‘‘NTR’’), at § 131.36. The specific waters to which the NTR criteria apply include: Waters of the State defined as bays or estuaries and waters of the State defined as inland, i.e., all surface waters of

the State not ocean waters. These waters specifically include the San Francisco Bay upstream to and including Suisun Bay and the Sacramento-San Joaquin Delta. This section does not apply instead of the NTR for

this criterion.

p. A criterion of 20 ug/l was promulgated for specific waters in California in the NTR and was promulgated in the total recoverable form. The specific waters to which the NTR criterion applies include: Waters of the San Francisco Bay upstream to and including Suisun Bay and the Sacramento-San Joaquin Delta; and waters of Salt Slough, Mud Slough (north) and the San Joaquin River, Sack Dam

to the mouth of the Merced River. This section does not apply instead of the NTR for this criterion. The State of California adopted and EPA approved a site specific criterion for the San Joaquin River, mouth of Merced to Vernalis; therefore, this section does not apply to these waters.

q. This criterion is expressed in the total

recoverable form. This criterion was promulgated for specific waters in California in the NTR and was promulgated in the total recoverable form. The specific waters to which the NTR criterion applies include: Waters of the San Francisco Bay upstream to and including Suisun Bay and the Sacramento-San Joaquin Delta; and waters of Salt Slough, Mud Slough (north) and the San Joaquin River, Sack Dam to Vernalis. This criterion does not apply instead of the NTR for these waters. This criterion applies to

additional waters of the United States in the State of California pursuant to 40 CFR 131.38(c). The State of California adopted and EPA approved a site-specific criterion for the Grassland Water District, San Luis National Wildlife Refuge, and the Los Banos State Wildlife Refuge; therefore, this criterion does not apply to these waters.

r. These criteria were promulgated for specific waters in California in the NTR. The specific waters to which the NTR criteria apply include: Waters of the State defined as bays or estuaries including the San Francisco Bay upstream to and including Suisun Bay and the Sacramento-San Joaquin Delta. This section does not apply instead of the NTR for

these criteria.

s. These criteria were promulgated for specific waters in California in the NTR. The specific waters to which the NTR criteria apply include: Waters of the Sacramento-San Joaquin Delta and waters of the State defined as inland ( i.e., all surface waters of the State not bays or estuaries or ocean) that include a MUN use designation. This section does not apply instead of the NTR for these

criteria.

t. These criteria were promulgated for specific waters in California in the NTR. The specific waters to which the NTR criteria apply include: Waters of the State defined as bays and estuaries including San Francisco Bay upstream to and including Suisun Bay and the Sacramento-San Joaquin Delta; and waters of the State defined as inland (i.e., all surface waters of the State not bays or estuaries or ocean) without a MUN use designation. This section does not apply

instead of the NTR for these criteria.

u. PCBs are a class of chemicals which include aroclors 1242, 1254, 1221, 1232, 1248, 1260, and 1016, CAS numbers

53469219, 11097691, 11104282, 11141165, 12672296, 11096825, and 12674112, respectively. The aquatic life criteria apply to

the sum of this set of seven aroclors.

v. This criterion applies to total PCBs, e.g., the sum of all congener or isomer or homolog or aroclor analyses.

w. This criterion has been recalculated pursuant to the 1995 Updates: Water Quality

Criteria Documents for the Protection of Aquatic Life in Ambient Water, Office of Water, EPA–820-B–96–001, September 1996. See also Great Lakes Water Quality Initiative

Criteria Documents for the Protection of Aquatic Life in Ambient Water, Office of Water, EPA–80–B–95–004, March 1995.

x. The State of California has adopted and EPA has approved site specific criteria for the Sacramento River (and tributaries) above Hamilton City; therefore, these criteria do not apply to these waters.

General Notes to Table in Paragraph (b)(1)

1. The table in this paragraph (b)(1) lists all of EPA’s priority toxic pollutants whether or not criteria guidance are available. Blank spaces indicate the absence of national section 304(a) criteria guidance. Because of variations in chemical nomenclature systems, this listing of toxic pollutants does not duplicate the listing in Appendix A to 40 CFR Part 423–126 Priority Pollutants. EPA

has added the Chemical Abstracts Service (CAS) registry numbers, which provide a unique identification for each chemical.

2. The following chemicals have organoleptic-based criteria recommendations that are not included on this chart: zinc, 3- methyl-4-chlorophenol.


### 31717 Federal Register / Vol. 65, No. 97 / Thursday, May 18, 2000 / Rules and Regulations

3. Freshwater and saltwater aquatic life criteria apply as specified in paragraph (c)(3)

of this section.

(2) Factors for Calculating Metals
Criteria. Final CMC and CCC values should be rounded to two significant figures.

(i) CMC = WER × (Acute Conversion

Factor) × (exp { m A [1n (hardness)]+ b A } ) (ii) CCC = WER × (Acute Conversion Factor) × (exp { m C [1n (hardness)]+ b C} ) (iii) Table 1 to paragraph (b)(2) of this

section:

Metal m A bA m C b C

Cadmium .................................................................................................. 1.128

¥ 3.6867 0.7852

¥ 2.715 Copper ..................................................................................................... 0.9422

¥ 1.700 0.8545

¥ 1.702 Chromium (III) .......................................................................................... 0.8190 3.688 0.8190 1.561

Lead ......................................................................................................... 1.273

¥ 1.460 1.273

¥ 4.705

Nickel ....................................................................................................... 0.8460 2.255 0.8460 0 .0584
Silver ........................................................................................................ 1.72

¥ 6.52

Zinc .......................................................................................................... 0.8473 0.884 0.8473 0.884

Note to Table 1: The term ‘‘exp’’ represents the base e exponential function.

(iv) Table 2 to paragraph (b)(2) of this section:

Metal Conversion factor (CF) for
freshwater acute
criteria CF for freshwater chronic
criteria CF for saltwater
acute criteria CF a for saltwater chronic
criteria

Antimony ................................................................................................ ( d) (d) ( d) (d)

Arsenic ................................................................................................... 1.000 1.000 1.000 1.000 Beryllium ................................................................................................ ( d) (d) ( d) (d)

Cadmium ................................................................................................ b 0.944 b 0.909 0.994 0.994 Chromium (III) ........................................................................................ 0.316 0.860 ( d) (d) Chromium (VI) ....................................................................................... 0.982 0.962 0.993 0.993 Copper ................................................................................................... 0.960 0.960 0.83 0.83

Lead ....................................................................................................... b 0.791 b 0.791 0.951 0.951 Mercury .................................................................................................. ......................

...... .......................... .......................... .......................... Nickel ..................................................................................................... 0.998 0.997 0.990 0.990
Selenium ................................................................................................ ....................... ..... (c) 0.998 0.998 Silver ...................................................................................................... 0.85 (d) 0.85 (d) Thallium ................................................................................................. ( d) (d) ( d) (d)

Zinc ........................................................................................................ 0.978 0.986 0.946 0.946

Footnotes to Table 2 of Paragraph (b)(2):

a Conversion Factors for chronic marine criteria are not currently available. Conversion Factors for acute marine criteria have been used for
both acute and chronic marine criteria.

b Conversion Factors for these pollutants in freshwater are hardness dependent. CFs are based on a hardness of 100 mg/l as calciu m carbonate (CaCO 3 ). Other hardness can be used; CFs should be recalculated using the equations in table 3 to paragraph (b)(2) of this section.

c Bioaccumulative compound and inappropriate to adjust to percent dissolved.

d EPA has not published an aquatic life criterion value.

Note to Table 2 of Paragraph (b)(2): The term ‘‘Conversion Factor’’ represents the
recommended conversion factor for converting a metal criterion expressed as the
total recoverable fraction in the water column to a criterion expressed as the dissolved fraction in the water column. See ‘‘Office of Water Policy and Technical Guidance on Interpretation and Implementation of Aquatic Life Metals Criteria’’, October 1, 1993, by Martha G. Prothro, Acting Assistant
Administrator for Water available from Water Resource Center, USEPA, Mailcode RC4100, M Street SW, Washington, DC, 20460 and the note to § 131.36(b)(1).

(v) Table 3 to paragraph (b)(2) of this

section:

Acute Chronic

Cadmium .............................. CF=1.136672—[(ln { hardness } ) (0.041838)] .................. CF = 1.101672—[(ln { hardness } )(0.041838)] Lead ..................................... CF=1.46203—[(ln { hardness } )(0.145712)] ..................... CF = 1.46203—[(ln { hardness } )(0.145712)]

(c) Applicability. (1) The criteria in paragraph (b) of this section apply to the State’s designated uses cited in paragraph (d) of this section and apply concurrently with any criteria adopted by the State, except when State regulations contain criteria which are more stringent for a particular parameter and use, or except as provided in footnotes p, q, and x to the table in paragraph (b)(1) of this section.

(2) The criteria established in this section are subject to the State’s general rules of applicability in the same way
and to the same extent as are other Federally-adopted and State-adopted numeric toxics criteria when applied to the same use classifications including mixing zones, and low flow values
below which numeric standards can be exceeded in flowing fresh waters.

(i) For all waters with mixing zone regulations or implementation procedures, the criteria apply at the appropriate locations within or at the boundary of the mixing zones; otherwise the criteria apply throughout the water body including at the point of discharge into the water body.

(ii) The State shall not use a low flow

value below which numeric standards can be exceeded that is less stringent than the flows in Table 4 to paragraph (c)(2) of this section for streams and

rivers.

(iii) Table 4 to paragraph (c)(2) of this

section:


### 31718 Federal Register / Vol. 65, No. 97 / Thursday, May 18, 2000 / Rules and Regulations

Criteria Design flow

Aquatic Life Acute

Criteria (CMC). 1 Q 10 or 1 B 3

Aquatic Life Chronic

Criteria (CCC). 7 Q 10 or 4 B 3

Human Health Criteria. Harmonic Mean Flow

Note to Table 4 of Paragraph (c)(2): 1. CMC (Criteria Maximum Concentration) is the water quality criteria to protect against acute effects in aquatic life and is the highest instream concentration of a priority toxic pollutant consisting of a short-term average not to be exceeded more than once every three years on the average.

2. CCC (Continuous Criteria Concentration) is the water quality criteria to protect against chronic effects in aquatic life and is the highest in stream concentration of a priority toxic pollutant consisting of a 4-day average not to be exceeded more than once every three years on the average.

3. 1 Q 10 is the lowest one day flow with an average recurrence frequency of once in 10 years determined hydrologically.

4. 1 B 3 is biologically based and indicates an allowable exceedence of once every 3 years. It is determined by EPA’s computerized method (DFLOW model).

5. 7 Q 10 is the lowest average 7 consecutive day low flow with an average recurrence frequency of once in 10 years determined hydrologically.

6. 4 B 3 is biologically based and indicates

an allowable exceedence for 4 consecutive days once every 3 years. It is determined by EPA’s computerized method (DFLOW model).

(iv) If the State does not have such a

low flow value below which numeric standards do not apply, then the criteria included in paragraph (d) of this section apply at all flows.

(v) If the CMC short-term averaging period, the CCC four-day averaging period, or once in three-year frequency is inappropriate for a criterion or the site to which a criterion applies, the State may apply to EPA for approval of an alternative averaging period, frequency, and related design flow. The

State must submit to EPA the bases for any alternative averaging period, frequency, and related design flow. Before approving any change, EPA will publish for public comment, a document proposing the change.

(3) The freshwater and saltwater aquatic life criteria in the matrix in paragraph (b)(1) of this section apply as

follows:

(i) For waters in which the salinity is equal to or less than 1 part per thousand 95% or more of the time, the applicable

criteria are the freshwater criteria in Column B; (ii) For waters in which the salinity is equal to or greater than 10 parts per thousand 95% or more of the time, the applicable criteria are the saltwater criteria in Column C except for selenium in the San Francisco Bay estuary where the applicable criteria are

the freshwater criteria in Column B (refer to footnotes p and q to the table in paragraph (b)(1) of this section); and

(iii) For waters in which the salinity is between 1 and 10 parts per thousand as defined in paragraphs (c)(3)(i) and (ii) of this section, the applicable criteria are the more stringent of the freshwater or saltwater criteria. However, the Regional Administrator may approve

the use of the alternative freshwater or saltwater criteria if scientifically

defensible information and data demonstrate that on a site-specific basis the biology of the water body is dominated by freshwater aquatic life

and that freshwater criteria are more appropriate; or conversely, the biology of the water body is dominated by saltwater aquatic life and that saltwater criteria are more appropriate. Before approving any change, EPA will publish for public comment a document proposing the change.

(4) Application of metals criteria. (i) For purposes of calculating freshwater aquatic life criteria for metals from the equations in paragraph (b)(2) of this section, for waters with a hardness of 400 mg/l or less as calcium carbonate,

the actual ambient hardness of the

surface water shall be used in those equations. For waters with a hardness of over 400 mg/l as calcium carbonate, a hardness of 400 mg/l as calcium

carbonate shall be used with a default Water-Effect Ratio (WER) of 1, or the

actual hardness of the ambient surface

water shall be used with a WER. The same provisions apply for calculating the metals criteria for the comparisons provided for in paragraph (c)(3)(iii) of

this section.

(ii) The hardness values used shall be consistent with the design discharge conditions established in paragraph (c)(2) of this section for design flows and mixing zones.

(iii) The criteria for metals (compounds #1—#13 in the table in paragraph (b)(1) of this section) are expressed as dissolved except where otherwise noted. For purposes of calculating aquatic life criteria for metals from the equations in footnote i to the table in paragraph (b)(1) of this section and the equations in paragraph (b)(2) of this section, the water effect ratio is generally computed as a specific pollutant’s acute or chronic toxicity

value measured in water from the site covered by the standard, divided by the respective acute or chronic toxicity value in laboratory dilution water. To

use a water effect ratio other than the default of 1, the WER must be

determined as set forth in Interim

Guidance on Determination and Use of Water Effect Ratios, U.S. EPA Office of Water, EPA–823–B–94–001, February 1994, or alternatively, other scientifically defensible methods adopted by the State as part of its water quality standards program and approved by EPA. For calculation of criteria using site-specific values for both the hardness and the water effect ratio, the hardness used in the equations in paragraph (b)(2) of this section must be determined as required in paragraph (c)(4)(ii) of this section. Water hardness

must be calculated from the measured calcium and magnesium ions present, and the ratio of calcium to magnesium should be approximately the same in standard laboratory toxicity testing

water as in the site water.

(d)(1) Except as specified in paragraph (d)(3) of this section, all waters assigned any aquatic life or human health use classifications in the Water Quality

Control Plans for the various Basins of the State (‘‘Basin Plans’’) adopted by the

California State Water Resources Control Board (‘‘SWRCB’’), except for ocean waters covered by the Water Quality Control Plan for Ocean Waters of California (‘‘Ocean Plan’’) adopted by

the SWRCB with resolution Number 90– 27 on March 22, 1990, are subject to the criteria in paragraph (d)(2) of this section, without exception. These criteria apply to waters identified in the Basin Plans. More particularly, these criteria apply to waters identified in the Basin Plan chapters designating

beneficial uses for waters within the region. Although the State has adopted several use designations for each of these waters, for purposes of this action, the specific standards to be applied in paragraph (d)(2) of this section are based on the presence in all waters of some aquatic life designation and the presence or absence of the MUN use designation (municipal and domestic supply). (See Basin Plans for more detailed use definitions.)

(2) The criteria from the table in paragraph (b)(1) of this section apply to

the water and use classifications defined in paragraph (d)(1) of this section as

follows:


### 31719 Federal Register / Vol. 65, No. 97 / Thursday, May 18, 2000 / Rules and Regulations

Water and use classification Applicable criteria

(i) All inland waters of the United States or enclosed bays

and estuaries that are waters of the United States that include a MUN use designation. (A) Columns B1 and B2—all pollutants (B) Columns C1 and C2—all pollutants (C) Column D1—all pollutants

(ii) All inland waters of the United States or enclosed bays

and estuaries that are waters of the United States that do not include a MUN use designation. (A) Columns B1 and B2—all pollutants (B) Columns C1 and C2—all pollutants (C) Column D2—all pollutants

(3) Nothing in this section is intended to apply instead of specific criteria, including specific criteria for the San Francisco Bay estuary, promulgated for
California in the National Toxics Rule at § 131.36.

(4) The human health criteria shall be applied at the State-adopted 10 (

¥ 6)
risk level.

(5) Nothing in this section applies to waters located in Indian Country.

(e) Schedules of compliance. (1) It is presumed that new and existing point source dischargers will promptly comply with any new or more restrictive water quality-based effluent limitations (‘‘WQBELs’’) based on the water quality criteria set forth in this

section.

(2) When a permit issued on or after May 18, 2000 to a new discharger contains a WQBEL based on water quality criteria set forth in paragraph (b) of this section, the permittee shall comply with such WQBEL upon the commencement of the discharge. A new discharger is defined as any building, structure, facility, or installation from which there is or may be a ‘‘discharge of pollutants’’ (as defined in 40 CFR 122.2) to the State of California’s inland surface waters or enclosed bays and estuaries, the construction of which commences after May 18, 2000. (3) Where an existing discharger reasonably believes that it will be infeasible to promptly comply with a new or more restrictive WQBEL based on the water quality criteria set forth in this section, the discharger may request approval from the permit issuing authority for a schedule of compliance.

(4) A compliance schedule shall require compliance with WQBELs based on water quality criteria set forth in paragraph (b) of this section as soon as possible, taking into account the dischargers’ technical ability to achieve compliance with such WQBEL.

(5) If the schedule of compliance exceeds one year from the date of permit issuance, reissuance or modification,
the schedule shall set forth interim requirements and dates for their achievement. The dates of completion between each requirement may not exceed one year. If the time necessary for completion of any requirement is more than one year and is not readily divisible into stages for completion, the permit shall require, at a minimum, specified dates for annual submission of progress reports on the status of interim requirements.

(6) In no event shall the permit issuing authority approve a schedule of compliance for a point source discharge which exceeds five years from the date of permit issuance, reissuance, or modification, whichever is sooner. Where shorter schedules of compliance are prescribed or schedules of compliance are prohibited by law, those provisions shall govern.

(7) If a schedule of compliance exceeds the term of a permit, interim permit limits effective during the permit shall be included in the permit and addressed in the permit’s fact sheet or

statement of basis. The administrative record for the permit shall reflect final permit limits and final compliance dates. Final compliance dates for final permit limits, which do not occur during the term of the permit, must occur within five years from the date of issuance, reissuance or modification of the permit which initiates the compliance schedule. Where shorter schedules of compliance are prescribed or schedules of compliance are prohibited by law, those provisions shall govern.

(8) The provisions in this paragraph (e), Schedules of compliance, shall expire on May 18, 2005.

[FR Doc. 00–11106 Filed 5–17–00; 8:45 am]

BILLING CODE 6560–50–P