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The document was marked with 37 Deletions, 53 Insertions, 1 Move. 6560 50 P U. S. ENVIRONMENTAL PROTECTION AGENCY 40 CFR Part 63 [ OAR 2005 0155; FRL ]

RIN 2060 AK18 National Perchloroethylene Air Emission Standards for Dry Cleaning Facilities AGENCY: Environmental Protection Agency ( EPA).

ACTION: Proposed rule.

SUMMARY: The EPA is proposing revised standards to limit emissions of perchloroethylene ( PCE) from existing and new dry cleaning facilities. In 1993, EPA promulgated technology based emission standards to control emissions of PCE from dry cleaning facilities. As required by section 112( d)( 6) of the Clean Air Act ( CAA), EPA has reviewed the standards and is proposing revisions to take into account new developments in production practices, processes, and control technologies. In addition, pursuant to CAA section 112( f), EPA has evaluated the remaining risk to public health and the environment following implementation of the technology based rule and is proposing more stringent standards in order to protect public health with an ample margin of safety. The proposed standards are expected to provide further reductions of PCE beyond the 1993 national emission standards for hazardous air pollutants ( NESHAP),

based on application of equipment and work practice 3 standards.

DATES: Comments. Comments must be received on or before [ INSERT DATE 60 DAYS AFTER DATE OF PUBLICATION OF THE PROPOSED RULE IN THE FEDERAL REGISTER].

Public Hearing. If anyone contacts EPA requesting to speak at a public hearing by [ INSERT DATE 15 DAYS AFTER DATE OF PUBLICATION OF THE PROPOSED RULE IN THE FEDERAL REGISTER], a public hearing will be held on [ INSERT DATE 30 DAYS AFTER DATE OF PUBLICATION OF THE PROPOSED RULE IN THE FEDERAL REGISTER], and if that date falls on a weekend, the hearing will be held the next business day. Under the Paperwork Reduction Act, comments on the information collection provisions must be received by OMB on or before [ INSERT DATE 30 DAYS AFTER DATE OF PUBLICATION OF THE PROPOSED RULE IN THE FEDERAL REGISTER].

ADDRESSES: Comments. Submit your comments, identified by Docket ID No. OAR 2005 0155, by one of the following methods:

° www. regulations. gov. Follow the on line instructions for submitting comments.

° Agency Web site: http:// www. epa. gov/ edocket.

EDOCKET, EPA's electronic public docket and comment system, will be replaced by an enhanced Federal wide electronic docket management and 4 comment system located at www. regulations. gov.

When that occurs, you will be redirected to that site to access the docket and submit comments.

Follow the on line instructions for submitting comments.

° E mail: a and r Docket@ epa. gov, Attention Docket ID No. OAR 2005 0155.

° Fax: ( 202) 566 1741, Attention Docket ID No. OAR

2005 0155.

° Mail: U. S. Postal Service, send comments to: EPA Docket Center ( 6102T), Attention Docket ID No.

OAR 2005 0155, 1200 Pennsylvania Avenue, NW,

Washington, DC 20460. Please include a total of two copies. In addition, please mail a copy of your comments on the information collection provisions to the Office of Information and Regulatory Affairs, Office of Management and Budget ( OMB), Attn: Desk Officer for EPA, 725 17th St., NW, Washington, DC 20503.

° Hand Delivery: In person or by courier, deliver your comments to: EPA Docket Center ( 6102T),

Attention Docket ID No. OAR 2005 0155, 1301 Constitution Avenue, NW, EPA West Building, Room B 108, Washington, DC 20004. Such deliveries are only accepted during the Docket's normal hours of 5 operation, and special arrangements should be made for deliveries of boxed information. Please include a total of two copies.

Instructions: Direct your comments to Docket ID No. OAR

2005 0155. EPA's policy is that all comments received will be included in the public docket without change and may be made available online at www. regulations. gov, including any personal information provided, unless the comment includes information claimed to be confidential business information ( CBI) or other information whose disclosure is restricted by statute. Do not submit information that you consider to be CBI or otherwise protected through www. regulations. gov or e mail. Send or deliver information identified as CBI to only the following address: Mr. Roberto Morales, OAQPS Document Control Officer, EPA ( C404 02), Attention Docket ID No. OAR 2005 0155, Research Triangle Park, NC 27711.

Clearly mark the part or all of the information that you claim to be CBI. The www. regulations. gov website is an " anonymous access" system, which means EPA will not know your identity or contact information unless you provide it in the body of your comment. If you send an e mail comment directly to EPA without going through www. regulations. gov,

your e mail address will be automatically captured and included as part of the comment that is placed in the public docket and made available on the Internet. If you submit an 6 electronic comment, EPA recommends that you include your name and other contact information in the body of your comment and with any disk or CD ROM you submit. If EPA cannot read your comment due to technical difficulties and cannot contact you for clarification, EPA may not be able to consider your comment. Electronic files should avoid the use of special characters, any form of encryption, and be free of any defects or viruses. For additional information about EPA's public docket visit the EPA Docket Center homepage at http:// www. epa. gov/ epahome/ dockets. htm or see the Federal Register of May 31, 2002 ( 67 FR 38102).

Docket. All documents in the docket are listed in the www. regulations. gov index. Although listed in the index,

some information is not publicly available, e. g., CBI or other information whose disclosure is restricted by statute.

Certain other material, such as copyrighted material, will be publicly available only in hard copy. Publicly available docket materials are available either electronically in www. regulations. gov or in hard copy at the EPA Docket Center, Docket ID No. OAR 2005 0155, EPA West Building, Room B 102, 1301 Constitution Ave., NW, Washington, DC. The EPA Docket Center Public Reading Room is open from 8: 30 a. m. to 4: 30 p. m., Monday through Friday, excluding legal holidays.

The telephone number for the Public Reading Room is ( 202)

566 1744, and the telephone number for the EPA Docket Center 7 is ( 202) 566 1742. A reasonable fee may be charged for copying docket materials.

Public Hearing: If a public hearing is held, it will begin at 10: 00 a. m. and will be held at EPA's campus at 109 T. W.

Alexander Drive, Research Triangle Park, NC, or at an alternate facility nearby. Persons interested in presenting oral testimony or inquiring as to whether a public hearing is to be held should contact Ms. Janet Eck, Coatings and Consumer Products Group, Emission Standards Division, EPA ( C539 03), Research Triangle Park, NC 27711, telephone ( 919)

541 7946., at least 2 days in advance of the hearing. If no one contacts Ms. Eck in advance of the hearing with a request to present oral testimony at the hearing, we will cancel the hearing.

FOR FURTHER INFORMATION CONTACT: For questions about the proposed rule, contact Ms. Rhea Jones, EPA, Office of Air Quality Planning and Standards, Emission Standards Division,

Coatings and Consumer Products Group ( C539 03), Research Triangle Park, NC 27711; telephone number ( 919) 541 2940;

fax number ( 919) 541 5689; e mail address:

jones. rhea@ epa. gov. For questions on the residual risk analysis, contact Mr. Neal Fann, EPA, Office of Air Quality Planning and Standards, Emission Standards Division, Risk and Exposure Assessment Group ( C404 01), Research Triangle 8 Park, NC 27711; telephone number ( 919) 541 0209; fax number ( 919) 541 0840; e mail address: fann. neal@ epa. gov.

SUPPLEMENTARY INFORMATION:

Regulated Entities. Categories and entities potentially regulated by the proposed rule are industrial and commercial PCE dry cleaners. The proposed rule affects the following categories of sources:

Category NAICS1 Code Examples of Potentially Regulated Entities Coin operated Laundries and Dry Cleaners Dry Cleaning and Laundry Services ( except coin operated)

Industrial Launderers 812310 812320 812332 Dry to dry machines Transfer machines Dry to dry machines Transfer machines Dry to dry machines Transfer machines 1 North American Industry Classification System.

This table is not intended to be exhaustive, but rather provides a guide for readers regarding entities likely to be regulated by the proposed rule. To determine whether your facility is regulated by the proposed rule, you should examine the applicability criteria in 40 CFR 63.320 of subpart M ( 1993 Dry Cleaning NESHAP). If you have any questions regarding the applicability of the proposed rule to a particular entity, contact the person listed in the preceding FOR FURTHER INFORMATION CONTACT section.

Submitting CBI. Do not submit information which you claim 9 to be CBI to EPA through EDOCKET, regulations. gov, or email Clearly mark the part or all of the information that you claim to be CBI. For CBI information in a disk or CD ROM that you mail to EPA, mark the outside of the disk or CD ROM as CBI and then identify electronically within the disk or CD ROM the specific information that is claimed as CBI.

In addition to one complete version of the comment that includes information claimed as CBI, a copy of the comment that does not contain the information claimed as CBI must be submitted for inclusion in the public docket. Information marked as CBI will not be disclosed except in accordance with procedures set forth in 40 CFR part 2.

If you have any questions about CBI or the procedures for claiming CBI, please consult either of the persons identified in the FOR FURTHER INFORMATION CONTACT section.

Worldwide Web ( WWW). In addition to being available in the docket, an electronic copy of the proposed rule is also available on the WWW. Following the Administrator's signature, a copy of the proposed rule will be posted on EPA's Technology Transfer Network ( TTN) policy and guidance page for newly proposed or promulgated rules at http:// www. epa. gov/ ttn/ oarpg. The TTN provides information and technology exchange in various areas of air pollution control. 10 Outline. The information presented in this preamble is organized as follows:

I. Background A. What is the statutory authority for regulating hazardous air pollutants ( HAP)? B. What are PCE dry cleaning facilities? C. What are the health effects of PCE? D. What does the 1993 NESHAP require? II. Summary of Proposed Rule A. What are the proposed requirements for major sources? B. What are the proposed requirements for area sources? C. What are the proposed requirements for transfer machines at major and area sources? III. Rationale for the Proposed Rule A. What is our approach for developing residual risk standards? B. How did we estimate residual risk? C. What are the residual risks from major sources? D. What are the options for reducing risk, their costs, and risk reduction impacts for major sources? E. What is our proposed decision on acceptable risk and ample margin of safety for major sources? F. What are the risks from typical area sources? G. What are the options for reducing risk, their costs, and risk reduction impacts for typical area sources? H. What is our proposal for addressing the remaining emissions for typical area sources? I. What are the risks from co residential area sources? J. What is our proposed decision on co residential area sources? K. What determination is EPA proposing pursuant to review of the 1993 Dry Cleaning NESHAP under CAA section 112( d)( 6)? L. What additional changes are we making to the 1993 Dry Cleaning NESHAP? IV. Solicitation of Public Comments A. Additional Requirements for Highest Risk Facilities B. Requirement for PCE Sensor and Lockout as New Source MACT for Major Sources C. Alternative Performance based Standard for Existing Major Sources D. Environmental Impacts of PCE Emissions E. Additional Time for Complying with Provisions for Transfer Machines V. Statutory and Executive Order Reviews A. Executive Order 12866: Regulatory Planning and Review B. Paperwork Reduction Act 11 C. Regulatory Flexibility Act D. Unfunded Mandates Reform Act E. Executive Order 13132: Federalism F. Executive Order 13175: Consultation and Coordination with Indian Tribal Governments G. Executive Order 13045: Protection of Children from Environmental Health and Safety Risks H. Executive Order 13211: Actions Concerning Regulations That Significantly Affect Energy Supply, Distribution, or Use I. National Technology Transfer Advancement Act I. Background A. What is the statutory authority for regulating hazardous air pollutants ( HAP)?

Section 112 of the CAA establishes a two stage regulatory process to address emissions of hazardous air pollutants ( HAP) from stationary sources. In the first stage, after EPA has identified categories of sources emitting one or more of the HAP listed in the CAA, section 112( d) calls for us to promulgate national technology based emission standards for sources within those categories that emit or have the potential to emit any single HAP at a rate of 10 tons or more per year or any combination of HAP at a rate of 25 tons or more per year ( known as major sources),

as well as for certain area sources emitting less than those amounts. These technology based standards must reflect the maximum reductions of HAP achievable ( after considering cost, energy requirements, and non air health and environmental impacts) and are commonly referred to as 12 maximum achievable control technology ( MACT) standards.

For area sources, CAA section 112( d)( 5) provides that the standards may reflect generally available control technology or management practices in lieu of MACT, and are commonly referred to as generally available control technology ( GACT) standards. We published MACT and GACT standards for PCE dry cleaning facilities on September 22,

1993 at 58 FR 49376. The EPA is then required, pursuant to section 112 ( d)( 6), to review these technology based standards and to revise them " as necessary, taking into account developments in practices, processes and control technologies," no less frequently than every 8 years.

The second stage in standard setting is described in section 112( f) of the CAA. This provision requires, first,

that EPA prepare a Report to Congress discussing ( among other things) methods of calculating risk posed ( or potentially posed) by sources after implementation of the MACT standards, the public health significance of those risks, the means and costs of controlling them, actual health effects to persons in proximity to emitting sources,

and recommendations as to legislation regarding such remaining risk. The EPA prepared and submitted this report ( Residual Risk Report to Congress, EPA 453/ R 99 001) in March 1999. The Congress did not act on any of the recommendations in the report, thereby triggering the second 13 stage of the standard setting process, the residual risk phase.

Section 112( f)( 2) of the CAA requires us to determine for each section 112( d) source category whether the MACT standards protect public health with an ample margin of safety. If the MACT standards for HAP " classified as a known, probable, or possible human carcinogen do not reduce lifetime excess cancer risks to the individual most exposed to emissions from a source in the category or subcategory to less than 1 in 1 million," EPA must promulgate residual risk standards for the source category ( or subcategory) as necessary to protect public health with an ample margin of safety. The EPA must also adopt more stringent standards if required to prevent an adverse environmental effect ( defined in section 112( a)( 7) as " any significant and widespread adverse effect * * * to wildlife, aquatic life, or natural resources * * *."), but must consider cost, energy, safety,

and other relevant factors in doing so.

B. What are PCE dry cleaning facilities?

Dry cleaners use PCE in a dry cleaning machine to clean all types of garments, including clothes, gloves, leather garments, blankets, and absorbent materials. There are approximately 28,000 PCE dry cleaning facilities in the United States. Of the 28,000 dry cleaners, 15 of the facilities are major sources and the remaining are area 14 sources. Major source PCE dry cleaners are those that emit 10 tons or more of PCE per year upon the compliance date of the 1993 Dry Cleaning NESHAP. The 1993 Dry Cleaning NESHAP defines this as facilities that purchase more than 2,100 gallons ( gal) of PCE per year ( 1,800 gal per year if the facility uses transfer machines). Area sources are typically the common neighborhood dry cleaner. Area sources were divided into large or small in the 1993 Dry Cleaning NESHAP, with large area sources defined as those facilities that use between 140 to 2,100 gal of PCE per year ( or 140 to 1,800 gal per year if the facility uses transfer machines).

Small area sources use less than 140 gal per year. Some area sources are collocated in the same building with residences. In the 1993 Dry Cleaning NESHAP we did not specifically discuss these sources, but in this notice we refer to them as co residential dry cleaners. A coresidential dry cleaning facility is located in a building in which people reside. Co residential facilities are located primarily in urban areas.

In general, PCE dry cleaning facilities can be classified into three types: commercial, industrial, and leather. Commercial facilities typically clean household items such as suits, dresses, coats, pants, comforters,

curtains, and formalwear. Industrial dry cleaners clean heavily stained articles such as work gloves, uniforms, 15 mechanics' overalls, mops, and shop rags. Leather cleaners mostly clean household leather products like jackets and other leather clothing. The 15 major sources include eight industrial facilities, five commercial facilities, and two leather facilities. The five commercial facilities are each the central plant for a chain of retail storefronts. We do not expect any new source facilities constructed in the future to be major sources. Based on the low emission rates of current PCE dry cleaning machines and the typical business models used in the industrial and commercial dry cleaning sectors, it is unlikely that any new sources that are constructed will emit PCE at major levels, or that any existing area sources will become major sources due to business growth.

Dry cleaning machines can be classified into two types:

transfer and dry to dry. Similar to residential washing machines and dryers, transfer machines have a unit for washing/ extracting and another unit for drying. Following the wash cycle, PCE laden articles are manually transferred from the washer/ extractor to the dryer. The transfer of wet fabrics is the predominant source of PCE emissions in these systems. Dry to dry machines wash, extract, and dry the articles in the same drum in a single machine, so the articles enter and exit the machine dry. Because the transfer step is eliminated, dry to dry machines have much 16 lower emissions than transfer machines.

New transfer machines are effectively prohibited at major and area sources due to the 1993 Dry Cleaning NESHAP requirement that new dry cleaning systems eliminate any emissions of PCE while transferring articles from the washer to the dryer. Therefore, transfer machines are no longer sold. Existing transfer machines are becoming an increasingly smaller segment of the dry cleaning population as these machines reach the end of their useful lives and are replaced by dry to dry machines. There are approximately 200 transfer machines currently being used,

all at area sources.

The primary sources of PCE emissions from dry to dry machines are the drying cycle and fugitive emissions from the dry cleaning equipment ( including equipment used to recycle PCE and dispose of PCE laden waste). Machines are designed to be either vented or non vented during the drying cycle. Approximately 200 dry cleaners ( 1 percent) use vented machines, and the remaining facilities use the lowerpolluting non vented machines. ( The 1993 Dry Cleaning NESHAP prohibits new dry cleaning machines at major and area sources that vent to the atmosphere while the dry cleaning drum is rotating.) In vented machines, the majority of emissions from the drying cycle are vented outside the building. In non vented machines, dryer emissions are 17 released when the door is opened to remove garments.

Currently, the largest sources of emissions from dry cleaning are from equipment leaks, which come from leaking valves and seals, and the loading and unloading of garments.

C. What are the health effects of PCE?

The main health effects of PCE are neurological, liver,

and kidney damage following acute ( short term) and chronic ( long term) inhalation exposure. Animal studies have reported an increased incidence of liver cancer in mice via inhalation, kidney cancer and mononuclear cell leukemia in rats. PCE was considered to be a " probable carcinogen"

( Group B) when assessed under the previous 1986 Guidelines by the EPA Science Advisory Board. See the risk characterization memorandum in the public docket for additional information regarding the health effects of PCE.

D. What does the 1993 NESHAP require?

The 1993 NESHAP prescribes a combination of equipment,

work practices, and operational requirements. The requirements for process controls are summarized in table 1 of this preamble. The 1993 Dry Cleaning NESHAP defines major and area sources based on the annual PCE purchases for all machines at a facility. The consumption criterion ( which affects the amount of PCE purchased) varies depending on whether the facility has dry to dry machines only,

transfer machines only, or a combination of both. The 18 affected source is each individual dry cleaning system.

Table 1. Summary of the 1993 Dry Cleaning NESHAP Process Controls Sources Annual PCE Purchased New1 ( after 12/ 9/ 91) Existing2 Major Sources Dry to dry ONLY > 2,100 gal/ yr Transfer ONLY > 1,800 gal/ yr Dry to dry AND Transfer > 1,800 gal/ yr Dry to dry machines with a refrigerated condenser, AND carbon adsorber operated immediately before or as the door is opened. Dry to dry machines: must have refrigerated condenser3.

Transfer machines: must be enclosed in a room exhausting to a dedicated carbon adsorber. Large Area Sources Dry to dry ONLY 140 to 2,100 gal/ yr Transfer ONLY 200 to 1,800 gal/ yr Dry to dry AND Transfer 140 to 1,800 gal/ yr Dry to dry machines with a refrigerated condenser. Dry to dry machines: must have a refrigerated condenser3.

Transfer machines: No controls required.

Small Area Sources Dry to dry ONLY < 140 gal/ yr Transfer ONLY < 200 gal/ yr Dry to dry AND Transfer < 140 gal/ yr Same as large area sources. No controls required.

1 No new transfer machines are allowed after 9/ 23/ 93. 2 Compliance date = 9/ 23/ 96. 3 Alternatively, carbon adsorber is allowed only if installed before 9/ 22/ 93.

In addition, all sources must comply with certain operating requirements, including recording PCE purchases, 19 storing PCE and PCE containing waste in non leaking containers, and inspecting for perceptible leaks. Owners or operators are required to operate and maintain the control equipment according to procedures specified in the 1993 Dry Cleaning NESHAP and to use pollution prevention procedures,

such as good operation and maintenance, for both dry cleaning machines and auxiliary equipment ( such as filter,

muck cookers, stills, and solvent tanks) to prevent liquid and vapor leaks of PCE from these sources.

II. Summary of Proposed Rule A. What are the proposed requirements for major sources?

Under the proposed revisions, the requirements for all new and existing major sources would be the same. The proposed revisions would require the implementation of an enhanced leak detection and repair ( LDAR) program and the use of dry to dry machines that do not vent to the atmosphere ( closed loop) during any phase of the dry cleaning cycle. A refrigerated condenser and a secondary carbon adsorber would be required control equipment for all machines. The secondary carbon adsorber would control the PCE emissions during the final stage of the dry cleaning cycle immediately before and as the drum door is opened.

Under the enhanced LDAR program, the facility owner or operator would have to use a PCE gas analyzer 20 ( photoionization detector, flameionization detector, or infrared analyzer) and perform leak checks according to EPA Method 21 on a monthly basis. The facility owner or operator would also be required to continue the weekly perceptible leak check according to the requirements of the 1993 Dry Cleaning NESHAP.

B. What are the proposed requirements for area sources?

For existing area sources ( large and small), the proposed revisions would require implementation of an enhanced LDAR program and a prohibition on the use of existing transfer machines. All other existing area source standards would remain the same as in the 1993 Dry Cleaning NESHAP.

For new area sources ( large and small), the proposed rule would require implementation of an enhanced LDAR program and use of a non vented dry to dry machine with a refrigerated condenser and secondary carbon adsorber. In addition, the proposed rule would prohibit the use of new PCE machines in co residential dry cleaning facilities.

The enhanced LDAR program for area sources would require facilities to use a halogenated leak detector ( instead of a more costly gas analyzer proposed for major sources) to perform leak checks on a monthly basis. The facility would also be required to continue to inspect for perceptible leaks biweekly for small area sources and weekly 21 for large area sources according to the requirements of the 1993 Dry Cleaning NESHAP.

For co residential area sources, we are proposing two options. The first proposed option would effectively prohibit new PCE sources from locating in residential buildings by requiring that owners or operators eliminate PCE emissions from the dry cleaning process. Existing coresidential sources, under this option, would only be subject to the same requirements proposed for all other existing area sources. The second proposed option would,

instead of a prohibition on new co residential sources,

require that existing and new co residential sources comply with standards based on those required by New York State Department of Environmental Conservation ( NYSDEC) in their Title 6 NYCRR Part 232 rules, which include using machines equipped with refrigerated condensers and carbon adsorbers,

enclosed in a vapor barrier to help prevent exposures to PCE emissions. We expect to select one of these options, with possible modifications in response to public comments, in the final rule.

C. What are the proposed requirements for transfer machines at major and area sources?

The proposed rule would effectively prohibit the use of all existing transfer machines 90 days from the effective date of the final rule by requiring owners or operators to 22 eliminate any PCE emissions from clothing transfer between the washer and dryer. Similarly, the installation of new transfer machines was prohibited by the 1993 Dry Cleaning NESHAP. We estimate that about 200 transfer machines remain in use within the population of 28,000 dry cleaning machines located at area sources ( estimated one PCE dry cleaning machine per facility with approximately 28,000 facilities).

Most of these machines will be at or near the end of their useful economic life by the time final rule requirements are promulgated. The typical life of a dry cleaning machine is 10 to 15 years. By the end of 2006, the newest transfer machines in the industry will be 13 years old.

III. Rationale for the Proposed Rule A. What is our approach for developing residual risk standards?

Following our initial determination that the individual most exposed to emissions from the category considered exceeds a 1 in 1 million individual cancer risk, our approach to developing residual risk standards is based on a two step determination of acceptable risk and ample margin of safety. The first step, consideration of acceptable risk, is only a starting point for the analysis that determines the final standards. The second step determines an ample margin of safety, which is the level at which the 23 1 This reading is confirmed by the Legislative History to CAA section 112( f); see, e. g., " A Legislative History of the Clean Air Act Amendments of 1990," vol. 1, page 877 ( Senate Debate on Conference Report).

2 Legislative History, vol. 1, p. 877, stating that: ". . . the managers intend that the Administrator shall interpret this requirement [ to establish standards reflecting an ample margin of safety] in a manner no less protective of the most exposed individual than the policy set forth in the Administrator's benzene regulations . . .."

3 Residual Risk Report to Congress. March 1999. EPA 453/ R 99 001, page ES 11. standards are set.

The terms " individual most exposed," " acceptable level," and " ample margin of safety" are not specifically defined in the CAA. However, CAA section 112( f)( 2)( B)

refers positively to the interpretation of these terms in our 1989 rulemaking ( 54 FR 38044, September 14, 1989),

" National Emission Standards for Hazardous Air Pollutants:

Benzene Emissions from Maleic Anhydride Plants,

Ethylbenzene/ Styrene Plants, Benzene Storage Vessels,

Benzene Equipment Leaks, and Coke By Product Recovery Plants ( Benzene NESHAP)," essentially directing us to use the interpretation set out in that notice 1 or to utilize approaches affording at least the same level of protection 2 .

We likewise notified Congress in the Residual Risk Report that we intended to utilize the Benzene NESHAP approach in making CAA section 112( f) residual risk determinations 3 .

In the Benzene NESHAP ( 54 FR 38044, September 14, 24 4 Id. 1989), we stated as an overall objective:

. . . in protecting public health with an ample margin of safety, we strive to provide maximum feasible protection against risks to health from hazardous air pollutants by ( 1) protecting the greatest number of persons possible to an individual lifetime risk level no higher than approximately 1 in 1 million; and ( 2) limiting to no higher than approximately 1 in 10 thousand [ i. e., 100 in 1 million] the estimated risk that a person living near a facility would have if he or she were exposed to the maximum pollutant concentrations for 70 years.

As explained more fully in our Residual Risk Report,

these goals are not " rigid line[ s] of acceptability," but rather broad objectives to be weighed " with a series of other health measures and factors 4 ."

B. How did we estimate residual risk?

The " Residual Risk Report to Congress" ( EPA 453/ R 99

001) provides the general framework for conducting risk assessments to support decisions made under the residual risk program. The report acknowledged that each risk assessment design would have some common elements, including a problem formulation phase, an analysis phase, and the risk characterization phase. The risk assessment for PCE dry cleaners used both site specific data for many modeling parameters and population characteristics derived from 25 5 Additional details are provided in the risk characterization memorandum in the rulemaking docket.

6 Residual Risk Report to Congress, pp. B  18 and B  22. The approach used to assess the risks associated with standards for the dry cleaning industry are consistent with the technical approach and policies described in the Report to Congress. census data, as well as default assumptions for exposure parameters  some of which were assumed to be health protective ( e. g., exposure frequency and exposure duration,

70 year constant emission rates) 5 , 6 . To estimate the cancer risk and non cancer hazard for major source facilities, we performed refined modeling for a subset of major source facilities we determined were representative of all major sources, including industrial cleaners, commercial cleaners,

and leather cleaners. Facilities within each of these three specializations tend to be homogenous with respect to factors that affect the emissions, pollutant dispersion, and population size in the modeling radius, allowing us to extrapolate risks from facilities modeled to those that were not modeled. We used a combination of modeling and monitoring approaches to analyze risks for area sources.

See the risk characterization memorandum in the public docket for a complete discussion of the major and area source risk assessment.

1. How did we estimate the atmospheric dispersion of PCE emitted from major and area sources? 26 7 USEPA. 2005. Guidelines for Carcinogen Risk Assessment. EPA/ 650/ P 03/ 001B. Risk Assessment Forum, Washington, DC.

8 March 9, 1988 letter to Lee Thomas, Administrator, U. S. Environmental Protection Agency, from Norton Nelson, Chair, Executive Committee of EPA Science Advisory Board.

9 USDHHS. 1989. Report on Carcinogens, Fifth Edition; U. S. Department of Health and Human Services, Public Health Service, National Toxicology Program. We used the Industrial Source Complex Short term model,

version 3 ( ISCST 3) to estimate the dispersion of PCE from facilities to receptor locations. For a complete description of the dispersion modeling, please see the risk characterization memorandum.

2. How did we assess public health risk associated with PCE emitted from PCE dry cleaners?

PCE has been associated with a variety of health effects, including cancer. Although PCE has not yet been reassessed under the Agency's recently revised Guidelines for Cancer Risk Assessment 7 , it was considered to be a " probable carcinogen" ( Group B) 8 when assessed under the previous 1986 Guidelines by the EPA Science Advisory Board.

Since that time, the United States Department of Health and Human Services has concluded that PCE is " reasonably anticipated to be a human carcinogen 9 ," and the International Agency for Research on Cancer has concluded 27 10 IARC. 1995. Monographs on the evaluation of carcinogenic risks to humans. Volume 63. Dry Cleaning, Some Chlorinated Solvents and Other Industrial Chemicals. ISBN 9283212630. Geneva, Switzerland. that PCE is " probably carcinogenic to humans 10 ."

In our assessment of public health risk associated with PCE emitted from PCE dry cleaners, we considered risks of cancer and other health effects. Cancer risks associated with inhalation exposure were assessed using lifetime cancer risk estimates. The noncancer risks were characterized through the use of hazard quotient ( HQ) and hazard index ( HI) estimates. An HQ is calculated as the ratio of the exposure concentration of a pollutant to its health based non cancer threshold.

In this assessment, values that are below 1.0 are not likely to be associated with adverse health effects. An HI is the sum of HQ for pollutants that target the same organ or system. For dry cleaners, PCE is the only HAP emitted,

therefore, HI and HQ are the same.

Several sources were considered for cancer and noncancer dose response assessment information. In a 1998 assessment of PCE cancer risks associated with dry cleaners,

EPA's Office of Prevention, Pesticides, and Toxic Substances ( OPPTS) derived and used a lifetime inhalation unit risk estimate ( URE) of 7.1 x 10 7 per microgram per cubic meter 28 11 USEPA. 1998. Cleaner Technologies Substitutes Assessment: Professional Fabricare Processes. EPA 744 B 98 001. U. S. Environmental Protection Agency, Office of Pollution Prevention and Toxics, Washington, DC.

12 USEPA. 1996. Addendum to the Health Assessment Document for Tetrachloroethylene ( Perchloroethylene), Updated Carcinogenicity Assessment for Tetrachloroethylene ( Perchloroethylene, PERC, PCE). EPA/ 600/ 8 82/ 005FA. External Review Draft. U. S. Environmental Protection Agency, Office of Health and Environmental Assessment, Washington, DC.

13 CDHS. 1991. Health Effects of Tetrachloroethylene ( PCE). California Department of Health Services ( subsequently CalEPA, Office of Environmental Health Hazard Assessment), Berkeley, CA.

14 H. J. Clewell, P. R. Gentry, J. E. Kester, and M. E. Andersen. 2005. Evaluation of physiologically based pharmacokinetic perchloroethylene. ( ug/ m3) 11 . This reflected an update of the URE of 5.8 x 10 7 per ug/ m3 that was derived by EPA in the 1980s 12 . The PCE cancer dose response assessments developed by others include a lifetime URE of 5.9 x 10 6 per ug/ m3 developed by the California Environmental Protection Agency ( CalEPA) 13 ,

and a lifetime URE of 3.8 x 10 7 per ug/ m3 developed by Clewell and others 14 .

We are currently reevaluating the available information on health effects of PCE, including cancer, as part of a hazard and dose response assessment for the Agency's Integrated Risk Information System ( IRIS). The cancer component of this evaluation is being conducted in accordance with the 2005 Guidelines for Carcinogen Risk 29 15 JISA ( Japan Industrial Safety Association). 1993. Carcinogenicity Study of Tetrachloroethylene by Inhalation in Rats and Mice. Data No. 3 1. Available from: EPA IRIS Information Desk.

16 NTP. 1986. NTP technical report on the toxicology and carcinogenesis of tetrachloroethylene ( perchloroethylene) ( CAS No. 127 18 4) in F344/ N rats and B6C3F1 mice ( inhalation studies). National Toxicology Program, Research Triangle Park, NC. NTP TR 311, NIH Publication No. 86 2567. August 1986. Assessment. Data have become available from the Japanese Industrial Safety Association ( 1993) that includes rodent inhalation studies with a cancer bio assay which was not considered by the sources above 15 . The document describing the evaluation is expected to be released for external scientific peer review and public comment. The projected schedule for completion of the IRIS assessment is available at http:// cfpub. epa. gov/ iristrac/ index. cfm.

While all of the available lifetime URE are based on the same animal bioassay 16 ( 1986), there are several factors contributing to the differences in magnitude among them.

One significant contributing factor is characterization of human metabolism of PCE. This is an area in which widely diverging quantitative estimates have been published, and their use leads to notable differences in human cancer doseresponse value derived from animal data, illustrated to some extent by the range of values presented above.

As an interim approach in lieu of the completed IRIS 30 17 USEPA. March 1999. Residual Risk Report to Congress. Office of Air Quality Planning and Standards, Research Triangle Park, NC 27711. EPA 453/ R 99 001; available at http:// www. epa. gov/ ttn/ oarpg/ t3/ meta/ m8690. html. assessment, we used two dose response values to characterize cancer risk. These two values were chosen to represent the best available peer reviewed science. As we have stated previously, we will not be relying exclusively on IRIS values, but will be considering all credible and readily available assessments 17 . We used the CalEPA URE ( 5.9 x 10 6 per ug/ m3) and the estimate developed by OPPTS ( 7.1 x 10 7 per ug/ m3). Both are derived with consideration of findings of liver tumors in mouse laboratory bioassays, with the OPPTS value additionally considering laboratory findings of mononuclear cell leukemia in rats, and both have received public comment and scientific peer review by external panels. Dose response modeling performed in both assessments involved use of metabolized doses with different estimates of human PCE metabolism contributing to differences in the resulting URE.

Effects other than cancer associated with long term inhalation of PCE in worker or animal studies include neurotoxicity, liver and kidney damage, and, at higher levels, developmental effects. To characterize noncancer hazard in lieu of the completed IRIS assessment, we used the 31 18 ATSDR. 1997. Toxicological Profile for Tetrachloroethylene. Department of Health and Human Services, Public Health Services, Agnecy for Toxic Substances and Disease Registry, Atlanta, Georgia.

19 V. Vu. 1997. Memorandum titled " Provisional RfC for perchloroethylene" From Vanessa Vu, Acting Director, Health and Environmental Review Division, to William Waugh, Acting Directory, Chemical Screening and Risk Assessment Division, OPPT, USEPA. As cited in OPPTS 1998. Cleaner Technologies Substitutes Assessment: Professional Fabricare Processes. EPA 744 B 98 001. USEPA, Office of Pollution Prevention and Toxics, Washington, DC. Agency for Toxic Substances and Disease Registry's ( ATSDR)

Minimum Risk Level ( MRL) ( 270 ug/ m3) 18 . This value is based on a study of neurological effects in workers in dry cleaning shops, and is derived in a manner similar to EPA's method for derivation of reference concentrations ( Rfc), and with scientific and public review. The ATSDR MRL is quite similar to the provisional RfC ( 170 ug/ m3) derived by OPPTS in 1997 based on a study of kidney effects in workers in dry cleaning shops 19 that reported effects at similar exposure concentrations than those elsewhere reported associated with neurological effects. The OPPTS value was termed a provisional RfC because it was derived by a single EPA program office with limited cross office review. This value is based on a study of neurological effects in workers in dry cleaning shops. Since that time, more recent studies have been published, particularly with regard to more 32 20 USEPA. 2004. Summary report of the peer review workshop on the neurotoxicity of tetrachloroethylene ( perchloroethylene) discussion paper. National Center for Environmental Assessment, Washington, DC; EPA 600 R 04 041. Available online at http:// www. epa. gov/ ncea. sensitive neurological effects at lower exposures 20 . We are reviewing these and all of the available information on the noncancer health effects of PCE as part of the IRIS assessment.

The proposed rule is based on both the risk estimates derived using both the CalEPA cancer dose response values and the ATSDR noncancer MRL. The CalEPA cancer doseresponse value is higher than the value derived by OPPTS,

leading to higher cancer risk estimates. Given our uncertainty regarding the pending IRIS dose response values,

we have considered the range of available potencies with which to calculate inhalation cancer risk. We calculate cancer risk using both values, but propose to use the CalEPA value. We request comment on both this approach of using the more health protective end of the dose response range and our selection of dose response values. Based on the findings and status of the IRIS assessment at the time of promulgation, we may reassess our estimates of cancer risk and noncancer hazard. The Agency is aware that some stakeholders have suggested that we defer certain action pending completion of the IRIS assessment for PCE. In 33 today's notice, we request comment on our proposal to use the available CalEPA and OPPTS potency values, and we request comments on whether we should defer further development of the risk assessment and any rulemakings under section 112( f)( 2) for area sources pending completion of the IRIS assessment for PCE.

3. How did we assess environmental impacts of major sources and typical area sources?

The chemical properties of PCE suggest that once it is emitted into the atmosphere as a vapor, it is not likely to partition significantly into soil, water, or sediment.

Based on fugacity modeling, we estimate that 99.8 percent of ambient PCE remains in the atmosphere, with the remainder partitioning into water ( 0.17 percent), and soil ( 0.05 percent). Thus, PCE emitted from major stationary sources is not likely to pose a significant ecological risk due to any exposure pathway other than inhalation.

Further, to assess the potential inhalation risk to mammals from PCE inhalation, we compared the minimum lowest observable adverse effect level ( LOAEL) for rats with the highest level of modeled ambient concentration from PCE cleaners; the rat LOAEL for PCE can be found in the ATSDR toxicological profile that documents the development of the MRL ( http:// www. atsdr. cdc. gov/ toxprofiles/ tp18. html). The lowest rat LOAEL ( 9 parts per million ( ppm), or 60 mg/ m3) is 34 about 2,000 times higher than the highest modeled postcontrol ambient concentrations from major stationary sources.

This large margin of exposure leads us to conclude that risks to mammals from PCE inhalation are likely insignificant, obviating the need to further quantify ecological risks to any degree.

In the atmosphere, PCE is known to degrade into many compounds, including trichloroacetic acid ( TCAA). TCAA is a persistent, known phytotoxin, which has been discontinued as a herbicide. Atmospheric transformation of PCE to TCAA is the subject of great debate, with potential conversion efficiencies estimated to be on the order of 5 to 15 percent. However, there are very few data quantifying TCAA concentrations in the air, precipitation, water, soil, or sediment in the United States. This scarcity of data makes it difficult to determine whether there is any potential for adverse ecological impacts on plant life from PCE emissions from dry cleaners due to conversion to TCAA. While we have no direct evidence that this will present a significant ecological risk, we nonetheless invite public comment and solicit additional scientific information on this issue.

Since our results showed no screening level ecological effects, we do not believe that there is any potential for an effect on threatened or endangered species or on their 35 critical habitat within the meaning of 50 CFR 402.14( a).

Because of these results, we concluded a consultation with the Fish and Wildlife Service is not necessary.

C. What are the residual risks from major sources?

Table 2 of this preamble summarizes the estimated risks remaining for the seven modeled major source facilities after compliance with MACT. In performing residual risk assessments under the CAA section 112( f)( 2), EPA believes it may evaluate potential risk based on consideration of both emission levels allowed under the MACT standard and actual emissions levels achieved in compliance with MACT. See,

e. g., 70 FR 19992, 19998 ( April 15, 2005). Generally,

allowable emissions are the maximum levels sources could emit and still comply with existing standards. It is also reasonable that we consider actual emissions when available,

as a factor in both steps of the residual risk determination, to avoid unrealistic inflation of risk levels or where other factors suggest basing the evaluation soley on allowables is not appropriate. Essentially, the existing dry cleaning MACT standard is comprised of equipment standards and various work practices. Compliance with the existing MACT standard is demonstrated by use of the required equipment and implementation of the required work practices, and there are no numeric emissions levels to model. Therefore, the seven facilities were modeled using 36 actual 2000 2002 emissions and are representative of the emissions from major sources. We conclude that the sampled facilities represent characteristics of the major source facility population, including commercial, industrial, and leather facilities. The risk analysis shows that each of the seven modeled facilities poses a cancer risk of 1 in 1 million or greater. The highest maximum individual cancer risk ( MIR) is between 300 in 1 million and 2,400 in 1 million. The MIR is the lifetime risk of developing cancer for the individual facing the highest estimated exposure over a 70 year lifetime. Five of the modeled facilities pose a risk greater than 100 in 1 million ( the presumptive unacceptable risk level), and about 550 people are exposed at this level. One facility has a HQ of greater than 1.0.

As described below in section III. E, we expect a continuing decline in PCE emissions even in the absence of additional Federal regulation. These baseline risk estimates do not reflect such a trend, therefore; baseline risks are likely to be overestimated.

Table 2. Major Source Baseline Risk Estimates for Modeled Facilities after Application of 1993 Dry Cleaning NESHAP, Based on 70 year Exposure Duration1 Parameter MACT Level ( OPPTS URE) MACT Level ( CalEPA URE)

MIR from facility with highest risk 300 in 1 million 2,400 in 1 million 37 Maximum HQ from facility with highest risk based on ATSDR MRL 2 2 Population at risk across all modeled facilities ( modeled to 10 kilometers ( km):

> 1 in 1 million 16,000 175,000 > 10 in 1 million 800 12,500 > 100 in 1 million 10 550 Total population exposed 3,300,000 3,300,000 1 In this table, all risk and population estimates are rounded.

To account for the fact that individuals may move through areas ( microenvironments) of differing concentrations during their daily activities, EPA conducted an exposure variability analysis in which it used the Total Risk Integration Methodology Exposure model ( TRIM. Expo, also known as the Air Pollutant Exposure Model 3, or APEX3). The TRIM. Expo model uses a personal profile approach in which it stochastically simulates exposures for individuals of differing demographic characteristics and associated daily activity patterns. The model output provides a distribution of exposure estimates which are intended to be representative of the study population with respect to their demographically based behavior, in terms of the microenvironments through which they move during a day and throughout a year ( see http:// www. epa. gov/ ttn/ fera for more 38 21 Note that the ISCST 3 modeling results do not match earlier risk estimates due to the fact that EPA used an earlier set of ISCST 3 modeling results for the TRIM. Expo analysis. The original ISCST 3 results are retained here so that the comparison with TRIM. Expo will be consistent. information regarding the model). To estimate cancer risk,

EPA assumes that this 1 year exposure scenario continues for 70 years. Table 3 contrasts ISCST 3 and TRIM. Expo estimates of population risk for the worst case facility, using the CalEPA URE; this example is illustrative only 21 .

Table 3. Comparison of ISCST 3 Exposure Estimates with Activity patterned/ day, lifetime exposure ( ISCST 3+ Trim. Expo)

Model Total Population at Cancer Risk > 100 in 1 million > 10 in 1 million > 1 in 1 million ISCST 3 900 14,000 75,000 TRIM. Expo 400 9,000 80,000 TRIM. Expo provides a more central tendency estimate of risk by accounting for variability in personal exposure.

The table above shows a smaller number of individuals exposed at the higher levels of cancer risk and a slightly larger number of individuals exposed at a cancer risk of at least 1 in 1 million. While we performed this analysis for the worst case facility, it is reasonable to infer that the risk distribution above would be similar to the remainder of the major source facilities. One limitation of this 39 22 Risk estimates derived using maximum exposure concentration. analysis is that we assume continuous 70 year exposure when calculating cancer risk, and some individuals are likely to move away from the facility. However, given the large number of area source dry cleaners nation wide, and the consequent ubiquity of PCE exposure, it is unlikely that the PCE exposure of individuals moving out of the TRIM. Expo study area would fall to zero.

For illustrative purposes, below we provide estimates of individual inhalation cancer risk based on different assumptions regarding exposure duration. In contrast to the TRIM. Expo estimates above, the risk estimates below do not account for personal activity patterns and assume that individuals receive continuous exposure for the duration noted.

Table 4. Estimates of Individual Inhalation Cancer Risk Based on Different Exposure Durations Estimated Lifetime Cancer Risk Assumed Exposure Duration 22 70 50 30 20 10 Risk per Million ( CalEPA) 2,400 1,700 1,030 700 340 Risk per Million ( OPPTS) 300 210 130 90 40 D. What are the options for reducing risk, their costs, and risk reduction impacts for major sources? 40 We evaluated several methods for reducing risks. These methods include enhanced LDAR and three emission control technologies.

Enhanced LDAR. Enhanced LDAR would require the facility owner or operator to use a portable PCE gas analyzer to perform leak checks on a monthly basis. Two major sources and several State and local agencies currently use a photoionization detector, one type of gas analyzer,

for leak inspections. The detection probe is moved slowly along the equipment part, and if PCE is detected, the device gives a concentration reading of the leak. The proposed leak definition is a concentration of 25 ppm. Portable gas analyzers cost about $ 3,300 and have a 10 year life expectancy. The facility would be required to continue to perform the weekly perceptible leak checks as required by the 1993 Dry Cleaning NESHAP. A nominal amount of additional labor would be required as a result of the proposed requirement to use a gas analyzer. We estimated 1 hour of labor per machine per month to perform the leak inspection. The estimated total capital cost to the industry to establish an enhanced LDAR program is $ 40,000,

with a annual cost savings of $ 390,000. The cost savings is due to reduced PCE consumption.

Control Technologies. Three types of emission control technologies can be used to reduce emissions from dry 41 cleaning machines. The first two are a refrigerated condenser and a secondary carbon adsorber. The third technology is a PCE sensor and lockout. By using the first two control technologies together, and by operating them properly, a significant amount of PCE can be recovered.

Refrigerated condensers are the most effective method for reducing PCE from the drying cycle. They are used to condense PCE vapor for reuse. By operating at lower temperatures than water cooled condensers, refrigerated condensers recover more PCE from the drying air and reduce emissions. By the end of the cool down cycle, refrigerated condensers can reduce PCE concentrations in the drum to between 2,000 and 8,600 ppm. Refrigerated condensers require relatively little maintenance, needing only to have their refrigerant recharged and to have lint removed from the coils ( yearly or even less frequently).

A secondary carbon adsorber controls the PCE emissions during the final stage of the dry cleaning cycle just prior to the drum door opening. A carbon adsorber removes organic compounds from air by adsorption onto a bed of activated carbon as the air passes over the bed. Carbon adsorbers have a PCE removal efficiency of 95 percent or greater.

Properly designed and operated secondary adsorbers have been shown to reduce the PCE concentration in the drum from several thousand ppm to less than 100 ppm, and in some 42 cases, to less than 10 ppm. Most new dry cleaning machines sold today are equipped with secondary carbon adsorbers.

Carbon adsorbers require periodic desorption to recover PCE and maintain their peak PCE collection efficiency.

The technologies currently in use by major and area source dry cleaners include vented dry to dry machines with water cooled condensers and carbon adsorbers, non vented ( closed loop) dry to dry machines with refrigerated condensers, non vented dry to dry machines with refrigerated condensers and secondary carbon adsorbers and transfer machines. To meet a standard requiring a refrigerated condenser and secondary carbon adsorber, existing dry cleaning machines without this control could be retrofitted,

or new replacement machines could be purchased depending on the remaining useful life of each existing machine. The costs to add control technologies range from $ 13,000 to $ 40,000 per machine, depending on the size of the existing machine and the level of control of the machine. Machine replacement costs are approximately $ 900 to $ 1,000 per pound of capacity. Additional analysis of costs can be found in the Background Information Document in the public docket.

A PCE sensor is the third control technology used in machines with a secondary carbon adsorber. The sensor controls the carbon adsorption cycle to achieve a set PCE concentration in the drum. This device uses a single beam 43 infrared photometer to measure the concentration of PCE in the drum, and prolongs the carbon adsorption cycle until the concentration set point is achieved. An interlock ( lock out) ensures that the PCE set point has been attained before the machine door can be opened.

Regulatory Options. We considered three options for reducing risk from major source dry cleaners. Option I would require all major sources to use an enhanced LDAR program and have dry to dry machines with a refrigerated condenser and a secondary carbon adsorber. Option II would require a PCE sensor and lock out in addition to the Option I controls. Option III would require no PCE emissions from major sources ( a ban on the use of PCE).

Table 5 of this preamble shows the costs and risk estimates for each regulatory option. The population risk estimates were extrapolated from the seven modeled facilities to all 15 major source facilities. The cost estimates are also for all 15 major source facilities.

Table 5. Risk Estimates and Costs of Control Options for Major Sources Based on 70 year Exposure Duration1 Parameter MACT Level Option I Option II Option III MIR from facility with highest risk ( CalEPA URE) 2,400 in 1 million 270 in 1 million 150 in 1 million NA2 44 23 Modeled to 10 km. MIR from facility with highest risk ( OPPTS URE) 300 in 1 million 30 in 1 million 20 in 1 million NA Maximum HQ from facility with highest risk 2 0.2 0.1 NA Population at risk across all facilities 23 ( population risk range represents difference between OPPTS and CalEPA URE):

> 1 in 1 million 35,000 to 375,000 2,000 to 55,000 1,000 to 26,000 NA > 10 in 1 million 2,000 to 27,000 20 to 1,800 10 to 900 NA > 100 in 1 million 10 to 1,200 0 to 13 0 to 6 NA Total population exposed ( within 10 km) 9,300,000 NA Capital Cost ($ 1000)  830 5,700 8,200 Annualized Cost ($ 1000)  ( 220) 420 Not Estimated Emission Reduction ( tons per year ( tpy))  209 249 ( 40 incremental 293 ( 44 incremental

1 In this table, risk estimates are based on both OPPTS and the CalEPA URE. All risk and population estimates are rounded. 2 NA = not applicable. Under Option III, risk from PCE would be eliminated, however, potential risks from 45 alternative solvents were not analyzed.

E. What is our proposed decision on acceptable risk and ample margin of safety for major sources?

Section 112( f)( 2)( A) of the CAA states that if the MACT standards for a source emitting a:

... known, probable, or possible human carcinogen do not reduce lifetime excess cancer risks to the individual most exposed to emissions from a source in the category... to less than one in one million, the Administrator shall promulgate [ residual risk] standards... for such source category.

The residual risk to the individual most exposed to emissions from PCE dry cleaners is estimated at 1 in 1 million or greater at each major source dry cleaner modeled.

Major source dry cleaners subject to the proposed rule emit a possible to probable human carcinogen, and, as shown in table 3 of this preamble, we estimate that the MIR associated with the 1993 Dry Cleaning NESHAP limits is between 300 in 1 million and 2,400 in 1 million. Therefore,

we believe a residual risk standard is necessary.

In the 1989 Benzene NESHAP, the first step of the residual risk decision framework is the determination of acceptable risk ( i. e., are the estimated risks due to emissions from these facilities " acceptable"). This determination is based on health considerations only,

without consideration of costs. The determination of what represents an " acceptable" risk level is based on a judgment 46 of " what risks are acceptable in the world in which we live"

( 54 FR 38045, 1987, quoting the Vinyl Chloride decision at DC Circuit Courts Decision in NRDC vs. EPA, 824 F. 2d at 1165) recognizing that our world is not risk free.

In the 1989 Benzene NESHAP, we stated that a MIR of approximately 100 in 1 million should ordinarily be the upper end of the range of acceptable risks associated with an individual source of pollution. We characterized the MIR as " the estimated risk that a person living near a facility would have if he or she were exposed to the maximum pollutant concentrations for 70 years." We explained that this measure of risk " is an estimate of the upper bound of risk based on conservative assumptions, such as continuous exposure for 24 hours per day for 70 years." We acknowledge that the MIR " does not necessarily reflect the true risk,

but displays a conservative risk level which is an upper bound that is unlikely to be exceeded."

Understanding that there are both benefits and limitations to using MIR as a metric for determining acceptability, we acknowledged in the 1989 Benzene NESHAP that " consideration of maximum individual risk. . . must take into account the strengths and weaknesses of this measure of risk." Consequently, the presumptive risk level of 100 in 1 million provides a benchmark for judging the acceptability of MIR, but does not constitute a rigid line for making that 47 determination. In establishing a presumption for the acceptability of maximum risk, rather than a rigid line for acceptability, we explained in the 1989 Benzene NESHAP that risk levels should also be weighed with a series of other health measures and factors, including the following:

° The numbers of persons exposed within each individual lifetime risk range and associated incidence within,

typically, a 50 km ( about 30 miles) exposure radius around facilities.

° The science policy assumptions and estimation uncertainties associated with the risk measures.

° Weight of the scientific evidence for human health effects.

° Other quantified or unquantified health effects.

° The overall incidence of cancer or other serious health effects within the exposed population.

In some cases, these health measures and factors taken together may provide a more realistic description of the magnitude of risk in the exposed population than that provided by MIR alone.

Based on use of the criteria identified above, we judge the level of risk resulting from regulatory option I to be acceptable for this source category ( table 3 of this preamble). This option requires dry cleaning machines at all major sources to have an enhanced LDAR program and 48 closed loop, dry to dry machines with refrigerated condensers and secondary carbon adsorbers. The calculated MIR is between 30 in 1 million and 270 in 1 million. While the upper end of this risk range is greater than the presumptively acceptable level of MIR under the 1989 Benzene NESHAP formulation ( 100 in 1 million), we also considered other factors in making our determination of acceptability,

as directed by the 1989 Benzene NESHAP. The principal factors that influenced our decision were that nearly all of the population living within 10 km of each facility receive cancer risk at less than 1 in 1 million. Considering the very small number of individuals that are estimated to receive greater than 100 in 1 million cancer risk coupled with the exposure and dose response assessment methodology that was conservatively health protective, it is likely that no actual persons are exposed at risk levels above 100 in 1 million. Among the exposed population of 9.3 million individuals, a maximum of between 0 and 13 people are estimated to receive risks of more than 100 in 1 million.

Under option I, the exposure to maximum exposed individuals would be reduced from between 300 in 1 million to 2,400 in 1 million to between 30 in 1 million and 270 in 1 million.

Total combined cancer incidence would be between 0.002 and 0.003 cases per year for all seven major source facilities that were modeled. In addition, no significant non cancer 49 health effects are predicted. The maximum HQ would be reduced from 2 to 0.2, and no adverse ecological impacts are predicted under option I. In addition, we expect that PCE usage will continue to drop as has been the trend over the past 10 years. This trend has been caused by the greater use of alternative solvents, older machines at the end of their useful lives being replaced with newer, lower emitting dry to dry machines with refrigerated condensers and secondary carbon adsorbers, and State and industry programs that improve machine efficiency and reduce PCE consumption.

All of these factors will cause risks to continue to decrease in the future in the absence of further Federal regulatory requirements. Therefore, we have determined that the risks associated with regulatory option I are acceptable after considering MIR, the population exposed at different risk levels, the projected absence of noncancer effects and adverse ecological effects, and the projected decline in PCE usage.

While not relevant for determining the acceptable risk level, the national capital costs of regulatory option I are $ 830,000 and annualized cost savings of $ 220,000. Most facilities would recognize a cost savings primarily from implementing the enhanced LDAR program. Leak detection and repair is a pollution prevention approach where reduced emissions translate into less PCE consumption and reduced 50 operating costs because facilities would need to purchase less PCE. The capital costs for individual facilities would range from $ 0 to $ 313,000, with a median cost of $ 51,000.

Annualized costs would range from a cost savings of $ 106,000 per year to a cost of $ 22,000 per year.

The second step in the residual risk decision framework is the determination of standards that are equal to or lower than the acceptable risk level and that protect public health with an ample margin of safety. In making this determination, we considered the estimate of health risk and other health information along with additional factors relating to the appropriate level of control, including costs and economic impacts of controls, technological feasibility, uncertainties, and other relevant factors,

consistent with the approach of the 1989 Benzene NESHAP.

We evaluated regulatory option II as the first level of control more stringent than the acceptable risk level for this source category. Our analysis showed a relatively small incremental risk reduction beyond that achieved by option I. Under option I, one of the seven modeled facilities would pose risks greater than 100 in 1 million using the CalEPA URE and no facility would pose risks greater than 100 in 1 million using the OPPTS URE. Under option II, this facility would still have risks above 100

in 1 million using the CalEPA URE only. For the other six 51 modeled facilities, the risks would remain in the range of 10 in 1 million under option II using the CalEPA URE and risks would drop below the range of 10 in 1 million for three of seven facilities using the OPPTS URE.

The national capital cost for option II ( all 15 major sources) is $ 5.7 million with an annualized cost of $ 420,000. These costs include retrofitting PCE sensors and lockout systems on machines that were manufactured in 1998 or later, and the costs of replacing machines installed before 1998, which cannot reliably meet the same level of emission reduction with a PCE sensor.

Overall, option II has high costs considering the relatively low risk reduction for most of the major sources.

These costs do not achieve a significant risk reduction for most sources. Consequently, we determined that requiring the addition of a PCE sensor and lock out was not a reasonable or economically feasible option for all major sources.

We also evaluated regulatory option III, a ban on PCE use, as a level of control more stringent than the acceptable risk level for this source category. This would completely eliminate risk from PCE for the population around the 15 major source facilities by essentially eliminating the sources of PCE. The costs to eliminate PCE usage at major sources would require a capital cost to the industry 52 of approximately $ 8.2 million. This estimate was based on the total cost of replacing all PCE machines with machines using an alternative solvent ( not an incremental cost of a new PCE machine versus a new alternative solvent machine).

Alternative solvents currently being used in the industry include cyclic siloxanes, liquid carbon dioxide,

wetcleaning, and synthetic hydrocarbon. There are some uncertainties that these solvents do not have the cleaning power ( kB value) of PCE for the heavy soiled or greasy garments like leather work gloves and aprons which are the typical garments cleaned by industrial major sources. There are some fabrics that cannot be cleaned in the alternative solvents. There are also some uncertainties about whether the waste from alternative solvent systems would be classified as hazardous. Alternative solvents have a role in the industry, and are being used for certain cleaning applications. However, there is not enough experience to determine that these technologies are sufficiently demonstrated for all applications such that PCE should be eliminated from the marketplace. Therefore, we have determined that regulatory option III is not a viable option at this time considering cost, economic impacts, technical feasibility, and uncertainties.

Based on the information analyzed for the three options, we are proposing that option I provides an ample 53 margin of safety to protect public health for major sources in the dry cleaning industry.

F. What are the risks from typical area sources?

We are not mandated to develop residual risk standards for area sources regulated by GACT. Under our discretion,

we have developed estimates of the remaining risk for these sources. In estimating the inhalation cancer risk that area sources pose, we considered the risks from facilities co located with residences ( co residential area sources)

separately from those located in all other settings ( typical area sources).

To assess risks from area sources, we first analyzed readily available data. The 1999 National Air Toxics Assessment ( NATA) provides census tract level estimates of cancer risk and noncancer hazard across the United States for a subset of the 188 HAP. Using this assessment, we were able to generate a course scale estimate of population risk for PCE area source dry cleaners by scaling the NATA cancer for PCE by the relative contribution of area source cleaners to PCE emissions. See table 6 below for a summary of the NATA derived estimated risks for area source cleaners.

Table 6. Estimated NATA Derived Population Cancer Risk for PCE Area Source Dry Cleaners Dose Response Value Estimated Cancer Risk at Least: 54 100 in 1 million 10 in 1 million 1 in 1 million OPPTS 0 0 960,000 CalEPA 0 400,000 56,000,000 This assessment provides a screening level estimate of PCE risk to the general population.

Next, we performed a " model facility" assessment. In this modeling scenario, we used information regarding typical facility size and dispersion parameters and average and upper end emissions of a facility meeting the 1993 Dry Cleaning NESHAP to create a set of " model facilities." See the risk characterization memorandum in the public docket for a complete description of the two modeling methodologies. Table 7 of this preamble summarizes the cancer and noncancer risk for typical area sources ( excluding transfer machines).

Table 7. Estimated Incremental Lifetime Individual Cancer Risk and Non Cancer Hazard for Typical Area Sources Using a Range of Emissions and Worst Case Dispersion Modeling Risk Estimate Model Facility Emissions Average ( 0.5 tons) 99th percentile ( 4 tons) Maximum ( 8 tons)

MIR ( OPPTS URE) 2 in 1 million 20 in 1 million 30 in 1 million MIR ( CalEPA URE) 15 in 1 million 120 in 1 million 220 in 1 million Noncancer HQ1 0.001 0.07 0.1 1 HQ estimates have been rounded. 55 G. What are the options for reducing risk, their costs, and risk reduction impacts for typical area sources?

We evaluated three control measures to reduce risks from typical area sources. These measures are an enhanced LDAR program for area sources, elimination of emissions from existing transfer machines, and the use of a refrigerated condenser and secondary carbon adsorber ( same control technologies described above for major sources). These control measures have been commercially demonstrated at area source dry cleaners in the United States. The three control measures were used to develop two regulatory options to reduce risk.

The enhanced LDAR program for area sources would require the use of a halogenated leak detector instead of a gas analyzer, which is being proposed for major sources.

The cost of a halogenated leak detector ($ 250) is significantly less than a gas analyzer ($ 3,300). A gas analyzer is a more accurate device that provides a quantitative reading of PCE concentration. This device can be particularly useful in pinpointing leaks at major sources that have high background concentrations of PCE. The halogenated leak detector is a non quantitative device that provides an audible or visual display when it detects a leak above 25 ppm. We have concluded that a halogenated leak detector is sufficient for detecting leaks at area source 56 dry cleaners and will provide a significant improvement in reducing emissions compared to the current requirement to inspect for perceptible leaks only.

Transfer machines have substantially higher emissions than dry to dry machines. The 1993 Dry Cleaning NESHAP effectively bans new transfer machines, but existing machines were grandfathered. In 1993, we determined that the capital costs required to replace all transfer machines would have created an adverse economic impact on a substantial portion of the industry, especially small businesses that had recently purchased new transfer machines. We estimate that about 200 transfer machines remain in use within the population of 28,000 dry cleaning machines located at area sources ( estimated one PCE dry cleaning machine per facility with approximately 28,000 facilities). Most of these machines will be at or near the end of their useful economic life by the time final rule requirements are promulgated. The typical life of a dry cleaning machine is 10 to 15 years. By the end of 2006, the newest transfer machines in the industry will be 13 years old. Replacing these machines with new machines meeting the requirements for new sources under the proposed amendments would reduce PCE emissions substantially.

We developed two regulatory options to evaluate area source risk reductions. Option I would require enhanced 57 LDAR and eliminate emissions from existing transfer machines by requiring that they be replaced with new machines. This option would apply to both large and small area sources.

Option II would require all area sources to use a refrigerated condenser and secondary carbon adsorber in addition to option I. Table 8 of this preamble summarizes the cancer and noncancer risks from these control options.

Table 8. Estimated Maximum1 Cancer Risk and Noncancer Hazard for Typical Area Sources Risk Metric Control Option 1993 NESHAP Option I  LDAR Option II  LDAR + Secondary Controls Estimated Lifetime Cancer Risk ( OPPTS URE) 30 in 1 million 20 in 1 million 15 in 1 million Estimated Lifetime Cancer Risk ( CalEPA URE) 220 in 1 million 175 in 1 million 110 in 1 million Noncancer HQ 0.1 0.1 0.1 Capital Cost ($ 1,000,000)  $ 12.4 $ 85.7 Annualized Cost ($ 1,000,000)  ($ 2.7) $ 7.9 Emission Reduction ( tpy)  3,236 5,749 1 Assumes a facility using a dry to dry machine with a refrigerated condenser emitting 8 tons of PCE a year ( highest known emitting dry to dry machine). Risks from 58 transfer machines are not included in the tables. The costs and risk estimates in this table do not consider the impacts of future trends of declining PCE usage.

H. What is our proposal for addressing the remaining emissions for typical area sources?

We are considering adopting a residual risk decision process for area sources which is based on that used for major sources. This involves first determining an acceptable level of risk to the public and then determining an ample margin of safety to protect public health,

considering costs and economic impacts of controls,

technological feasibility, uncertainties, and other relevant factors. We request comments on this approach for area sources.

AS part of this rulemaking, we have determined that exposure to emissions under the 1993 Dry Cleaning NESHAP constitutes an acceptable level of risk for typical area sources. Currently, we estimate that more than 98 percent of 28,000 existing dry cleaners use a dry to dry machine with a refrigerated condenser to comply with the 1993 Dry Cleaning NESHAP or State emission standards. Using the most health protective modeling assumptions for meteorology and location, the model facility analysis indicated that the highest known emitting area source would pose cancer risks of between 30 in 1 million and 220 in 1 million. The risk from the vast majority of area sources would be 59 substantially less. For example, cancer risk for the typical area source, which emits approximately 0.5 ton of PCE per year, is estimated at between 4 in 1 million and 15

in 1 million. In addition, the assessment showed no significant acute health effects ( HQ of 1.0 for the highest emitting area source facility). Considering the relatively low level of risk posed by the great majority of area sources, the projected absence of significant noncancer and ecological effects, and the projected decline in PCE usage,

we believe that the 1993 Dry Cleaning NESHAP level of control results in an acceptable level of risk to the public.

Replacing transfer machines with new dry to dry equipment would reduce risks from the potentially highest emitting sources. Under either option I or II,

transfer machines would be replaced with dry to dry machines with a refrigerated condenser and a secondary carbon adsorber ( i. e., the proposed new source requirements for area sources, which are discussed below).

For dry to dry machines, equipment leaks are the largest source of emissions, particularly from older dry cleaning machines. While the perceptible leaks program under the 1993 Dry Cleaning NESHAP may prevent major leaks,

a substantial emission reduction can be achieved by earlier leak detection using an instrument like a halogenated 60 hydrocarbon leak detector.

Therefore, to protect public health with an ample margin of safety, we are proposing to eliminate the use of transfer machines and require an enhanced LDAR program for dry to dry machines ( option I). This option would reduce PCE emissions by 3,200 tpy and reduce risks to the public from between 30 in 1 million and 220 in 1 million to between 20 in 1 million and 175 in 1 million.

Option I would require total capital costs of $ 12 million. The enhanced LDAR program would cost about $ 5 million. About 20,000 facilities would be required to purchase a halogenated hydrocarbon detector at a cost of $ 250 each. About 200 facilities would be required to replace their existing transfer machines with dry to dry machines with refrigerated condensers and carbon adsorber at a cost of about $ 36,000 each for a total industry cost of $ 7.3 million. Annually, option I is expected to result in a cost savings to industry of about $ 2.7 million per year.

Cost saving would be realized because both replacement of transfer machines and enhanced LDAR will reduce annual PCE consumption. The reduction in annual PCE consumption at the 200 businesses that would replace transfer machines is more than sufficient to offset the annualized cost of the new equipment. In particular, we believe most of the transfer machines are at the end of their useful life and it would be 61 economically beneficial for the facilities to replace the transfer machines with dry to dry machines. Thus, we believe the economic impacts to the affected businesses and facilities are negligible. Finally, these costs and risk estimates do not consider the impacts of future trends of declining PCE usage.

We are not proposing the option of requiring existing area sources to install secondary carbon adsorbers ( option II). Secondary carbon adsorbers would reduce maximum risks at the highest risk area sources from between 20 in 1 million and 175 in 1 million under option I to between 15

in 1 million and 110 in 1 million under option II. Under option II, about 7,500 facilities would be required to raise capital to install carbon adsorbers ( 27 percent of the industry). For these sources, the capital costs for compliance would be about $ 85 million with an annualized cost of about $ 8 million. The capital cost for individual facilities would range from $ 4,000 to $ 45,000. A majority of sources that would be affected by option II are small businesses. For these small businesses, the annualized costs would average from 10 to 20 percent of sales, and this amount is much higher than the average profit per unit of sales that small dry cleaners normally experience ( 1 to 3 percent). This cost would lead to a high number of small businesses owning affected facilities that will likely close 62 due to the lack of available capital for the needed investment in carbon adsorbers. Therefore, we are not proposing to require a secondary carbon adsorber on existing area sources, because the risk reduction would be relatively minor and the costs would impose adverse economic impacts on a number of small businesses.

Text Moved Here: 1 We do not believe that the proposed requirements for area sources pose more than a minimal burden,; however, we specifically ask for comment on methods by which EPA could focus the additional regulatory requirements being proposed by this rule to only those area sources ( typical and coresidential which pose significant risks to human health.

For example, we seek comments on whether there could be a methodology by which facilities could conduct site specific risk assessments to demonstrate that their PCE emissions pose cancer risk levels that are less than 1 in 1 million,

with a HI of less than 1, and with no acute human health risks or adverse environmental effects, and thereby avoid the additional requirements that would otherwise apply under the proposed rule revisions. Comments should address whether such an approach is feasible ( for example, if facilities would be able to conduct these risk assessments),

the legal authority for such an approach, the methodology 63 sources would use for conducting risk assessments, the specific criteria by which potential " low risk" sources would be evaluated, the mechanism for evaluating and determining whether source risk assessments meet those criteria, how the process would be implemented by Federal and/ or State and local agencies, how it would be enforced ( for example, through a permitting program or other regulatory structure to ensure that any sources found to be " low risk" remain so), and what would be the consequences if and when a source, for whatever reason, is found to no longer qualify as a " low risk" source.

End Of Moved Text I. What are the risks from co residential area sources?

Residents living in the same building with a dry cleaner may receive significantly higher exposures to PCE than people not living above or in the same building as a dry cleaner. We estimate there are approximately 1,300 co residential dry cleaning facilities in the United States.

Residents in these buildings can receive elevated PCE concentrations because PCE vapor travels through the building walls and up elevator and pipe shafts into residences. Emissions of PCE also can enter from the ambient air into residences via open windows. Even after the dry cleaner closes, PCE absorbed onto surfaces can continue to be emitted throughout the day and night. To 64 assess potential risks, we used indoor air monitoring data collected by the New York Department of Health and the New York State Department of Environmental Conservation ( NYSDEC)

between 2001 2003 as part of an epidemiological study examining neurological endpoints. In considering the New York data, it should be recognized that the data resulted from an epidemiological study, and dry cleaner building and apartment inclusion and exclusion criteria influenced buildings that were ultimately sampled. Also, certain buildings were identified in order to potentially increase the likelihood of finding apartments with elevated PCE levels. Data collected during this period indicate that resident exposures ranged from a geometric mean of 33 ug/ m3 to a maximum of 5,000 ug/ m3. The New York Department of Health collected these data during the final implementation of title 6 NYCRR Part 232 rules, which require the use of a refrigerated condenser and secondary carbon adsorber, and a vapor barrier or room enclosure around co residential dry cleaning machines. We extrapolated these 24 hour samples to lifetime exposure to estimate inhalation cancer risk and noncancer hazard. For a full description of the methodology that we used, see the risk characterization memorandum in the public docket. Table 9 of this preamble summarizes the inhalation cancer risk and noncancer hazard of co residential area sources. 65 Table 9. Estimated Incremental Lifetime Individual Cancer Risk and Noncancer Hazard for Co residential Area Sources Using a Range of Monitored Exposures Risk Metric3 Distribution of Monitored Exposure Lower 5th Percentile2 Median Geometric Mean Upper 95th Percentile Maximum Estimated Lifetime Cancer Risk ( OPPTS URE) 4 in 1 million 10 in 1 million 20 in 1 million 500 in 1 million 4,000 in 1 million Estimated Lifetime Cancer Risk ( CalEPA URE) 30 in 1 million 50 in 1 million 200 in 1 million 4,000 in 1 million 30,000 in 1 million Noncancer HQ1 0.02 0.06 0.1 3 20 1 HQ estimates have been rounded. 2 The lowest 5th percentile of exposure is equal to the nondetect limit of the monitors, which is 5ug/ m3. 3 These estimates reflect only facilities in full compliance with Title 6 NYCRR Part 232.

To better characterize inhalation cancer risk among residents of apartments co located with area source cleaners, we performed a sensitivity analysis in which we varied the assumed exposure duration. Table 10 illustrates the results from this analysis.

Table 10. Estimated High End Cancer Risks for Residents of Co located Apartments: Exposure Duration Sensitivity 66 24 Cancer risk estimates derived using 95th percentile PCE exposures for monitoring data from facilities in full compliance with NYSDEC requirements. Analysis 24 Estimated Lifetime Cancer Risk Assumed Exposure Duration 70 years 50 years 30 years 20 years 10 years Risk per million ( CalEPA URE) 4,000 3,000 2,000 1,000 600 Risk per million ( OPPTS URE) 500 400 200 100 80 HQ 7 5 3 2 1 Inhalation cancer risk estimates using the 95th percentile exposure level range from a maximum of between 4,000 and 500 in 1 million, assuming 70 year exposure to between 600 and 80 in 1 million assuming 10 year exposure.

The PCE exposure concentrations presented in table 11 of this preamble show the potential risk levels that co residential sources may pose. The MIR was predicted at between 4,000 in 1 million and 30,000 in 1 million, which is higher than the maximum risk at both major sources and typical area sources. This table suggests that maximum coresidential area source risks are about 13 times higher than the maximum major source risks and about 140 times higher than the maximum typical area source risk.

Table 11. Comparison of PCE Exposure Concentrations by Type 67 25 Estimate range represents difference between estimated risk using OPPTS and CalEPA URE. of Facility 25 Facility Coresidential area source Typical Area Source Major Source Maximum Exposure Concentration ( ug/ m3) 5,0001 37 405 Geometric Mean Exposure Concentration ( ug/ m3) 33 1 1.3 Maximum Inhalation Risk ( per million) 3,000 to 30,0002 30 to 220 300 to 2,400 Maximum Noncancer HQ 20 0.1 2 Geometric Mean Noncancer HQ 0.1 0.004 0.004 1 New York Department of Health monitoring data. 2 Inhalation cancer risks were extrapolated from 24 hour monitoring data, assuming continuous exposure for 70 years at the maximum monitored concentration.

J. What is our proposed decision on co residential area sources?

We are proposing two options for co residential area sources in today's proposal. We expect to select one of these options, with possible modifications in response to comments, in the final rule. The first option addresses both risks and technological developments for new coresidential area sources as a combined CAA Section 112( f) 68 residual risk and Section 112( d)( 6) rulemaking, and is described further in this section. This is consistent with the approach we are taking for typical area sources and for major sources. However, for existing co residential area sources under this option, we are not exercising our discretion to impose a section 112( f) residual risk standard, but only a section 112( d)( 6) standard. We recognize that developing residual risk standards for area sources is discretionary under the CAA, and that emissions reductions can also be achieved through more stringent additional standards under CAA section 112( d)( 6) that do not rely upon our section 112( f) authority. Therefore, we are also proposing a second option to achieve emissions reductions through a technology based standard for both existing and new co residential sources relying only on our Section 112( d)( 6) authority, as discussed below and in section III. K.

WAs our first option, we are proposing different requirements for new and existing co residential sources.

For new sources, we propose not to allow any new co residential machines that emit PCE. Our proposal is based on the high end estimated MIR of between 4,000 in 1 million and 30,000 in 1 million, and on our conclusion that risks from new co residential sources should be substantially reduced. These risk estimates are based on 69 monitored concentrations taken from apartments above coresidential dry cleaners with the level of equipment control required by NYSDEC in their title 6 NYCRR Part 232 rules ( e. g., a refrigerated condenser and secondary carbon adsorber, and a vapor barrier or room enclosure). We request comment on whether a control option for new sources similar to Title 6 NYCRR Part 232 rules would substantially reduce the risks from new co residential For new co residential sources.

T, the most stringent possible control option with the greatest risk reduction is a prohibition of new co residentialsuch sources. This option would eliminate PCE risks for new sources and require that any new dry cleaning machines located in a residential building would have to use an alternative cleaning solvent. We believe the owner/ operator can choose from several types of alternative solvent dry cleaning systems to use in a residential building.

The national capital costs of this regulatory option for new co residential sources are $ 8.6 million, and the annualized costs are approximately $ 950,000. These cost estimates are based on the assumption that existing facilities will replace PCE machines that have reached the end of their useful lives (~ 15 years) and are estimated for facilities affected within the first 5 years after the final 70 rule takes effect. These costs reflect the incremental cost between replacing existing machines with PCE machines with refrigerated condensers and carbon adsorbers, and replacing them with machines using hydrocarbon solvents. This analysis includes costs for all affected facilities, such as the cost incurred to install fire protection sprinklers required by most applicable fire codes to operate a hydrocarbon technology, that would not be necessary with other options. Cost estimates would be much lower if facilities using this option have sprinkler systems in place, or if they choose a less costly alternative garment cleaning option utilizing non flammable solvents, or conducting dry cleaning operations off site from the coresidential facility. We estimate that this control option for new co residential sources may, after about 15 years,

result in the elimination of cancer risks from all coresidential sources, as existing sources would be replaced by new non PCE sources. This means that maximum individual risk levels due to these sources would decline from between 30,000 and 4,000 in 1 million to 0; average individual risk would decline from between 1,000 and 200 in 1 million to 0;

and annual incidence would decline from between 2.2 and 0.3 cases per year to 0. These risk reduction estimates for all co residential dry cleaners are subject to a number of limitations, the greatest of which are likely: ( 1) the 71 degree to which the small sampled subset of co residential dry cleaners ( 16) is representative of the full set ( about 1,300) of all co residential dry cleaners; ( 2) our uncertainty of the size of the affected population; and ( 3)

the possible range of cancer potency factors used in our analysis, which is reflected in the ranges of the risk metrics reported above.

We request comment, as an alternative approach, on the adoption of the NYSDEC title 6 NYCRR Part 232 rules ( or similar standards) as the basis for control standards for new sources, instead of prohibition on any new coresidential machines that emit PCE. We request data on the emission levels, exposure, risks, and costs of meeting the level of control required by NYSDEC and for any other control options for co residential sources that may substantially reduce risks from new sources ( e. g., periodic gasket replacement in lieu of inspections).

Finally, wWe also recognize that a proposal to prohibit new co residential sources could encourage continued operation of existing co residential PCE machines beyond their useful lives rather than replacement with new machines. We request comment on a sunset provision, where,

after some period of time that reflects the typical lifetime of a dry cleaning machine, existing co residential sources would have to be replaced with new machines that do not emit 72 PCE.

WAs part of this first option, we are proposing the alternative of no additional control requirements for existing co residential dry cleaners at this time beyond the proposed requirements for existing area sources. However,

we also request comment on the appropriateness of adopting other alternatives such as the NYSDEC title 6 NYCRR Part 232 rules for existing co residential facilities in the final rule.

In particular, we are continuing to analyze the potential health risks at co residential sources and the range of options to reduce these risks. Options under consideration range from voluntary initiatives to regulatory action. About 1,100 of the estimated 1,300 co residential sources are located in New York and California. These sources are controlled with the technology equivalent to the requirements of the 1993 Dry Cleaning NESHAP for new major sources; plus, the facilities in New York have installed room enclosures to reduce exposure from residual emissions.

In addition, under the proposed requirements of this first option, all existing co residential sources would be required to adopt an enhanced LDAR program and all transfer machines would be eliminated. While the standards proposed for typical existing area sources would, in our view,

protect public health with an ample margin of safety if 73 applied to typical area sources, we are not prepared to reach this conclusion regarding these standards for existing co residential area sources. Therefore, under this option,

these standards for existing co residential sources are proposed only under the authority of CAA Section 112( d)( 6).

At this time we have limited data on co residential sources outside of New York and California. We do not know how representative the dataset is of all facilities in New York City. We do not know how many people are exposed at other sources and if the exposure and risk levels in other parts of the United States are similar to those in New York City buildings. We have little information on the distribution of PCE concentrations, the number of persons living in co residential buildings, or the number of persons exposed to various PCE concentration levels. Based on the New York monitoring data, we know the level of PCE concentrations can vary substantially within co residential buildings. While we believe that the dataset used for this risk assessment represents a high quality set of measurements which is appropriate for estimating risks, we are also aware that the dataset may contain a selection bias due to the fact that the study from which the data were taken was an epidemiological study aimed at identifying high exposures within minority and economically disadvantaged populations. Moreover, we are also aware that variable 74 attention to work practices, difficulties in achieving compliance with newly installed equipment, and poor ventilation in sampled apartments may also have increased the measured concentration values relative to the remaining population of apartments co located with area source dry cleaners. Thus, we specifically request comment on the appropriateness of using this dataset to develop a risk assessment which represents the population of co residential facilities. We also request any additional data that might be used to characterize these risks.

If a long term time series dataset of concentration measurements were available, we would estimate chronic exposure based on it to take into account the true temporal variability of exposures. However, we do not have such a dataset. Instead, we base our exposure and risk estimates on snapshot data available, recognizing that an extrapolation from short term monitoring values can lead to an upward bias of the high end chronic exposures and risks and a downward bias of the low end chronic exposures and risks. We request comment on ways to minimize these biases.

In evaluating the potential impact on risk reduction of NYSDEC requirements, our analysis focused on those facilities which were deemed to be in compliance with the NYSDEC part 232 regulations. However, it is not always clear from the available data what the exact compliance 75 status of the facilities werewas at the time that measurements were taken. For example, we note that the highest measured exposure level ( 5,000 ug/ m3), which is associated with a facility that was reported to be in full compliance with the NYSDEC regulations at the time of the measurements, has been called into question by industry stakeholders based on evidence that the facility was inspected and found to be out of compliance ( due to equipment operation problems) approximately 2 months after the measurements were taken. These problems were remedied and compliance was certified a week later. This uncertainty in exact compliance status leads to an uncertainty in whether the measured concentration values actually reflect a level of control consistent with implementation of the NYSDEC requirements. Thus, we request comment on whether and to what extent temporal variability or compliance problems among the facilities located in buildings with the sampled apartments may have biased the sampled measurements high or low and influenced the results of the risk assessment.

While we arethis first option does not proposingpropose additional controls for existing co residential area sources at this time, given the high risk levels estimated at existing co residential facilities, we are very concerned about potential health risks posed by PCE dry cleaners that 76 are located inside residential buildings. ForBecause of this reason, we request comment on the adoption ofalternative approaches that might protect public health with an ample margin of safety.

As our second option for addressing co residential sources, we propose the NYSDEC title 6 NYCRR Part 232 rules ( or similar standards) as the basis for control standards for both new and existing sources, instead of prohibition on any new co residential machines that emit PCE and the standards proposed for typical area sources and existing coresidential sources. This option is proposed only under the authority of CAA section 112( d)( 6). The NYSDEC requires that co residential dry cleaning machines have refrigerated condensers and secondary carbon adsorbers, and that equipment be housed inside a vapor barrier with general ventilation to the outside air for both new and existing facilities. Facilities must conduct weekly leak inspections using a leak detection device such as a halogenated hydrocarbon detector. Facilities are required to obtain annual third party inspections, and must make available the most recent inspection report to interested individuals for their review. The NYSDEC also requires that the facility owner and/ or manager and the dry cleaning machine operator be certified by an organization that offers a training program approved by the State agency. Most co residential 77 facilities meet the New York standards ( of the 1,300 coresidential facilities nationwide, approximately 900 are in New York), but approximately 240 facilities across the country would need to upgrade their equipment to comply with this second proposal option. The capital cost of this option is approximately $ 3 million, and the annual cost is $ 0.5 million. These estimates include the cost for approximately 240 existing facilities to either upgrade or replace their existing equipment to include a refrigerated condenser and carbon adsorber, install a vapor barrier and conduct the leak detection and repair described above.

These estimates do not include the cost of third party inspections and operator training, so cost impacts may be understated. Emissions reduction is estimated to be about 48 tons per year from the use of refrigerated condensers and carbon adsorbers. Vapor barriers do not remove emissions,

but contain them to help prevent exposures to emissions.

The cost effectiveness of this option is approximately $ 10,000/ ton.

For this second option, we request data on the emission levels, exposure, and risks associated with meeting the level of control required by the NYSDEC as the basis of control standards for existing sources.

Text Was Moved From Here: 1 78 and for any other control options for co residential sources that may substantially reduce emissions from co residential sources ( e. g., periodic gasket replacement in lieu of inspections).

K. What determination is EPA proposing pursuant to review of the 1993 Dry Cleaning NESHAP under CAA section 112( d)( 6)?

Section 112( d)( 6) of the CAA requires us to review and revise MACT standards, as necessary, every 8 years, taking into account developments in practices, processes, and control technologies that have occurred during that time.

If we find relevant changes, we may revise the MACT standards and develop additional standards. We do not interpret CAA section 112( d)( 6) as requiring another analysis of MACT floors for existing and new sources.

For major sources, we considered as a MACT alternative the same options considered above for residual risk ( table 5 of this preamble). The use of a PCE sensor/ lock system ( option II on table 5 of this preamble) is an option more stringent than the level of control that we are proposing to protect the public from residual risks with an ample margin of safety. The system would reduce emissions by 40 tpy.

Total capital costs are estimated to be $ 5.7 million for the 15 major sources with an annualized cost of $ 420,000.

Additional analysis of costs can be found in the Background Information Document in the public docket. The incremental 79 cost effectiveness of the option is $ 17,000 per ton of PCE removed ( overall, considering all 15 facilities).

Consequently, we propose that requiring enhanced LDAR and a refrigerated condenser/ secondary carbon adsorber would meet the requirements for CAA section 112( d)( 6).

Section 112( d)( 6) of the CAA also requires that we review and, if necessary, revise the technology based standards for area sources. The 1993 Dry Cleaning NESHAP for area sources was based on the use of generally available control technology ( GACT). The options selected for evaluating GACT for existing area sources are the same two options that we discussed above; enhanced LDAR and eliminating transfer machines ( option I on table 8 of this preamble), and the use of secondary carbon adsorbers ( option II on table 8 of this preamble). Option I would reduce emissions by an estimated 3,200 tpy and would result in a net cost savings to area sources. Option II would reduce emissions by an additional 3,000 tpy. However, as explained above, retrofitting a secondary carbon adsorber would not be cost effective for many existing area source dry cleaners.

Consequently, we propose that requiring enhanced LDAR and eliminating transfer machines at existing area sources would meet the requirements forof CAA section 112( d)( 6).

For new machines located at area source dry cleaners,

we are proposing the use of refrigerated condensers, 80 secondary carbon adsorbers, and enhanced LDAR. Requiring the use of secondary carbon adsorbers on new machines will not impose any significant new costs to the industry,

because the majority of new machines today are sold with secondary carbon adsorbers. Vented machines, water cooled condensers, and transfer machines are no longer sold. Many area source dry cleaners are buying this latest technology ( dry to dry machine with refrigerated condenser and secondary carbon adsorber) because they are easier to operate, use less PCE, and produce less hazardous waste. In addition, several States require the use of this technology.

A machine manufacturer stated that 70 percent of the new PCE machines sold in the year 2000 were dry to dry machines with refrigerated condensers and secondary carbon adsorbers, and by 2003 nearly all of the PCE machines sold would have this technology. New York and, beginning in 2007, California,

will require this technology for all existing major and area sources. Due to the vast number of area sources compared to major sources, the majority of the new PCE machines are purchased by area sources to replace older technology machines. Therefore, we are proposing the use of dry to dry machines with refrigerated condensers and secondary carbon adsorbers for new machines at area sources to meet the requirements forof CAA section 112( d)( 6).

For co residential area sources, the most stringent 81 standards currently in place are those enforced by NYSDEC.

They require that dry cleaning machines have refrigerated condensers and secondary carbon adsorbers, and that equipment be housed inside a vapor barrier with general ventilation to the outside air for both new and existing facilities. Facilities must conduct weekly leak inspections using a leak detection device such as a halogenated hydrocarbon detector. Facilities are required to obtain annual third party inspections, and must make available the most recent inspection report to interested individuals for their review. The NYSDEC also requires that the facility owner and/ or manager and the dry cleaning machine operator be certified by an organization that offers a training program approved by the State agency. ( described in section III. J). In some cases, these and related requirements have been effective in reducing exposure levels; the mean exposure has dropped by tenfold since 1997 ( McDermott, et.

al., 2005). However, as described earlier, a monitoring study in New York City suggests that risk levels after implementation of these standards may remain relatively high. We are considering, as an alternative approach,

adoption of theUnder our first option for addressing coresidential area sources discussed above in section III. J of this notice, we are not proposing the NYSDEC levels of control under Section 112( d)( 6). However, under the second 82 option for co residential sources, we are proposing under CAA section 112( d)( 6) standards based on those required by NYSDEC Part 232 ( or similar) regulations ( see docket for details) for new and existing co residential sources. By adopting the NYSDEC standards for, which would be modified,

as appropriate, to function as nationally applicable federal standards rather than state standards. While the first proposed option would eventually eliminate exposures from co residential sources, this second option would initially reduce exposures from existing co residential sources, this alternative would reduce exposures more than the first option to require enhanced LDAR for all area sources. This alternative approachsecond option for co residential sources eliminates the continued use of equipment without secondary carbon adsorbers at new and existing co residential sources;

this contrasts with the first option discussed underin section J above, which prohibits the use of new PCE machines and may give facilities the incentive to prolong the use of existing machines rather than purchase newer, lower emitting PCE machines. Most co residential facilities meet the New York standards ( of the 1,300 co residential facilities nationwide, approximately 900 are in New York), but several hundred facilities across the country would need to upgrade their equipment to comply with this alternative approach at existing sources. With respect to new facilities, this 83 alternative approachoption would allow new co residential facilities to use PCE only if they also use equipment with refrigerated condensers and secondary carbon adsorbers housed in a vapor barrier. We request comment on whether the NYSDEC standards meet the requirements of CAA section 112( d)( 6) forWhile this option achieves additional emission controls for many existing co residential facilities.

We recognize that developing residual risk standards for area sources is discretionary under the CAA, and that emission reductions cansources, we are not prepared to conclude that it would protect public health with an ample margin of safety from risks from co residential sources. As discussed in section III. J, the first proposal option would achieve this level of protection for new sources. EPA is seeking comment and additional information in section III. J to help assess risk reductions that could be achieved through more stringent additional standards under the required technology review for area sources under CAA section 112( d)( 6). We request comment on the appropriateness of regulating co residential and other area sources under section 112( d)( 6) and not exercising our discretion to regulate under the section 112( f) risk authority. Under the section 112( d)( 6) authority, we would consider the NYSDEC level of regulatory control and other control options discussed in this proposal. application of 84 standards similar to NYSDEC part 232.

L. What additional changes are we making to the 1993 Dry Cleaning NESHAP?

In 40 CFR 63.322( e), we are deleting the term " diverter valve," but retaining the requirement to prevent air drawn into the door of the dry cleaning machine from passing through the refrigerated condenser. We are proposing this change because some newer machines accomplish this objective without a diverter valve. This change does not subject sources to any new requirements and does not change the requirement for machines with diverter valves.

In 40 CFR 63.322( m) and 40 CFR 63.324( d), we are changing " perceptible leaks" to " leaks" because the requirements now apply to both the monthly inspection for vapor leaks, which would require the use of a leak detection instrument, as well as the weekly or biweekly inspections for perceptible leaks. This harmonizing change would not change the nature of existing inspection requirements. To support the proposed requirements for monthly vapor leak inspection, we have proposed to add definitions of " vapor leak," " PCE gas analyzer," and " halogenated hydrocarbon detector."

The 40 CFR 63.323( b) would be revised to add PCE gas analyzers as an acceptable monitoring instrument in addition to colorimetric tubes. Major sources would need a PCE gas 85 analyzer for enhanced leak detection and repair. This analyzer could also be used for monitoring a carbon adsorber. Also, the phrase " or removal of the activated carbon" would be added to clarify that any major source required to use a carbon adsorber is required to monitor the adsorber exhaust weekly for PCE. Previously, this requirement was unclear for sources that disposed of the carbon instead of desorbing it.

IV. Solicitation of Public Comments We request comments on all aspects of the proposed amendments. We are also considering additional rule amendments and specifically solicit comments on these potential amendments. The additional amendments are described in the following sections. All significant comments received will be considered in the development and selection of the final amendments.

A. Additional Requirements for Highest Risk Facilities For one of the modeled major source facilities, the estimated emissions after installing controls required by the proposed rule would pose a MIR greater than 100 in 1 million using the CalEPA URE. An alternative approach we are considering is establishing more stringent requirements for this source. We would like information about whether such an approach would be appropriate and what would be a suitable regulatory basis for creating a separate class for 86 this major source. We are considering requiring this facility to install a PCE sensor and lockout on each dry cleaning machine.

Under the proposed rule, this facility would be required to install a refrigerated condenser and secondary carbon adsorber. Most dry cleaning machines with secondary carbon adsorbers sold in this country since 1998 are equipped with a lockout that prevents the drum from being opened until the completion of the timed adsorption cycle.

These machines have been demonstrated to achieve a concentration inside the drum of less than 300 ppm without a PCE sensor. The addition of a sensor ensures that this target concentration will be met for every load, thereby preventing episodes of high emissions caused by operator error or machine malfunction.

The PCE sensor and lockout system originally was developed to meet the 2. BImSchV German Emission Control Law, which requires a PCE concentration in the dry cleaning machine drum of less than 2 grams per cubic meter (~ 300 ppm)

at the end of the drying cycle. Dry cleaning machines equipped with PCE sensors are widely used in Germany and are available in the United States. However, there is limited experience with this technology in the United States. We are aware of only two commercial dry cleaners in the United States and one industrial dry cleaner in Canada that use a 87 PCE sensor. Because of the limited United States experience, we do not have emission test data to evaluate the performance of this system relative to machines with a timed lockout system, particularly with industrial articles such as work gloves. The emissions reductions that we used to evaluate the PCE sensor and lockout system were based on estimates of solvent mileage ( pounds garments cleaned per gal of PCE used) compared to machines with a refrigerated condenser and secondary carbon adsorber. The estimated mileage of the various dry cleaning systems was obtained from engineering judgment by several industry experts.

Facilities using a PCE sensor and lockout system could possibly observe a wide range of emission reduction potential. For example, facilities that use good maintenance procedures and follow manufacturers specifications would achieve lower emission reductions than facilities with poor maintenance procedures. This control technology ensures optimal operation of the carbon adsorber by preventing the door from being opened until the PCE concentration in the drum is less than 300 ppm at the end of the drying cycle. Facilities with good maintenance procedures will have fewer high emission episodes caused by premature termination of the drying cycle.

We solicit comments on the appropriateness of requiring greater emission reduction at the highest risk source, the 88 performance of the PCE sensor and lockout system and its effectiveness in reducing risks from this source, and the basis for creating a separate class for this major source dry cleaner. We also request information on the feasibility, cost, and amount of emission reduction that could be achieved at this source through other techniques,

such as the use of alternative solvents or other approaches.

B. Requirement for PCE Sensor and Lockout as New Source MACT for Major Sources We are considering making PCE sensor and lockout controls a requirement for new machines installed at major sources. The decision to select option I instead of this control option for major sources was based on the relatively small emission reduction estimated to result from the installation of PCE sensor and lockout controls. We would like additional data on the amount of PCE reduction achieved by these controls in both industrial and commercial applications, and about how site specific factors influence the reduction achieved.

C. Alternative Performance based Standard for Existing Major Sources We are considering establishing an alternative performance based standard for existing major sources. The alternative standard would be a facility wide PCE use limitation ( e. g., gal PCE per year, solvent mileage or other 89 metrics), which would be determined as a percent reduction of actual PCE use from a baseline year. If adopted, a source could elect to comply with either the proposed process vent controls ( i. e., closed loop machine with refrigerated condenser and secondary carbon adsorber) or the performance based alternative. Facilities that use the performance based alternative still would be required to comply with the operating controls ( i. e., enhanced leak detection and repair, etc.) in the proposed rule.

The alternative standard would provide more flexibility in choosing the method of reducing emissions. This flexibility provides the opportunity to decrease compliance costs, reduce recordkeeping, and simplify compliance and enforcement. We anticipate that any facility selecting this alternative would reduce emissions by replacing some machines with alternative solvent machines and continuing to operate some PCE machines without secondary controls.

Additional emission reductions could also be achieved by more aggressive maintenance and leak detection programs.

The performance based alternative we are considering would limit annual PCE consumption on a facility wide basis.

Usage of PCE correlates directly with PCE emissions. The limit would be based on the average fraction of emissions reduced by the control technology requirement for the different types of affected sources. For the three major 90 source industrial facilities that would be required to make equipment changes to comply with the proposed rule, the average estimated facility wide emission reduction,

including enhanced leak detection and repair, would be 76 percent. For the four affected major source commercial facilities, the average estimated total emission facility wide reduction would be 67 percent. These reductions are relative to estimated emissions from these facilities in 2002. Therefore, we envision that facilities that clean industrial articles such as work gloves would be required to reduce PCE usage by at least 76 percent. For facilities that do not clean work gloves or shop rags, we envision a PCE reduction of 67 percent. For a description of how the emission reduction percentages were estimated,

refer to the Background Information Document in the public docket. The baseline year for determining the PCE usage limit would be 2002. Annual PCE usage would be calculated based on the amount of PCE purchased during the calendar year, adjusted for the PCE in use and storage at the beginning and end of the calendar year.

If the performance alternative is selected, the required PCE usage percent reduction levels will be prescribed in the final rule. The percent reductions would be selected to be equivalent to the emission reductions achieved by the technology based MACT requirements and the 91 residual risk requirements adopted in the final rule.

The performance based alternative would apply only to existing major sources. New major sources are not eligible for these performance based alternative standards because no baseline PCE data exists for determining a required emission reduction level. This alternative also would not be practicable for area sources because the proposed rule has no process vent requirements for existing area sources. The only requirements for existing area sources are the ban on transfer machines, enhanced LDAR, and the operating requirements. Moreover, most area sources operate only one dry cleaning machine.

We solicit comments on whether such an approach would be appropriate for major sources. We would also like comments from affected sources regarding the likelihood that they would select this alternative standard. In addition,

we welcome comments on other options for a performance based alternative. Please include in your comments how the option ensures equivalent emission reductions to the proposed equipment standards and how the option could be enforced,

including any recordkeeping needed.

D. Environmental Impacts of PCE Emissions As discussed above, due to the large margin of exposures relative to known thresholds, risks to mammals from PCE inhalation are likely insignificant. Also, the 92 scarcity of data makes it difficult to identify any potential for adverse ecological impacts to plant life from PCE emissions from dry cleaners due to conversion to TCAA.

While we have no direct evidence that this will present a significant ecological risk, we nonetheless, invite public comment and solicit additional scientific information on this issue.

E. Additional Time for Complying with Provisions for Transfer Machines As discussed in section III. H of this preamble, we are proposing to eliminate the use of transfer machines. Per section 112( f) of the CAA, sources have 90 days to comply with health based standards. However, we are soliciting comment on what additional time beyond the 90 day compliance period, if any, might be necessary for area sources to replace existing transfer machines with dry to dry machines,

and on whether, if EPA were to grant area sources replacing transfer machines additional compliance time in the final rule, any further steps should be taken by these area sources before achieving compliance to assure that the health of persons will be protected from imminent endangerment, consistent with section 112( f)( 4)( B) of the CAA.

V. Statutory and Executive Order Reviews A. Executive Order 12866, Regulatory Planning and Review 93 Under Executive Order 12866 ( 58 FR 51735, October 4,

1993), EPA must determine whether the regulatory action is " significant" and, therefore, subject to OMB review and the requirements of the Executive Order. The Executive 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.

Pursuant to the terms of Executive Order 12866, OMB has determined that it considers this proposed rule a " significant regulatory action" within the meaning of the Executive Order. The EPA has submitted this action to OMB for review. Changes made in response to OMB suggestions or recommendations will be documented in the public record. 94 B. Paperwork Reduction Act The information collection requirements in this proposed rule have been submitted for approval to the OMB under the Paperwork Reduction Act, 44 U. S. C. 3501, et seq.

The Information Collection Request ( ICR) document prepared by EPA has been assigned EPA ICR number 1415.06 and OMB Control Number 2060 0234.

The 2005 proposed revisions to the Dry Cleaning NESHAP contain recordkeeping and reporting requirements beyond the recordkeeping and reporting requirements that were promulgated on September 22, 1993. Owners or operators will continue to keep records and submit required reports to us or the delegated State regulatory authority. Notifications,

reports, and records are essential in determining compliance and are required, in general, of all sources subject to the 1993 Dry Cleaning NESHAP. Owners or operators subject to the 1993 Dry Cleaning NESHAP continue to maintain records and retain them for at least 5 years following the date of such measurements, reports, and records. Information collection requirements that were promulgated on September 22, 1993 in the Dry Cleaning NESHAP prior to the 2005 proposed amendments, as well the NESHAP General Provisions ( 40 CFR part 63, subpart A), which are mandatory for all owners or operators subject to national emission standards,