United States
Environmental Protection
Agency
Office of Air Quality
Planning and Standards
Research Triangle Park NC 27711 August 1 984
Air
Ambient Monitoring
of Significant
Deterioration (PSD)
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Ambient Monitoring Guidelines
for Prevention of Significant
Deterioration (PSD)
by
Monitoring and Data Analysis Division
Office of Air Quality Planning and Standards
and
Environmental Monitoring Systems Laboratory
Office of Research and Development
U.S. ENVIRONMENTAL PROTECTION AGENCY
Research Triangle Park, North Carolina 27711
August 1984
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FOREWORD
Many Individuals were involved in the preparation of this document
and should be contacted if any questions arise in the application of the
guideline.
Subject Area
Ambient Air Quality
Monitoring
Meteorological
Moni tori ng
Qua! ity Assurance
(Ambient Air
Quality)
PSD Policy and
Interpretation
of Regulations
Acceptable Methods
Non-Criteria
Pollutants
Contact
Stan Sleva
David Lutz
James Dicke
Larry Purdue
Jack Puzak
Mike Trutna
Larry Purdue
Ken Rehme
Phone Number
(Area Code 919)
541-5651
541-5651
541-5681
541-2665
541-2188
541-5591
541-2665
541-2666
FTS Number
629-5651
629-5651
629-5681
629-2665
629-2188
629-5591
629-2665
629-2666
ii
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LIST OF CHANGES
The draft changes noted below have been made to incorporate the proposed
regulatory changes. EPA welcomes comments on these draft changes only,
since the remainder of the guideline was subject to public review in 1980.
The visibility section was also updated to reflect current guidance published
since this guideline was printed.
1. Forward, page ii
Current phone numbers are included.
2. Introduction, page 2
New paragraph added for particulate matter.
3. Section 2.1.1, page 4
added for listing of criteria pollutants.
4. Section 2.4.1(b), page 7
Significant impact for PM^g added.
5. Section 2.4.4, page 9
New section added for provisions for PM^g in transition period.
6. Old transition Section 2.5.2 for 1980 PSD regulations deleted, page 10.
7. Section 2.5.2, page 10
New section added for transition period for PM^Q and TSP.
8. Section 2.6(b) , page 13
New section added for PM^g transition for non-reference methods.
9. Section 2.7, page 13
Special sampling frequency added for PM^g.
10. Section 3.3.2 page 23.
New section added for new TSP siting criteria.
11. Section 3.3.3, page 24
New section added for siting criteria for PM^g monitors. Siting criteria
for other criteria pollutants were renumbered.
12. Table 3, page 31
included in revised table.
13. Section 4, page 36
Introduction revised to reflect quality assurance requirements for lead
have been promulgated, and also include
14. Section 4.1.3.3, page 39
added to title.
15. Section 4.1.3.4, page 40
Section revised to include
iii
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Changes (Continued)
16. Section 4.1.5, page 42
Section revised to include
17. Section 5.L, page 45
New reference added in fifth paragraph.
18. Section 5.2, page 48
Visibility rule making updated.
19. Section 6.1.1, page 49
Uind direction system error changed to 5 degrees.
20. Section 6.1.6, page 50
Dewpoint temperature changed to + 30°C.
21. Section 6.1.10, page 51
Visibility rule making updated.
22. Section 7, page 52
New reference added in last paragraph.
23. Table A-l, page A-4
Significant emissions rate added for PMig.
24. Table A-2, page A-6
Significant monitoring concentration added for
25. Table A-3, page A-8
Significant ambient air quality impact added for PM^g and units corrected
for CO.
26. Appendix A, Section 3, Box 16, page A-18
added.
27. Appendix A, Section 3, Box 25, page A-21
added.
28. REFERENCES
New references added for PM^g and others noted above, all references
renumbered as necessary.
IV
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TABLE OF CONTENTS
Page
1. INTRODUCTION [[[ 1
2. GENERAL REQUIREMENTS AND CONSIDERATIONS- .......................... 3
2.1 Monitoring Data Rationale .................................... 3
2.1.1 Criteria Pollutants - Preconstruction Phase ----------- 3
2.1.2 Criteria Pollutants - Postconstruction Phase ---------- 4
2.1.3 Noncriteria Pollutants - Preconstruction and
Postconstruction Phase -------------------------------- 5
2.2 Monitoring Objective and Data Uses ....... ---------- ..... -- 5
2.3 VOC and 03 Monitoring Requirements --------------------------- 5
2.4 Use of Representative Air Quality Data------- ---------------- 6
2.4.1 Monitor Location -------------------------------------- 6
2.4.2 Data Qual ity ................ - ......................... 8
2.4.3 Currentness of Data ----------------------------------- 8
2.4.4 Provisions for PMiQ and TSP in Transition Period
of 1985 PSD Regulations ............................... 9
2.5 Duration of Monitoring --------------------------------------- 9
2.5.1 Normal Conditions ------------------------------------- 9
2.5.2 Transition Period for PM and TSP .................... 10
2.5.2.1 Transition Within 10 Months Ater Promulgation- 10
2.5.2.2 Transition During 10-16 Months After
Promul gation ------------------ ...... --- ------- 11
2.5.2.3 Transition During 16-24 Months After
Promulgation ---------------------------------- 12
2.5.2.4 Period Following 24 Months After Promulgation- 12
2.6 Sampling Methods and Procedures -------- ...... ---------------- 13
2.7 Frequency of Sampling ---------------------------------------- 13
2.8 Monitoring Plan ---------------------------------------------- 14
2.9 Meteorological Parameters and Measurement Methods ------------ 14
3. NETWORK DESIGN AND PROBE SITING CRITERIA .......................... 16
3.1 Network Design ----------------------------------------------- 16
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TABLE OF CONTENTS (Continued)
3.2.1 Reconstruction Phase 16
3.2.2 Postconstruction Phase- 18
3.2.3 Special Concerns for Location of Monitors 18
3.3 Probe Siting Criteria - - 18
3.3.1 Total Suspended Particulates (TSP) (for applications
submitted before 6 months after promulgation) 20
3.3.1.1 Vertical Placement - 20
3.3.1.2 Spacing from Obstructions 20
3.3.1.3 Spacing from Roads 21
3.3.1.4 Other Considerations - 21
3.3.2 Total Suspended Particulates (TSP) (for applications
submitted later than 6 months after promulgation) 23
3.3.2.1 Vertical Placement - 23
3.3.2.2 Spacing from Obstructions- 23
3.3.2.3 Spacing from Roads 23
3.3.2.4 Other Considerations 24
3.3.3 Particulate Matter (PMio) 24
3.3.3.1 Vertical Placement - 24
3.3.3.2 Spacing from Obstructions 24
3.3.3.3 Spacing from Roads 25
3.3.3.4 Other Considerations 25
3.3.4 Sulfur Dioxide (Stfc) 25
3.3.4.1 Horizontal and Vertical Probe Placement 25
3.3.4.2 Spacing from Obstructions 25
3.3.5 Carbon Monoxide (CO) - 25
3.3.5.1 Horizontal and Vertical Probe Placement 25
3.3.5.2 Spacing from Obstructions 26
3.3.5.3 Spacing from Roads 26
3.3.6 Ozone (03) 26
3.3.6.1 Vertical and Horizontal Probe Placement 26
3.3.6.2 Spacing from Obstructions 26
3.3.6.3 Spacing from Roads 26
3.3.7 Nitrogen Dioxide (N02) - 27
3.3.7.1 Vertical and Horizontal Probe Placement 27
3.3.7.2 Spacing from Obstructions 27
vi
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TABLE OF CONTENTS (Continued)
Page
3.3.8 Lead (Pb) - 27
3.3.8.1 Vertical Placement 27
3.3.8.2 Spacing from Obstructions 28
3.3.8.3 Spacing from Roads 28
3.3.8.4 Other Considerations - 28
3.3.9 Noncriteria Pollutants 28
3.3.9.1 Vertical Placement- - 28
3.3.9.2 Spacing from Obstructions 28
3.3.9.3 Other Considerations 29
3.4 Probe Material and Pollutant Sample Residence Time 29
3.5 Summary of Probe Siting Requirements 29
4. QUALITY ASSURANCE FOR AIR QUALITY DATA ----- 36
4.1 Quality Assurance for Criteria Air Pollutants 36
4.1.1 General Information 36
4.1.2 Quality Control Requirements 37
4.1.2.1 Organizational Requirements 37
4.1.2.2 Primary Guidance 37
4.1.2.3 Pollutant Standards 38
4.1.2.4 Performance and System Audit Programs 38
4.1.3 Data Quality Assessment Requirements 38
4.1.3.1 Precision of Automated Methods 38
4.1.3.2 Accuracy of Automated Methods 39
4.1.3.3" Precision of Manual Methods 39
4.1.3.4 Accuracy of Manual Methods 40
4.1.4 Calculations for Automated Methods 41
4.1.4.1 Single Analyzer Precision 41
4.1.4.2 Single Analyzer Accuracy 42
4.1.5 Calculations for Manual Methods 42
4.1.5.1 Single Instrument Precision for TSP, Pb,
and PMio 42
4.1.5.2 Single Instrument Accuracy for TSP and PMiQ 43
4.1.5.3 Single Instrument Sampling Accuracy for Pb 43
4.1.5.4 Single-Analysis-Day Accuracy for Pb 43
vn
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TABLE OF CONTENTS (Continued)
Page
4.1.6 Organization Reporting Requirements 43
4.2 Quality Assurance for Noncriteria Air Pollutants 43
4.2.1 Selection of Method- 43
4.2.2 Cal ibration 44
4.2.3 Data Validation - 44
4.2.4 Standard and Split Samples 44
5. METEOROLOGICAL MONITORING 45
5.1 Data Required 45
5.2 Exposure of Meteorological Instruments 46
6. METEOROLOGICAL INSTRUMENTATION 49
6.1 Specifications 49
6.1.1 Wind Systems (horizontal wind) 49
6.1.2 Wind Systems (vertical wind) ~ 49
6.1.3 Wind Fluctuations- 49
6.1.4 Vertical Temperature Difference 50
6.1.5 Temperature 50
6.1.6 Humidity 50
6.1.7 Radiation - Solar and Terrestrial 50
6.1.8 Mixing Height - - 50
6.1.9 Precipitation 51
6.1.10 Visibility - - 51
7. QUALITY ASSURANCE FOR METEOROLOGICAL DATA 52
8. DATA REPORTING - 53
8.1 Air Quality Data Reporting 53
8.2 Meteorological Data Format and Reporting 53
APPENDIX A - PROCEDURES TO DETERMINE IF MONITORING DATA WILL BE
REQUIRED FOR A PSD APPLICATION
1. INTRODUCTION A-l
2. PSD PERMIT APPLICATION PROCEDURES - - A-l
2.1 Part 1 - Source Applicability Determination A-l
2.2 Part 2 - Pollutant Applicability Determination A-3
2.3 Part 3 - BACT Analysis - A-5
2.4 Part 4 - Ambient Air Quality Analysis A-5
2.5 Part 5 - Source Impact Analysis A-7
viii
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TABLE OF CONTENTS (Continued)
2.6 Part6 - Additional Impact Analysis A-7
2.7 Part 7 - File Complete PSD Application A-7
3. DECISIONS FOR MONITORING DATA REQUIREMENTS A-10
REFERENCES A-23
ix
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1. INTRODUCTION
The Clean Air Act Amendments of 1977, Part D, Prevention of
Significant Deterioration, require that certain new major stationary
sources and major modifications be subject to a preconstruction review
which includes an ambient air quality analysis. Furthermore, the Act
requires that an analysis be conducted in accordance with regulations
promulgated by the EPA. In this regard, the Agency promulgated PSD
regulations [1] on June 19, 1978, which included ambient monitoring
requirements. Guidelines were published in May 1978 [2] to discuss
monitoring for PSD purposes. However, in response to the June 18, 1979
preliminary Court Decision (Alabama Power Company v. Costle, 13 ERC
1225), EPA proposed revised PSD regulations L3J on September 5, 1979.
The final court decision was rendered December 14, 1979 [4]. Based on
the public comments to the September 5, 1979 proposed PSD regulations
and the December 14, 1979 court decision, EPA promulgated new PSD regula-
tions on August 7, 1980. Some of the pertinent provisions of the 1980
PSD regulations that affect PSD monitoring are discussed below:
(a) Potential to emit.
The PSD regulations retain the requirement that new major
stationary sources would be subject to a new source review on
the basis of potential to emit. However, the annual emission
potential of a source will be determined after the application
of air pollution controls rather than before controls as was
generally done under the 1978 regulations [1].
(b) De minimi's cutoffs.
The PSD regulations will exempt on a pollutant specific basis
major modifications and new major stationary sources from all
monitoring requirements when emissions of a particular pollutant
are below a specific significant emission rate, unless the
source is near a Class I area. Also included are significant
air quality levels which may be used to exempt sources or
modifications from PSD monitoring when the air quality impacts
from the sources or modifications are below specified values.
(c) Noncriteria pollutants.
The 1978 PSD regulations [1] required monitoring only for those
pollutants for which national ambient air quality standards
exist. However, there are a number of pollutants for which
no ambient standards exist (noncriteria pollutants) but which
are regulated under new source performance standards and
national emission standards for hazardous pollutants. The
1980 regulations [5] require an ambient air quality analysis
for all regulated pollutants emitted in significant amounts.
This analysis will generally be based on modeling the impact
of the pollutants in lieu of collecting monitoring data.
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(d) Preconstruction monitoring.
A list of air quality concentrations is included in the PSD
regulations as criteria for generally exempting proposed sources
or modifications from collecting monitoring data. Basically,
monitoring data will be required if the existing air quality
and the impact of the proposed source or modification is equal
to or greater than these concentrations. In certain cases,
even though the air quality impact or background air quality
may be less than these concentrations, monitoring data may be
required if the proposed source or modification will impact a
Class I area, nonattainment area, or area where the PSD incre-
ment is violated.
(e) Postconstruction monitoring.
The PSD regulations include authority to require postconstruc-
tion monitoring. In general, EPA may require postconstruction
monitoring from large sources or sources whose impacts will
threaten standards or PSD increments. The permit granting
authority will make this decision on a case-by-case basis.
On March 20, 1984, [6] EPA proposed revisions to the National Ambient
Air Quality Stardards (NAAQS) for Particulate Matter. Also, revisions
were proposed in 1984 [7] to revise the PSD regulations to account for
the proposed NAAQS change. The 1984 proposed PSD revisions will not
require any new data gathering requirements beyond the 1980 PSD require-
ments for PSD applications submitted prior to 10 months after promulgation
of the anticipated 1985 revised PSD regulations. New monitoring require-
ments for PMio and TSP will be phased in for PSD applications submitted
between 10 and 24 months after promulgation of the 1985 revised PSD regu-
lations. In addition, all new monitoring requirements for PM^o and TSP
will be in effect 24 months after promulgation.
Because of the revisions to the PSD regulations, this guideline has
been modified to reflect such revisions. The purpose of this guideline
is to address those items or activities which are considered essential in
conducting an ambient air quality monitoring program. Guidance is given
for designing a PSD air quality monitoring network as well as the opera-
tional details such as sampling procedures and methods, duration of
sampling, quality assurance procedures, etc. Guidance is also given for
a meteorological monitoring program as well as the specifications for
meteorological instrumentation and quality assurance procedures.
An appendix is included to show how the ambient air quality analysis
fits in the overall PSD requirements. Flow diagrams are presented to
aid a proposed source or modification in assessing if monitoring data
may be required.
General adherence to the guidance contained in this document should
ensure consistency in imp! ementi ng the PSD monitoring regulations.
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2. GENERAL REQUIREMENTS AND CONSIDERATIONS
2.1 Monitoring Data Rationale
The court decision [4] has affirmed the Congressional intent in the
Clean Air Act as it relates to PSD monitoring requirements. The court
ruled that section 165(e)(l) of the Clean Air Act requires that an air
quality analysis be conducted for each pollutant subject to regulation
under the Act before a major stationary source or major modification
could construct. This analysis may be accomplished by the use of modeling
and/or monitoring the air quality. EPA has discretion in specifying the
choice of either monitoring or modeling, consistent with the provisions
in section 165(e)(2). As will be discussed later, modeling will be used
in most cases for the analysis for the noncriteria pollutants.
The court ruled that section 165(e)(2) of the Clean Air Act requires
that continuous preconstruction air quality monitoring data must be
collected to determine whether emissions from a source will result in
exceeding the National Ambient Air Quality Standards (NAAQS). Further,
the data could be used to verify the accuracy of the modeling estimates
since modeling will be the principal mechanism to determine whether
emissions from the proposed source or modification will result in exceeding
allowable increments. In regard to monitoring requirements, the court
stated that EPA had the authority to exempt de minimi's situations.
Postconstruction monitoring data requirements are addressed in
section 165(a)(7) of the Clean Air Act. Sources may have to conduct
such monitoring to determine the air quality effect its emissions may
have on the area it impacts. EPA has the discretion of requiring monitoring
data and the court stated that guidelines could be prepared to show the
circumstances that may require postconstruction monitoring data.
In view of the provisions of sections 165(e)(l), 165(e)(2), and
165(a)(7) of the Clean Air Act, the de mini mis concept, and sections of
the final PSD regulations, Sections 771.1, 2.1.2 and 2.1.3 present the
basic rationale which generally will be followed to determine when
monitoring data will or will not be required. It should be noted that
the subsequent use of "monitoring data" refers to either the use of
existing representative air quality data or monitoring the existing air
qua!ity.
Additional discussion and flow diagrams are presented in Appendix A
of this guideline which show various decision points leading to a
determination as to when monitoring data will or will not be required.
Also, these procedures indicate at what points a modeling analysis must
be performed.
2.1.1 Criteria Pollutants - Preconstruction Phase
For the criteria pollutants (S02, CO, and NOg) continuous air quality
monitoring data must, in general, be used to establish existing air quality
concentrations in the vicinity of the proposed source or modification.
For VOC emissions, continuous ozone monitoring data must be used to
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establish existing air quality concentrations in the vicinity of the
proposed source or modification. For TSP, PMig, and lead, the 24-hour
manual method will be used to establish the existing air quality concen-
trations. However, no preconstruction monitoring data will generally be
required if the ambient air quality concentration before construction is
less than the significant monitoring concentrations. (The significant
monitoring concentrations for each pollutant are shown in Table A-2 in
the appendix to this guideline.) To require monitoring data where the air
quality concentration of a pollutant is less than these values would be
questionable because these low level concentrations cannot reasonably be
determined because of measurement errors. These measurement errors may
consist of errors in sample collection, analytical measurement, calibra-
tion, and interferences.
Cases where the projected impact of the source or modification is
less than the significant monitoring concentrations would also generally
be exempt from preconstruction monitoring data, consistent with the de
mini mis concept. [40 CFR 51.24( i) (8) and 40 CFR 52.2K i) (8)].
The one exception to the de minimi's exemption occurs when a proposed
source or modification would adversely impact on a Class I area or would
pose a threat to the remaining allowable increment or NAAQS. For those
situations where the air quality concentration before construction is
near the significant monitori.ng concentration, and there are uncertainties
associated with this air quality situation, then preconstruction air
quality monitoring data may be required. These situations must be
evaluated on a case-by-case basis by the permit granting authority
before a final decision is made.
2.1.2 Criteria Pollutants - Postconstruction Phase
EPA has discretion in requiring postconstruction monitoring data
under section 165(a) (7) of the Clean Air Act and in general will not
require postconstruction monitoring data. However, to require air
quality monitoring data implies that the permit granting authority will
have valid reasons for the data and, in fact, will use the data after it
is collected. Generally, this will be applied to large sources or
sources whose impact will threaten the standards or PSD increments.
Examples of when a permit granting authority may require postconstruction
monitoring data may include:
a. NAAQS are threatened - The postconstruction air quality is
projected to be so close to the NAAQS that monitoring is needed to
certify attainment or to trigger appropriate SIP related actions if
nonattainment results.
b. Source impact is uncertain or unknown - Factors such as complex
terrain, fugitive emissions, and other uncertainties in source or emission
characteristics result in significant uncertainties about the projected
impact of the source or modification. Postconstruction data is justified
as a permit condition on the basis that model refinement is necessary to
assess the impact of future sources of a similar type and configuration.
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2.1.3 Noncriten'a Pollutants - Preconstruct!'on and Postconstructlon Phase
Consistent with section 165(e)(l) of the Clean Air Act, EPA believes
that an analysis based on modeling of the impact of noncriteria pollutants
on the air quality should generally be used in lieu of monitoring data.
The permit granting authority, however, does have the discretion of
requiring preconstruction and postconstruction monitoring data. Before
a permit granting authority exercises its discretion in requiring monitor-
ing data, there should be an acceptable measurement method approved by
EPA (see Section 2.6) and the concentrations would generally be equal
to or greater than the significant monitoring concentrations (shown in
Table A-2 of the appendix).
A permit granting authority may require monitoring data in cases
such as (a) where a State or other jurisdiction has a standard for a
noncriteria pollutant and the emissions from the proposed source or
modification pose a threat to the standard, (b) where the reliability of
emission data used as input to modeling existing sources is highly
questionable, especially for the pollutants regulated under the national
emission standards for hazardous pollutants, and (c) where available
models or complex terrain make it difficult to estimate air quality or
impact of the proposed source or modification.
2.2 Monitoring Objective and Data Uses
The basic objective of PSD monitoring is to determine the effect
emissions from a source are having or may have on the air quality in any
area that may be affected by the emission. Principal uses of the data
are as follows:
(a) To establish background air quality concentrations in the
vicinity of the proposed source or modification. These background
levels are important in determining whether the air quality before or
after construction are or will be approaching or exceeding the NAAQS or
PSD i ncrement.
(b) To validate and refine models. The data will be helpful in
verifying the accuracy of the modeling estimates.
2.3 VOC and 03 Monitoring Requirements
The previous 0.24 ppm nonmethane organic compound (NMOC) standard,
which was used as a guide for developing State Implementation Plans to
attain the 03 ambient standard, has been rescinded. However, VOC
emissions are the precursors in the formation of ozone. Consequently,
any new source or modified existing source located in an unclassified or
attainment area for ozone that is equal to or greater than 100 tons per
year of VOC emissions will be required to monitor ozone. VOC monitoring
will not be required.
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2.4 Use of Representative Air Quality Data
The use of existing representative air quality data was one of the
options discussed in Section 2.1 for monitoring data. In determining
whether the data are representative, three major items which need to be
considered are monitor location, quality of the data, and currentness of
the data.
2.4.1 Monitor Location
The existing monitoring data should be representative of three
types of areas: (1) the location(s) of maximum concentration increase
from the proposed source or modification, (2) the location(s) of the
maximum air pollutant concentration from existing sources, and (3) the
location(s) of the maximum impact area, i.e., where the maximum pollutant
concentration would hypothetically occur based on the combined effect of
existing sources and the proposed new source or modification. Basically,
the locations and size of the three types of areas are determined through
the application of air qual ity model s. The areas of maximum concentration
or maximum combined impact vary in size and are influenced by factors
such as the size and relative distribution of ground level and elevated
sources, the averaging times of concern, and the distances between impact
areas and contributing sources.
In situations where there is no existing monitor in the modeled
areas, monitors located outside these three types of areas may or may
not be used. Each determination must be made on a case-by-case basis.
In order to clarify EPA's intent regarding the use of existing
monitoring data, some examples are included to demonstrate the overall
intent.
(a) Case I - If the proposed source or modification will
be constructed in an area that is generally free from the impact of
other point sources and area sources associated with human activities,
then monitoring data from a "regional" site may be used as representative
data. Such a site could be out of the maximum impact area, but must be
similar in nature to the impact area. This site would be characteristic
of air quality across a broad region including that in which the proposed
source or modification is located. The intent of EPA is to limit the
use of these "regional" sites to relatively remote areas, and not to use
them in areas of multisource emissions or areas of complex terrain.
(b) Case II - If the proposed construction will be in an area of
multi source emissions and basically flat terrain, then the proposed
source or modification may propose the use of existing data at nearby
monitoring sites if either of the following criteria are met.
1. The existing monitor is within 10 km of the points of
proposed emissions, or
2. The existing monitor is within or not farther than 1 km
away from either the area(s) of the maximum air pollutant concentration
from existing sources or the area(s) of the combined maximum impact from
existing and proposed sources.
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If the existing monitor(s) meets either of the above two
conditions, the data could be used together with the model estimates to
determine the concentrations at all three types of areas discussed
earlier in this section.
As an example of the first criterion, if an existing monitor is
located within 10 km from the points of proposed emissions but not
within the boundaries of the modeled areas of either of the three loca-
tions noted above, the data could be used together with model estimates
to determine the concentrations at the three types of required area.
The next example applies to the second criterion. In evaluating
the adequacy of the location of existing monitors, the applicant must
first, through modeling, determine the significant ambient impact area
of the proposed source. In general, except for impact on Class I areas,
the application of air quality models for the purpose of determining
significant ambient impact would be limited to 50 km downwind of the
source or to that point where the concentration from the source falls
below the levels shown in Table A-3 of the Appendix. For Class I areas,
a significant impact is 1 pg/nr (24-hr) for PM^n, TSP, and SOo. The appli-
cant would then identify within this significant impact area the area(s)
of the maximum air pollutant concentration from existing sources and the
area(s) of the combined maximum impact from existing and proposed sources.
The area(s) of estimated maximum concentration from existing sources or
the estimated maximum combined impact area(s) are determined as follows:
First, within the modeled significant ambient impact area, estimate the
point of maximum concentration from existing sources, and the point of
combined maximum impact (existing and proposed source). Using these
concentration values, determine the areas enclosed by air quality concen-
tration isopleths equal to or greater than one half of the respective
estimated maximum concentration. An existing monitor located within or
not farther than 1 km away from of any of these areas can yield represen-
tative data.
The rationale for considering the use of existing data collected
from monitors satisfying the above criteria is that modelers have a
reasonable degree of confidence in the modeling results within the 10 km
distance and the maximum concentrations from most sources are likely
to occur within this distance. Generally, the modeling results in this
flat terrain case may under or over predict by a factor of two, and thus
the actual maximum impact from the source(s) could occur at points where
the model predicts one half of this impact. Data collected within or not
farther than 1 km from areas may be considered as representative.
(c) Case III - If the proposed construction will be in an area of
multisource emissions and in areas of complex terrain, aerodynamic downwash
complications, or land/water interface situations, existing data could
only be used for PSD purposes if it were collected (1) at the modeled
location(s) of the maximum air pollution concentration from existing
sources, (2) at the location(s) of the maximum concentration increase
from the proposed construction, and (3) at the location(s) of the maximum
impact area. If a monitor is located at only one of the locations mentioned
above and the locations do not coincide, the source would have to monitor
at the other locations.
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It must be emphasized that the permit granting authority may choose
not to accept data proposed under the cases discussed above. This may
occur because of additional factors, especially in Case II which were
not discussed but must be considered, such as uncertainties in data bases
for modeling and high estimates of existing air quality resulting in
possible threats to the applicable standards. Because of such situations,
the permit granting authority must review each proposal on a case-by-case
basis to determine if the use of existing data will be acceptable. It
is important for the proposed source or modification to meet with the
permit granting authority to discuss any proposed use of existing data.
If the data are not acceptable, then a monitoring program would have to
be started to collect the necessary data.
2.4.2 Data Quality
The monitoring data should be of similar quality as would be obtained
if the applicant monitored according to the PSD requirements. As a
minimum, this would mean:
1. The monitoring data were collected with continuous instrumentation,
No bubbler data should be included. See Section 2.4 for frequency
of particulate pollutant sampling.
2. The applicant should be able to produce records of the
quality control performed during the time period at which
the data were collected. Such quality control records should
include calibration, zero and span checks, and control checks.
In addition, quality control procedures should be a minimum
specified in the instrument manufacturer's operation and
instruction manual.
3. Historical data that were gathered from monitors which were
operated in conformance with Appendix A or B of the Part 58
regulations [8] would satisfy the quality assurance requirements.
.. . %
4. The calibration and span gases (for CO, S02 and N02) should
be working standards certified by comparison to a National
Bureau of Standards gaseous Standard Reference Material.
5. The data recovery should be 80 percent of the data possible
during the information effort.
2.4.3 Currentness of Data
The air quality monitoring data should be current. Generally, this
would mean for the preconstruction phase that the data must have been
collected in the 3-year period preceding the permit application, provided
the data are still representative of current conditions. When such data
are required, the noncriteria pollutant data must also have been collected
in the 3-year period preceding the permit application provided that an
acceptable measurement method was used. For the postconstruction phase,
the data must be collected after the source or modification becomes
operational.
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2.4.4 Provisions for PMjp and TSP in Transition Period of 1985 PSD Regulations
Section 2.5.2 discusses the use of existing representative air quality
data for PIQ and TSP during the phasing in of the 1985 PSD amendments for
particulate matter. References are cited for using existing nonreference
?MIQ and/or PMi5 data where available, or TSP data. Existing representative
air quality data for PMio collected later than 12 months after promulgation
of the 1985 PSD regulations must have been collected using reference or
equivalent PM^o method samplers. Also, representative air quality data for
TSP collected later than 6 months after promulgation of the 1985 PSD regula-
tions must have been collected using the siting criteria as discussed
in Section 3.3.2.
2.5 Duration of Monitoring
2.5.1 Normal Conditions
If a source must monitor because representative air quality
data are not available for the preconstruction monitoring data requirement,
then monitoring generally must be conducted for at least 1 year prior to
submission of the application to construct. Also, if a source decides to
monitor because representative air quality data are not available for the
postconstruction monitoring data requirement, then monitoring must also be
conducted for at least 1 year after the source or modification becomes op-
erational. However, under some circumstances, less than 1 year of air
quality data may be acceptable for the preconstruction and postconstruction
phases. This will vary according to the pollutant being studied. For all
pollutants, less than a full year will be acceptable if the applicant demon-
strates through historical data or dispersion modeling that the data are
obtained during a time period when maximum air quality levels can be expected.
However, a minimum of 4 months of air quality data will be required. As
discussed in Section 2.1.3, monitoring for noncriteria pollutants will
generally not be required.
Special attention needs to be given to the duration of monitoring
for ozone. Ozone monitoring will still be required during the time
period when maximum ozone concentrations will be expected. Temperature
is one of the factors that affect ozone concentrations, and the maximum
ozone concentrations will generally occur during the warmest 4 months of
the year, i.e., June-Sept ember. However, historical monitoring data
have shown that the maximum yearly ozone concentration for some areas
may not occur from June-September. Therefore, ozone monitoring will
also be required for those months when historical ozone data have shown
that the yearly maximum ozone concentrations have occurred during months
other than the warmest 4 months of the year. This requirement is in
addition to monitoring during the wannest 4 months of the year. If
there is an interval of time between the wannest 4 months of the year
and month where historical monitoring data have shown that the maximum
yearly ozone concentration has occurred, then monitoring must also be
conducted during that interval. For example, suppose historical data
have shown the maximum yearly ozone concentration for at least 1 year
occurred in April. Also, suppose the warmest 4 months for that particular
area occurred June-September. In such cases, ozone monitoring would be
required for April (previous maximum concentration month), May (interval
month), and June-September (warmest 4 months).
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Some situations may occur where a source owner or operator may not
operate a new source or modification at the rated capacity applied for
in the PSD permit. Generally, the postconstruction monitoring should
not begin until the source is operating at a rate equal to or greater
than 50 percent of its design capacity. However, in no case should the
postconstruction monitoring be started later than 2 years after the
start-up of the new source or modification.
If the permit granting authority has determined that less than 1
year of monitoring data is permissible, the source must agree to use the
maximum values collected over this short period for comparison to all
applicable short-term standards, and the average value for the short
period as the equivalent of the annual standard.
It should also be noted that the above discussion of less than 1
year of data pertains to air quality data, not meteorological data. When
the air quality impact must be determined using a dispersion model, the
preferred meteorological data base is at least 1 year of on-site data.
Although less than 1 year of data may be sufficient to determine the
acceptability for a model, once the model has been accepted, a full year
of meteorological data must be used in the PSD analysis.
2.5.2 Transition Period for PMip and TSP
The PSD regulatory changes for particulate matter (PMio and Tsp)
[7] provide for a transition period for phasing in the PM^g and TSP
monitoring data requirements. The term "monitoring data" was previously
defined in Section 2.1 as the use of existing representative air quality
data or monitoring to determine the existing air quality.
2.5.2.1 Transition Within 10 Months After Promulgation - The first
provision of the regulations concerning a transition period is in section
52.21(i)(ll)(i) and relates to applications for a PSD permit submitted
within 10 months after promulgation of the 1985 PSD amendments. During
this 10-month period, the permit granting authority has the discretion of
waiving the preconstruction monitoring data requirements for the ambient
air quality analysis discussed in Appendix A of this guideline. In all
cases no applicant would be required to initiate monitoring during this
period. However, the requirement to use existing air quality data would
be discretionary. The discretion would be based in part on the availability
of existing air quality data which could include total suspended particulate
matter data, PM^o data, as well as inhalable particulate matter (PMis) data.
The PMi5 data would be from samplers with inlets designed for a 50 percent
collective efficiency at 15 ym. The PMi5 data could be from dichotomous
samplers or high volume samplers with a size selective inlet of 15 pm.
(a) Comparing Representative Air Quality Data to PMig NAAQS.
In situations where existing PMjo and/or PMis data are available, the
data may be" used for describing the existing air quality levels for
comparison with the PM^Q NAAQS. Reference [9] describes procedures for
estimating ambient PM]_Q concentrations from PM]^ ambient air measurements.
The PM^ data multiplied by a correction factor of 0.8 may be assumed to be
equivalent to PM^o- Existing TSP data may only be used as a "one-for-one"
substitute for comparison to the PM^Q NAAQS.
10
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Concerning the priorities for using existing air quality data, the
first preference is to use ambient PM^o data. The second preference is
to use inhalable particulate (PMis) measurements obtained with a dichoto-
mous sampler or a size selective high volume sampler. The third preference
is to use total suspended particulte (TSP) data. Also, combinations of
the above data may be used.
( b) Comparing TSP Representative Air Quality Data to TSP Secondary
NAAQS. Existing TSP data may be used directly for comparison to the TSP
secondary NAAQS during this period. The siting criteria described in
Section 3.3.1 would be used for these monitors.
2.5.2.2 Transition During 10-16 Months After Promulgation - The second
provision of the regulations concerning a transition period is in section
52.21(i)(ll)(ii) and relates to applications for a PSD permit submitted
between 10 and 16 months after promulgation of the regulations. If pre-
construction monitoring data are required in the ambient air quality
analysis during this 10 to 16-month period, the applicant must use repre-
sentative air quality data or collect monitoring data.
(a) Comparing P reconstruction Air Quality Data to PMjQ NAAQS.
Existing representative PM^o and/ or PM^s air quality data may be used
if available. The priorities and calculations for using these data
were described in Section 2.5.2.1. Existing TSP data cannot be used dur-
ing during this transition period.
If the applicant collects new PM^o and/ or PM^s monitoring data, the
data should have been collected from the date 6 months after promulgation
of the 1985 PSD amendments to the time the PSD application becomes other-
wise complete. The preferences for PMiQ and PM^ data were previously
discussed.
(b) Comparing TSP P reconstruction Air Quality Data to TSP NAAQS.
Existing representative TSP air quality data may be used during this
period for comparision with the TSP secondary NAAQS. These data, however,
must be from TSP monitors sited using the new criteria in Section 3.3.2.
If the applicant collects new TSP monitoring data, the TSP monitors must
also be sited using the new criteria in Section 3.3.2. When collecting
new monitoring data, the data should have been collected from the date 6
months after promulgation of the 1985 PSD amendments to the time the PSD
application becomes otherwise complete.
(c)' Other Considerations and Explanations. As discussed in Section
2.5.1, less than the maximum amount of data (10 months in this case) moni-
toring data will be acceptable if the applicant demonstrates, through
historical data or dispersion modeling, that the data would be obtained
during a time period when the maximum air quality can be expected. The
minimum of 4 months of air quality data would still be required. The
assumptions for the 10-month figure were derived by assuming that 5 months
are needed for instrument and equipment procurement, 1 month to install
the equipment, calibrate and ensure satisfactory operation, and a minimum
of 4 months of monitoring data. The upper range of 16 months after promul
gation for use of non-reference PMio monitoring is based on the assumption
that within 11 months after promulgation, reference or equivalent method
samplers for PMio would be designated by EPA and would be commercially
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available. Furthermore, 1 month would be needed to install the equipment,
calibrate, and ensure satisfactory operation, and a minimum of 4 months
would be needed for gathering monitoring data.
2.5.2.3 Transition During 16-24 Months After Promulgation - The third
transition period provision of the regulations is in section 52.21(m)(l )( vii)
and relates to applications for a PSD permit submitted between 16 and 24
months after promulgation of the regulations. If preconstruction monitor-
ing data are required in the ambient air quality analysis during this 16
to 24-month period, the applicant must use representative air quality
data or collect monitoring data.
(a) Comparing Preconstruction Air Quality Data to PMio NAAQS. .
If existing representative PMiq and/ or PMis air quality data are available
they may be used. The priorities and calculations for using these data
were described in Section 2.5.2.1. Existing TSP data cannot be used
during this transition period. If no PMiQ or PM15 representative air
quality data are available, the applicant will have to collect monitoring
data using only reference or equivalent PMio method samplers. The sampling
must be conducted for at least 12 months during the period from 12 months
after promulgation to the time when the application is completed, except
if the permit granting authority determines that a complete and adequate
analysis can be accomplished with monitoring data'over a shorter period
(but in no case less than 4 months).
(b) Comparing TSP Preconstruction Air Quality Data to TSP NAAQS.
Existing representative TSP air quality data may be used during this
period for comparison with the TSP secondary NAAQS if sited using the new
criteria in Section 3.3.2. If new PSD monitor! ng data are collected by
the applicant, the TSP monitors must also be sited using the new criteria
in Section 3.3.2. The TSP sampling must be conducted during the period
from 12 months after promulgation to the time when the application is
completed, except if the permit granting authority determines that a
complete and adequate analysis can be accomplished with monitoring data
over a shorter period (but in no case less than 4 months).' "
2.5.2.4 Period Following 24 Months After Promulgation - For applications
for a PSD permit submitted later than 24 months after promulgation, the
transition period would no longer be in effect. If preconstruction mon-
itoring data are required in the ambient air quality analysis, the appli-
cant must use representative air quality data or collect monitoring data.
(a) Comparing Preconstruction Air Quality Data to PMio NAAQS. If
existing representative PMio air quality data are available, they may be
used. However, existing PMio representative air quality data collected
later than 24 months after the promulgation of the 1985 PSD amendments
must have been collected using reference or equivalent PMio method sam-
plers. If no PMjo representative air quality data are available, the
applicant will have to collect monitoring data using only reference or
equivalent PMio method samplers.
(b) Comparing TSP Preconstruction Air Quality Data to TSP NAAQS.
Existing representative TSP air quality data may be used for comparison
with the TSP secondary NAAQS if sited using the new criteria in Section
3.3.2. If new PSD monitoring data are collected by the applicant, the
TSP monitors must also be sited using the new criteria in Section 3.3.2.
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2.6 Sampling Methods and Procedures
(a) Criteria pollutants.
All ambient air quality monitoring must be done with continuous
Reference or Equivalent Methods, with the exception of particulate matter
and lead for which continuous Reference or Equivalent Methods do not exist.
For particulate matter and lead, samples must be taken in accordance with
the Reference Method. The Reference Methods are described in 40 CFR 50.
A list of designated continuous Reference or Equivalent Methods can be
obtained by writing Environmental Monitoring Systems Laboratory, Department
E (MD-76), U.S. Environmental Protection Agency, Research Triangle Park,
NC 27711.
(b) PMio Transition for Won- reference Methods
As discussed in Section 2.5.2, non- reference monitors for F*MIQ
may be used for applications submitted prior to 16 months after promulga-
tion of the 1985 PSD regulations. These could include PMio monitors as
well as inhalable particulate matter (PMis) monitors. The PMis monitors
could be dichotomous monitors or high volume monitors with a size selec-
tive inlet of 15 pm.
(c) Noncriteria pollutants.
For noncriteria pollutants, a list of acceptable measurement
methods is available upon request by writing Environmental Monitoring
Systems Laboratory, Quality Assurance Division (MD-77), U.S. Environmental
Protection Agency, Research Triangle Park, NC 27711. This list of accept-
able methods will be reviewed at least annually and are available from
the above address. Measurement methods considered candidates for the
noncriteria pollutant list should be brought to the attention of EPA at
the address given above.
2.7 Frequency of Sampling
For all gaseous pollutants and for all meteorological parameters,
continuous analyzers must be used. Thus, continuous sampling (over the
time period determined necessary) is required. For particulate pollu-
tants, except for PMio, daily sampling (i.e., one sample every 24 hours)
is required except in areas where the applicant can demonstrate that signi-
ficant pollutant variability is not expected. In these situations, a
sampling schedule less frequent than every day would be permitted. However,
a minimum of one sample every 6 days will be required for these areas.
The sampling frequency would apply to both preconstruction and postcon-
struction monitoring.
The sampling frequency for PMio monitors is determined by the
, or TSP concentrations relative to the PMio NAAQS. The philosophy is
to use existing data where possible to determine the PMio sampling frequency.
The frequencies discussed below are consistent with the Part 58 sampling
frequencies [6]. If PMio data are available but not from the locations as
specified in Section 2.4.1, then modeling could be used in conjunction with
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the data to estimate the PMio concentrations in the appropriate sampling
area(s) to determine the PMio sampling frequency. If these estimated concen-
trations were < 80 percent of the PMjQ NAAQS, then a minimum of one sample
every 6 days would be required for PM^Q monitors; for >80 - <90 percent of
the ?MIQ NAAQS, a minimum of one sample every other day would be required;
and for >_90 percent of the PMiQ NAAQS every day sampling would be required.
PMi5 data would be treated the same way except the data must be multiplied
by a correction factor 0.8 to be equivalent to
Reference [9] describes how TSP data* may also be used to estimate the
probability of exceeding the PMiQ NAAQS in the appropriate sampling area(s)
for purposes of determining the PMiQ sampling frequency. If the probabilities
are < .20 of the PMio NAAQS, then a minimum of one sample every 6 days would
be required for PMiQ monitors; for >_. 20 - <.50 probabilities, a minimum of
one sample every other day would be required; and for >_.50 probabilities,
every day sampling would be required. These probability intervals are in
line with the percent of the NAAQS intervals specified when using PMio data.
In those cases where no PMio, PMi5, or TSP data are available to
determine the PM^Q sampling frequency, the PMiQ expected concentrations
could be estimated by modeling. These estimated concentrations would be
used to calculate the percentage of the PMio NAAQS and the resulting PMio
sampling frequency as discussed above for the cases where PMio data were
available.
2.8 Monitoring Plan
A monitoring plan prepared by the source should be submitted to and
approved by the permit granting authority before any PSD monitoring
begins. Note that approval of the monitoring plan before a monitoring
program is started is not a requirement. However, since the network
size and station locations are determined on a case-by-case basis, it
would be prudent for the owner or operator to seek review of the network
and the overall monitoring plan from the permit granting authority prior
to collecting data. This review could avoid delays in the processing of
the permit application and could also result in the elimination of any
unnecessary monitoring. Delays may result from insufficient, inadequate,
poor, or unknown quality data. Table 1 lists the types of information
that should be included in the monitoring plan.
2.9 Meteorological Parameters and Measurement Methods
Meteorological data will be required for input to dispersion models
used in analyzing the impact of the proposed new source or modification
on ambient air quality and the analyses of effects on soil, vegetation,
and visibility in the vicinity of the proposed source. In some cases,
representative data are available from sources such as the National
Weather Service. However, in some situations, on-site data collection
will be required. The meteorological monitoring and instrumentation
considerations are discussed in Sections 5 and 6.
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TABLE 1. MINIMUM CONTENTS OF A MONITORING PLAN
SOURCE ENVIRONMENT DESCRIPTION (within 2 km of source)
topographical description
land-use description
topographical map of source and environs (including location of
existing stationary sources, roadways, and monitoring sites)
climatological description
quarterly wind roses (from meteorological data collected at the
source or other representative meteorological data)
II. SAMPLING PROGRAM DESCRIPTION
time period for which the pollutant(s) will be measured
rationale for location of monitors (incl ude modeling results and
analysis of existing soures in the area)
rationale for joint utilization of monitoring network by other
PSD sources
III. MONITOR SITE DESCRIPTION " "
Universal Transverse Mercator (UTM) coordinates
height of sampler (air intake) above ground
distance from obstructions and heights of obstructions
distance from other sources (stationary and mobile)
photographs of each site (five photos: one in each cardinal direc-
tion looking out from each existing sampler or where a future
sampler will be located, and one closeup of each existing sampler
or where a future sampler will be located. Ground cover should be
included in the closeup photograph.)
IV. MONITOR DESCRIPTION
name of manufacturer
t description of calibration system to be used
type of flow control and flow recorder
V. DATA REPORTING
format of data submission
t frequency of data reporting
VI. QUALITY ASSURANCE PROGRAM
t calibration frequency
independent audit program
internal qua!ity control procedures
data precision and accuracy calculation procedures
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3. NETWORK DESIGN AND PROBE SITING CRITERIA
A source subject to PSD should proceed with designing a PSD monitoring
network only after going through the procedure in Appendix A to determine
if monitoring data will be required. To fulfill that requirement, a source
may use representative air quality data which was discussed in Section 2.4
or monitor. This section presents guidance to be used if an applicant
decides to monitor in lieu of using representative air quality data.
3.1 Network Design
The design of a network for criteria and noncriteria pollutants
will be affected by many factors, such as topography, climatology,
population, and existing emission sources. Therefore, the ultimate
design of a network for PSD purposes must be decided on a case-by-case
basis by the permit granting authority. Section 3.2 discusses the number
and location of monitors for a PSD network. Additional guidance on the
general siting of the monitors may be found in references 10-14 which
discuss highest concentration stations, isolated point sources, effects
of topography, etc. Probe siting criteria for the monitors are discussed
in Section 3.3. The guidelines presented here should be followed to the
maximum extent practical in developing the final PSD monitoring network.
3.2 Number and Location of Monitors
The number and location of monitoring sites will be determined on a
case-by-case basis by the source owner or operator and reviewed by the
permit granting authority. Consideration should be given to the effects
of existing sources, terrain, meteorological conditions, existence of
fugitive or reentrained dusts, averaging time for the pollutant, etc.
Generally, the number of monitors will be higher where the expected
spatial variability of the pollutant in the area(s) of study is higher.
3.2.1 Preconstruction Phase
Information obtained in the ambient air quality analysis in Appendix
A will be used to assist in determining the number and location of monitors
for the preconstruction phase. The air quality levels before construction
were determined by modeling or in conjunction with monitoring data. The
screening procedure (or more refined model) estimates were determined in
Appendix A.
The source should first use the screening procedure or refined model
estimates to determine the general location(s) for the maximum air quality
concentrations from the proposed source or modification. Secondly, the
source should determine by modeling techniques the general location(s)
for the maximum air quality levels from existing sources. Thirdly, the
modeled pollutant contribution of the proposed source or modification
should be analyzed in conjunction with the modeled results for existing
sources to determine the maximum impact area. Application of these
models must be consistent with EPA's "Guideline on Air Quality Models"
[15]. This would provide sufficient information for the applicant to
place a monitor at (a) the location(s) of the maximum concentration
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increase expected from the proposed source or modification, (b) the
location(s) of the maximum air pollutant concentration from existing
sources of emissions, and (c) the location(s) of the maximum impact area,
i.e., where the maximum pollutant concentration would hypothetically
occur based on the combination effect of existing sources and the pro-
posed new source or modification. In some cases, two or more of these
locations may coincide and thereby reduce the number of monitoring
stations.
Monitoring should then be conducted in or as close to these areas
as possible (also see discussion in Section 3.2.3). Generally, one to
four sites would cover most situations in multisource settings. For
remote areas in which the permit granting authority has determined that
there are no significant existing sources, a minimum number of monitors
would be needed, i.e., one or probably two at the most. For new sources,
in these remote areas, as opposed to modifications, some concessions will
be made on the locations of these monitors. Since the maximum impact
from these new sources would be in remote areas, the monitors may be
located, based on convenience or accessibility, near the proposed new
source rather than near the maximum impact area since the existing air
quality would be essentially the same in both areas. However, the maximum
impact area is still the preferred location.
When industrial process fugitive particulate emissions are involved,
the applicant should locate a monitor at the proposed source site (also
see Section 3.2.3). If stack emissions are also involved, a downwind
location should also be selected. For fugitive hydrocarbon emissions,
the applicant should locate a monitor downwind of the source at the point
of expected maximum ozone concentration contribution. This location will
be found downwind during conditions that are most conducive to ozone for-
mation, such as temperature above 20°C (68°F) and high solar radiation
intensity. For hydrocarbon emissions from a stack, the applicant should
also locate the monitor in the area of expected maximum ozone concentra-
tion. For both fugitive and stack emissions, the selection of areas of
highest ozone concentrations will require wind speed and direction data
for periods of photochemical activity. Monitoring for ozone will only be
necessary during the seasons when high concentrations occur.
Since ozone is the result of a complex photochemical process, the
rate of movement across an area of the air mass containing precursors
should be considered. The distance from the proposed source to the
monitor for an urban situation should be about equal to the distance
traveled by the air moving for 5 to 7 hours at wind speeds occurring
during periods of photochemical activity. In an urban situation, ozone
formation over the initial few hours may be supressed by nitric oxide
(NO) emissions. For a point source, the NO interactions may be minimal,
and the travel time to the expected maximum ozone concentration may be 3
to 4 hours downwind. In general, the downwind distance for the maximum
ozone site should generally not be more than 15 to 20 miles from the
source because a lower wind speed (2-3 miles per hour) with less dilution
would be a more critical case. Additionally, the frequency that the
wind would blow from the source over the site diminishes with increasing
distances.
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3.2.2 Postconstruction Phase
As discussed above for preconstruction monitoring, appropriate dis-
persion modeling techniques are used to estimate the location of the
air quality impact of the new source or modification. Monitors should
then be placed at (a) the expected area of the maximum concentration
from the new source or modification, and (b) the maximum impact area(s),
i.e., where the maximum pollutant concentration will occur based on the
combined effect of existing sources and the new source or modification.
It should be noted that locations for these monitors may be different
from those sites for the preconstruction phase due to other new sources
or modifications in the area since the preconstruction monitoring.
Generally, two or three sites would be sufficient for most situations
in multisource areas. In remote areas where there are no significant
existing sources, one or two sites would be sufficient. These sites
would be placed at the locations indicated from the model results. The
same concerns discussed in Section 3.2.1 regarding industrial process
fugitive particulate emissions, fugitive hydrocarbon emissions, and ozone
monitoring would also be applicable for the postconstruction phase.
3.2.3 Special Concerns for Location of Monitors
For the preconstruction and postconstruction phases, modeling is
used to determine the general area where monitors would be located. Some
of the modeled locations may be within the confines of the source's bound-
ary. However, monitors should be placed in those locations satisfying
the definition of ambient air. Ambient air is defined in 40 CFR 50.1(e)
as "that portion of the atmosphere, external to buildings, to which the
general public has access." Therefore, if the modeled locations are
within an area excluded from ambient air, the monitors should be located
downwind at the boundary of that area.
In some cases, it is simply not practical to place monitors at the
indicated modeled locations. Some examples may include over open bodies
of water, on rivers, swamps, cliffs, etc. The source and the permit
granting authority should determine on a case-by-case basis alternative
locations.
3.3 Probe Siting Criteria
The desire for comparability in monitoring data requires adherence
to some consistent set of guidelines. Therefore, the probe siting cri-
teria discussed below must be followed to the maximum extent possible
to ensure uniform collection of air quality data that are comparable and
compatible.
Before proceeding with the discussion of pollutant specific probe
siting criteria, it is important to expand on the discussion in Section
3.2 of the location of monitors. In particular, reference is made to
two monitoring objectives.
Case 1: Locating monitors to determine the maximum concentration
from the proposed source and/or existing sources.
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Case 2: Locating monitors to determine where the combined
impact of the proposed source and existing sources
would be expected to exhibit the highest concentrations.
For Case 1, the driving force for locating the siting area of the
monitor as well as the specific location of the probe or instrument shelter
is the objective of measuring the maximum impact from the proposed source.
Two Case 1 examples are given. Consider the first situation in which a
proposed source would be emitting pollutants from an elevated stack. Under
these circumstances, sufficient mixing generally occurs during the transport
of the emissions from the stack to the ground resulting in small vertical
gradients near ground level, thus, a wide range of probe heights, 3-15 meters
for gases and 2-15 meters for particulates is acceptable. For the same
objective (maximum concentration from proposed source), consider the second
example in which pollutants would be emitted from a ground level source.
In this case, the concentration gradient near the ground can be large,
thereby requiring a much tighter range of acceptable probe heights. For
ground level sources emitting pollutants with steep vertical concentration
gradients, efforts should be made to locate the inlet probe for gaseous
pollutant monitors as close to 3 meters (a reasonable practical represen-
tation of the breathing zone) as possible and for particulate monitors
using the hi-volume sampler 2 to 7 meters above ground level. The ration-
ale for the 3 meters is that for gaseous pollutant measurements, the inlet
probe can be adjusted for various heights even though the monitor is loca-
ted in a building or trailer. On the contrary, the 2-3 meter height for
the hi-volume sampler placement is not practical in certain areas. The 7
meter height allows for placement on a one story building and is reasonably
close to representing the breathing zone.
Turn now to the second monitoring objective, Case 2, which is
locating monitors to determine the maximum impact area taking into consid-
eration the proposed source as well as existing sources. The critical
element to keep in mind in locating a monitor to satisfy this objective
is that the intent is to maximize the combined effect. Thus, in one
circumstance, the existing source might contribute the largest impact.
The importance of the above discussion to the topic of probe siting cri-
teria is that in attempting to locate a monitor to achieve this objective,
the placement of the probe or instrument shelter can vary depending upon
which source is the predominant influence on the maximum impact area. As
an extreme example, consider the situation where a proposed elevated
source would emit CO into an urban area and have maximum combined CO
impact coincident to an area adjacent to a heavily traveled traffic
corridor. It is known that traffic along corridors emit CO in fairly
steep concentration gradients so the placement of the probe to measure
the areas of highest CO concentration can vary significantly with probe
height as well as distance from the corridor. In this example, the
traffic corridor has the major influence on the combined impact and
therefore controls the probe placement. As noted in the CO probe siting
criteria in Section 3.3.3 as well as Appendix E of the May 10, 1979
Federal Register promulgation of the Ambient Air Monitoring Regulations
L8J, the required probe height in such microscale cases is given as 3 +_
1/2 meters while the distance of the probe from the roadway would be
between 2 and 10 meters.
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As another example, consider the case where the same proposed CO
source would emit CO at elevated heights and have a combined maximum CO
impact in an urban area that is only slightly affected by CO emissions
from a roadway. The combined impact area in this case is far enough
away from the two sources to provide adequate mixing and only small
vertical concentration gradients at the impact area. In this case, the
acceptable probe height would be in the range of 3-15 meters.
It is recognized that there may be other situations occurring which
prevent the probe siting criteria from being followed. If so, the
differences must be thoroughly documented. This documentation should
minimize future questions about the data.
The desire for comparability in monitoring data requires adherence
to some consistent set of guidelines. Therefore, the probe siting
criteria discussed below must be followed to the maximum extent possible
to ensure uniform collection of air quality data that are comparable and
compatible. To achieve this goal, the specific siting criteria that are
prefaced with a "must" are defined as a requirement and exceptions must
be approved by the permit granting authority. However, siting criteria
that are prefaced with a "should" are defined as a goal to meet for
consistency, but are not a requirement.
3.3.1 Total Suspended Particulates (TSP)
Section 3.3.1 is applicable only for the following cases. PSD
applications submitted before the date 6 months after promulgation of the
1985 PSD regulations would use this siting criteria when collecting TSP
monitoring data. Also, representative air quality data for TSP collected
before the date 6 months after promulgation of the 1985 PSD regulations
could use this siting criteria. For both cases above, data collected
after the 6 month date would use the TSP siting criteria described in
Section 3.3.2.
3.3.1.1 Vertical Placement - The most desirable height for a TSP monitor
is near the breathing zone. However, practical considerations such as
prevention of vandalism, security, accessibility, availability of electri-
city, etc., generally require that the sampler be elevated. Therefore,
a range of acceptable heights needs to be used. In addition, the type
of source, i.e., elevated or ground level, predominantly influencing the
area of impact must be considered when locating the monitor. For purposes
of determining elevated source impact, the sampler air intake must be
located 2-15 meters above ground level. The lower limit was based on a
compromise between ease of servicing the sampler and the desire to avoid
reentrainment from dusty surfaces. The upper limit represents a compromise
between the desire to have measurements which are most representative of
population exposures, and the considerations noted earlier. For ground
level sources with steep vertical concentration gradients, the air
intake must be as close to the breathing zone as practical.
3.3.1.2 Spacing from Obstructions - If the sampler is located on a roof
or other structure, then there must be a minimum of 2 meters separation
from walls, parapets, penthouses, etc. Furthermore, no furnace or
incineration flues should be nearby. The separation distance from flues
is dependent on the height of the flues, type of waste or fuel burned,
20
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and quality of the fuel (ash content). For example, if the emissions
from the chimney are the result of natural gas combustion, no special
precautions are necessary except for the avoidance of obstructions,
i.e., at least 2 meters separation. On the other hand, if fuel oil,
coal, or solid waste is burned and the stack is sufficiently short so
that the plume could reasonably be expected to impact on the sampler
intake a significant part of the time, other buildings/locations in the
area that are free from these types of sources should be considered for
sampling. Trees provide surfaces for particulate deposition and also
restrict airflow. Therefore, the sampler should be placed at least 20
meters from trees.
Obstacles such as buildings must also be avoided so that the distance
between obstacles and the sampler is at least twice the height that the
obstacle protrudes above the sampler. In addition, there must be unre-
stricted airflow in an arc of at least 270° around the sampler, and the
predominant direction for the season of greatest pollutant concentration
potential must be included in the 270° arc.
3.3.1.3 Spacing from Roads - A number of studies [16-23] support the
conclusion that particulate concentrations decrease with increasing
height of the monitor and distance from the road. Quite high concentra-
tions have been reported at monitors located at a low elevation close to
heavily traveled roads. Moreover, monitors located close to streets are
within the concentrated plume of particulate matter emitted and generated
by vehicle traffic. Therefore, ambient monitors for TSP should be located
beyond the concentrated particulate plume generated by traffic, and not
so close that the heavier reentrained roadway particles totally dominate
the measured ambient concentration.
An analysis of various monitoring studies [24] shows that a linear
relationship between sampler height and distance from roadways defines a
zone where the plume generated by traffic greater than approximately 3,000
vehicles per day is diminished. Figure 1 illustrates this relationship
by showing two zones where TSP monitors could be located. Zone A repre-
sents locations which are recommended and Zone B represents locations
which should be avoided in order to minimize undesirable roadway influen-
ces. Roads with lower traffic (less than approximately 3,000 vehicles
per day) are generally not considered to be a major source or vehicularre-
lated pollutants, and so as noted in Figure 1 do not preclude the use of
monitors in Zone B for those situations. However, note that for those
cases where the traffic is less than approximately 3,000 vehicles per
day, the monitor must be located greater than 5 meters from the edge of
the nearest traffic lane and 2 to 15 meters above ground level.
In the case of elevated roadways where the monitor must be placed
below the level of the roadway, the monitor should be located no closer
than approximately 25 meters from the edge of the nearest traffic lane.
This separation distance applies for those situations where the road is
elevated greater than 5 meters above the ground level, and applies to
all traffic volumes.
3.3.1.4 Other Considerations - Stations should not be located in an
unpaved area unless there is vegetative ground cover year round so that
the impact of reentrained or fugitive dusts will be kept to a minimum.
Additional information on TSP probe siting may be found in reference 10.
21
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ZONE C (UNACCEPTABLE)
ZONE A (ACCEPTABLE)
ZONE U (NOT RECOMMENDED)
10 20 25 30
DISTANCE FROM EDGE OF NEAREST TUAPriC LANE, molor»a
"APPLIES WHERE ADT >3 000
Figure 1. Acceptable zone for sitiny TSP monitors
-------
3.3.2 Total Suspended Particulates (TSP)
The siting criteria for TSP in this section is applicable for PSD
applications submitted later than 6 months after the promulgation of the
1985 PSD regulations.
3.3.2.1 Vertical Placement - Practical considerations such as prevention
of vandalism, security, accessibility, availability of electricity, etc.,
generally require that a TSP sampler be elevated rather than at ground
level. Therefore, a range of acceptable heights needs to be used.. In
addition, the type of source, i.e., elevated or ground level, predominantly
influencing the area of impact must be considered when locating the mon-
itor. Therefore, the sampler for measuring maximum impact from ground
level sources must be 2-7 meters above ground level unless it can be shown
that maximum concentrations exist at higher elevations. Samplers located
to monitor for elevated sources are allowed a wider range of heights for
locating the air inlet of the monitor. For TSP samplers, the acceptable
range for monitoring emissions from elevated sources is 2-15 meters.
3.3.2.2 Spacing from Obstructions - If the sampler is located on a roof
or other structure, then there must be a minimum of 2 meters separation
from walls, parapets, penthouses, etc. Furthermore, no furnace or incin-
eration flues should be nearby. The separation distance from flues is
dependent on the height of the flues, type of waste or fuel burned, and
quality of the fuel (ash content). For example, if the emissions from
the chimney are the result of natural gas combustion, no special precau-
tions are necessary except for the avoidance of obstructions, i.e., at
least 2 meters separation. On the other hand, if fuel oil, coal, or
solid waste is burned and the stack is sufficiently short so that the
plume could reasonably be expected to impact on the sampler intake a
significant part of the time, other buildings/locations in the area that
are free from these types of sources should be considered for sampling.
Trees provide surfaces for particulate deposition and also restrict
airflow. Therefore, the sampler should be placed at least 20 meters from
trees.
Obstacles such as buildings must also be avoided so that the distance
between obstacles and the sampler is at least twice the height that the
obstacle protrudes above the sampler. In addition, there must be unre-
stricted airflow in an arc of at least 270° around the sampler, and the
predominant direction for the season of greatest pollutant concentration
potential must be included in the 270° arc.
3.3.2.3 Spacing from Roads - A number of studies [16-23] support the
conclusion that particulate concentrations decrease with increasing height
of the monitor and distance from the road. Quite high concentrations
have been reported at monitors located at a low elevation close to heavily
traveled roads. Moreover, monitors located close to streets are within
the concentrated plume of particulate matter emitted and generated by
vehicle traffic, thus to determine the impact of TSP from motor vehicles,
it is desirable to locate the sampler near the roadway.
An analysis of various monitoring studies [24] shows that a linear
relationship between sampler height and distance from roadways defines a
zone where the plume generated by traffic greater than approximately
3,000 vehicles per day is diminished. To determine the combined impact
23
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of TSP from a proposed source and motor vehicles, it is desirable for the
TSP monitors to be located in the enhanced portion of the plume. For
those situations where the emissions from a proposed source would impact
close to a roadway, the air intake of the monitor must be located 5-15
meters from the edge of the nearest traffic lane. Also for these situa-
tions, the air intake must be 2-7 meters above ground level.
3.3.2.4 Other Considerations - Stations should not be located in an
unpaved area unless there is vegetative ground cover year round so that
the impact of reentrained or fugitive dusts will be kept to a minimum.
Additonal information on TSP probe siting may be found in reference 10.
3.3.3 Particulate Matter
3.3.3.1. Vertical Placement - Although there are limited studies on
the PMio concentration gradients around roadways or other ground level
sources, references 16, 17, 19, 25, and 26 show a distinct variation in
the distribution of TSP and Pb levels near roadways. TSP, which is greatly
affected by gravity, has large concentration gradients, both horizontal
and vertical, immediately adjacent to roads. Pb, being predominantly sub-
micron in size, behaves more like a gas and does not exhibit steep vertical
and horizontal gradients as does TSP. PM^o, being intermediate in size
between these two extremes exhibits dispersion properties of both gas and
settleable particulates and does show vertical and horizontal gradients
[27]. Similar to monitoring for other pollutants, optimal placement of the
sampler inlet for PMio monitoring should be at breathing height level. How-
ever, practical factors such as prevention of vandalism, security, and safety
precautions must also be considered when siting a PMio monitor. Given these
considerations, the sampler inlet for ground level source monitoring must be
2-7 meters above ground level. For PMio samplers, the acceptable range for
monitoring emissions from elevated sources is 2-15 meters above ground level.
3.3.3.2 Spacing from Obstructions - If the sampler is located on a roof
or other structure, then there must be a minimum of 2 meters separation
from walls, parapets, penthouses, etc. No furnace or incineration flues
should be nearby. This separation distance from flues is dependent on
the height of the flues, type of waste or fuel burned, and quality of the
fuel (ash content). In the case of emissions from a chimney resulting
from natural gas combustion, the sampler should be placed, as a precaution-
ary measure, at least 5 meters from the chimney.
On the other hand, if fuel oil, coal, or solid waste is burned and
the stack is sufficiently short so that the plume could reasonably be
expected to impact on the sampler intake a significant part of the time,
other buildings/locations in the area that are free from these types
of sources should be considered for sampling. Trees provide surfaces
for particulate deposition and also restrict airflow. Therefore, the
sampler should be placed at least 20 meters from trees.
The sampler must also be located away from obstacles such as buildings,
so that the distance between obstacles and the sampler is at least twice
the height that the obstacle protrudes above the sampler. There must
also be unrestricted airflow in an arc of at least 270° around the sampler,
and the predominant wind direction for the season of greatest pollutant
concentration potential must be included in the 270° arc.
24
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3.3.3.3 Spacing from Roads - For these situations where the emissions
from a proposed source would impact close to a roadway, the air intake
for the monitor must be located between 5-15 meters from the edge of the
nearest traffic lane. Monitors located in this area would thus measure
the combined impact from the proposed source and the roadway. The sampler
air intake must be 2-7 meters above ground level.
3.3.3.4 Other Considerations - Stations should not be located in an
unpaved area unless there is vegetative ground cover year round so that
the impact of reentrained or fugitive dusts will be kept to a minimum.
Additional information on PMio siting may be found in reference 28.
3.3.4 Sulfur Dioxide ($02)
3.3.4.1. Horizontal and Vertical Probe Placement - As with TSP monitoring,
the most desirable height for an S02 inlet probe is near the breathing
height. Various factors enumerated before may require that the inlet
probe be elevated, consideration must also be given to the type of source
predominantly influencing the impact area. For elevated sources, the inlet
probe must be located 3 to 15 meters above ground level. For ground
level sources, locate as close to the breathing zone as possible. If the
inlet probe is located on the side of the building, then it should be
located on the windward side of the building relative to the prevailing
winter wind direction. The inlet probe must also be located more than 1
meter vertically or horizontally away from any supporting structure and
also away from dirty, dusty areas.
3.3.4.2 Spacing from Obstructions - No furnace or incineration flues,
or other minor sources of S02 should be nearby. The separation distance
is dependent on the height of the flues, type of waste or fuel burned,
and the quality of the fuel (sulfur content). If the inlet probe is
located on a roof or other structure, it must be at least 1 meter from
walls, parapets, penthouses, etc.
The inlet probe should.be placed more than 20 meters from trees and
must be located away from obstacles and buildings. The distance between
the obstacles and the inlet probe must be at least twice the height that
the obstacle protrudes above the inlet probe. Airflow must also be unre-
stricted in an arc of at least 270° around the inlet probe, and the pre-
dominant direction for the season of greatest pollutant concentration
potential must be included in the 270° arc. If the probe is located on
the side of a building, 180° clearance is required. Additional information
on S02 probe siting criteria may be found in reference 11.
3.3.5 Carbon Monoxide (CO)
3.3.5.1 Horizontal and Vertical Probe Placement - Because of the importance
of measuring population exposure to CO concentrations, optimum CO sampling
should be done at average breathing heights. However, practical factors
require that the inlet probe be higher. In general, for CO emitted at
elevated heights, the inlet probe for CO monitoring should be 3-15 meters
above ground level. For those situations where the emissions from a pro-
posed source would impact a street canyon or corridor type area in an
urban area, and the area is predominantly influenced by the traffic from
the street canyon or traffic corridor, the inlet probe should be positioned
3 _+ 1/2 meters above ground level which coincides with the vertical probe
25
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placement criteria for a street canyon/corridor type site [8]. The
criteria is more stringent than the 3 to 15 meter range specified earlier
because CO concentration gradients resulting from motor vehicles traveling
along street canyon or corridors are rather steep and show wide variations
in CO levels at different heights. The 3 meter height is a compromise
between breathing height representation and such factors as the prevention
of obstructions to pedestrians, vandalism, etc.
In addition to the vertical probe criteria, the inlet probe must
also be located more than 1 meter in the vertical or horizontal direction
from any supporting structure.
3.3.5.2 Spacing from Obstructions - Airflow must also be unrestricted
in an arc of at least 270" around the inlet probe, and the predominant
direction for the season of greatest pollutant concentration potential
must be included in the 270° arc. If the probe is located on the side
of a building, 180° clearance is required.
3.3.5.3 Spacing from Roads - For those situations discussed above where
the emissions from a proposed source would impact a street canyon/corridor
type area, the inlet probe must be located at least 10 meters from an
intersection and preferably at a midblock location. The inlet probe must
also be placed 2-10 meters from the edge of the nearest traffic lane.
Additional information on CO probe siting may be found in reference 12.
3.3.6 Ozone (03)
3.3.6.1 Vertical and Horizontal Probe Placement - The inlet probe for
ozone monitors should be as close as possible to the breathing zone. The
complicating factors discussed previously, however, require that the probe
be elevated. The height of the inlet probe must be located 3 to 15 meters
above ground level. The probe must also be located more than 1 meter
vertically or horizontally away from any supporting structure.
3.3.6.2 Spacing from Obstructions - The probe must be located away from
obstacles and buildings such that the distance between the obstacles and
the inlet probe is at least twice the height that the obstacle protrudes
above the sampler. The probe should also be located at least 20 meters
from trees. Since the scavenging effect of trees is greater for ozone
than for some of the other pollutants, strong consideration should be
used in locating the inlet probe to avoid this effect. Airflow must be
unrestricted in an arc of at least 270° around the inlet probe, and the
predominant direction for the season of greatest pollutant concentration
potential must be included in the 270° arc. If the probe is located on
the side of a building, 180° clearance is required.
3.3.6.3 Spacing from Roads - It is important in the probe siting process
to minimize destructive interferences from sources of nitric oxide (NO)
since NO readily reacts with ozone. Regarding NO from motor vehicles,
Table 2 provides the required minimum separation distances between road-
ways and ozone monitoring stations. These distances were based on recal-
culations using the methodology in reference 13 and validated using more
recent ambient data collected near a major roadway. The minimum separa-
tion distance must also be maintained between an ozone station and other
similar volumes of automotive traffic, such as parking lots. Additional
information on ozone probe siting criteria may be found in reference 13.
26
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Table 2. MINIMUM SEPARATION DISTANCE BETWEEN OZONE MONITORS
AND ROADWAYS (EDGE OF NEAREST TRAFFIC LANE)
Roadway Average Daily Traffic,Minimum Separation Distance Between
Vehicles Per Day Roadways and Monitors, Meters
< 10,000
~ 15,000
20,000
40,000
70,000
>11 0,000
> 10*
"20
30
50
100
>250
^Distances should be interpolated based on traffic flow.
3.3.7 Nitrogen Dioxide (N02)
3.3.7.1 Vertical and Horizontal Probe Placement - As discussed for
previous pollutants, the acceptable ranges for a monitor/probe inlet for
monitoring N02 emissions in an area principally influenced by an elevated
source is 3-15 meters. For areas influenced primarily by a ground level
source, the height should be as close to 3 meters as possible. Regarding
the distance of the probe from the supporting structure, a vertical or
horizontal distance of 1 meter must be maintained.
3.3.7.2 Spacing from Obstructions - Buildings, trees, and other obstacles
can serve as scavengers of N02- Tn order to avoid this kind of interfer-
ence, the station must be located well away from such obstacles so that
the distance between obstacles and the inlet probe is at least twice the
height that the obstacle protrudes above the probe. Also, a probe inlet
along a vertical wall is undesirable because air moving along that wall
may be subject to possible removal mechanisms. Similarly, the inlet
probe should also be at least 20 meters from trees. There must be unre-
stricted airflow in an arc of at least 270° around the inlet probe, and
the predominant direction for the season of greatest pollutant concentra-
tion potential must be included in the 270° arc. If the probe is located
on the side of the building, 180° clearance is required. Additional
information on N0£ probe siting criteria may be found in reference 13.
3.3.8 Lead (Pb)
3.3.8.1 Vertical Placement - Breathing height is the most desirable
location for the vertical placement of the Pb monitor. However, practical
factors previously mentioned require that the monitor be elevated. In
elevating the sampler, consideration must be given to ground level emissions
(whether they be stationary or mobile sources) with steep vertical concen-
tration gradients. Placing the shelter too high could result in measured
values significantly lower than the level breathed by the general public.
Accordingly, the sampler for ground level source monitoring must be located
2 to 7 meters above ground level. In contrast, samplers to monitor for
elevated sources, as noted in previous discussion, are allowed a wider
range of heights for locating the sampler/inlet probe. For Pb samplers,
the acceptable range for monitoring emissions from elevated sources is
2-15 meters above ground level.
27
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3.3.8.2 Spacing from Obstructions - A minimum of 2 meters of separation
from walls, parapets, and penthouses is required for samplers located on
a roof or other structure. No furnace or incineration flues should be
nearby. The height of the flues and the type, quality, and quantity of
waste or fuel burned determine the separation distances from flues. For
example, if the emissions from the chimney have a high lead content and
there is a high probability that the plume would impact on the sampler
during most of the sampling period, then other buildings/locations in
the area that are free from the described sources should be chosen for
the monitoring site. The sampler should be placed at least 20 meters
from trees, since trees absorb particles as well as restrict airflow.
The sampler must be located away from obstacles such as buildings,
so that the distance between obstacles and the sampler is at least twice
the height that the obstacle protrudes above the sampler. There must
also be unrestricted airflow in an arc of at least 270° around the
sampler, and the predominant direction for the season of greatest pollution
concentration potential must be included in the 270° arc.
3.3.8.3 Spacing from Roads - For those situations discussed in Section
3.3.8.1 where the emissions from a proposed source would impact close to
a major roadway (greater than approximately 30,000 ADT), the air intake
for the monitor must be located within 15-30.meters from the edge of the
nearest traffic lane. Monitors located in this area would thus measure
the combined impact from the proposed source and the roadway. The sampler
air intake must be 2 to 7 meters above ground level.
3.3.8.4 Other Considerations - Stations should not be located in an
unpaved area unless there is vegetative ground cover year round so that
the impact of reentrained or fugitive dusts will be kept to a minimum.
Additional information on Pb siting criteria may be found in reference 14.
3.3.9 Noncriteria Pollutants
3.3.9.1 Vertical Placement - Similar to the discussion on criteria
pollutants, the most desirable height for monitors/inlet probes for
noncriteria pollutants is near the breathing zone. Again, practical
factors require that the monitor/ inlet probe be elevated. Furthermore,
consideration must be given to the type of source, i.e., elevated, ground
level, stationary, or mobile. As the case may be, for noncriteria parti-
culate pollutant monitors, the following monitor/inlet probe ranges are
acceptable: for impact areas predominantly influenced by elevated sources,
2-15 meters;.for ground level sources 2 to 7 meters. Regarding noncriteria
gaseous pollutants, acceptable heights are as follows: areas impacted
primarily by elevated sources, 3-15 meters; areas affected principally by
ground level sources, as close to 3 meters as possible.
3.3.9.2 Spacing from Obstructions - If the sampler/inlet probe is located
on a roof or other structure, then there must be a minimum of 2 meters
separation from walls, parapets, penthouses, etc. No furnace or inciner-
ation flues should be nearby. This separation distance from flues is
dependent on the height of the flues, type of waste or fuel burned, and
quality of the fuel. For example, if the emissions from the chimney
contain a high concentraton of the noncriteria pollutant that is being
measured and there is a high probability that the plume would impact the
28
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sampler/inlet probe during most of the sampling period, then other buildings/
locations in the area that are free from the described sources should be
chosen for the monitoring site. The sampler/inlet probe should also be
placed at least 20 meters from trees.
The sampler/inlet probe must be located away from obstacles and
buildings such that the distance between the obstacles and the sampler/
inlet probe is at least twice the height that the obstacle protrudes
above the sampler/inlet probe. Airflow must be unrestricted in an arc
of at least 270° around the sampler/inlet probe, and the predominant
direction for the season of greatest pollutant concentration potential
must be included in the 270° arc. If the inlet probe is located on the
side of a building, 180° clearance is required.
3.3.9.3 Other Considerations - Stations for measuring particulate non-
criteria pollutants should not be located in an unpaved area unless there
is vegetative ground cover year round so that the impact of reentrained
or fugitive dusts will be kept to a minimum.
3.4 Probe Material and Pollutant Sample Residence Time
For reactive gases, special probe material must be used. Studies
[29-33] have been conducted to determine the suitability of materials
such as polypropylene, polyethylene, polyvinylchloride, tygon, aluminum,
brass, stainless steel, copper, pyrex glass, and teflon for use as intake
sampling lines. Of the above materials, only pyrex glass and teflon have
been found to be acceptable for use as intake sampling lines for all the
reactive gaseous pollutants. Furthermore, EPA [34] has specified borosi-
1icate glass or FEP teflon as the only acceptable probe materials for
delivering test atmospheres in the determination of reference or equiva-
lent methods. Therefore, borosilicate glass, FEP teflon, or their
equivalent must be used for inlet probes.
No matter how unreactive the sampling probe material is initially,
after a period of use, reactive particulate matter is deposited on the
probe walls. Therefore, the time it takes the gas to transfer from the
probe inlet to the sampling device is also critical. Ozone in the pre-
sence of NO will show significant losses even in the most inert probe
material when the residence time exceeds 20 seconds [35]. Other studies
[36-37] indicate that a 10-second or less residence time is easily achiev-
able. Therefore, sampling probes for reactive gas monitors must have a
sampler residence time less than 20 seconds.
3.5 Summary of Probe Siting Requirements
Table 6 presents a summary of the requirements for probe siting criteria
with respect to distances and heights. These criteria are specified for
consistency between pollutants and to allow the use of a single manifold
for monitoring more than one pollutant at a site.
. 29
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TABLE 3. SUMMARY OF PROBE SITING CRITERIA
Height Above
Pollutant Ground, Meters3
Distance from Supporting
Structure, Meters
Vertical Horizontal
Other Spacing Criteria
TSP
2 - 15
>2
(old criteria
for Section 3.3.1)
1,
2.
3.
4,
5.
Should be >20 meters from trees.
Distance from sampler to obstacle, such as
buildings, must be at least twice the
height the obstacle protrudes above the
sampler.
Must have unrestricted airflow 270° arc
around the sampler.
No furnace or incineration flues should
be nearby.0
Must have minimum spacing from roads. This
varies with height of monitor (see Figure 1)
CO
o
TSP
2 - 7
>2
(new criteria for impact near
roadway and/or ground level sources)
1.
2.
3,
4.
5.
Should be >20 meters from trees.
Distance from sampler to obstacle, such as
buildings, must be at least twice the
height the obstacle protrudes above the
sampler.
Must have unrestricted airflow 270° arc
around the sampler.
No furnace or incineration flues should
be nearby.c
Must be 5-15 meters from roads.
TSP 2 - 15
(new criteri a)
>2
1.
2.
3.
4.
5.
Should be >20 meters from trees.
Distance from sampler to obstacle, such
buildings, must be at least twice the
height the obstacle protrudes above the
sampler.
Must have unrestricted airflow 270° arc
around the sampler.
No furnace or incineration flues should
be nearby.c
Must have minimum spacing from roads.
as
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TABLE 3. SUMMARY OF PROBE SITING CRITERIA
(continued)
Pollutant
Height Above
Ground, Meters3
Distance from Supporting
Structure, Meters
Vertical Horizontal15
Other Spacing Criteria
2 - 7
>2
t
(impact near
major roadway
and/or ground
level sources)
1.
2.
3.
4.
Should be >20 meters from trees.
Distance from sampler to obstacle, such
as buildings, must be at least twice
the height the obstacle protrudes above
the sampler.
Must have unrestricted airflow 270° arc
around the sampler.
No furnace or incineration flues which
emit particulate matter should be
nearby.0
Must be 5-15 meters from roads.
2-15
>2
1.
2.
3.
4.
Should be >20 meters from trees.
Distance from sampler to obstacle, such
as buildings, must be at least twice the
height the obstacle protrudes above the
sampler.
Must have unrestricted airflow 270° arc
around the sampler.
No furnace or incineration flues which
emit particulate matter should be
nearby.0
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TABLE 3. SUMMARY OF PROBE SITING CRITERIA
(continued)
Distance from Supporting
Structure, Meters
Height Above
Pollutant Ground, Meters3 Vertical Horizontal''
S02 3-15 >1 >1 1.
2.
Other Spacing Criteria
Should be >20 meters
Distance from inlet c
from trees .
>robe to obstacle,
such
as buildings, must be at least twice the
height the obstacle protrudes above the
inlet probe.
3. Must have unrestricted airflow 270° arc
around the inlet probe, or 180° if probe is
on the side of a building.
4. No furnace or incineration flues should be
nearby.0
CO
ro
CO
(street canyon)
3 + 1/2
>1
1.
2.
3.
Must be >10 meters from intersection and
should be at a midblock location.
Must be 2-10 meters from edge of nearest
traffic lane.
Must have unrestricted airflow 180° around
the inlet probe.
CO
(non-street
canyon/corridor)
3-15
>1
Must have unrestricted airflow 270° around
the inlet probe, or 180° if probe is on the
side of a building.
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TABLE 3. SUMMARY OF PROBE SITING CRITERIA
(continued)
Height Above
Pollutant Ground, Meters8
Distance from Supporting
Structure, Meters
Vertical
Horizontal^
Other Spacing Criteria
3 - 15
>1
>1
1. Should be >20 meters from trees.
2. Distance from inlet probe to obstacle, such
as buildings, must be at least twice the
height the obstacle protrudes above the
inlet probe.
3. Must have unrestricted airflow 270° arc
around the inlet probe, or 180° if probe
is on the side of a building.
4. Spacing from roads varies with traffic
(see Table 2).
OJ
OJ
N02
3-15
>1
1. Should be >20 meters from trees.
2. Distance from inlet probe to obstacle, such
as buildings, must be at least twice the
height the obstacle protrudes above the
inlet probe.
3. Must have unrestricted airflow 270° arc
around the inlet probe, or 180° if probe
is on the side of a building.
Pb
(impact near
major roadway
and/or ground
level sources)
2 - 7
>2
1.
2.
3.
4.
5.
Should be >20 meters from trees.
Distance from sampler to obstacle, such as
buildings, must be at least twice the height
obstacle protrudes above the sampler.
Must have unrestricted airflow 270° arc
around the sampler.
No furnace or incineration flues which emit
lead should be nearby.0
Must be 15-30 meters from major roadways.
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TABLE 3. SUMMARY OF PROBE SITING CRITERIA
(continued)
Pollutant
Height Above
Ground, Meters3
Distance from Supporting
Structure, Meters
Vertical
Horizontal0
Other Spacing Criteria
Pb
2-15
>2
1.
2.
3.
4.
Should be >20 meters from trees.
Distance from sampler to obstacle,
such as buildings, must be at least
twice the height the obstacle protrudes
above the sampler.
Must have unrestricted airflow 270° arc
around the sampler.
No furnace or incineration flues which
emit lead should be nearby.0
Particulate
Noncriteria
Pollutants
2 - 7 for
ground 1evel
sources;
2 - 15 for
elevated sources
>2
1. Should be >20 meters from trees.
2. Distance from sampler to obstacle, such
as buildings, must be at least twice
the height the obstacle protrudes
above the sampler.
3. Must have unrestricted airflow 270° arc
around the sampler.
4. No furnace or incineration flues which
emit the noncriteria pollutant should
be nearby.0
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TABLE 3. SUMMARY OF PROBE SITING CRITERIA
(continued)
Pollutant
Height Above
Ground, Meters3
Distance from Supporting
Structure, Meters
Vertical Horizontal5
Other Spacing Criteria
OJ
en
Gaseous
Noncriteria
Pollutants
3-15
1. Should be >20 meters from trees.
2. Distance from inlet probe to obstacle,
such as buildings, must be at least
twice the height obstacle protrudes
above the inlet probe.
3. Must have unrestricted airflow 270° arc
around the inlet probe, or 180° if the
probe is on the side of a building.
4. No furnace or incineration flues which
emit the noncriteria pollutant should
be nearby.5
aFor ground level sources, monitors/inlet probes should be placed as close to the breathing zone as possible.
probe is located on rooftop, this separation distance is in reference to walls, parapets, or penthouses
located on the roof.
C0i stance is dependent on height of furnace or incineration flue, type of fuel or waste burned, and
quality of fuel. This is to avoid undue influences from minor pollutant sources.
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4. QUALITY ASSURANCE FOR AIR QUALITY DATA
On May 10, 1979, EPA promulgated quality assurance requirements for
PSD monitoring for $03, NOJ?, 03, CO, and TSP. These quality assurance
requirements are Appendix B of 40 CFR 58 (reference 8). Section 4.1
describes minimum quality assurance requirements (promulgated and planned)
for PSD monitoring for all criteria air pollutants (S02, N02, 03, CO,
TSP, Pb and PM^Q). Monitoring organizations are required to meet
quality assurance requirements of Appendix B at the time the station is
put into operation.
Currently, quality assurance for PSD monitoring for noncriteria air
pollutants are EPA recommendations only. EPA promulgated requirements are
not available for noncriteria air pollutants. Section 4.2 describes
minimum quality assurance recommendations for noncriteria air pollutants.
4.1 Quality Assurance for Criteria Air Pollutants
4.1.1 General Information
The following specifies the minimum quality assurance requirements of
an organization operating a network of PSD stations. These requirements
are regarded as the minimum necessary for the control and assessment of the
quality of the PSD ambient air monitoring data submitted to EPA. Organiza-
tions are encouraged to develop and implement quality assurance programs
more extensive than the minimum required or to continue such programs
where they already exist.
Quality assurance consists of two distinct and equally important
functions. One function is the assessment of the quality of the monitoring
data by estimating their precision and accuracy. The other function is the
control, and improvement, of the quality of the monitoring data by implemen-
tation of quality control policies, procedures, and corrective actions.
These two functions form a control loop; when the assessment function
indicates that the data quality is inadequate, the control effort must
be increased until the data quality is acceptable.
In order to provide uniformity in the assessment and reporting of data
quality, the assessment procedures are specified explicitly in Sections
4.1.3, 4.1.4, 4.1.5 and 4.1.6.
In contrast, the control and corrective action function encompasses a
variety of policies, procedures, specifications, standards, and corrective
measures which have varying effects on the resulting data, quality. The
selection and degree of specific control measures and corrective actions
used depend on a number of factors such as the monitoring methods and
equipment used, field and laboratory conditions, the objectives of the
monitoring, the level of data quality needed, the expertise of personnel,
36
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the cost of control procedures, pollutant concentration levels, etc.
Accordingly, quality control requirements are specified in general
terms, in Section 4.1.2 to allow each organization to develop a quality
control system which is most effective for its own circumstances.
For purposes here, "organization" is defined as a source owner/operator,
a government agency, or their contractor which operates an ambient air
pollution monitoring network for PSD purposes.
4.1.2 Quality Control Requirements
4.1.2.1 Organizational Requirements - Each organization must develop
and implement a quality control program consisting of policies, procedures,
specifications, standards and documentation necessary to:
(a) meet the monitoring objectives and quality assurance requirements
of the permit granting authority
(b) minimize loss of air quality data due to malfunctions or out-
of-control conditions,
The quality control program must be described in detail, suitably
documented, and approved by the permit granting authority.
4.1.2.2 Primary Guidance - Primary guidance for developing the quality
control program is contained in references 38 and 39, which also contain
many suggested procedures, checks, and control specifications. Section
2.0.9 of reference 39 describes the specific guidance for the development
of a quality control program for PSD automated analyzers and manual
methods. Many specific quality control checks and specifications for
manual methods are included in the respective reference methods described
in 40 CFR 50, or in the respective equivalent method descriptions available
from EPA (see Section 2.6). Similarly, quality control procedures related
to specifically designated reference and equivalent analyzers are contained
in their respective operation and instruction manuals. This guidance,
and any other pertinent information from appropriate sources, should be
used by organizations in developing their quality control programs.
As a minimum each quality control program must have operational
procedures for each of the following activities:
(a) selection of methods, analyzers, or samplers,
(b) installation of equipment,
(c) calibration,
(d) zero and span checks and adjustments of automated analyzers,
(e) control checks and their frequency,
(f) control limits for zero, span and other control checks, and
respective corrective actions when such limits are surpassed,
(g) calibration and zero/span checks for multiple range analyzers
(h) preventive and remedial maintenance
(i) recording and validating data
(j) documentation of quality control information.
37
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As previously mentioned, specific guidance for each activity listed
above that must be a part of an organization's quality control program
is described in Section 2.0.9 of reference 39.
4.1.2.3 Pollutant Standards - Gaseous standards (permeation tubes,
permeation devices or cylinders of compressed gas) used to obtain test
concentrations for CO, S02, and N02 must be working standards certified
by comparison to a National Bureau of Standards (NBS) gaseous Standard
Reference Material (SRM). A traceability protocol for certifying a
working standard by direct comparison to an NBS SRM is given in reference
40. Direct use of an NBS SRM as a working standard is not prohibited
but is discouraged because of the limited supply and expense of NBS
SRM's. When available, gas manufacturers' cylinder gases Certified
Reference Materials "CRM" may be substituted for NBS SRM cylinder gases
in establishing traceability.
Test concentrations for ozone must be obtained in accordance with
the UV photometric calibration procedure specified in Appendix D of
40 CFR 50, or by means of an ozone transfer standard which has been
certified. Consult reference 41 for guidance on ozone transfer standards.
Flow measurements must be made by a flow measuring instrument which
is traceable to an authoritative volume or other standard.
4.1 .2.4 Performance and System Audit Programs - The organization operating
a PSD monitoring network must participate in EPA's national performance
audit program. The permit granting authority, or EPA, may conduct system
audits of the ambient air monitoring programs of organizations operating
PSD networks. See Section 1.4.16 of reference 38 and Sections 2.0.11 and
2.0.12 of reference 39 for additional information about these programs.
Organizations should contact either the appropriate EPA Regional Quality
Control Coordinator or the Quality Assurance Division, EMSL/RTP, at the
address given in reference 40 for instructions for participation.
4.1 .3 Data Quality Assessment Requirements
4.1.3.1 Precision of Automated Methods - A one-point precision check must
be carried out at least once every two weeks on each automated analyzer
used to measure SOg, N02, 03, and CO. The precision check is made by
challenging the analyzer with a precision check gas of known concentration
between 0.008 and 0.10 ppm for S02, N02, and 03 analyzers, and between 8
and 10 ppm for CO analyzers. The standards from which precision check test
concentrations are obtained must meet the specifications of section 4.1.2.3.
Except for certain CO analyzers described below, analyzers must operate in
their normal sampling mode during the precision check, and the test atmosphere
must pass through all filters, scrubbers, conditioners, and other components
used during normal ambient sampling and as much of the ambient air inlet
system as is practicable. If permitted by the associated operation or
instruction manual, a CO analyzer may be temporarily modified during the
precision check to reduce vent or purge flows, or the test atmosphere
may enter the analyzer at a point other than the normal sample inlet,
provided that the analyzer's response is not likely to be altered by
these deviations from the normal operational mode.
38
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If a precision check is made in conjunction with zero/span adjustment,
it must be made prior to such zero and span adjustments. The difference
between the actual concentration of the precision check gas and the
.concentration indicated by the analyzer is used to assess the precision
of the monitoring data as described in Section 4.1.4.1. Report data
only from automated analyzers that are approved for use in the PSD network.
4.1 .3.2 Accuracy of Automated Methods - Each sampling quarter audit each
analyzer that monitors for S02, N02, 03, or CO at least once. The audit
is made by challenging the analyzer with at least one audit gas of known
concentration from each of the following ranges which fall within the
measurement range of the analyzer being audited:
Concentration Range, ppm
Audit Point
1
2
3
4
S02, N02, 03
0.03 to 0.08
0.15 to 0.20
0.40 to 0.45
0.80 to 0.90
CO
3 to 8
15 to 20
40 to 45
80 to 90
The standards from which audit gas test concentrations are obtained must
meet the specifications of Section 4.1.2.3. Working and transfer standards
and equipment used for auditing must be different from the standards and
equipment used for calibration and spanning. The auditing standards and
calibration standards may be referenced to the same MBS SRM or primary UV
photometer. The auditor must not be the operator/analyst who conducts the
routine monitoring, calibration, and analysis.
The audit shall be carried out by allowing the analyzer to analyze an
audit test atmosphere in the same manner as described for precision checks
in Section 4.1.3.1. The exception given in Section 4.1.3.1 for certain CO
analyzers does not apply for audits.
The difference between the actual concentration of the audit test gas
and the concentration indicated by the analyzer is used to assess the
accuracy of the monitoring data as described in Section 4.1.4.2. Report
data only from automated analyzers that are approved for use in the PSD
network.
4.1.3.3 Precision of Manual Methods - (a) JSP and PMip Methods. For a given
organization1 s monitoring network, one sampling site must have collocated
samplers. A site with the highest expected 24-hour pollutant concentration
must be selected. The two samplers must be within 4 meters of each other
but at least 2 meters apart to preclude airflow interference. Calibration,
sampling, and analysis must be the same for both collocated samplers as well
as for all other samplers in the network. The collocated samplers must be
operated as a minimum every third day when continuous sampling is used.
When a less frequent sample schedule is used, the collocated samplers must
39
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be operated at least once each week. For each pair of collocated samplers,
designate one sampler as the sampler which will be used to report air quality
for the site and designate the other as the duplicate sampler. The differences
in measured concentration (pg/ir?) between the two collocated samplers are
used to calculate precision as described in Section 4.1.5.1.
(b) Pb Methods. The operation of collocated samplers at one sampling
site must be used to assess the precision of the reference or an equivalent
lead method. The procedure to be followed for lead methods is the same as
described in 4.1.3.3(a) for the TSP and PM methods.
4.1.3.4 Accuracy of Manual Methods - (a) TSP and PMjp Methods. Each sampling
quarter audit the flow rate of each sampler at least once.
Audit the flow at the normal flow rate, using a certified flow transfer
standard (see reference 39). The flow transfer standard used for the
audit must not be the same one used to calibrate the flow of the sampler
being audited, although both transfer standards may be referenced to the
same primary flow or volume standard. The difference between the audit
flow measurement and the flow indicated by the sampler's flow indicator
is used to calculate accuracy, as described in Section 4.1.5.2
Great care must be used in auditing high-volume samplers having
flow regulators because the introduction of resistance plates in the
audit device can cause abnormal flow patterns at the point of flow
sensing. For this reason, the orifice of the flow audit device should
be used with a normal glass fiber filter in place and without resistance
plates in auditing flow regulated high- volume samplers, or other steps
should be taken to assure that flow patterns are not perturbed at the
point of flow sensing.
(b) Pb Methods. For the reference method (Appendix G of 40 CFR 50)
each sampling quarter audit the flow rate of each high-volume lead sampler
at least once. Audit the flow rate at one flow rate using a reference flow
device described in Section 2.2.8 of reference 39, or a similar flow
transfer standard. The device used for auditing must be different from
the one used to calibrate the flow of the high-volume sampler being audited.
The auditing device and the calibration device may both be referenced to
the same primary flow standard. With the audit device in place, operate
the high-volume sampler at its normal flow rate. The difference in flow
rate (in m^/min) between the audit flow measurement and the flow indicated
by the sampler's normal flow indicator are used to calculate accuracy as
described in Section 4.1.5.3.
Great care must be used in auditing high-volume sampler having flow
regulators because the introduction of resistance plates in the audit
device can cause abnormal flow patterns at the point of flow sensing.
For this reason, the orifice of the flow audit device should be used
with a normal glass fiber filter in place without resistance plates to
audit flow regulated high-volume samplers, or other steps should be
taken to assure that flow patterns are not perturbed at the point of
flow sensing.
Each sampling quarter, audit the lead analysis using glass fiber
filter strips containing a known quantity of lead. Audit samples are
prepared by depositing a lead solution on 1.9 cm by 20.3 cm (3/4 inch
by 8 inch) unexposed glass fiber filter strips and allowing to dry
40
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thoroughly. The audit samples must be prepared using reagents different
from those used to calibrate the lead analytical equipment being audited.
Prepare audit samples in the following concentration ranges:
Equivalent Ambient
Cone, yg Pb/strip Cone. yg Pb/m3*
100 to 300 0.5 to 1.5
600 to 1000 3.0 to 5.0
*Equivalent ambient lead concentration in yg/rn is based on sampling
at 1.7 mVmin for 24 hours on 20.3 cm x 25.4 (8 inch x 10 inch) glass
fiber filter.
Audit samples must be extracted using the same extraction procedure
used for exposed filters.
Analyze at least one audit sample in each of the two ranges each
day that samples are analyzed. The difference between the audit concentration
(in yg Pb/strip) and the analyst's measured concentration (in yg Pb/strip)
are used to calculate analysis accuracy as described in Section 4.1.5.4.
The accuracy of an equivalent method is assessed in the same manner
as the reference method. The flow auditing device and lead analysis
audit samples must be compatible with the specific requirements of the
equivalent method.
4.1 .4 Calculations for Automated Methods
4.1.4.1 Single Analyzer Precision - Each organization, at the end of each
sampling quarter, shall calculate and report a precision probability interval
for each analyzer. Directions for calculations are given below and directions
for reporting are given in Section 4.1.6. If monitoring data are invalidated
during the period represented by a given precision check, the results of
that precision check shall be excluded from the calculations. Calculate
the percentage difference (d-j) for each precision check using equation 1.
Yi - XT ' (1 )
d,- = - x 100
XT
where: Yj = analyzer's indicated concentration from the i-th precision
check,
Xj = known concentration of the test gas used for the i-th precision
check.
41
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For each instrument, calculate the quarterly average (3j), equation 2, and
the standard deviation (Sj), equation 3.
1 n (2)
dj = rf , , di
9
<
(3)
Where n is the number of precision checks on the instrument made during
the sampling quarter. For example, n should be 6 or 7 if span checks are
made bi-weekly during a quarter.
Calculate the 95 percent probability limits for precision using
equations 4 and 5.
Upper 95 Percent Probability Limit = dj + 1.96 Sj (4)
Lower 95 Percent Probability Limit = dj - 1.96 Sj (5)
4.1.4.2 Single Analyzer Accuracy - Each organization, at the end of each
sampling quarter, shall calculate and report the percentage difference for
each audit concentration for each analyzer audited during the quarter.
Directions for calculations are given below (directions for reporting
are given in Section 4.1.6).
Calculate and report the percentage difference (d^) for each audit
concentration using equation 1 where Y-j is the analyzer's indicated
concentration from the i-th audit check and X?- is the known concentration
of the audit gas used for the i-th audit check.
4.1 .5 Calculations for Manual Methods
4.1.5.1 Single Instrument Precision for JSP, Pb, and PMjp. Estimates of
precision for ambient air quality particulate measurements are calculated
from results obtained from collocated samplers as described in section
4.1.2.3. At the end of each sampling quarter, calculate and report a
precision probability interval, using weekly results from the collocated
samplers. Directions for calculations are given below, and directions
for reporting are given in Section 4.1.6.
For the paired measurements obtained as described in sections 4.1.2.3(a)
and 4.1.2.3(b), select all pairs in which both measurements are above 20
yg/m3 for TSP, 0.25 yg/m3 for Pb, or 20 yg/m3 for PM1Q. For each selected
pair, calculate the percent difference (d-j) using equation 1, where Y^ is the
concentration of pollutant measured by the duplicate sampler, and X-j is
the concentration measured by the sampler reporting air quality for the
site. Calculate the quarterly average percent difference (dj), equation
2, standard deviation (Sj), equation 3, and upper and lower 95 percent
probability 1 imts for precision (equations 6 and 7).
42
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Upper 95 Percent Probability Limit = dj + 1.96 Sj/ fT~ (6)
Lower 95 Percent Probability Limit = dj - 1.96 Sj/ i~T~ (7)
4.1.5.2 Single Instrument Accuracy for JSP and PMjp - Each organization,
at the end of each sampling quarter, shall calculate and report the
percentage difference for each high-volume or PM^g sampler audited
during the quarter. Directions for calculation are given below and
directions for reporting are given in Section 4.1.6.
For the flow rate audit described in Section 4.1.3.4, let Xi
represent the known flow rate and Y-j represent the indicated flow rate.
Calculate the percentage difference (d-j) using equation 1.
4.1.5.3 Single Instrument Sampling Accuracy for Pb - Each organization,
at the end of each sampling quarter, shall calculate and report the
percentage difference for each high-volume lead sampler audited during
the quarter. Directions for calculation are given in Section 4.1.5.2 and
directions for reporting are given in Section 4.1.6.
4.1.5.4 Single-Analysis-Day Accuracy for Pb - Each organization, at the
end of each sampling quarter, shall calculate and report the percentage
difference for each Pb analysis audit during the quarter. Directions
for calculations are given below and directions for reporting are given
in Section 4.1.6.
For each analysis audit for Pb described in Section 4.1.3.4(b), let
X-j represent the known value of the audit sample and Yj the indicated
value of Pb. Calculate the percentage difference (d-j) for each audit at
each concentration level using equation 1.
4.1.6 Organization Reporting Requirements
At the end of each sampling quarter, the organization must report
the following data assessment information: (a) for automated analyzers -
precision probability limits from Section 4.1.4.1 and percentage differences
from Section 4.1.4.2, and (b) for manual methods - precision probability
limits from Section 4.1.5.1 and percentage differences from Sections
4.1.5.2, 4.1.5.3 and 4.1.5.4. The precision and accuracy information
for the entire sampling quarter must be submitted with the air monitoring
data. All data used to calculate reported estimates of precision and
accuracy including span checks, collocated sampler and audit results
must be made available to the permit granting authority upon request.
4.2 Quality Assurance for Noncriteria Air Pollutants
At the present time, there are no EPA regulations on quality assurance
for PSD monitoring of noncriteria air pollutants. The following are EPA
recommendations for a minimum quality assurance program for noncriteria
pollutants.
4.2.1 Selection of Method
Selection of the measurement method for noncriteria air pollutants
is extremely important. A list of acceptable measurement methods for
noncriteria air pollutants is available and may be obtained by writing:
43
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U.S. Environmental Protection Agency, Environmental Monitoring Systems
Laboratory, Quality Assurance Division (MD-77), Research Triangle Park,
North Carolina 27711. This list of acceptable methods will be revised
at least annually and be available from the above address. Measurement
methods considered candidates for the noncriteria pollutant list should
be brought to the attention of EPA at the address given above.
4.2.2 Calibration
Calibration procedures described in the acceptable methods should
be followed and a schedule for calibrations should be established. In
addition, flow measurement devices used to measure sampling rate should
be calibrated and a schedule established for recalibration. Calibration
procedures for several flow measurement devices (rotameter, critical
orifice, mass flow meter, and wet test meter) are described in Section
2.1.2 of reference 39. All calibration procedures should be written and
maintained up-to-date by a document control system. A description of one
document control system that has been found to be effective is discussed
in Section 1.4.1 of reference 38.
4.2.3 Data Validation
Measurement data of poor quality may be worse than no data at all.
Therefore, the monitoring organization should establish data validation
procedures and implement these procedures to invalidate data of question-
able quality. Examples of data validation procedures for criteria pollu-
tants described in Section 2.0.9 of reference 39 may be useful as a guide
in establishing data validation procedures for noncriteria pollutants.
4.2.4 Standard and Split Samples
Where possible, standard samples containing the pollutant of
interest should be analyzed periodically during the analysis of collected
samples. This practice is useful in helping to determine if the analytical
system is in control. Splitting samples with another laboratory is quite
useful in determining if there are unidentified biases in the analytical
system.
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5. METEOROLOGICAL MONITORING
5.1 Data Required
The preconstruction review of proposed major emitting facilities
will require the use of meteorological data. It is essential that
such data be representative of atmospheric dispersion conditions at
the source and at locations where the source may have a significant
impact on air quality. The representativeness of the data is dependent
upon (a) the proximity of the meteorological monitoring site to the
area under consideration, (b) the complexity of the topography of
the area, (c) the exposure of the meteorological sensors, and (d) the
period of time during which the data are collected. More guidance
for determining representativeness is presented in reference 42.
A data base representative of the site should consist of at
least the following data:
a. hourly average wind speed and direction
b. hourly average atmospheric stability based on Pasquill stability
category or wind fluctuations (aQ), or vertical temperature
gradient combined with wind speed
c. hourly surface temperature at standard height for climatological
comparisons and plume rise calculations
d. hourly precipitation amounts for climatological comparisons.
In addition, hourly average mixing heights may be necessary for the
air quality impact analysis. In most cases, this may be limited to an
extrapolation of twice-daily radiosonde measurements routinely collected
by the National Weather Service (NWS). Sections 5.2 and 6.1 contain
specific information on instrument exposure and specifications.
Requirements for additional instrumentation and data will depend
upon the availability of information needed to assess the effects of
pollutant emissions on ambient air quality, soils, vegetation, and
visibility in the vicinity of the proposed source. The type, quantity,
and format of the required meteorological data will also be influenced
by the input requirements of the dispersion modeling techniques used in
the air quality analysis. Any application of dispersion modeling must
be consistent with the EPA "Guideline on Air Quality Models" [15]. The
guideline makes specific recommendations concerning air quality models
and data bases. It also specifies those situations for which models,
data, and techniques other than those recommended therein, may be applied.
Site-specific data are always preferable to data collected off-site.
The availability of site-specific meteorological data permits relatively
detailed meteorological analyses and subsequent improvement of dispersion
model estimates. An important source of background information pertaining
to on-site meteorological instrumentation is contained in an EPA workshop
report [43]. Off-site meteorological data may be used in lieu of site-
specific data only if it is agreed by source owner and permit granting
45
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authority that the off-site data are reasonably representative of atmospheric
conditions in the area under consideration. The off-site meteorological
data can sometimes be derived from routine measurements by NWS stations.
The data are available as individual observations and in summarized form
from the National Climatic Data Center, Federal Building, Asheville, NC
28801. On the other hand, if the nearest source of off-site data is con-
siderably removed from the area under consideration, and especially if
there are significant terrain features, urban areas, or large bodies of
water nearby, it may be necessary that the required meteorological data
be site-specific.
In some cases, it will be necessary that data be collected at more
than one site in order to provide a reasonable representation of atmospheric
conditions over the entire area of concern. Atmospheric conditions may
vary considerably over the area. In some cases, (e.g., complex terrain)
it will not be feasible to adequately monitor the entire meteorological
field of concern. Then the only recourse is to site the stations in
areas where characteristic and significant airflow patterns are likely to
be encountered. In any event, one of the meteorological stations should
be located so that it represents atmospheric conditions in the immediate
vicinity of the source.
Although at least 1 year of meteorological data should be available,
a shorter period of record that conforms to the air quality monitoring
period of record discussed in Section 2.5 is acceptable when approved
by the permit granting authority. If more than 1 year of data is avail-
able, it is recommended that such data be included in the analysis. Such
a multiyear data base allows for more comprehensive consideration of
variations in meteorological conditions that occur from year to year. .A
5-year period of record will usually yield an adequate meteorological
data base for considering such year-to-year variations.
In all cases, the meteorological data used must be of at least
the quality of data collected by the National Weather Service. Desired
features of instrumentation for collecting meteorological data are
discussed in Section 6.1.
5.2 Exposure of Meteorological Instruments
Measurements of most meteorological parameters are affected by the
exposure of the sensor. Jo obtain comparable observations at different
sites, the exposures must be similar. Also, the exposure should be such
that the measured parameters provide a good representation of pollutant
transport and dispersion within the area that the monitoring site is
supposed to represent. For example, if wind flow data over a fairly
broad area are desired, the wind sensors should be away from the immediate
influence of trees, buildings, steep slopes, ridges, cliffs, or hollows.
The standard exposure of wind instruments over level open terrain
is 10 meters above the ground. Open terrain is defined as an area where
the distance between the anemometer and any obstruction to the wind flow
is at least five times the height of the obstruction. Where a standard
exposure is unobtainable at this height, the anemometer should be installed
at such a height that its indications are reasonably unaffected by local
obstructions and represent as closely as possible what the wind at 10
46
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on assessing adverse aerodynamic effects due to local obstructions is
contained in reference 44. In locating wind sensors in rough terrain or
valley situations, it will be necessary to determine if local effects
such as channeling, slope and valley winds, etc., are important, or
whether the flow outside those zones of influence is to be measured. If
the analysis concerns emissions from a tall stack, it may be desirable
to avoid the local influences. On the other hand, if pollution from
low-level sources is the main concern, the local influences may be
important.
If the source emission point is substantially above the standard
10-meter level for wind measurements, additional wind measurements at
the height of the emission point and at plume height are desirable.
Such measurements are used to determine the wind regime in which the
effluent plume is transported away from the source. (The wind speed and
direction 50 to 100 meters or more above the surface are often considerably
different than at the 10-meter level.) An instrumented tower is the most
common means of obtaining meteorological measurements at several elevations
in the lower part of the atmospheric boundary layer. For wind instruments
mounted on the side of a tower, precautions must be taken to ensure that
the wind measurements are not unduly influenced by the tower. Turbulence
in the immediate wake of a tower (even a latticetype tower) can be severe.
Thus, depending on the supporting structure, wind measuring equipment
should be mounted (e.g., on booms) at least two structure widths away
from the structure, and two systems mounted on opposite sides of the
structure will sometimes be necessary. A wind instrument mounted on top
of a tower should be mounted at least one tower width above the top. If
there is no alternative to mounting instruments on a stack, the increased
turbulence problem [45], must be explicitly resolved to the satisfaction
of the permit granting authority.
Atmospheric stability is another key factor in pollutant dispersion
downwind of a source. The stability category is a function of static
stability (related to temperature change with height), convective turbulence
(caused by heating of the air at ground level), and mechanical turbulence
(a function of wind speed and surface roughness). A procedure for estima-
ting stability category is given by Turner [46] which requires information
on solar elevation angle, cloud cover, ceiling height, and wind speed.
The hourly observations at NWS stations include cloud cover, ceiling
height, and wind speed. Alternative procedures for estimating stability
category may be applied if representative data are available. For example,
stability category estimates may be based upon horizontal wind direction
fluctuations [47], or vertical gradients of temperature and wind speed
[48]. To obtain a representative reading of the air temperature, the
temperature sensor should be protected from thermal radiation from the
sun, sky, earth, and any surrounding objects, and must be adequately ven-
tilated. Aspirated radiation shields are designed to provide such protec-
tion. (Note that ambient temperature data are also commonly required
for plume rise estimates used in dispersion model calculations.)
Mixing height is another parameter that can be important in some
cases. Mixing height is the distance above the ground to which relatively
free vertical mixing occurs in the atmosphere. For estimating long-term
average concentrations, it is adequate to use a representative annual
47
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average mixing height [49]. However, in many cases, and especially for
estimates of short-term concentrations, twice-daily or hourly mixing
height data are necessary. Such data can sometimes be derived [49] from
representative surface temperatures and twice-daily upper air soundings
collected by selected NWS stations.
Precipitation collectors must be located so that obstructions do
not prevent the precipitation from falling into the collector opening or
force precipitation into the opening. Several collectors may be required
for adequate spatial resolution in complex topographic regimes.
Final rule making entitled "Visibility Protection for Federal Class
I Areas," was published in the Federal Register on December 2, 1980. The
regulations are applicable to 36 States 1 isted in the action. Although
these States are not required to establish visibility monitoring networks,
they should consult with the Federal Land Managers to determine monitoring
needs. Paragraph 51.305 states that the SIP strategies "must take into
account current and anticipated visibility monitoring research, the avail-
ability of appropriate monitoring techniques and such guidance as is pro-
vided by the Agency." Visibility definitions, monitoring methods, modeling
considerations and impact assessment approaches are among the subjects of
three EPA reports: (1) "Protecting Visibility: An EPA Report to Congress"
[50], (2) "Interim Guidance for Visibility Monitoring" [51], and (3)
"Workbook for Estimating Visibil ity Impairment" [52]. Also, since publi-
cation of the final rule, the National Park Service has established a
visibil ity monitoring system. The States or permit granting authority
should consider these resources when handling visibility new source
review questions.
Additional information and guidance on siting and exposure of
meteorological instruments is contained in reference 53.
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6. METEOROLOGICAL INSTRUMENTATION
6.1 Specifications
Meteorological instrumentation used for PSD monitoring must yield
reasonably accurate and precise data. Accuracies and allowable errors
are expressed in this section as absolute values for digital systems;
errors in analog systems may be 50 percent greater. For example, an
allowable error expressed as 5 percent means the recorded value should
be within +5 percent of the true value for digital systems, and +7.5
percent for analog systems. Records should be dated, and should be
accurate to within 10 minutes. Wind speed and direction (or vector
components) should be recorded continuously on strip recorders at
intervals not to exceed 60 seconds for a given variable; digital
recorders may be used as backup. These specifications apply to the
meteorological instruments used to gather the site specific data that
will accompany a PSD permit application. When the use of existing
representative meteorological data is approved by the permit granting
authority, the instrumentation should meet, as a minimum, NWS standards
[54-55].
6.1.1 Wind Systems (horizontal wind)
Wind direction and wind speed systems should exhibit a starting
threshold of less than 0.5 meter per second (m/s) wind speed (at 10
degrees deflection for direction vanes). Wind speed systems should be
accurate above the starting threshold to within 0.25 m/s at speeds equal
to or less than 5 m/s. At higher speeds, the error should not exceed 5
percent of the observed speed (maximum error not to exceed 2.5 m/s). The
damping ratio of the wind vane should be between 0.4 and 0.65 and the
distance constant should not exceed 5 m. Wind direction system errors
should not exceed 5 degrees, including sensor orientation errors. Wind
vane orientation procedures should be documented.
6.1.2 Wind Systems (vertical wind)
In complex terrain, downwash of plumes due to significant terrain
relief may pose a problem. If such .a problem potentially exists, it may
be necessary to measure the vertical component of the wind at the proposed
site, and as close as possible to stack height. The starting threshold for
the vertical wind speed component should be less than 0.25 m/s. Required
accuracy for the vertical wind speed component is as specified in Section
6.1.1 for horizontal speeds.
6.1.3 Wind Fluctuations
Determination of the on-site standard deviation of wind fluctuations,
or derived standard deviations of cross-plume concentrations may be necessary
if dispersion parameters are being developed for use at a specific site. Since
the analytical framework within which such wind fluctuations measurements/
statistics are to be incorporated is expected to be unique or applied on a
case-by-case basis, approval by the permit granting authority is required
49
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and no general requirements regarding specifications are outlined in this
guideline. Considerable care is required in the selection of wind instru-
ments and data logging systems, especially in the choice of sampling and
averaging times. Thus, response characteristics of wind sensors are
especially critical [56,57], Owners or operators designing programs incor-
porating these capabilities should submit a statement from a qualified
consultant identifying the adequacy of such wind system(s) within the
context of the overall PSD ambient monitoring program.
6.1.4 Vertical Temperature Difference
Errors in measured temperature difference should not exceed 0.003
°C/m.
6.1.5 Temperature
Errors in temperatures should not exceed 0.5°C if fog formation,
icing, etc., due to water spray or water vapor emitted from the facility
may be a problem. Otherwise, errors should not exceed 1.0°C.
6.1.6 Humidity
Atmospheric humidity can be measured and expressed in several ways.
If the permit granting authority determines that a significant potential
exists for fog formation, icing, etc., due to effluents from the proposed
facility, error in the selected measurement technique should not exceed
an equivalent dewpoint temperature error of 0.5°C. Otherwise, errors in
equivalent dewpoint temperature should not exceed 1.5°C over a dewpoint
range of -30°C to +30°C.
6.1.7 Radiation - Solar and Terrestrial
The determination of Pasquill stability class may be based on
whether the solar radiation is termed strong, moderate, or slight. Stability
class can be determined from sun elevation and the presence, height, and
amount of clouds [46], or by using a pyranometer and/or net radiometer
during the daytime and a net radiometer at night. Such radiation-to-stability
relationships are expected to be site-specific, and the responsibility for
demonstrating their accuracy lies with the permit applicant. General accuracy
for pyranometers and net radiometers used in a PSD monitoring network is
expected to be +5 percent.
6.1 .8 Mixing Height
Mixing height data may be derived from NWS upper air data. If
available data are determined to be inappropriate by the permit granting
authority, such data may be obtained on-site by the permit applicant [58]
The instrument system to be used is not specified in this guideline, but
its precision and resolution should not exceed the limits associated with
NWS radiosonde systems [54,55].
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6.1.9 Precipitation
A recording precipitation collector should have a resolution of
0.25 mm (0.01 inches) liquid precipitation per hour at precipitation
rates up to 7.6 cm/hour. Accuracy should be within 10 percent of the
recorded value. A heated system should be used to assure proper measure-
ment of frozen precipitation. A suitable windscreen should be used.
6.1.10 Visibility
Visibility can be measured within 5 percent of true over visual
ranges of about 80 meters to 3 km with available transmissometers.
Estimates can be based upon very short path lengths using other types of
equipment such as nephelometers [59]. At this time, the combined use of
a multi-wavelength telephotometer, integrating nephelometer and
particulate monitor, together with color photography, should prove most
helpful in documenting baseline visibility related parameters. These
as well as other components of a visibility monitoring program, are
discussed in reference 51. Reference 50 also contains much background
information.
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7. QUALITY ASSURANCE FOR METEOROLOGICAL DATA
All equipment should receive an appropriate examination and calibration
prior to initial installation to assure the acquisition of the maximum
amount of usable data within the error limits specified herein. Inspection,
servicing, and calibration of equipment must be scheduled throughout the
measurement program at appropriate intervals to assure at least 90 percent
data retrieval for each variable measured at sites where continuous air
quality monitors are being operated. At remote sites, data retrieval
for measured variables should not fall below 80 percent. In addition,
the joint frequency for the recovery of wind and stability data should not
fall below 90 percent on an annual basis; missing data periods must not
show marked correlation with the various meteorological cycles.
Calibration of systems should be accomplished no less frequently
tharn once every 6 months. In corrosive or dusty areas, the interval
should be reduced to assure adequate and valid data acquisition.
If satisfactory calibration of a measuring system can be provided
only by the manufacturer or in special laboratories, such as wind-tunnel
facilities, arrangements should be made for such calibrations prior to
acquisition of the equipment. A parts inventory should be maintained at
a readily accessible location to minimize delays in restoring operations
after system failures.
An independent meteorological audit {by other than one who conducts
the routine calibration and operation of the network) should be performed
to provide an on-site calibration of instruments as well as an evaluation
of (a) the network installation, (b) inspection, maintenance, and calibra-
tion procedures, and logging thereof, (c) data reduction procedures,
including spot checking of data, end (d) data logging and tabulation
procedures. The on-site visit (requiring as little as 1 day in many
cases) should be made within 60 days after the network is first in full
operation, and a written audit/evaluation should be provided to the
owner. This report should be retained by the owner. Any problems should
be corrected and duly noted as to action taken in an addendum to the
audit report. A reproducible copy of the audit report and the addendum
should be furnished with the source construction permit application.
Such independent meteorological audit-evaluations should be performed
about each 6 months. The last such inspection should be made no more than
30 days prior to the termination of the measurement program, and while the
measurement operation is in progress.
The 1983 publication "Quality Assurance Handbook for Air Pollution
Measurement Systems: Volume IV. Meteorological Measurements" [60]
should be consulted for more information. Major sections in this volume
address (1) quality assurance of the measurement process, (2) methods for
judging the suitability of sensor siting, and (3) meteorological data
validation.
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8. DATA REPORTING
8.1 Air Quality Data Reporting
A summary of the air quality data, the raw air quality data, and
the quality assurance data discussed in Section 4.1.6 must be submitted
to the permit granting authority at the time of submittal of the PSD
application. There should be a prior agreement between the source and
the permit granting authority as to whether the raw data should be
submitted in addition to a summary of the data. Some sources may also
desire to submit data periodically to the permit granting authority for
review to identify any problems in the data as they occur. Note that
this is not a requirement. The applicant and the permit granting authority
should have a prior agreement as to the format and procedure for the
data submission. The air quality data should preferably be submitted in
SAROAD format and in a machine readable form. A printout of the contents
of the tape or cards should also be included. All raw data not previously
submitted (i.e., calibration data, flow rates, etc.) should be retained
for 3 years and submitted upon request to the permit granting authority.
For continuous analyzers, at least 80 percent of the individual
hourly values should be reported by the source in any sampling period.
For manual methods (TSP and particulate pollutants), 80 percent of the
individual 24-hour values should be reported in any sampling period.
This capture rate is important because of the short duration of a PSD
monitoring program. In addition, there should not be a correlation
between missing data periods and expected highest concentrations.
8.2 Meteorological Data Format and Reporting
Because of the different data requirements for different types of
analyses that might be used to evaluate various facilities, there is no
fixed format that applies to all data sets. However, a generalization
can be made: all meteorological parameters must be collated in chrono-
logical order and tabulated according the observation time, and be furnished
to the permit granting authority upon request. All meteorological variables
that have a SAROAD parameter code should be submitted in SAROAD format.
All units should be in the SI system (International System of Units)
[61]. All input data (in the format required by the analytical procedures
selected) used in, and all results of, the air quality analyses must be
furnished to the permit granting authority upon request.
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APPENDIX A
PROCEDURES TO DETERMINE IF MONITORING DATA WILL
BE REQUIRED FOR A PSD APPLICATION
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1. INTRODUCTION
This appendix has been included in this guideline to aid both the
reviewing authorities and the source applicants in determining if
monitoring data will or will not be required under PSD. The major
considerations leading to a monitoring data decision have been simplified
for presentation in this appendix. This discussion represents the
Federal requirements and the minimum State program requirements. It is
important to identify the reviewing authority, whether it be the local
or State air pollution control agency, or the Regional Office of EPA for
the final requirements. For a complete discussion on the complex PSD
issues, the reader is referred to the PSD regulations and the preamble
discussion [5,7].
2. PSD PERMIT APPLICATION PROCEDURES
Figure A-l shows a simplified organizational overview of the proce-
dures to be followed in the preparation of a PSD permit application.
Figure A-l shows that these procedures are divided into seven parts.
This division is only for illustrative purposes within this appendix and
is intended only to separate the complex procedures into distinct subparts.
Within the Part 1-Source Applicability Determination, both candidate new
and modified major sources are reviewed to see if PSD review will apply.
The Part 2-Pollutant Applicability Determination shows those pollutants
emitted from subject .sources that may or may not be exempted from further
analysis. The Part 3-BACT Analysis is to ensure the application of
best available control technology (BACT) on subject pollutants. Air
quality analysis covered in Part 4 includes both modeling and monitoring
data considerations for certain BACT pollutants. The Part 5-Source Impact
Analysis is to demonstrate that the proposed emissions would not cause
or contribute to a violation of any NAAQS or PSD increment. The Part 6-
Additional Impact Analysis is to ensure that the proposed emissions
increases would not impair visibility, or impact on soils and vegetation.
Finally, Part 7 represents the complete PSD application which transfers
to the permit granting authority the results of all the analysis from
the first six parts. Normally, the source applicant will supply all the
information including the BACT and air quality analyses to make the
necessary determinations. Each of these seven parts is discussed below
in Sections 2.1-2.7. Section 3 contains flow diagrams and discussion
of the first four parts that pertain to the decision whether monitoring
data will or will not be required.
2.1 Part 1 - Source Applicability Determination
The first step in the PSD program is to determine if a proposed new
or modified source is subject to the PSD regulations. The first test
for PSD applicability is that the proposed construction must involve a
major stationary source. Thus, the candidate construction must either
be a proposed new major stationary source or involve the modification of
an existing major stationary source. The criteria in determining whether
A-l
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Part 1 - Source Applicability Determination
Part 2 - Pollutant Applicability Determination
Parts-BACT Analysis
Part 4 - Ambient Air Quality Analysis
l
Part 5 - Source Impact Analysis
Part 6 - Additional Impact Analysis
Part 7 - Complete PSD Application
Figure A-1. Simplified procedures for the preparation of a PSD permit application.
A-2
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the affected source is sufficiently large (in terms of emissions) to be
a new major stationary source or major modification is based on considera-
tion of its potential to emit at rates exceeding certain threshold values.
Potential to emit is the capability at maximum design capacity to emit a
pollutant after the application of all required air pollution control
equipment, taking into account all federally enforceable requirements
restricting the type or amount of source operation. A major modification
is generally a physical change in or a change in the method of operation
of a major stationary source which would result in a significant net
emissions increase for any regulated pollutant. (There are several
changes that are exempted from being considered a major modification.)
Also, the proposed source or modification must locate in a PSD areaan
area designated as "attainment" or "unclassifiable." If the proposed
source or modification would meet certain tests and commence construction
in a continuous fashion at the proposed site within a reasonable time, a
PSD permit under the August 7, 1980 regulations would not be necessary.
Lastly, there are specific new sources and modifications that are exempted
from PSD review. All of the above considerations are explained in more
detail in Section 3 of this appendix.
If it is determined that a new source or modification is subject to
the PSD regulations, then one must proceed to the Part 2-Pollutant
Applicability Determination in order to learn how the pollutant-specific
requirements of PSD may apply.
2.2 Part 2 - Pollutant Applicability Determination
If a source applicant has determined that a proposed new source or
modification would be subject to the PSD requirements, then the applicant
must assess whether the pollutants the project would emit are subject to
PSD. If a new major stationary source emits pollutants for which the
area it locates in is designated nonattainment, then the source is
exempt from PSD review for those pollutants. These sources must,
however, meet the applicable requirements of new source review (NSR) for
each nonattai nment pollutant. If a major construction proposed for a
PSD area involves only changes for nonattainment pollutants, then the
source is not subject to PSD. These sources must meet the appropriate
nonattainment NSR under the SIP for the pollutant. Once the question of
NSR jurisdiction is resolved, then the PSD review applies to significant
emissions increases of regulated air pollutants.
Specific numerical cutoffs which define what emissions increases
are "significant" are shown in Table A-l. These emissions rates will be
used for pollutants to be emitted from a PSD source unless the new
source or modification is to be located within 10 km of a Class I area
[1]. For these situations, the proposed source or modification must be
prepared to demonstrate that it would not have a significant impact with
respect to a Class I area. A Class I significant impact is defined as
one microgram per cubic meter (ug/m^ or more for a 24-hour average.
Further details on how the significant emission rates in Table A-l were
derived may be found in the preamble discussion of the PSD regulations
[51.
A-3
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TABLE A-l. SIGNIFICANT EMISSIONS RATES
'Pollutant Emissions Rate (tons/year)
Carbon monoxide 100
Nitrogen oxides 40
Sulfur dioxide 40
Particulate Matter 25 (TSP)
Particulate Matter 15 (PM^o)
Ozone (volatile organic compounds) 40
Lead 0.6
Asbestos - 0.007
Beryllium 0.0004
Mercury 0.1
Vinyl chloride 1.0 _%
Fluorides 3
Sulfuric acid mist 7
Total reduced sulfur (including HgS) 10
Reduced sulfur (including H2$) 10
Hydrogen sulfide 10
A-4
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If the emissions from a new source will be significant, or if the
net emissions increase from a proposed modification will be significant,
then one must proceed to the Part 3-BACT Analysis for these pollutants.
2.3 Part 3 - BACT Analysis
Any major stationary source or major modification subject to PSD
must conduct an analysis to ensure application of best available control
technology (BACT) for all applicable pollutants. During each analysis,
which will be done on a case-by-case basis, the reviewing authority will
evaluate the energy, environmental, economic, and other costs associated
with each alternative technology. The reviewing authority will then specify
an emissions limitation for the source that reflects the maximum degree
of reduction achievable with all these concerns in mind for each pollutant
regulated under the Act. In no event can an emission limitation be
required which would be less stringent than any applicable standard of
performance under 40 CFR Parts 60 and 61.
After the BACT determination, the source must then investigate the
need for each pollutant subject to BACT (BACT pollutant) to also undergo
the remaining analyses for this pollutant.
2.4 Part 4 - Ambient Air Quality Analysis
Each application by a PSD source or modification must contain an
air quality analysis for each BACT pollutant to demonstrate that its new
pollutant emissions would not violate either the applicable NAAQS or the
applicable PSD increment. This analysis ensures that the existing air
quality is better than that required by national standards and that
baseline air quality is not degraded beyond the applicable PSD increment.
Two narrow exemptions to this requirement are specified in the regulations
and involve certain existing sources with low BACT emissions and sources
of temporary emissions meeting certain criteria.
In making the above determinations, many PSD sources must first
assess the existing air quality for each applicable air pollutant that
it emits in the affected area. The requirement to monitor existing air
quality may not apply to (a) pollutants for which the new emissions
proposed by the applicant would cause impacts less than the significant
monitoring concentrations (Table A-2), or (b), situations where the
background concentration of the pollutant is below the significant
monitoring values. This exemption should not be used when there is an
apparent threat to an applicable PSD increment or NAAQS based on modeling
alone or when there is a question of adverse impact on a Class I area.
When monitoring data are required, the applicant must provide ambient
montioring data that represent air quality levels in the year's period
preceding the PSD application. Where existing data are not judged
representative or adequate, then the applicant must conduct its own
monitoring program. Typically, monitoring data are used by applicants
to support or extend the assessment made with air quality dispersion
model ing.
A-5
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TABLE A-2. SIGNIFICANT MONITORING CONCENTRATIONS
Pollutant
Air Quality Concentration (ug/m^)
and Averagi ng Time
Carbon monoxide
Nitrogen dioxide
Sulfur dioxide
Particulate Matter
Particulate Matter
Ozone
Lead
Asbestos
Beryl!ium
Mercury
Vinyl chloride
Fluorides
Sul furic acid mist
Total reduced sulfur (including
Reduced sulfur (including H2S)
Hydrogen sulfide
575 (8-hour)
14 (Annual )d
13 (24-hour)
10 (24-hour) for TSP
10 (24-hour) for PM10
a
0.1 (3-month )d
b
0.001 (24-hour)e
0.25 (24-hour)
15 (24-hour)
0.25 (24-hour)
b
c
c
0.2 (l-hour)e
aNo specific air quality concentration for ozone is prescribed. Exemptions
are granted when a source's VOC emissions are < 100 tons/year.
No acceptable monitoring techniques available at this time. Therefore,
monitoring is not required until acceptable techniques are available.
cNo acceptable monitoring techniques available at this time. However,
techniques are expected to be available shortly.
averaging times are corrected to be consistent with the averaging time
of the standard.
eThese concentrations are corrected from the previous printing and are
approximately five times the minimum detectable concentrations. These
concentrations are consistent with other values in this table.
A-6
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In addition to the above discussion, EPA in general intends to limit
the application of air quality models to a downwind distance of 50
kilometers. This is because dispersion parameters commonly in use are
based on experiments relatively close to sources, and extending these
parameters to long downwind distances results in great uncertainty as to
accuracy of the model estimates at such distances. EPA does not intend
to analyze the impact of a source beyond the point where the concentrations
from the source fall below certain levels (generally based on Class I
increments) shown in Table A-3. However, since the 1977 Clean Air Act
Amendments provide special concern for Class I areas, any reasonably
expected impacts for these areas must be considered irrespective of the
50 km limitation on the above significant values.*
2.5 Part 5 - Source Impact Analysis
The proposed source or modification must demonstrate that significant
net emissions increases {including secondary emissions and fugitive
emissions), would not cause or contribute to air pollution in the violation
of any NAAQS or any applicable maximum allowable increase over the
baseline concentration in any area.
2.6 Part 6 - Additional Impact Analysis
An applicant is also required to analyze whether its proposed
emissions increases would impair visibility, or impact on soils or
vegetation. Not only must the applicant look at the direct effect of
source emissions on these resources, but it also must consider the
impacts from general commercial, residential, industrial and other
growth associated with the proposed source or modification.
2.7 Part 7 - File Complete PSD Application
After completion of the proceeding analyses, the source may submit
a PSD application to the permit granting authority. The application,
after being judged complete and being reviewed for proper determination
of applicability, BACT, and air quality impacts, must undergo adequate
*It should be noted that there are three separate and distinct sets of
values which are considered "significant" within the PSD program:
(a) Significant emissions rates;
(b) Significant monitoring concentrations; and
(c) Significant ambient impacts (including the specific significant
Class I area impacts).
As pointed out, each set of values has a different application, and
therefore, this guideline has been worded to clarify the appropriate
values to be used while assessing the need to collect monitoring data.
A-7
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TABLE A-3. SIGNIFICANT AMBIENT AIR QUALITY IMPACTS
Pollutant
S02
TSP
PM10
N02
CO
Averaging Time
Annual 24-Hour 8-Hour 3-Hour 1 Hour
1 yg/m3 5 yg/m3 25 yg/m3
1 yg/m3
1 yg/m3 5 yg/m3
1 yg/m3
0.5 mg/m3 -- 2 mg/m3
NOTE: This table does not apply to Class I areas. A significant impact
for Class I areas is 1 \>g/w on a 24-hour basis for PM^j and S02.
A-8
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public participation. The regulations solicit and encourage participa-
tion by the general public, industry, and other affected persons impacted
by the proposed major stationary source or major modification. Specific
public notice requirements, including a public comment period and the
opportunity for a public hearing must be met before the PSD review agency
takes final action on a PSD application. The public notice must indicate
whether the reviewing authority has proposed approval, denial, or condi-
tional approval of the proposed major source or major modification.
Consideration is given to all comments received provided they are relevant
to the scope of the review.
The source shall also submit all information necessary to perform
any analysis in Parts 1-6 above or make any determinations required in
Parts 1-6. Such information shall include (a) a description of the
nature, location, design capacity, and typical operating schedule of the
proposed source or modification, including specifications and drawings
showing its design and plant layout, (b) a detailed schedule for construc-
tion of the proposed source or modification, and (c) a detailed descrip-
tion as to what system of continuous emission reduction is planned for
the proposed source or modification, emission estimates, and any other
information necessary to determine that best available control technology
would be applied. The proposed source or modification shall also provide
information on (a) the air quality impact of the proposed source or
modification, including meteorological and topographical data necessary
to estimate such impact, and (b) the air quality impacts, and the nature
and extent of any or all general commercial, residential, industrial,
and other growth which has occurred since August 7, 1977 in any area the
proposed source or modification would affect.
A-9
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3. DECISIONS FOR MONITORING DATA REQUIREMENTS
Figure A-l and the discussion that followed in Section 2 provided
an overview of the various activities relating to a PSD permit application.
This section will go into more detail on those activities that need to
be considered in deciding if air quality monitoring data will be required.
It should be noted that the procedures described in this appendix
do not include any details on how the modeling analyses are to be conducted
but only indicate at what points (boxes) the results of such analyses
are necessary. Also, while these procedures lead to a determination of
when air quality monitoring is likely to be required, they do not lead
to a decision as to when meteorological monitoring is necessary (for
model input). Guidance on the requirements and procedures for conducting
modeling analyses is contained in reference 15. Section 5 of this
guideline describes general meteorological monitoring requirements, and
reference 62 also provides further guidance on this subject.
Figures A-2 and A-3 show various steps that must be made for a
proposed PSD source or modification in order to assess how the monitoring
data requirement might apply. The decisions in these flow diagrams must
be applied separately for each regulated pollutant that would be emitted
from a proposed source or modification. Boxes 1-14 apply to Figure A-2
and boxes 15-29 apply to Figure A-3
Box 1. Is proposed source a major stationary source or major modification
locating in a PSD area?
A major stationary source is defined as any one of 28 source categories
(Table A-4) which emits, or has the potential to emit, 100 tons per year
or more of any pollutant regulated under the Act. In addition, the
definition includes any other stationary source which emits, or has the
potential to emit, 250 tons per year or more of any regulated pollutant.
Finally, major stationary source also means any physical change occurring
at a stationary source (which prior to the change is not major) if the
change by itself would be major. That is, the change itself would
result in an equivalent stationary source which would emit 100 tons per
year or more for any pollutant regulated under the Act for any one of
the 28 source categories (Table A-4), or 250 tons per year for any other
stationary source. The pollutants regulated under the Act were shown in
Part 2-Pollutant Applicability Determination.
A stationary source generally includes all pollutant-emitting
activities which belong to the same industrial grouping, are located on
contiguous or adjacent properties, and are under common control. Pollutant
activities which belong to the same major group as defined in a standard
industrial classification scheme developed by the Office of Management
and Budget are considered part of the same industrial grouping.
The rest of the PSD size applicability for proposed new stationary
sources is simply that the candidate source would be a major stationary
A-10
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1. Is proposed source
a major stationary source or
a major modification locating
in a PSD area?
1
Part 1 -
Source Applicability
Determination
3. Is construction proposed
YES / ior an area which is designated^ NO
nonattainment area ior the
regulated pollutant? *
J
5. Is proposed source
' ' or modification within
10 km of a Class I area?/
YES
6. Class I area
screening procedure
7. More refined model
(optional). Note: May
require gathering of
meteorological data.
9. Are new emissions or net \
. emissions increase of the \
\ regulated pollutant > Table A-1?/
/8. Will the proposed source^
' / or modification impact
\ on a Class I area?
YES
YES
/ 11. Is proposed construction a \ _
( relocation of a portable -
\ facility with previous permit?
/12. Are there potential impacts \ yEt.
\ °'
on a Class I area, or areas
known increment violation?
Part 2 -
Pollutant Applicability
Determination
P
14. Apply BACT
]
Part 3 -
BACT Analvsis
* Procedures are to be repeated for
all regulated pollutants which would
be emitted by the proposed construction.
(
c
Part 4
Ambient Air Quality Analysis
Part 3
Part 6
- Source Impact Analysis
- Additional Impact Analysis
Part 7
- Complete PSD Application
Figure A-2. Procedures used to determine the monitoring data requirement.
A-ll
-------
Part 1 - Source Applicability Determination
JL
| Part 2 . Pollulanl Applicability Determination
I ~
| Part 3 - BACT Analysis"]
NO/
' 15. Are the allowable emissions or the \
net emissions increase temporary,
impacting no Class I area, or impacting
no area where the PSD increment
is violated! /
, YES
16. Wifl the proposed \
source or modification
emil VOQ /
NO,
H8. Is there an apparent threat >
to the NAAQS, or is there
a potential adverse impact
on a Class I area)
LYES
YES
' 19. Will proposed source or \
modification perform post- \
approval monitoring in lieu V~
of preconstruction monitoring /
data? /
20. Estimate existing air quality.
Note: May require gathering
of meteorological data.
21. Estimate air quality impacts of
proposed construction.
Use screening procedure
or more refined model
Use 'good engineering practice"
Consider 50 ton/year exemption
22. Is the existing air
quality < Table A-2!
-YES
NO/23. Are the air quality \yjs
impacts < Table A-2? /
YES /2S. Are proposed emissions
a criteria pollutant or VOC?
24. Is there an apparent threat to
the PSD increments or NAAQS. \YES
or is there a potential adverse
impact on a Class I area!
,26. Is there an approved
NO /
1 ' monitoring technique
available?
Part 4 -
Ambient
Air Quality
Analysis
27. Preconstruction monitoring data required.
Use representative air quality data
Monitor (source specific)
28. No preconstruction
monitoring data required
29. Preconstruction monitoring
data may be required
Part 5 - Source Impact Analysis
Part 6- Additional Impact Analysis
Part 7- Complete PSD Application
FIGURE A-3. PROCEDURES USED TO DETERMINE THE MONfTORINC DATA REQUIREMENT.
A-12
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TABLE A-4. MAJOR STATIONARY SOURCES
1. Fossil-fuel fired steam electric plants of more than 250,000,000
British thermal units per hour heat input
2. Coal cleaning plants (with thermal dryers)
3. Kraft pul p mills
4. Portland cement plants
5. Primary zinc smelters
6. Iron and steel mill plants
7. Primary aluminum ore reduction plants
8. Primary copper smelters
9. Municipal incinerators capable of charging more than 250 tons of
refuse per day
10. Hydrofluoric acid plants
11. Sulfuric acid plants
12. Nitric acid plants
13. Petroleum refineries
14. Lime plants
15. Phosphate rock processing plants
16. Coke oven batteries
17. Sulfur recovery plants
18. Carbon black plants (furnace process)
19. Primary lead smelters
20. Fuel conversion plants
21. Sintering plants
22. Secondary metal production plants
23. Chemical process plants
24. Fossil-fuel boilers (or combinations thereof) totaling of more than
250,000,000 British thermal units per hour heat imput
25. Petroleum storage and transfer units with a total storage capacity
exceeding 300,000 barrels
26. Taconite ore processing plants
27. Glass fiber processing plants
28. Charcoal production plants
A-13
-------
source in terms of its potential to emit. The applicability rules for
determining whether a major modification would occur are more complex.
A "major modification" is generally a physical change in or a
change in the method of operation of a major stationary source which
would result in a significant net emissions increase in the emissions of
any regulated pollutant. In determining if a proposed increase would
cause a significant net increase to occur, several detailed calculations
must be performed. First, the source owner must quantify the amount of
the proposed emissions increase. This amount will generally be the
potential to emit of the new or modified unit. Second, the owner must
document and quantify all emissions increases and decreases that have
occurred or will occur contemporaneously (generally within the past five
years) and have not been evaluated as part of a PSD review. The value
of each contemporaneous decrease and increase is generally determined by
subtracting the old level of actual emissions from the new or revised
one. Third, the proposed emissions increase and the unreviewed contem-
poraneous changes must then be totalled. Finally, if there is a resultant
net emissions increase that is larger than values specified in Table
A-1, the modification is major and subject to PSD review.
Certain changes are exempted from the definition of major modification.
These include: (a) routine maintenance, repair and replacement; (b) use
of an alternative fuel or raw material by revision of an order under sections
2(a) and (b) of the Energy Supply and Environmental Coordination Action
of 1974 (or any superseding legislation); (c) use of an alternative fuel
by reason of an order or rule under section 125 of the Clean Air Act;
(d) use of an alternative fuel at a steam generating unit to the extent
it is generated from municipal solid waste; (e) use of an alternative
fuel or raw material which the source was capable of accommodating; before
January 6, 1975 or which the source is approved to use under any permit
issued under 40 CFR 52.21 , or under regulations approved pursuant to 40
CFR 51.24; and (f) an increase in the hours of operation, or the production
rate. The last two exemptions, (e) and (f), can be used only if the corres-
ponding change is not prohibited by certain permit conditions established
after January 6, 1975.
If the size of a proposed source or modification thus qualifies as
major, its prospective location or existing location must also qualify
as a PSD area, in order for PSD review to apply. A PSD area is one
formally designated by the state as "attainment" or "unclassifiable" for
any polluant for which a national ambient air quality standard exists.
This geographic applicability test generally does not take into account
what new pollutant emissions caused the construction to be major. It
looks simply at whether the source is major for any pollutant and will
be located in a PSD area. The one exception is that if a major stationary
source emits only nonattainment pollutants, then no PSD review would
apply.
If a proposed source or modification would be subject to PSD review
based on size, location, and pollutants emitted, it still may escape the
PSD review requirements under certain grandfather provisions under 40 CFR
A-14
-------
.52.21(1). For example, a proposed source or modification that was not
subject to the 1978 PSD rules and had received all necessary Federal,
State and local air permits before August 7, 1980, would not be subject
to the 1980 regulations. (See the PSD regulations for other exemptions.)
Finally, the PSD regulations contain some specific exemptions for
some forms of source construction. The requirements of the PSD regula-
tions do not apply to any major stationary source or major modification
that is (a) a nonprofit health or educational institution (only if such
exemption is requested by the governor), or (b) a portable source which
has already received a PSD permit and proposes relocation, or the source
or modification would be a major stationary source or major modification
only if fugutive emissions, to the extent quantifiable, are considered
in calculating the potential to emit of the stationary source or modifi-
cation and the source does not belong to any of the categories listed in
Table A-4.
Box 2. No PSD permit needed.
If the source has met the appropriate deadlines for construction;
and is not a major stationary source, a major modification, is not
located in a PSD area, or is not subject to the specific exemptions
mentioned above, the PSD program is not applicable, and therefore, no
PSD permit is needed.
Box 3. Is construction proposed for an area which is designated
nonattainment area for the regulated pollutant?
If the project is a major stationary source or a major modification,
the prospective location must also qualify as a PSD area in order for
the PSD review to apply. A PSD area is defined as an area formally
designated by the State as "attainment" or "unclassifiable" for any pollu-
tant for which a NAAQS exists. An area not classified as either "attain-
ment" or "unclassifiable" would be classified as "nonattai nment". If the
proposed construction is in a nonattainment area for any pollutant, pro-
ceed to box 4 for that pollutant; for all other regulated pollutants,
proceed to box 5.
Box 4. No further PSD analysis for that pollutant.
If the proposed major stationary source or major modification will
emit pollutants from an area that has been designated as "nonattainment",
then the proposed source or modification is exempt from further PSD
review for only those pollutants. However, the proposed source or
modification must meet the applicable preconstruction requirements for
each nonattainment pollutant. (See 40 CFR 51.18 and 40 CFR 52.24.)
The pollutant applicability determination would be continued for
all other regulated pollutants (except nonattainment pollutants) emitted
by a proposed major stationary source or major modification by proceeding
to box 5.
A-15
-------
Box 5. Is proposed source or modification within 10 km of a Class I
area?
The PSD regulations [40 CFR 51.24(b)(23)(iii) and 40 CFR 52.21(b)(23)
(iii)] require that a proposed source or modification, which plans to
construct within 10 km of a Class I area must demonstrate that if it
would not impact the area, (less than 1 yg/m^) even if the proposed
emissions are below the applicable significant emissions rates listed in
Table A-l. If the proposed source or modification is within 10 km of a
Class I area, proceed to box 6; if not, proceed to box 9.
Box 6. Class I area screening procedure.
If the proposed source or modification is within 10 km of a Class I
area, then the screening procedures described in reference 62 may be
used to estimate the impact on the Class I area. This screening procedure
is based on a simple but conservative model for estimating each concentra-
tion due to the emissions from the proposed source or modification.
Box 7. More refined model (optional).
A proposed source or modification may choose not to accept or use
the concentration estimates derived from the screening procedures in box
6, and may elect to use a more refined model which would more adequately
reflect the impact on the Class I area from the proposed source or modifi-
cation. It should be emphasized that in order to perform a refined
modeling analysis, it may be necessary to collect 1 year of on-site
meteorological data for the model input if an adequate amount of represen-
tative data are not already available. The application of any model used
in this analysis must be consistent with reference 15 as discussed in
section 5.1. The application of any different model must be approved by
EPA in order to avoid any delays in the processing of the permit applica-
tion. Applicants should consult with the reviewing authority before
investing considerable resources in the use of the different models.
Therefore, the documentation and specific description of the model should
be provided to the reviewing authority before the results are submitted.
The concentration estimates from the screening procedure or the refined
model, are subsequently used in the Part 4-Ambient Air Quality Analysis
and Part 5-Source Impact Analysis.
Box 8. Will the proposed source or modification impact on a Class I
area?
If a proposed source or modification is within 10 km of a Class I
area, the proposed source or modification must be prepared to demonstrate
for each regulated pollutant it would emit that there would be no signifi-
cant impact on the Class I area. Significant impact is defined in the
PSD regulations [40 CFR 51.24(b)(23)(iii) and 40 CFR 52.2K b)(23)( iii)]
as 1 microgram per cubic meter (yg/rrP) or more, 24-hour average.
Box 9. Are new emissions or net emissions increase of the regulated
pollutant >Table A-l?
A-16
-------
If the proposed source or modification is not within 10 km of a
Class I area, or if the proposed source is within 10 km of a Class I
area and has no significant impact on the Class I area, then the emissions
for each pollutant from the proposed source of modification are compared
to the significant emissions rates in Table A-l.
Box 10. No further analysis for that pollutant.
If the emissions from the proposed source or modification are not
significant as defined in Table A-l, no further analysis is required for
that pollutant. However, a similar review must be performed for all
other regulated pollutants by proceeding to box 5 for the next pollutant.
Box 11. Is proposed construction a relocation of a portable facility
with previous permit?
This question is actually an applicability question that is normally
considered under the Part 1-Source Applicability Determination. However,
there are certain other questions (see boxes 3, 5 and 8 of Figure A-2)
which are normally asked under pollutant applicability that are also
germane to permitting a portable facility relocation. Thus, the reason
for including box 11 in Part 2.
The source must be a portable facility which has previously received
a permit under the PSD regulations, the owner proposes to relocate the
facility, and emissions at the new location would be temporary (not
exceeding its allowable emissions). If the facility meets these require-
ments, then proceed to box 12; if not, proceed to box 14.
Box 12. Are there potential impacts on a Class I area, or areas of known
increment violation?
The emissions from the portable source should not exceed its
allowable emissions, and the emissions from the temporary source should
impact no Class I area and no area where an applicable increment is known
to be violated. If there are potentially adverse impacts on a Class I
area, or significant impacts on areas of known increment violation,
proceed to box 14; if not, proceed to box 13.
Box 13. No PSD permit required.
If there are no potential impacts on a Class I area, or areas of
known increment violation, no PSD permit is required.
Box 14. Apply BACT.
"Best available control technology" means an emissions limitation
(including a visible emission standard) based on the maximum degree of
reduction for each pollutant subject to regulation under the Act which
would be emitted from any proposed major stationary source or major
modification which the Administrator, on a case-by-case basis, taking
into account energy, environmental, and economic impacts and other
costs, determines is achievable for such source or modification through
application of production processes or availabl e methods, systems, and
A-17
-------
techniques, including fuel cleaning or treatment or innovative fuel
combustion techniques for control of such pollutant. In no event shall
application of best available control technology result in emissions of
any pollutant which would exceed the emissions allowed by any applicable
standard under 40 CFR Parts 60 and 61. If the Administrator determines
that technological or economic limitations on the application of measure-
ment methodology to a particular emissions unit would make the imposition
of an emissions standard infeasible, a design, equipment, work practice,
operational standard, or combination thereof, may be prescribed instead
to satisfy the requirement for the application of best available control
technology. Such standard shall, to the degree possible, set forth the
emissions reduction achievable by implementation of such design, equipment,
work practice or operation, and shall provide for compliance by means
which achieve equivalent results.
Box 15. Are the allowable emissions or the net emissions increase
temporary, impacting no Class I area, or impacting no area
where the PSD increment is violated?
Temporary emissions are defined as emissions from a temporary
source that would be less than 2 years in duration, unless the Adminis-
trator determines that a longer time period would be appropriate. If
all of the conditions above are not met, proceed to box 16; if they are
met, proceed to Part 7-Complete PSD Application.
Box 16. Will the proposed source or modification emit VOC?
If the proposed source or modification will emit VOC, proceed to
box 17; if not, proceed to box 20. Also proceed to box 20 if the
pollutants are TSP, PMio, S02, CO, NOe, or Pb.
Box 17. Are VOC emissions < Table A-2?
If the VOC emissions rates from the proposed source or modification
are less than the value in Table A-2 (100 tons/year), proceed to box 18;
if not, proceed to box 19.
Box 18. Is there an apparent threat to the NAAQS, or is there a potential
adverse impact on a Class I area?
If the projected air quality after construction is equal to or
greater than 90 percent of the NAAQS, a threat to the NAAQS would generally
exist. Potential adverse impacts on a Class I area must be determined on
a case-by-case basis by the permit granting authority. Therefore, if
there is an apparent threat to the NAAQS, or if there are potential
adverse impacts on a Class I area, then proceed to box 19; if not,
proceed to box 20.
A-18
-------
Box 19. Will proposed source modification perform postapproval monitoring
in lieu of preconstruction monitoring data?
The PSD regulations [40 CFR 51.24(m)(1)(v) and 40 CFR 52.21(m)(l)
(vi)] give special considerations regarding ozone monitoring data to new
or modified sources of volatile organic compounds which have satisfied
all conditions of 40 CFR 51, Appendix A, section IV. This section
generally requires affected sources to meet lowest achievable emission
rate limitations, secure emissions offsets which provide an overall net
air quality improvement, and ensure all other major sources in the same
State are in compliance with the applicable SIP. If a proposed source
or modification has met all of the above conditions for VOC, then the
proposed source or modification may provide postapproval monitoring data
for ozone in lieu of providing preconstruction data. Postapproval
monitoring data are data collected after the date of approval of the PSD
application. However, in no case should the postapproval monitoring be
started later than 2 years after the start-up of the new source or
modification.
If the proposed source or modification will provide postapproval
monitoring, proceed to the Part 5-Source Impact Analysis; if not,
proceed to box 20 for the remainder of the ambient air quality analysis.
Box 20. Estimate existing air quality.
The proposed source or modification must perform an initial analysis
to estimate the existing air quality concentrations. The screening pro-
cedures described in reference 62 may be used. The screening procedures
are based on simple models for estimating air quality due to the emissions
from existing and approved but not yet built sources. A proposed source
or modification may choose not to accept or use the concentration estimates
derived from the screening procedure above, and may elect to use a more
refined model which would more adequately reflect the impact from existing
sources. It should be emphasized that in order to perform a refined
modeling analysis, it is generally necessary to collect 1 year of on-site
meteorological data for the model input. The application of any model
used in this analysis must be consistent with reference 15 as discussed
in section 5.1. The application of any model should be approved by the
permit granting authority to avoid any future delays in the processing of
the permit application. Therefore, the documentation of the specific
description of the model should be provided to the permit granting
authority before the results are submitted.
The concentration estimates from the screening procedure or the
optional refined model will be used in the remaining portions of the
ambient air quality analysis.
A-19
-------
Box 21. Estimate air quality impacts of proposed construction.
The proposed source or modification must estimate its air quality
impacts to demonstrate that its new pollutant emissions would not violate
either the applicable NAAQS or the applicable PSD increment. The proposed
source or modification must use the screening procedures or more refined
model, consider "good engineering practice" for stack height, and consider
the TSP and S02 increment exclusion for Class II areas under 50 tons per
year exemption. These factors are discussed in more detail below.
(a) Screening procedure or more refined model.
If the proposed source or modification used the screening
procedure or more refined model in box 6 or 7 previously to estimate the
impact, then those results may be used in this impact analysis. If the
screening procedure or more refined model was not previously determined,
then the screening procedures described in reference 62 may be used.
This screening procedure is based on a simple model for estimating each
concentration due to the emissions from the proposed source or modification,
A proposed source or modification may choose not to accept or use the
concentration estimates derived from the screening procedure above, and
may elect to use a more refined model which would more adequately reflect
the impact from the proposed source or modification. It should be
emphasized that in order to perform a refined modeling analysis, it is
generally necessary to collect 1 year of on-site meteorological data for
the model input. The application of any model used in this analysis
must be consistent with reference 15 as discussed in Section 5.1. The
application of any model should be approved by the permit granting
authority to avoid any future delays in the processing of the permit
application. Therefore, the documentation and specific description of
the model should be provided to the permit granting authority before the
results are submitted.
The concentration estimates from the screening procedure or
the optional refined model will be used in the remaining portions of the
ambient air quality analysis.
(b) "Good engineering practice" (GEP) for stack height.
The 1978 PSD regulations [1] provide for requiring GEP in the
impact analysis for stack heights. The degree of emission limitations
required for the control of any air pollutant would not be affected by
stack heights (in existence after December 31, 1970) as exceeds good
engineering practice, or any other dispersion techniques implemented
after then.
(c) Consider 50 tons per year exemption.
The PSD regulations [40 CFR 51.24(1) (7) and 40 CFR 52.21(1) (7)]
as they apply to a major modification exempt PMio and S02 from the Class
II increment consumption review if all of the following conditions are
met: (1) the net increase of all pollutants regulated under the Act
after application of BACT would be less than 50 tons/year, (2) no pollutant
would be causing or contributing to a violation of the standards (NAAQS),
and (3) source must have been in existence on March 1, 1978.
A-20
-------
The results of the impact analysis as described in this box will be
used for subsequent portions of the ambient air quality analysis.
Box 22. Is the existing air quality < Table A-2?
The proposed source or modification must determine the existing air
quality concentration in the area of impact of the proposed source or
modification before construction for each applicable pollutant. Modeling
by itself or in conjunction with monitoring data would be used for this
determination. Application of these models must be consistent with
reference 15.
If the proposed source or modification is remote and not affected
by other readily identified man-made sources, two options for determining
existing air quality concentrations from existing data are available.
The first option is to use air quality data collected in the vicinity of
the proposed source or modification, the second option is to use average
measured concentrations from a "regional" site to establish a background
concentration. Additional guidance on determining the background air
quality concentrations may be found in reference 15. See also the
discussion or use of representative air quality data in Section 2.4 of
this guideline.
If the existing air quality is less than the values in Table A-2,
proceed to box 24; if not, proceed to box 23.
Box 23. Are the air quality impacts < Table A-2?
The projected impact of the proposed source or modification was
previously determined by the screening procedure or refined model esti-
mates. These modeled concentrations are compared to the significant
monitoring concentrations shown in Table A-2. If these modeled concen-
trations are less than the values in Table A-2, proceed to box 24; if
not, proceed to box 25.
Box 24. Is there an apparent threat to PSD increments or NAAQS, or is
there a potential adverse impact on a Class I area?
An apparent threat to a PSD increment is consumption by the proposed
source or modification of 90 percent or more of the remaining allowable
increment. An apparent threat to the NAAQS is when the projected air
quality after construction is equal to or greater than 90 percent of the
NAAQS. Potential adverse impacts on a Class I area must be determined
on a case-by-case basis by the permit granting authority.
Therefore, if there is an apparent threat to PSD increments or
NAAQS, or if there is a potential adverse impact on a Class I area,
proceed to box 29; if not, proceed to box 28.
Box 25. Are proposed emissions a criteria pollutant or VOC?
Determine if the pollutant is a criteria pollutant (TSP, PMio, S02,
CO, N02 or Pb) or VOC. If the pollutant is a criteria pollutant or
VOC, proceed to box 27; if not, proceed to box 26.
A-21
-------
Box 26. Is there an approved monitoring technique available?
Acceptable measurement methods currently exist for some noncriteria
pollutants, while other methods are currently under review and have not
been designated as an acceptable measurement method. Section 2.6 of
this guideline discussed the designation of acceptable measurement
methods for noncriteria pollutants. If an acceptable measurement method
does exist, proceed to box 29; if not, proceed to box 28.
Box 27. Reconstruction monitoring data required.
Reconstruction air qua! ity monitoring data are required for this
part of the ambient air quality analysis. The proposed source or modifica-
tion has the option of using representative air quality data or monitoring.
Considerations and constraints on the use of existing data were discussed
in Section 2.4 of this guideline. It should be noted that a dispersion
model may be used in verifying the representativeness of the data. If a
proposed source or modification chooses to monitor instead of using
representative air quality data, then the specifics to be followed on
network design, probe siting, quality assurance, number of monitors,
etc., were previously discussed in this guideline.
The monitoring data required in this box will be used in Parts 5,
6 and 7 of the PSD permit application.
Box 28. No preconstruction monitoring data required.
If there is no approved monitoring technique for the noncriteria
pollutants, or if there is no apparent threat to PSD increments or
NAAQS, or if there is no potentially adverse impact on a Class I area,
then generally no preconstruction monitoring data will be required.
However, proceed to the Part 5-Source Impact Analysis for remaining
analyses.
Box 29. Preconstruction monitoring data may be required.
The permit granting authority must determine on a case-by-case
basis if monitoring data will be required when there is an apparent
threat to PSD increments or NAAQS, or when there is a potential adverse
impact on a Class I area. Special attention must be given to Class I
areas where the proposed source or modification would pose a threat to
the remaining allowable increment. For those situations where the air
quality concentration before construction is near the concentrations
shown in Table A-2 and there are uncertainties associated with this air
quality determination then preconstruction air quality monitoring data
may be required. Some situations where noncriteria monitoring may be
required were discussed in Section 2.1.3 of this guideline.
Regardless of the monitoring data decision, proceed on to the Part
5-Source Impact Analysis for remaining analyses.
A-22
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REFERENCES
1. Federal Register 43:26380-26410. June 19, 1978.
2. Ambient Monitoring Guidelines for Prevention of Significant Deteri-
oration (PSD). U.S. Environmental Protection Agency, Research
Triangle Park, NC. OAQPS No. 1.2-096. May 1978.
3. Federal Register 44:51924-51959. September 5, 1979.
4. United States Court of Appeals, No. 78-1006, Alabama Power Company,
et. al., Petitioners v. Douglas M. Costle, as Administrator, Environ-
mental Protection Agency, et. al., Respondents. Decided December 14,
__
5. Federal Register 45:52676-52748. August 7, 1980.
6. Federal Register 49:10408-10462. March 20, 1984.
7. Federal Register (date of proposal) 1984.
8. Federal Register 44:27558-27604. May 10, 1979."
9. Pace, T.G. and N. H. Frank, Procedures for Estimating Probability of
Nonattai nment of a PM^o NAAQS Using Total Suspended Particulate or
Inhal able Particul ate Data. U.S. Environmental Protection Agency,
Research Triangle Park, NC. December 1982 (DRAFT).
10. Ludwig, F.L., J.H. Kealoha, and E. Shelar. Selecting Sites for
Monitoring Total Suspended Particulates. Stanford Research Institute,
Menlo Park, CA. Prepared for U.S. Environmental Protection Agency,
Research Triangle Park, NC. EPA Publication No. EPA-450/3 -77-018.
June 1977, Revised December 1977.
11. Ball, R.J. and G.E. Anderson. Optimum Site Exposure Criteria for
S02 Monitoring. The Center for the Environment and Man, Inc.,
Hartford, CT. Prepared for U.S. Environmental Protection Agency,
Research Triangle Park, NC. EPA Publication No. EPA -450/3 -77-013.
April 1977.
12. Ludwig, F.L. and J.H. S. Kealoha. Selecting Sites for Carbon Monoxide
Monitoring. Stanford Research Institute, Menlo Park, CA. Prepared
for U.S. Environmental Protection Agency, Research Triangle Park, NC.
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.. %
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