United States
Environmental Protection
Agency
Office of Air Quality
Planning and Standards
Research Triangle Park NC 27711
EPA-450/4-80-011
June 1980
Air
Guidance for Collection
of Ambient Non-Methane
Organic Compound
(NMOC) Data for Use
in 1982 Ozone SIP
Development, and
Network Design and
Siting Criteria for the
NMOC and NOX Monitors
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EPA-450/4-80-011
Guidance for Collection of Ambient
Non-Methane Organic Compound
(NMOC) Data for Use in 1982 Ozone
SIP Development, and Network and
Siting Criteria for the
NMOC and NOX Monitors
by
Monitoring and Data Analysis Division
U.S. ENVIRONMENTAL PROTECTION AGENCY
Office of Air, Noise, and Radiation
Office of Air Quality Planning and Standards
Research Triangle Park. North Carolina 27711
June 1980
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This report is issued by the Environmental Protection Agency to report
technical data of interest to a limited number of readers. Copies are
available free of charge to Federal employees, current EPA contractors
and grantees, and nonprofit organizations - in limited quantities - from
the Library Services Office (MD-35), U.S. Environmental Protection Agency,
Research Triangle Park, North Carolina 27711; or, for a fee, from the
National Technical Information Service, 5285 Port Royal Road, Springfield,
Virginia 22161.
This document has been reviewed by the Office of Air Quality Planning and
Standards, U.S. Environmental Protection Agency, and approved for publi-
cation. Subject to clarification, the contents reflect current Agency
thinking.
EPA-450/4-80-011
ii
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PURPOSE
The purpose of this document is to provide guidance for collection of
ambient non-methane organic compound (NMOC) data and siting of the monitoring
instruments. Ambient NMOC data will be needed as input to various photochemical
ozone models which may be used for the 1982 ozone SIPs. Special guidance on
NMOC monitoring is needed because:
(1) ambient NMOC monitoring has not been previously required, nor is it
routinely performed in more than a few areas of the Nation;
(2) NMOC monitoring is needed, not to determine compliance with a NMOC
ambient air quality standard, but to aid in control strategy planning activi-
ties associated with achievement of the ozone ambient standard;
(3) the nature and extent of NMOC monitoring varies depending on which
of several NMOC-03 relationships (models) is used for control strategy
planning.
(4) NMOC monitoring presents unique problems not generally encountered
in monitoring for other criteria pollutants; and,
(5) significant technical, logistical, and other problems exist with
currently available NMOC monitoring methodology.
This guideline attempts to explain these circumstances more completely
and provide guidance in effectively carrying out an ambient NMOC monitoring
program.
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BACKGROUND
Prior to the initial setting of National Ambient Air Quality Standards
(NAAQS) in 1971, few agencies outside of California performed air monitoring
for organic compounds. Even with the setting of the 0.24 ppm NAAQS, to be
used as a "guide" toward achieving the former 0.08 ppm oxidant standard, NMHC
(or NMOC) monitoring was not required because NMHC* is not a criteria pollu-
tant (health or welfare based standard) for which the NAAQS must be achieved.
In the early to mid-1970s, many State and local agencies began measuring
ambient NMOC, despite the fact that such measurements were not required by
EPA. Some agencies reported the measured values to the National Aerometric
Data Bank (NADB), but the accuracy of the NMOC data has often been questioned
because the early NMOC methodology was unreliable. The lack of a NMOC moni-
toring requirement and the unreliability of the methodology in routine field
use prompted a memorandum from OAQPS (in 1975 - copy attached), recommending
a moratorium on purchase of new NMOC instruments. This recommendation was
based on results of a contractor study of NMOC instrument user experience**
and some unpublished work carried out by EPA in North Carolina. Anticipating
a subsequent time when NMOC monitoring might be needed, the memorandum
recommended that existing NMOC analyzers be retained and that agencies con-
tinue to operate such analyzers for trend purposes, if desired. Indeed, some
agencies continued to monitor NMOC routinely.
* Henceforth in this document, non-methane hydrocarbons (NMHC) will be
referred to as NMOC, since the various methods of analysis also measure
organics other than hydrocarbons.
** EPA-650/4-75-08, December 1974, "Survey of Users of the EPA Reference
Method for Measurement of NMHC in Ambient Air"
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While there has been little further commercial development of continuous
NMOC monitoring instruments since the 1975 memorandum, this is not to imply
that nothing has been done in the interim about improving the measurements.
An EPA contractor study investigated the fundamentals of FIDs (flame-ionization
detector) used in NMOC analyzers, and also compared the responses of various
commercial instruments to ambient atmospheres.* In addition, ORD/RTP has
maintained a program for evaluating new NMOC measurement methods. ORD/RTP has
also attempted to identify the principal reasons for lack of reproducibility
of NMOC measurements between various instruments. Unfortunately, due to
inherent problems in measuring NMOC, any new measurement techniques which have
substantially better characteristics than the present continuous FID method
may not be available for several years. On the other hand, some presently
available instruments are thought to be capable of yielding acceptable data at
concentrations above about 0.5 ppmC if they are carefully maintained and
calibrated.
AMBIENT NMOC MONITORING METHODS
Two general categories of NMOC monitoring methods are available:
These are a) "continuous" and b) "discrete" or sometimes called "grab sample"
analysis.
Continuous Methods
Continuous methods provide hourly average NMOC concentrations, up to
24 per day, at fixed sites. They are somewhat analogous to N0/N09/N0
* EPA-600/4-77-033, June 1977, "Evaluation of the EPA Reference Method for
the Measurement of Non-Methane Hydrocarbons - Final Report".
3
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analyzers in that they provide separate measurements of total organic compounds
(TOC) and of methane (CH.). The difference between the TOC and CH. measure-
ments is (defined as) the NMOC measurement. Most NMOC analyzers are designed
to perform the subtraction automatically and provide a direct NMOC output.
The TOC and CH. measurements are made with a FID, but two methods for
separating the CH. from the TOC are in general use. Chromatographic analyzers
use adsorbent columns to separate the CH. from all other organic compounds.
These analyzers tend to be rather complex, require special operating pro-
cedures, and provide up to 12 analyses per hour rather than a truly continuous
measurement. Other analyzers use a catalytic process to separate CH. by
oxidizing all hydrocarbons other than CH. in a special control led-temperature
oxidizer. They may be either dual channel, in which the TOC and CH. are
measured simultaneously, or cyclic, where TOC and CH. are measured alter-
nately. Aside from operational complexity, both Chromatographic and catalytic
types of continuous NMOC analyzers are equally acceptable, subject to the
limitations discussed below.
Continuous NMOC analyzers suffer from a number of inherent technical
problems which limit the reproducibility of data which they provide. Chief
among these is the necessity of subtracting two comparably-sized numbers to
obtain a measure of the NMOC. Because the difference between the TOC and CH.
measurements—i.e., NMOC—is usually considerably smaller than either of the
individual TOC or CH. concentrations, small errors in the TOC or CH. measure-
ments may become large percent errors in the NMOC difference. Furthermore,
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ambient TOC and CH. concentrations must be measured on broad, relatively
insensitive ranges of the instrument in order to accommodate the frequent wide
excursions of the TOC and CH^ ambient concentrations.* Also, FIDs are sensi-
tive to changes in operating conditions such as flow rates, temperature,
burner cleanliness, etc., which may result in zero and span drift. These
characteristics make careful calibration and accurate balance of the TOC and
CH. channels imperative. However, with good operational and quality control
procedures which include careful attention to gas pressures and frequent zero,
span and calibration checks, the analyzers should yield useful measurements at
concentrations above about 0.5 ppmC.
Other NMOC analyzer problems over which the operator may have little or
no control include measurement of TOC and CH* in different samples of air due
to sequential, cyclic operation (usually not a problem for hourly averages),
non-uniform sensitivity to various organic compounds and from one analyzer
design to another, operational complexity, and potential safety hazard from
hydrogen gas which all FIDs require.
There is currently no reference or equivalent method for NMOC, nor is one
expected in the near term (3-5 years). However, it is recommended that
analyzers selected for NMOC monitoring in the next one to two years be of the
conventional FID type described above, using either chromatographic or cata-
lytic separation of CH.. Several such analyzers are currently available from
* For example, NMOC instruments are usually set to measure full-scale
concentrations of TOC of 10 ppm. If the TOC concentration were 5 ppm
and the CH4 concentration were 4 ppm, NMOC would be 1 ppm. Assuming
a 10% error in the TOC measurement--0.5 ppm—this would result in a
50% error—1 + 0.5 ppm—in the NMOC computations.
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manufacturers, such as the Bendix Corporation (Lewisburg, WV), Byron Instru-
ment Co. (Raleigh, NC), Meloy Laboratories, Inc. (Springfield, VA) and Mine
Safety Appliances Company (Pittsburgh, PA). In addition, older, out-of-
production analyzers such as the Beckman 6800 may be used if still in
servicable condition.
The use of a non-conventional NMOC analyzer may be considered, provided
its NMOC measurements have been characterized and found to be reasonably
relatable to sum-of-species measurements provided by sophisticated GC analysis
(see next section) or are otherwise deemed suitable for the application for
which the NMOC data will be used. Such non-conventional analyzers might be
based on techniques such as direct-reading backflush chromatography, processes
which convert all NMOC compounds to CH,, etc. Additional guidance on the
advantages and suitability of these new techniques will be forthcoming from
EPA as test, characterization and comparison data for them become available.
"Discrete" or "Grab-Sample" Analysis
More accurate and sensitive NMOC measurements can be obtained by analysis
of ambient air samples using a sophisticated, multi-component gas chromato-
graphic (GC) analysis system. The cost and complexity of such a system pre-
cludes jji^ situ monitoring; hence, ambient air samples must be collected in
plastic bags or stainless steel canisters and subsequently analyzed in a
laboratory. Furthermore, because of these costs and complexities, analysis
of ambient NMOC by this method is limited to short-term (1-2 months) studies
rather than year round monitoring. Discrete samples can be collected by
integration over a period of one hour or more, or grab samples can be collected
in a few seconds. They are transported to the chromatograph and analyzed
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within a few hours to minimize losses or contamination from the bag or
container.
The analysis yields individual species concentrations of low-to-medium
carbon number compounds (Co-Cif)). commonly found in ambient air. Individual
compounds may be combined into functional groups, such as paraffins, olefins,
aromatics, etc., if desired. A simple total NMOC measurement may be obtained
by summing the concentrations of the various individual compounds and groups
in the sample. This measurement provides accuracy superior to the continuous
NMOC measurement, especially at concentrations below 0.5 ppmC. The concen-
tration of individual compounds may be useful information for other air
pollution studies, also.
The sophisticated GC analysis of discrete samples and the high level of
expertise necessary for these complex procedures are a serious problem which
limits the usefulness of this method in routine applications. Such capability
cannot be developed in a few weeks, or even months, by an agency or private
laboratory. Standardized published techniques are not yet available; thus,
skill is acquired only by apprenticeship and experience. Even the number of
university or contractor laboratories presently able to perform these analyses
competently is very limited.* EPA will attempt to widen contractor support
capabilities by the summer of 1981. A guidance document outlining the pro-
cedures which should be followed in collecting, handling and analyzing samples
has recently been prepared.**
* Much of the current capability will be utilized in the Northeast
Corridor and other studies in the summer of 1980.
** EPA-45Q/4-8Q-008, April 1980, Guidance for the Collection and Use of
Ambient Hydrocarbon Species Data in Development of Ozone Control Strategies.
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CURRENT NMOC MONITORING REQUIREMENTS
Current NMOC ambient monitoring requirements stem entirely from the need
to control hydrocarbons as precursors to the photochemical formation of ozone.
Recent advancements in the development and verification of quantitative models
(e.g., photochemical dispersion models) relating NMOC emissions and NMOC
ambient concentrations to photochemical ozone concentrations now allow improved
estimation of the degree of NMOC control necessary to achieve the NAAQS for
ozone. Thus, NMOC data have become a necessary input to models that are used
to develop the ozone NAAQS attainment strategy. Current models (e.g., city-
specific EKMA* and sophisticated photochemical dispersion models) require NMOC
as input.
Method Applicability
Photochemical dispersion modeling is the most sophisticated type of
modeling. Photochemical models require detailed organic species data in
order to establish initial and boundary conditions - as well as continuous
NMOC data - for trouble shooting and verification of the model in each new
application. Organic species data are also needed to check the accuracy of
emission inventory estimates in various portions of the modeling region.
Grab samples of organic species taken by aircraft are needed as input and to
verify organic concentrations aloft in the model.
EKMA requires continuous measurements of the higher NMOC levels in the
polluted air mass in the areas of highest precursor emission density. Some
* Empirical Kinetic Modeling Approach
8
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measure of organic compounds upwind is needed to assess transport into the
area if this is thought to contribute significantly to the area's NMOC burden.
Because of possible inaccuracies of continuous measurements at lower concen-
trations, (i.e., < 0.5 ppmC), discrete sampling techniques and the summing of
non-methane organic species concentrations are recommended for upwind NMOC
measurements.
The NMOC data are to be collected during the season of peak ozone con-
centrations (summer). NMOC concentrations are often high in central urban
locations and at those times of the day (early morning) when accurate measure-
ments are required for the models. Also, NMOC concentrations are most often
high on those days when high values of ozone are measured later in the day.
Consequently, (with the exception of upwind measurements) NMOC concentrations
are more frequently expected to exceed the 0.5-1.0 ppmC threshold where the
continuous NMOC analyzer's accuracy is thought to be satisfactory for model
needs. Continuous NMOC measurements below 0.5 ppmC may be inaccurate for use
in the 03 models, even when the instruments are operated under the best quality
control procedures.
Additional Technical Assistance To Be Available
As noted earlier, errors due to variability with currently available
continuous NMOC analyzers are a problem, and limit their usefulness to higher
concentration measurements. To minimize these errors and to obtain maximum
usefulness of the continuous NMOC data, careful attention to calibration,
operational procedures, and quality assurance is necessary. Technical
guidance in these areas will be provided in a Technical Assistance Document
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(TAD) to be prepared by EMSL at Research Triangle Park, North Carolina.
Regional Offices will be notified and supplied copies of this TAD as soon
as it is available (expected in November 1980). For NMOC measurements to be
made in Summer 1980, interim guidance is given in an appendix to this document.
As the EPA's Environmental Monitoring Systems Laboratory (EMSL) develops
guidance on standard calibration procedures, quality assessment and quality
control procedures for existing NMOC analyzers, OAQPS plans to develop and to
present workshops on this material, as well as video tapes of such workshops,
in order to transfer the newly developed procedures and information to State
and local agencies in a timely fashion.
General technical guidance on organic species analysis by GC (including
recommendations for standardized procedures) has been developed for use by
State and local agencies (see Footnote on Page 7). However, it is generally
recommended that a competent contractor be sought to carry out this part of
the NMOC measurements, rather than for a State or local agency to attempt
such a measurement program, particularly if they have not had previous
experience with GC techniques.
Another reference source for monitoring guidance for NMOC includes the
May 10, 1979, Part 58, Monitoring Regulations. Further, the guidance docu-
ment, "Site Selection for the Monitoring of Photochemical Air Pollutants,"
EPA-450/3-78-013, April 1978, provides additional detailed guidance for
location of NMOC monitors and classifying spatial scales of representativeness.
10
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FUTURE NMOC MONITORING
Beyond the development of the 1982 SIPs, there will be a continuing need
for NMOC ambient monitoring data. Agencies should continue to utilize their
NMOC monitors to assess trends in ambient NMOC and ozone levels relative to
hydrocarbon emission reductions. This information will provide an additional
means (besides ozone trends) to assess the effectiveness of hydrocarbon (and
NO ) control strategies. Also, these trend data will provide further insight
A
into the projection capabilities of the models used.
Under the current SIP surveillance plan requirements, State and local
agencies will be conducting ambient monitoring at SLAMS* or NAMS* sites for the
various criteria pollutants. In view of the continuing needs for NMOC monitor-
ing, NMOC monitoring may be required as part of the NAMS networks. Thus,
analyzers purchased in earlier special monitoring efforts for the 1982 ozone
SIPs may eventually be incorporated into the NAMS network, with the resulting
data to be submitted to EPA for control strategy evaluation. It is anticipated
that Part 58 rulemaking revisions pertaining to NAMS NMOC monitoring would not
occur before calendar year 1982. During the time period after a State or local
agency has collected NMOC data for the 1982 SIPs, and up until the NMOC revi-
sions to Part 58, it is recommended that control agencies continue operating
and submitting NMOC data to EPA.
* SLAMS State/Local Air Monitoring System
** NAMS National Air Monitoring System
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NETWORK DESIGN AND SITING CRITERIA FOR NMQC/NOX MONITORS
A. General Conclusions
Two general considerations for all sites are recommended before discussing
specific criteria.
1. NMOC and NO analyzers should be collocated; and,
A
2. NMOC and NO levels and/or ratios should not be predominantly
A
influenced by the emissions from a single street or source.
B. Type and Location of Site
Although the following types of sites are listed in a general priority
order, it will be up to each specific user to determine the appropriate number
and mix of sites in the development of his individual SIP. Siting recommen-
dations for use in the EKMA model have been made in EPA-450/2-77-021a and
EPA-450/2-77-021b.
1. Maximum Emissions Density Site - This site should be located in
the area of maximum emissions. Automobile traffic density can be used as a
surrogate for NMOC/NO emissions. In an absence of traffic density maps,
A
the commercial business district of the urban area may be used to reflect the
area of maximum emissions. If there is a predominant summer morning wind
direction associated with the area, the downwind fringe of the area of maximum
emission density is preferable. If there is no predominant wind direction,
the centroid of these areas is preferable. Since the conversion of NMOC/NO
A
to oxidants occurs over a wide area and at elevated altitudes, the monitoring
site should reflect this, as well, and not merely be representative of the
12
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emissions of a single street. Therefore, the minimum height acceptable for
this type of monitoring is 10 meters. Minimum setbacks from roadways will be
the same as those found in the Part 58 guidance for N02 monitoring sites,
except that the setback requirements may be met by horizontal, vertical or
slant distance. These setbacks are reproduced in Table 1. Spacing from
obstructions is covered in Section C below.
Table 1. Minimum Separation Distance for NMOC/NO Stations and Roadways
(edge of nearest traffic lane)
Roadway Average Daily Traffic, Minimum Separation Distance Between
Vehicles Per Day Roadways and Stations, Meters
110,000 >10a
15,000 20
20,000 30
40,000 50
70,000 100
>110,000 >250
a Distances Should Be Interpolated Based on Traffic Flow
2. Industrial Source Emissions Site - Although the bulk of NMOC/NO
" ~^^^"~ ~ ™^^^™ j\
emissions comes from transportation sources, some urbanized areas have appre-
ciable emissions from the industrial sector. As with the maximum emission
density site, a downwind fringe area would be preferable. The spacing from
obstructions, height and setback criteria would be identical to the maximum
emission density site, with the additional restriction that the site should
not be within 200 meters of the 10° plume sector from a point source
constructed along the prevailing summertime morning wind direction.
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3. .Upwind background Site - Th'is *si;te is'used tn "some trode'Ting'appli-
cations that call for the ^incoming NMOC/NO to be handled 'differently from the
•/\
locally generated pollutants. 'As such, the 3 i tie should be located 10-35 km
upwind of the urbanized area in the most frequent summer wind direction. The
site should comply with setback requirements as shown in Table 1. Since the
upwind site should not be affected by local sources, the height criteria can be
less restrictive. Accordingly, the recommended height is 3-15 meters. The
spacing from obstructions is covered in Section C below.
4. Downwind Edge of City Site - This site is located further downwind
than the area of maximum emissions and, therefore, has had a chance for more
mixing than the maximum emission site. The specific siting criteria should
conform to that for the upwind background site.
C. Spacing from Obstructions
Buildings, trees and other obstacles may possibly scavenge N0?. In order
to avoid this kind of interference, 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. For similar
reasons, a probe inlet along a vertical wall is undesirable because air moving
along that wall may be subject to possible removal mechanisms. The inlet probe
should also be at least 20 meters from trees. There must be unrestricted
airflow in an arc of at least 270° around the inlet probe, and the predominant
wind 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 the
building, 180° clearance is required.
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SUMMARY
The following points summarize the guidance related to NMOC data
collection for 1982 SIPs:
NMOC data collection is needed for modeling to support development
of 1982 ozone SIPs.
NMOC monitoring activities will differ, depending upon the type
of ozone model to be used for control strategy development.
Requirements for use with EKMA are identified in EPA-450/2-77-021a
and EPA-450/2-77-021b.
NMOC data collection should take place during the oxidant
season, if not all year.
Continuous analyzers used for NMOC monitoring in the next one
to two years should be of the conventional selective oxidation or
chromatographic FID type. New, unconventional NMOC techniques may
be considered if characterization data are available to show suita-
bility.
Continuous monitors provide data useful for modeling at higher
concentrations (> 0.5-1 ppmC). Improved maintenance/operating/
quality assurance procedures are being developed to provide greater
assurance that acceptable data are collected.
Measurements made with continuous NMOC monitors are generally
expected to be useful, since many of them will be made during peak
NMOC season, at peak NMOC time during the day, and in the area of
peak NMOC emission density when ambient NMOC concentrations are
expected to be high.
Some organic species measurements may also be needed, especially
for determining upwind NMOC concentrations and for use in sophis-
ticated photochemical dispersion models if a State chooses to use
one of these models.
NMOC instruments should be collocated with NO instruments.
Monitoring sites should be carefully chosen in order to minimize
undue influence of emissions from single sources.
Additional guidance is available on:
- NMOC species data collection (EPA-450/4-80-008);
- maintenance/operating procedures for continuous analyzers
(in preparation - available by November 1980).
Long-range EPA plans call for considering requiring routine NMOC
monitoring at selected NAMS in major metropolitan areas.
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INTERIM GUIDANCE FOR NMOC MEASUREMENTS
NMOC analyzers should be set up and operated according to the manu-
facturer's instructions. Special attention should be given to matching or
balancing the TOC and CH^ responses, particularly on dual-FID analyzers, so
that the CH. is accurately subtracted from the TOC (whether done internally
by the analyzer or external to the analyzer). Flow rates, as well as other
operational parameters, should be measured to assure that they are correct.
For chromatographic analyzers, initial and periodic manual chromatograms
should be obtained to verify that the gating and operational sequences are
properly timed. Also, all maintenance procedures should be carried out
according to the manufacturer's instructions.
NMOC measurements should always be reported in ppmC (explained later)
and be referenced to a propane standard. This is because FID analyzers
respond differently to different organic compounds, and propane provides a
response close to the average FID response of the organic compounds in the
atmosphere. NMOC measurements referenced to propane are comparable to
total NMOC measurements made by GC species analysis and are appropriate
for use in EKMA.
The way that NMOC analyzers are referenced to propane differs, depend-
ing on the design of the analyzer. Analyzers having a direct NMOC output
with an individual span control may be physically calibrated directly with
propane. However, the TOC and CH^ responses may have to be first calibrated
16
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with CH. to insure that the CH. measurement is correctly subtracted from
the TOC measurement. Other analyzers must be calibrated with CH^. Then
the (TOC - CH.) reading (obtained either from the analyzer or by external
subtraction) must be corrected to propane as follows:
NMQC - - - A
where M and A are the least squares slope and intercept, respectively, of
the analyzer's response to a multipoint calibration with propane after the
physical calibration with CH^.
Familiarization with the instrument is essential to obtain accurate
calibration and to avoid unnecessary adjustments that would waste calibration
gas mixtures and complicate the procedure.
Cylinders containing compressed gas mixtures of known concentrations of
hydrocarbons in air are used for calibration of the analyzer. These concen-
tration standards should be certified by the supplier to be traceable to NBS
Standard Reference Materials (SRM) or should be otherwise referenced to such
SRM's. NMOC concentrations are expressed in parts per million carbon (ppmC),
which is simply the volumetric concentration (ppmV) multiplied by the carbon
number (number of carbon atoms per molecule) of the hydrocarbon compound (see
example below).
Two separate hydrocarbon standards are generally needed — a CH.-in-air
standard for calibrating and matching the CH. and TOC responses, and a
propane-in-air standard to calibrate the NMOC response. As an example, the
following standards would be appropriate for a 0 to 10 ppmC scale range:
17
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Standard ppmV Carbon Number ppmC Used to Calibrate
methane in air 8 1 8 CH^, TOC response
propane in air 3 3 9 NMOC response
A single gas cylinder containing both methane and propane standard con-
centrations may be used for periodic span checks between calibrations, but
such a combined standard will not allow the channel balance to be checked or
adjusted. Furthermore, a two component mixture is usually more expensive
and may not be as accurate as separate hydrocarbon standards. The following
examples are appropriate for combined standards, if this procedure is chosen:
Compound ppmV Carbon Number ppmC
Subtracting Analyzer:
methane 8 1 8
propane 339
CH, channel response: 8
NMOC channel response: 9
Nonsubtractjng Analyzer:
methane 3 1 3
propane 236
Total 9
CH4 channel response: 3
TOC channel response: 9
All methane standards should be specified to have less than 0.1 ppmC total
of other hydrocarbons as impurities. Absence of hydrocarbon impurities is
18
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important for precise analyzer balance and accurate calibration; all methane
standards should be checked for impurities before use.
Calibration concentrations may be provided directly by gas cylinders
containing the appropriate concentration levels. For multi-point calibration,
a separate cylinder is needed for each concentration level.
Greater economy can be realized by obtaining calibration concentrations
by dilution, since many different concentration levels may be provided from
a single standard cylinder, and consumption of the standard is greatly
reduced. In this case, the standard should have a concentration level of
several hundred ppmC. An ample source of clean, hydrocarbon-free zero air
is, of course, required. The dilution system must have suitable means to
control and accurately measure the flow rates of the standard and the zero
air, and the two flows must be thoroughly mixed.
All calibration gases should be introduced into the analyzer at atmo-
spheric pressure through the sample inlet. This can be facilitated by
installing a ''tee" fitting between the analyzer sample inlet and the cali-
bration source, with one leg of the tee left open to the atmosphere as a
yent. The flow of calibration gas must exceed the flow demand of the
analyzer at all times, with the excess released at the atmospheric pressure
yent. This atmospheric vent flow should be about 20 to 50% of the analyzer
flow to assure adequate venting without excessive waste of calibration gas.
Additional guidance or more specific information on the operation of NMOC
analyzers may be obtained from EMSL, Research Triangle Park, NC by calling
(919) 541-3791 (FTS 629-3791) or (919) 541-2622 (FTS 629-2622).
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UNITED SIAHIS ENVIRONMENT 1. I'HOTLCTION AGLNCY
Office of Air Quality Pic n.imj and Standards
Research Triangle Park, N rth Carolina 27711
M';;.|l.( i. The Unreliability of Non-Methan,/ Hydrocarbon IMTK: i >> nnv -\o7r
Analyzers and its Impact on IIC/O>: Strategies y'J
i-KOM: c. J. Stei'jerwald, Director
Office of Air Quality Planning and Standards
TO: Roger Strclow, Assistant /vdministrator
for Air and V;aste Management
Surveillance and Analysis Division Directors, Regions
Air and Hazardous Materials Division Directors, Regions I-X
Recent studies with commercial non-methane hydrocarbon
(NMIIC) analyzers have established the fact that these
instruments yield unreliable data. Not only do instru-
ments from different manufacturers produce different results,
even instruments from the same manufacturer, with supposedly
the s£ime characteristics, yield data sometimes differing
by a factor of two. (For comparison, measurements made witli
different S02 instruments have a correlation coefficient
of better than O.G5). These studies were carried out by
i;PA laboratories as well as contractors, and the results
are thus thought to be conclusive.
Iii an attempt to identify the source of trouble, one of
the NERC/RTP laboratories is contracting for a 15 month
study of the NMIIC instrumental technique. At this time,
it js thought that the solution lies in rigid specification
of the design and construction of the NMIIC analyser as well
as a strJct protocol for its operation. The contractor will
.'submit his report about January 1977. In the meantime,
however, the consequences of these studies and the distant
solution cause EPA concern in the following areas:
1. The doubt cast on the Appendix J curve.
2. The enforced delay in possibility of developing area
specific upper limit 1IC/OX curves.
3. The validation of HC/0X models.
4. The lack of knowledge about true NMIJC concentrations
and their trends in urban areas.
All of these arc interrelated, of course. Accepting
the situation as it exists, KPA's position on these areas
of concern should be as follows:
EPA Form 1370-6 (Rr». 6-72)
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2
Any doubt which may arise <.:<>;icerninq the Appendix J curve
is misplaced . LJata used to construct Appendix J did not co-mo
from these instruments — rather, from total hydrocarbon measure-
ments, in general. Under any circumstances, there is an abun-
dance of evidence from many other experimental programs shpwing
a relation between ambient hydrocarbons and photochemical
oxidants. Thus, despite the acknowledged deficiencies in the
Appendix J curve, it should still be used where appropriate in
11C/C,. reduction strategies.
A better relation may exist between non-methane hydrocarbon
and ozone, but the data are not available. There is reason to
believe, too, that such a relation differs from one metropolitan
area to another. V.'c had hopes of cons true timj arca-r.pccif ic
.Appendix J-like curves; and using these to better define required
hydrocarbon ei.'.i ssion reductions for the various areas. V/c
believe the idea is still a cjood one, but we suggest delaying
its i mpj eiuen ta tion until we have reliable MH11C data from good
instruments.
iMost of our laboratory work and field studies on IIC/0,,
relations arc not affected by this discovery of the faulty
I-.'MliC instrumental method. Usually gas chromatographic procedures
were used which are accurate for specific hydrocarbons. It is
onJy v; lie IT ambient hydrocarbon measurements are made by the
IJHIIC technique that we lose accuracy.
As you know, MH11C measurements are not required from the
states at the present time. In forthcoming revisions to
40 CFR 01.17, we had considered requiring those metropolitan
areas where ozone concentrations are estimated to be above the
N/\/K.i!j in 1977 to begin monitoring for Ni'iilC. This requirement
has now been deleted from the draft regulation but will be
reconsidered at the appropriate time.
It is our belief that the reference method for M-iliC,
detailed in <10 CFK 130.10 7\ppendix E, doer, not need to be
rescinded at this time, however, both because it never had
the force of being a required procedure for a criteria pollu-
tant and also because the basic procedure may still be valid.
'The specifications may just need to be Lightened up. OnJy
after the i:j;KC/KTP experimental program has been completed
will we knew whether it is necessary.
For those agencies which already have NfMlC anoly/ers,
it is ucbatabJe whether or not _thei.r use should be continued.
I'erh.ips "Hi-,.' "trend data would be interes t.i ng . However, it
is J mi rob.ib] e that past or present values have the required
accuracy for any absolute moaning at this time. On the
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other hand, Lliir; is not to say 'hat the .1 MS truments should
be junked. Depending on what j.:; i'ound within the next few
months, it may be possible to modify present instruments to
make their measurements meaningful. However, we certainly
cannot encourage the purchase of new NMIIC analyzers at this
time .
This memo has addressed only the subject of ambient NMIIC
analyses. Neither mobile source testing nor stationary source
testing is affected by this discovery of unreliable data from
these instruments since other analytical methods arc used.
In summary, because of design differences between various
NM1IC analyzers, data from these instruments are unreliable.
The questioned accuracy of the data obtained from such instru-
ments should in no v:ay discredit the belief that hydrocarbons
arc a major factor in the generation of photochemical oxidants.
Irradiation chamber studies, as well as ambient measurements
using gas chromatographic techniques, which do provide accurate
hydrocarbon data, have documented the role of hydrocarbons
in smog reactions.
cc: D. Dorchers
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TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1. REPORT NO.
EPA-450M-8Q-011
2.
3. RECIPIENT'S ACCESSION NO.
4. TITLE AND SUBTITLE Guidance for Collection of Ambient Non-
methane Organic Compound Data for Use In 1982 SIP Devel
opment, and Network Design and Siting Criteria for the
NMOC and NOx Monitors
5. REPORT DATE
6. PERFORMING ORGANIZATION CODE
7. AUTHOR(S)
8. PERFORMING ORGANIZATION REPORT NO.
9. PERFORMING ORGANIZATION NAME AND ADDRESS
Monitoring and Data Analysis Division
Office of Air Quality Planning and Standards
US Environmental Protection Agency
Research Triangle Park, NC 27711
10. PROGRAM ELEMENT NO.
11. CONTRACT/GRANT NO.
12. SPONSORING AGENCY NAME AND ADDRESS
13. TYPE OF REPORT AND PERIOD COVERED
14. SPONSORING AGENCY CODE
15. SUPPLEMENTARY NOTES
Project Officer; Dr. Harold G. Richter
16. ABSTRACT
Guidance is given on the selection, siting and use of NMOC monitoring
instruments for use in preparing 1982 Ozone SIPs. Some of the commercially available
NMOC continuous monitors can provide data useful for modeling and for development of
NMOC abatement strategies, if they are carefully maintained and calibrated.
Collection of grab samples of ambient air for subsequent analysis by GC methods may be
needed if a photochemical model is to be used, but this may be better done by a
contractor.
17.
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
b.lDENTIFIERS/OPEN ENDED TERMS C. COSATI Field/Group
NMOC Monitoring Strategies
NMOC Monitoring
1982 SIP Development
18. DISTRIBUTION STATEMENT
19. SECURITY CLASS (This Report)
21. NO. OF PAGES
25
20. SECURITY CLASS (Thispage/
22. PRICE
EPA Form 2220-1 (Rev. 4-77) PREVIOUS EDITION is OBSOLETE
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