Future-Year Ozone Isopleths for South Coast, San Joaquin Valley, and Maryland
1
Toyota Motor Engineering and Manufacturing North America, Inc., Ann Arbor, MI 48105, USA
2
Toyota Motor Corporation, Shizuoka 410-1198, Japan
3
Ramboll U.S. Corporation, Novato, CA 94998, USA
*
Author to whom correspondence should be addressed.
Atmosphere 2018, 9(9), 354; https://doi.org/10.3390/atmos9090354
Submission received: 24 August 2018
/
Revised: 11 September 2018
/
Accepted: 12 September 2018
/
Published: 14 September 2018
(This article belongs to the Special Issue Air Quality Prediction)
Abstract
:Many areas of the United States are working toward achieving the 2015 ozone National Ambient Air Quality Standard (NAAQS) attainment level. The objective of this study was to develop future-year (2030) volatile organic compounds and nitrogen oxides (VOC-NOx) isopleth diagrams of the 4th highest maximum daily 8-h average ozone design value concentrations at monitors of interest in the South Coast Air Basin (SoCAB) and San Joaquin Valley (SJV) in California, and in Maryland. The simulation results showed there would be attainment of the 2015 ozone NAAQS in 2030 without further controls at the selected monitors: 27% in SoCAB, 57% in SJV, and 100% in Maryland. The SoCAB ozone isopleths developed in this study were compared with those reported in the South Coast Air Quality Management District 2016 Air Quality Management Plan. There are several differences between the two modeling studies, the results are qualitatively similar for most of the monitors in the relative amounts of additional emission reductions needed to achieve the ozone NAAQS. The results of this study provide insight into designing potential control strategies for ozone attainment in future years for areas currently in non-attainment. Additional photochemical modeling using these strategies can then provide confirmation of the effectiveness of the controls.
1. Introduction
Many areas of the United States (U.S.) are trying to achieve the current National Ambient Air Quality Standards (NAAQS) attainment level for ozone. Ozone formation is linked to emissions of volatile organic compounds (VOCs) and nitrogen oxides (NOx) [1]. The chemistry leading to ozone production from emissions of VOC and NOx is non-linear [2]. Contour plots of ozone versus NOx and VOC emissions (ozone isopleths) are often employed to illustrate the non-linear response of ozone levels to NOx and VOC changes, and have been used in the past in the empirical kinetic modeling approach (EKMA) developed by the U.S. Environmental Protection Agency (EPA) to develop control strategies for ozone reduction [3]. Thus, the isopleths of ozone versus VOC and NOx emissions are often referred to as EKMA diagrams. The EKMA generates ozone isopleths for specific monitors in a city. Once the maximum measured ozone concentration at a monitor has been identified, the VOC and NOx reductions needed to achieve the NAAQS level are determined using the EKMA from the distance along the VOC and NOx axes to the isopleth that represents the desired peak ozone concentration mandated by the NAAQS. The abundance of VOCs relative to NOx is characterized by the VOC/NOx ratio. The VOC/NOx ratio is important in the behavior of the VOC-NOx-ozone system and has a major effect on how reductions in VOC and NOx affect ozone concentrations [4].
While the EKMA for regulatory planning has been superseded by photochemical grid modeling, the ozone isopleths are useful for understanding how ozone levels at a particular location may respond to reductions in NOx, VOC, or both. The objective of this study was to develop future-year (2030) VOC-NOx isopleth diagrams of the 4th highest maximum daily 8-h average (H4MDA8) ozone design value concentrations (DVC) at monitors of interest in the South Coast Air Basin (SoCAB) and San Joaquin Valley (SJV) in California, and in Maryland. These areas were selected to illustrate contrasting current ozone classification levels: SoCAB and SJV at extreme or severe [5], and Maryland at moderate or marginal [6]. Regions where ozone production is limited by the presence of nitrogen oxides or hydrocarbons are readily apparent in such a diagram [7]. The Comprehensive Air Quality Model with Extensions (CAMx) version 6.4 [8] is the latest version of the photochemical grid model (PGM) and was used to conduct several brute force scenarios. The CAMx allows for integrated “one-atmosphere” assessments of tropospheric air pollution (ozone, particulates, air toxics) over spatial scales ranging from neighborhoods to continents. It is a “state-of-the-science” open-source system that is computationally efficient, flexible, and publicly available. Meteorological fields are supplied to the CAMx from separate, commonly used weather prediction models such as the Weather Research and Forecasting (WRF) model. All emission inputs are supplied from external pre-processing systems. The CAMx simulates the emission, dispersion, chemical reaction, and removal of pollutants by marching the Eulerian continuity equation forward in time for each chemical species in a system of nested three-dimensional grids. The ozone isopleths developed in this study using the CAMx were compared with the South Coast Air Quality Management District (SCAQMD) 2016 Air Quality Management Plan (AQMP) [9] isopleths, which were generated with the U.S. EPA photochemical grid model, the Community Multiscale Air Quality (CMAQ) [10,11].
2. Method
In previous modeling studies, Collet et al. [12,13] simulated the entire contiguous U.S. (continental U.S. or CONUS) domain (396 vertical by 246 horizontal grid cells) at 12-km resolution with the CAMx 6.4. For this study, a different approach was adopted because the development of ozone isopleths relating ozone responses to NOx and VOC emissions changes required several tens of emissions scenario simulations to be conducted. This approach, referred to as brute force sensitivity analyses, is impractical for the large CONUS domain, since it is time- and resource-intensive. Since the objective of this study was to develop ozone isopleth diagrams for specific sub-regions of the country, sub-regional CAMx simulations were conducted to achieve the study objective. Specifically, the emissions scenario simulations were conducted for two subdomains using 12 km by 12 km grid resolution, one in the Western U.S. and the second in the Eastern U.S.
Figure 1 shows the two subdomains within the outer CONUS domain. The western subdomain (66 vertical by 105 horizontal grid cells) covers most of California and includes the SoCAB and SJV, while the eastern subdomain (40 vertical by 29 horizontal grid cells) covers Maryland and portions of the surrounding states.
The existing CAMx modeling databases used by Collet et al. [13] were developed for the CONUS domain. For that study, the 2025 CMAQ-ready emissions provided by the EPA were used for the future-year (2030) emissions. Future-year emissions from the natural source categories were assumed to be the same as the 2011 base-year emissions. The 2030 emissions for all anthropogenic source categories, except on-road mobile sources, were assumed to be the same as the EPA’s 2025 emissions case. The on-road mobile emissions for 2030 were developed using MOVES 2014 and the California Air Resources Board’s (CARB) EMFAC2014 models. It was necessary to develop new inputs for the two subdomains shown in Figure 1. The inputs for this study consist of the following: meteorology, emissions, land use, ozone column and photolysis rates, and boundary conditions. The gridded subdomain meteorological fields and land use data were developed by extracting (“windowing”) the subdomain data from the corresponding CONUS files. Ozone column and photolysis rate data were developed as new inputs for the subdomains. Boundary conditions for the subdomains were developed by first conducting base-year (2011) and future-year (2030) CONUS domain simulations in which the 3-dimensional (3-D) concentration outputs were saved, and then windowing these outputs for the subdomains.
The 2030 future-year emissions for the CONUS domain from the Collet et al. [13] study were windowed for the two subdomains in the Western and Eastern U.S. In that study, the 2030 future-year emissions were based on the 2025 projected emissions from the EPA 2011v6.2 platform and 2030 on-road mobile emissions generated using the latest on-road emission models. To perform the emission scenario simulations required for generating the ozone isopleths, the emissions within the sub-regions of interest (the two air basins in the western subdomain and the state of Maryland in the eastern subdomain) were adjusted. These adjustments were made using cell masks created by ArcGIS [14] that only mark the cells within the two air basins and the Maryland state boundary. A set of reduction factors (20%, 40%, 60%, and 80%) was applied to emissions of NOx (NO, NO2, HONO), anthropogenic VOCs (i.e., excluding isoprene, monoterpene, and sesquiterpene emissions), and CO in grid cells identified by the cell masks, resulting in a total of 25 emission scenarios, including the base emission scenario (0% reduction), for each subdomain.
The air quality modeling was conducted using the most recent version (6.4) of the CAMx with the CB6r4 chemical mechanism. The base-year (2011) and future-year (2030) simulations for the CONUS domain were conducted with the CAMx to develop boundary conditions for the 2011 and 2030 subdomain simulations. A 10-day spin-up period was used for the two CONUS domain simulations.
A total of 52 CAMx simulations were conducted for the ozone season (1 May to 30 September) for the two subdomains. These simulations consisted of a base-year simulation and 25 future-year simulations for each of the two subdomains. The base-year results are required to calculate future-year ozone design values for the California air basins and the state of Maryland using EPA’s Modeled Attainment Test Software (MATS). The base-year subdomain simulations and the future-year subdomain simulations used a 5-day period for spin-up. The 25 future-year emission scenario calculations correspond to a 5 by 5 matrix of future-year emissions (20%, 40%, 60%, 80%, and 100% NOx emissions by 20%, 40%, 60%, 80%, and 100% VOC and CO emissions).
3. Results
Following EPA guidance, the outputs of the base-year and future-year subdomain simulations were processed using EPA’s MATS to project future-year design values (DVF) at monitoring locations of interest. Briefly, the modeling results are used in a relative sense to scale observed site-specific 8-h ozone concentrations for current-year design values (DVC) based on the relative changes in the modeled 8-h ozone concentrations between the current and future years. The model-derived scaling factors are called relative response factors (RRFs), and are based on the relative changes in the modeling results between the current-year (2011) base case and the future-year (2030) emission scenarios. This is the recommended regulatory approach to determine future-year ozone design values, and is based on the assumption that the model can predict ozone responses to changes in emissions more accurately than it can predict absolute ozone concentrations.
Table 1 and Table 2 show the ozone NAAQS attainment status (70 ppb H4MDA8) for the three study areas without any additional controls. Table 1 provides the list of monitors in the two California air basins and state of Maryland where future-year ozone design values were calculated using the air quality modeling results and MATS, and the future-year ozone design values at these monitors. Table 2 quantifies the number of monitors in Table 1 which are in or not in attainment.
A matrix of 25 (5 × 5) future-year emission scenarios for each subdomain provides 25 future-year ozone design values at the selected monitors as a function of NOx and VOC emissions in the air basins of interest. This is a relatively coarse resolution, so it is necessary to use an interpolation technique, such as kriging, to obtain smooth contours of the ozone design values (ozone isopleths). Kriging is an advanced geostatistical procedure that generates an estimated surface from a scattered set of points. Although kriging was developed originally for applications in geostatistics, it is a general method of statistical interpolation that can be applied within any discipline to sampled data from random fields. It differs from simpler interpolation methods in that it uses the spatial correlation between sampled points to interpolate the values in the spatial field. Kriging has been used in other studies to develop ozone response surfaces [15,16]. PyKrige, a Python kriging library, was used for this purpose in the present study. The interpolation was performed using ordinary kriging, which is the most commonly used kriging algorithm and produces interpolation values by relying on an unknown mean value, allowing local influences due to nearby neighboring values. The original 5 × 5 matrix of values were interpolated to 81 × 81 data points, representing reductions in anthropogenic emissions in the California air basins and state of Maryland in increments of 1% from 0% to 80%. Standard Python libraries were then used to prepare the ozone isopleths.
Ozone isopleths (“EKMA diagrams”) for the selected monitors in the South Coast Air Basin are shown in Figure 2, while Figure 3 shows ozone isopleths for selected monitors in Fresno and Tulare, CA, and the state of Maryland. The x-axis shows the VOC anthropogenic emissions, and the y-axis the NOx anthropogenic emissions. Thus, the y-axis and x-axis represent anthropogenic emissions ranging from 20% to 100% of the base future-year air basin anthropogenic emissions (i.e., each tick mark represents 20%). Therefore, the 2030 DVF is at the 100% NOx and 100% VOC point, in the top right corner of the diagram. The color scheme for the ozone design values ranges from dark brown (85 ppb and higher) to dark blue (55 ppb and lower). The light blue region represents a level of about 70 ppb and provides a measure of the reductions in NOx and/or VOC required to reach attainment at a specific monitor.
4. Discussion
Table 3 provides the future-year projected NOx and VOC emission totals for the non-attainment areas, and the estimated NOx or VOC emission levels needed to attain the standards in tons/day and as a reduction percentage of the base future-year emissions. In the SoCAB, 3 of the 11 monitors (West Los Angeles, Los Angeles-North Main, and Anaheim) showed attainment of the 2015 ozone NAAQS level at projected 2030 SoCAB anthropogenic emissions without further controls. Table 3 shows that monitors in Glendora and Pasadena could meet the NAAQS with NOx or VOC reductions, while on a percentage basis, less NOx reductions are required than VOC reductions. Moving eastward in the SoCAB, VOC reductions to 80% will not reduce ozone to the NAAQS level. In Riverside, NOx reductions are projected to bring the area into compliance. The northwest and most eastern areas of the SoCAB (i.e., Santa Clarita, Reseda, Crestline, and San Bernardino) are not projected to achieve compliance with 80% NOx or VOC anthropogenic reductions. In the SJV area, four of seven monitors show attainment of the 2015 NAAQS level at projected 2030 anthropogenic emissions without further controls. To achieve attainment at the two monitors projecting non-attainment in the SJV (Fresno and Tulare), NOx reductions would be effective, while VOC reductions would not be useful. At all the Maryland monitors, future-year ozone levels are in attainment of the 2015 NAAQS level without further controls. The Maryland area is sensitive to changes in NOx and shows little to no sensitivity to VOC changes.
To compare this study’s ozone isopleths to those reported in the SCAQMD 2016 AQMP [9], the modeling platform and domain are shown in Table 4 for both studies.
Table 5 compares the additional reductions in future-year emission required to achieve attainment from the SCAQMD AQMP isopleths for 2031 and the 2030 isopleths from this study. For most of the monitors, the difference in the amount of NOx or VOC (in tons/day or percent reduction) needed to achieve the ozone NAAQS level from the two sets of isopleths is within +25%. The SCAQMD AQMP isopleths show more NOx-limited trends than the present study, possibly due to differences between the inputs and models used in the two studies (see Table 4).
5. Conclusions
This study developed future-year (2030) VOC-NOx isopleths of H4MDA8 ozone design values at selected monitors in the SoCAB and SJV in California, and Maryland. Photochemical grid modeling for a large number of VOC and NOx emission reduction scenarios (from 0% to 80%) were conducted to develop the isopleths of ozone design values versus VOC and NOx emissions in each region. The latest version of the photochemical grid model, CAMx 6.4, was used in this modeling study.
The modeling results showed that only 27% of the selected monitors in the SoCAB would reach attainment of the 2015 ozone NAAQS level in 2030 without further controls. In the SJV, 57% of the monitors would reach attainment without further controls. All monitors in Maryland were projected to reach attainment of the 2015 ozone NAAQS level in 2030 at base projected emission levels. The ozone isopleths for the SoCAB and SJV were used to determine the amount of additional controls that would be required to attain the standards in 2030. This analysis showed that the areas in the western and central portions of the basins could achieve attainment with NOx or VOC reductions or a combination of both, while areas between the central and eastern locations could achieve attainment with NOx reductions, but VOC reductions are not useful. Monitors in the northwest and easternmost areas of the SoCAB are not predicted to achieve attainment with an additional 80%-reduction in future-year anthropogenic NOx or VOC. In the SJV, additional NOx reductions are effective in achieving attainment at the two monitors projected to be in non-attainment in 2030, while VOC reductions are not effective. The Maryland area is sensitive to changes in NOx and shows little to no sensitivity to VOC changes, but all monitors are projected to be in attainment without further controls in 2030.
The SoCAB ozone isopleths developed in this study were compared with those reported in the SCAQMD 2016 AQMP. While there are several differences between the two modeling studies, the results are qualitatively similar (within +25%) for most of the monitors in the relative amounts of additional NOx and/or VOC reductions needed to achieve the ozone NAAQS level. This study shows that monitors in five areas will not attain the 70 ppb NAAQS with up to 80% reductions in NOx or VOC, while the SCAQMD isopleths show that NOx controls are effective in bringing these areas into attainment.
The results from this study provide insight into designing potential control strategies for ozone attainment in future years in areas currently in non-attainment. Additional photochemical modeling using these strategies can then provide confirmation of the effectiveness of the controls.
Author Contributions
Conceptualization: S.C., T.K., P.K., and T.S.; Formal analysis: T.K., P.K., and T.S.; Investigation: T.K., P.K., and T.S.; Methodology: T.K., P.K., and T.S.; Project administration: S.C. and P.K.; Software: P.K.; Validation: T.K., P.K., and T.S.; Visualization: S.C. and T.K.; Writing—original draft: S.C.; Writing—review & editing: T.K., P.K., and T.S.
Funding
This research received no external funding.
Conflicts of Interest
The authors declare no conflict of interest.
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Figure 1.
Western (blue outline) and eastern (red outline) subdomains within the 12-km resolution continental U.S. (CONUS) domain.
Figure 1.
Western (blue outline) and eastern (red outline) subdomains within the 12-km resolution continental U.S. (CONUS) domain.
Figure 2.
Future-year ozone design value isopleths (ppb) for monitors in the South Coast Air Basin (SoCAB): (a) Glendora, (b) Los Angeles-North Main, (c) Pasadena, (d) Anaheim, (e) Banning, and (f) Crestline.
Figure 2.
Future-year ozone design value isopleths (ppb) for monitors in the South Coast Air Basin (SoCAB): (a) Glendora, (b) Los Angeles-North Main, (c) Pasadena, (d) Anaheim, (e) Banning, and (f) Crestline.
Figure 3.
Future-year ozone design value isopleths (ppb) for monitors in (a) Fresno, CA; (b) Tulare, CA; (c) Baltimore, MD; and (d) Anne Arundel, MD.
Figure 3.
Future-year ozone design value isopleths (ppb) for monitors in (a) Fresno, CA; (b) Tulare, CA; (c) Baltimore, MD; and (d) Anne Arundel, MD.
Table 1.
List of monitoring sites selected for analysis and future-year design values (DVF) at these sites.
Table 1.
List of monitoring sites selected for analysis and future-year design values (DVF) at these sites.
| Air Basin | Monitor ID | Monitor Name | 2030 DVF (ppb) |
|---|---|---|---|
| SoCAB | Los Angeles_0016 | Glendora-Laurel | 83.4 |
| SoCAB | Los Angeles_0113 | West Los Angeles-VA Hospital | 58.7 |
| SoCAB | Los Angeles_1103 | Los Angeles-North Main Street | 58 |
| SoCAB | Los Angeles_2005 | Pasadena-S Wilson Avenue | 70.7 |
| SoCAB | Los Angeles_6012 | Santa Clarita | 84.3 |
| SoCAB | Orange_0007 | Anaheim | 58.6 |
| SoCAB | Riverside_0012 | Banning Airport | 82.8 |
| SoCAB | Riverside_6001 | Perris | 78.2 |
| SoCAB | San Bernardino_0005 | Crestline | 94.8 |
| SoCAB | San Bernardino_1004 | Upland | 85.7 |
| SoCAB | San Bernardino_2002 | Fontana-Arrow Highway | 89.1 |
| SJV | Fresno_5001 | Clovis-N Villa Avenue | 76.3 |
| SJV | Kern_0232 | Oildale-3311 Manor Street | 70.2 |
| SJV | Merced_0003 | Merced-S Coffee Avenue | 67.3 |
| SJV | San Joaquin_1002 | Stockton-Hazelton Street | 57.8 |
| SJV | Stanislaus_0005 | Modesto-14th Street | 63.4 |
| SJV | Tulare_0009 | Sequoia and Kings Canyon Natl Park | 78.4 |
| MD | Cecil_0003 | Fair Hill Natural Resource Management Area | 60.5 |
| MD | Harford_1001 | Edgewood | 68.1 |
| MD | Baltimore_1007 | Padonia | 60.7 |
| MD | Frederick_0037 | Frederick Airport | 59.4 |
| MD | Anne Arundel_0014 | Davidsonville | 58.2 |
| MD | Calvert_0011 | Calvert | 58.5 |
Table 2.
Number of DVF attainment areas in the monitoring sites selected for analysis.
| Total Listed | DVF in Attainment | DVF Non-Attainment | |
|---|---|---|---|
| Number (%) | Number (%) | ||
| South Coast Air Basin (SoCAB) | 11 | 3 (27%) | 8 (73%) |
| San Joaquin Valley (SJV) | 7 | 4 (57%) | 3 (43%) |
| Maryland State (MD) | 6 | 6 (100%) | 0 |
Table 3.
List of non-attainment area monitoring sites in relation to future-year ozone design values at the projected NOx and VOC levels, and NOx or VOC level needed in tons/day and as a percentage of reduction to attain 70 ppb 4th highest maximum daily 8-h average (H4MDA8).
Table 3.
List of non-attainment area monitoring sites in relation to future-year ozone design values at the projected NOx and VOC levels, and NOx or VOC level needed in tons/day and as a percentage of reduction to attain 70 ppb 4th highest maximum daily 8-h average (H4MDA8).
| NOx | VOC | |||||
|---|---|---|---|---|---|---|
| 2030 (Tons/Day) | 70 ppb Ozone Attainment (Tons/Day) | % Reduction | 2030 (Tons/Day) | 70 ppb Ozone Attainment (Tons/Day) | % Reduction | |
| Los Angeles_0016, Glendora | 264.3 | 85 | 68% | 357 | 82 | 77% |
| Los Angeles_2005, Pasadena | 264.3 | 200 | 24% | 357 | 300 | 16% |
| Riverside_0012, Banning | 264.3 | 111 | 58% | 357 | NA | |
| San Bernardino_0005, Crestline | 264.3 | NA | 357 | NA | ||
| Fresno_5001 | 153.6 | 90 | 41% | 541.7 | NA | |
| Tulare_0009 | 153.6 | 100 | 35% | 541.7 | NA | |
Table 4.
Numerical modeling platforms and domains for 2016 Air Quality Management Plan (AQMP) and this study.
Table 4.
Numerical modeling platforms and domains for 2016 Air Quality Management Plan (AQMP) and this study.
| 2016 AQMP | Present Study | |
|---|---|---|
| Modeling Base Year | 2012 | 2011 |
| Future Year | 2031 | 2030 |
| Time Frame | May 1–30 September | 1 May–30 September |
| Chemical Transport Model | CMAQ version 5.0.2 SAPRC07 with version “c” toluene updates | CAMx 6.4 with CB6r4 |
| Meteorological Model | WRF version 3.6 with updated land use | 2011 WRF |
| Spin-up | 5 days | 10 days |
| On-Road Emission | EMFAC2014 | EMFAC2014 |
| Off-Road Emission | Single package Category Specific Calculation | MOVES2014 |
| Modeling Domain | Grid: 154 by 102 624 km by 408 km | Grid: 66 by 105 792 km by 1260 km |
| Grid Resolution | 4 km by 4 km | 12 km by 12 km |
| Vertical Grid | 18 layers with 14 layers below 2000 m agl and 50 hPa as top boundary | 25 vertical layers (layer-collapsed from 35 WRF layers) |
| Boundary Conditions | Model for Ozone and Related Chemical Tracers (MOZART) | 36 km from GEOS-Chem simulation |
Table 5.
NOx and VOC levels required to achieve future-year (2030 for this study and 2031 for the AQMP) 70 ppb ozone design values at various monitors in the SoCAB. The monitor groups are ordered from east to west with monitors in each group ordered from north to south. NA means not achievable. For this paper, the two studies are considered similar when the differences between the reductions required to achieve attainment are within +25%.
Table 5.
NOx and VOC levels required to achieve future-year (2030 for this study and 2031 for the AQMP) 70 ppb ozone design values at various monitors in the SoCAB. The monitor groups are ordered from east to west with monitors in each group ordered from north to south. NA means not achievable. For this paper, the two studies are considered similar when the differences between the reductions required to achieve attainment are within +25%.
| NOx | VOC | |||||
|---|---|---|---|---|---|---|
| Tons/Day (% Reduction) | Tons/Day (% Reduction) | |||||
| Present Study | AQMP | Similar | Present Study | AQMP | Similar | |
| Base (tons/day) | 264 | 214 | Yes | 357 | 362 | Yes |
| Santa Clarita | NA | 130 (39%) | No | NA | NA | Yes |
| Reseda | NA | 160 (25%) | No | NA | 7 (98%) | Yes |
| West Los Angeles-VA Hospital | Attainment | Attainment | Yes | Attainment | Attainment | Yes |
| Los Angeles-North Main Street | Attainment | Attainment | Yes | Attainment | Attainment | Yes |
| Pico Rivera | Attainment | Attainment | Yes | Attainment | Attainment | Yes |
| Azusa | 211 (20%) | 150 (30%) | Yes | 325 (9%) | 200 (45%) | No |
| Glendora-Laurel | 85 (68%) | 83 (61%) | Yes | 102 (71%) | NA | No |
| Pomona | 150 (43%) | 110 (49%) | Yes | 234 (34%) | 90 (75%) | No |
| La Habra | Attainment | Attainment | Yes | Attainment | Attainment | Yes |
| Anaheim | Attainment | Attainment | Yes | Attainment | Attainment | Yes |
| Upland | 56 (79%) | 88 (59%) | Yes | NA | NA | Yes |
| Fontana-Arrow Hwy | NA | 80 (63%) | No | NA | NA | Yes |
| Riverside | 80 (70%) | 100 (53%) | Yes | NA | NA | Yes |
| Mira Loma | - | 124 (42%) | - | - | 40 (89%) | - |
| Lake Elsinore | 200 (24%) | 212 (1%) | Yes | 180 (50%) | 258 (29%) | Yes |
| Mission Viejo | Attainment | Attainment | Yes | Attainment | Attainment | Yes |
| Crestline | NA | 90 (58%) | No | NA | NA | Yes |
| San Bernardino | 75 (72%) | 108 (50%) | Yes | NA | NA | Yes |
| Redlands | NA | 85 (60%) | No | NA | NA | Yes |
| Banning | 111 (58%) | 104 (51%) | Yes | NA | NA | Yes |
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Collet, S.; Kidokoro, T.; Karamchandani, P.; Shah, T. Future-Year Ozone Isopleths for South Coast, San Joaquin Valley, and Maryland. Atmosphere 2018, 9, 354. https://doi.org/10.3390/atmos9090354
AMA Style
Collet S, Kidokoro T, Karamchandani P, Shah T. Future-Year Ozone Isopleths for South Coast, San Joaquin Valley, and Maryland. Atmosphere. 2018; 9(9):354. https://doi.org/10.3390/atmos9090354
Chicago/Turabian StyleCollet, Susan, Toru Kidokoro, Prakash Karamchandani, and Tejas Shah. 2018. "Future-Year Ozone Isopleths for South Coast, San Joaquin Valley, and Maryland" Atmosphere 9, no. 9: 354. https://doi.org/10.3390/atmos9090354
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