Refining fire emissions for air quality modeling with remotely sensed fire counts: A wildfire case study

Roy, Biswadev; Pouliot, George; Gilliland, Alice; Pierce, T.E.; Howard, Steven C.; Bhave, Prakash V.; Benjey, William

doi:10.1016/j.atmosenv.2006.08.037

Cited by 20 publications

(18 citation statements)

References 14 publications

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“…This perturbation function is then applied to GFEDv2 emissions to obtain daily estimated emissions without altering monthly emissions, similar to the approach used by Heald et al [2003]. This approach has been demonstrated to improve the accuracy of atmospheric simulations as opposed to using monthly averaged emissions [ Hyer et al , 2007; Roy et al , 2007]. Biomass burning data at 1° × 1° resolution are smoothed with a 7 day moving average to reduce the effect of a periodic bias associated with the polar orbit of MODIS [ Heald et al , 2003] and are regridded onto the 2° × 2.5° UMD‐CTM grid.…”

Section: Model Descriptionmentioning

confidence: 99%

The impact of North American anthropogenic emissions and lightning on long-range transport of trace gases and their export from the continent during summers 2002 and 2004

Martini¹,

Allen²,

Pickering³

et al. 2011

J. Geophys. Res.

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Section: Model Descriptionmentioning

confidence: 99%

The impact of North American anthropogenic emissions and lightning on long-range transport of trace gases and their export from the continent during summers 2002 and 2004

Martini¹,

Allen²,

Pickering³

et al. 2011

J. Geophys. Res.

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“…Emissions of O 3 precursors (VOCs and NO x ) from wildfires are highly variable and depend on the fuel and fire conditions with average molar VOCs/NO x ratios from 15 for savannahs to 150 for boreal forests (Akagi et al, 2011). Furthermore, the chemistry of VOCs/ NO x irradiated mixtures is non-linear and challenging to describe due to large number of VOCs and high emissions uncertainties (Roy et al, 2006). However, the variability in net O 3 production caused by fire emissions and photochemistry is reduced as plumes travel away from the fire due to transformations of NO x to PAN and VOCs to alkyl (R), alkoxy (RO) and alkylperoxy radicals (RO 2 ) within a few hours and vertical/horizontal mixing.…”

Section: Limitations Of Methodologymentioning

confidence: 99%

Assessment of the Contribution of Wildfires to Ozone Concentrations in the Central US-Mexico Border Region

Chalbot

Kavouras

DuBois

2013

Aerosol Air Qual. Res.

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The annual trends and spatiotemporal patterns of monthly 8-hour maximum ozone (8-hr max O 3 ) concentrations in the Paso del Norte region were analyzed, and their associations with fires were examined for the 2001-2010 period. Hourly O 3 measurements were retrieved from the Environmental Protection Agency (EPA) Air Quality System, while the times and locations of fires were acquired from the MODIS fire detection module. The absolute 8-hr max O 3 concentrations were comparable in urban, rural and background sites. Time series analysis of deseasonalized monthly 8-hr max O 3 levels showed statistically significant declining trends for most of the sites located in populated areas, and high correlation coefficients among these. Conversely, a 0.12 ppbv/yr increase of 8-hr max O 3 concentration was computed for Chiricahua, a background site located in a Class I protected area. Strong relationships between the monthly 8-hr max O 3 concentrations and categorical variables representing the number of fire detections for each month in six buffer zones were computed. Fire incidents near the sites (within 400 km) in central Arizona, central Texas and western Mexico triggered a decrease in the 8-hr max O 3 concentration by 1 to 12 ppbv in urban and rural sites, and an increase of 3 ppbv in Chiricahua. Conversely, fire incidents in southeast US, Cuba and central Mexico contributed from 5 up to 19 ppbv. These findings indicated that regional fire incidents may trigger high O 3 episodes, which may exceed air quality standards.

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“…Some studies [10,44] indicated that the poor temporally-allocated wildfire emissions may contribute to the biases in OC and EC predictions. Several studies based on 1999 NEI v3 indicated underestimation in wildfire emissions [8,45]. The emissions of EC and POA from the 2002 NEI v3 are much lower than those from the 1999 v3, particularly in the western US, indicating a possible underestimation in wildfire emissions to a greater extent than the 1999 v3 in this region, due likely to the use of older fuel loading information (George Pouliot, US EPA, personal communication, 2011).…”

Section: Elemental and Organic Carbon As Shown In Figures 3(g)-(h)mentioning

confidence: 99%

Application, Evaluation, and Process Analysis of the US EPA’s 2002 Multiple-Pollutant Air Quality Modeling Platform

Wang¹,

Zhang²

2012

ACS

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A multiple-pollutant version of CMAQ v4.6 (i.e., CMAQ-MP) has been applied by the US EPA over continental US in 2002 to demonstrate the model's capability in reproducing the long-term trends of ambient criteria and hazardous air pollutants (CAPs and HAPs, respectively) in support of regulatory analysis for air quality management. In this study, a comprehensive model performance evaluation for the full year of 2002 is performed for the first time for CMAQ-MP using the surface networks and satellite measurements. CMAQ-MP shows a comparable and improved performance for most CAPs species as compared to an older version of CMAQ that did not treat HAPs and used older versions of national emission inventories. CMAQ-MP generally gives better performance for CAPs than for HAPs. Max 8-h ozone (O 3 ) mixing ratios are well reproduced in the O 3 season. The seasonal-mean performance is fairly good for fine particulate matter (PM 2.5 ), sulfate , and mercury (Hg) wet deposition and worse for other CAPs and HAPs species.The reasons for the model biases may be attributed to uncertainties in emissions for some species (e.g., ammonia (NH 3 ), elemental carbon (EC), primary organic aerosol (POA), HAPs), gas/aerosol chemistry treatments (e.g., secondary organic aerosol formation, meteorology (e.g., overestimate in summer precipitation), measurements (e.g.,, and the use of a coarse grid resolution. CMAQ cannot well reproduce spatial and seasonal variations of column variables except for nitrogen dioxide (NO 2 ) and the ratio of column mass of HCHO/NO 2 . Possible reasons include inaccurate seasonal allocation or underestimation of emissions, inaccurate BCONs at higher altitudes, lack of model treatments such as mineral dust or plume-in-grid process, and limitations and errors in satellite data retrievals. The process analysis results show that in addition to transport, gas chemistry or aerosol/emissions play the most important roles for O 3 or PM 2.5 , respectively. For most HAPs, emissions are important sources and cloud processes are a major sink. Simulated 2 2 3 H O HNO P P and HCHO/NO 2 indicate VOC-limited chemistry in major urban areas throughout the year and in other non-urban areas in winter, but NO X -limited chemistry in most areas in summer.

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Refining fire emissions for air quality modeling with remotely sensed fire counts: A wildfire case study

Cited by 20 publications

References 14 publications

The impact of North American anthropogenic emissions and lightning on long-range transport of trace gases and their export from the continent during summers 2002 and 2004

The impact of North American anthropogenic emissions and lightning on long-range transport of trace gases and their export from the continent during summers 2002 and 2004

Assessment of the Contribution of Wildfires to Ozone Concentrations in the Central US-Mexico Border Region

Application, Evaluation, and Process Analysis of the US EPA’s 2002 Multiple-Pollutant Air Quality Modeling Platform

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