Light-absorbing organic carbon (OC), also termed brown carbon (BrC), from laboratory-based biomass burning (BB) has been studied intensively to understand the contribution of BB to radiative forcing. However, relatively few measurements have been conducted on field-based BB and even fewer measurements have examined BrC from anthropogenic combustion sources like motor vehicle emissions. In this work, the light absorption of methanol-extractable OC from prescribed and laboratory BB and gasoline vehicle emissions was examined using spectrophotometry. The light absorption of methanol extracts showed a strong wavelength dependence for both BB and gasoline vehicle emissions. The mass absorption coefficients at 365 nm (MAC365, m2 g−1C) – used as a measurement proxy for BrC – were significantly correlated (p < 0.05) to the elemental carbon (EC)/OC ratios when examined by each BB fuel type. No significant correlation was observed when pooling fuels, indicating that both burn conditions and fuel types may impact BB BrC characteristics. The average MAC365 of gasoline vehicle emission samples is 0.62 ± 0.76 m2 g−1C, which is similar in magnitude to the BB samples (1.27 ± 0.76 m2 g−1C). These results suggest that in addition to BB, gasoline vehicle emissions may also be an important BrC source in urban areas.
Carbonaceous aerosols are ubiquitous in the atmosphere and can directly affect Earth’s climate by absorbing and scattering incoming solar radiation1,2,3. Specifically, the black carbon (BC) component of carbonaceous aerosols, or soot, absorbs strongly across the spectral range (from ultraviolet [UV] to the infrared [IR]) showing a weak dependence on wavelength (λ)4,5,6. In direct contrast, the organic carbon (OC) component of aerosol is commonly treated as purely light scattering or “white”7, 8. The optical properties of these aerosols appear in many climate models that show scattering due to OC causes a cooling effect that offsets the warming effect due to BC9, 10. However, growing evidence suggests that certain chemical components of OC can absorb in the near UV and at shorter visible wavelengths impacting radiative forcing11,12,13,14. This component is often referred to as brown carbon (BrC). These light-absorbing BrC components may also influence aerosol photochemistry (e.g., photolysis) and health effects15.
Both field16 and laboratory measurements14, 17,18,19 have confirmed that biomass burning (BB) is an important primary source of BrC, which is also clearly observed in BB-impacted atmospheres20,21,22,23. There is also evidence of secondary BrC formation. For example, laboratory chamber studies indicate BrC formation following the photooxidation of volatile organic compounds (VOCs) emitted from biogenic (e.g., isoprene), BB (e.g., m-cresol), and motor vehicle (e.g., toluene) sources17, 24,25,26,27. However, the optical properties of OC emitted from other sources, particularly from fossil fuel combustion, are largely unstudied.
Based on existing studies of BrC from laboratory simulated BB, large variability in the spectral dependence associated with the chemical variability of BrC constituents has been observed28,29,30,31. In addition, the water-insoluble fraction of BrC has much stronger light absorption efficiency than the water-soluble fraction of BrC, and the light-absorbing efficiency of BrC depends largely on burn conditions (e.g., temperature)14, 15, 18, 32. However, chemical and optical information about the BrC emitted from prescribed or controlled burning is scant16, 33. Prescribed burning is a less intensive fire technique used in forest and agricultural land management, or for land restoration objectives. Prescribed agricultural burns prepare fields for planting, stimulate plant growth and yields, and control pests, whereas prescribed forest burning is used to abate aggressive wildfire and promote ecological succession and sustainability16. Despite the benefits, prescribed burning emits pollutants (e.g., particulate matter (PM), OC, and VOCs) that can have serious regional air quality impact34. For example, Tian et al.35 simulated the impact of BB emissions on PM2.5 in Georgia using a chemical transport model, which ascribed more than 50% of the regional PM2.5 to prescribed BB during January and March, 2002.
Motor vehicles are also a primary source of PM2.5 emissions to urban atmospheres. Lee et al.36 estimated PM2.5 source contributions to the southeastern United States using positive matrix factorization and chemical mass balance models, showing that motor vehicles contributed 17–25% of PM2.5 in urban areas, 6–13% greater than wood burning. However, the association between BrC and motor vehicle aerosol emissions is less certain than for BB. Kirchstetter and Novakov11 suggest that low-temperature incomplete combustion similar to what can occur during BB produces light-absorbing (organic) aerosol with much stronger spectral dependence than higher-temperature combustion processes like diesel combustion. Interestingly, Liu et al.37 investigated BrC based on water and methanol extracts of aerosols collected at urban, rural and near-road sites, finding that the near-road mass absorption efficiencies of water extracts are higher (>40%) than at the urban site. The derived absorbing component of the complex refractive index (k) of near-road aerosol was used to represent gasoline sources by Lu et al.38, which is subject to large uncertainty. However, direct measurements of BrC from primary vehicle emissions are still lacking.
This study attempts to address limitations in understanding BrC as it relates to primary source combustion emissions. In that vein, UV-Vis spectrometry was applied to measure the light-absorbing properties of OC in methanol extracts of prescribed and laboratory BB and gasoline vehicle aerosol emissions. The BB tests were conducted using a variety of fuels and fire conditions. We hypothesized that both the BB conditions and fuel type would impact the OC absorptivity. The gasoline vehicle emissions were sampled during different seasons (winter and summer) while also examining vehicle class (truck and car) and model year variables.
Sampling of prescribed burn
Table 1 provides the field location, fuels, and trial population for the prescribed burns. Kentucky blue grass residues (Poa prantensisi L., “KBG”), wheat stubble (Triticum aestivum L., “Wheat”), and chemically fallowed wheat stubble (“Wheat + Herbicide”) were burned in field in the northwestern United States (Nez Perce, ID and Walla Walla, WA). A grass plot consisting of various species of grasses, forbs, and turkey oak (Quercus laevis) and a forest plot of primarily long leaf pine (Pinus palustris) were burned at a forest field in the southeastern United States (Eglin Air Force Base, FL). Further description of the prescribed burns is given in supplementary information and Table S1, and Holder et al.39 exhaustively describe the forest prescribed burning. The sampling methods and instrumentation applied here were identical to those applied previously16, 33, 39. Briefly, both ground and aerial (aerostat) sampling with identical instrumentation packages were deployed during the prescribed burns. One instrumentation package, including continuous measurements of CO2 (LICOR-820, LICOR Bioscience), BC (AE51, Aethlabs) and particle size distribution (DustTrak DRX 8533, TSI), and batch sampling of PM2.5 (Impactor, SKC) etc., was attached to a helium filled, tethered aerostat (4.3 m in diameter) as the aerial sampling platform; a second instrumentation package was mounted on an all-terrain vehicle as the ground sampling platform. For the duration of each burn, PM2.5 was sampled at 10 L/min on TeflonTM and quartz filters (QF, diameter 43 mm, Pall) positioned downstream of a PM2.5 cyclone (URG). Multiple filters (up to three) were sequentially collected for selected burns to avoid overloading. At each field location, a background sample was obtained upwind of the burn capturing ambient air throughout the burn duration.
Laboratory fire simulations
With the exception of the “grass burn” at Eglin Air Force Base, FL, a corresponding laboratory fire simulation was conducted in an attempt to mimic prescribed burns. Fire simulations were conducted at the U.S. EPA (RTP, NC) Open Burn Test Facility (OBTF). Biomass fuel collection and fire simulation methods are described in detail elsewhere33, 39. Briefly, biomass fuels — gathered at the prescribed burn sites — were divided and burned in batches on an aluminum foil-coated steel pan in a 70 m3 enclosure. For consistency, the same instrumentation package used for field sampling was used for OBTF sampling. Background air samples were collected post-burn inside the OBTF.
Light-duty vehicle emissions
PM2.5 samples collected from gasoline vehicle exhaust were selected from the Kansas City Light-Duty Vehicle Emissions Study (KCVES) filter archive. Vehicle data, emissions testing protocols, and sampling details are given elsewhere40,41,42,43. In summary, the KCVES study separated passenger cars and light-duty trucks into four model year groups representing different technologies: carburetors (pre-1981), early fuel injectors (1981–1990), phase in Tier-1 standards (1991–1995) and National Low Emission Vehicles (1996–2005)43. Exhaust emissions from 496 vehicles recruited from the Kansas City metropolitan area were measured in two rounds: round 1 summer (261 vehicles), and round 2 winter (235 vehicles). Vehicles were tested on a portable chassis dynamometer in a warehouse at ambient temperature using the LA92 Unified Driving Cycle. The LA92 cycle is 15.7 km and consists of three operating phases, including “cold start” (phase 1), “hot running” (phase 2) and “hot start” (phase 3). Vehicle exhaust was cooled and diluted and drawn through a PM2.5 cyclone, followed by 47 mm TeflonTM and QF filters. PM2.5 samples were collected for each of the three phases of the LA92 cycle. In the present study, PM2.5 QF samples were selected from both rounds of emissions testing. Supplementary Table S2 provides vehicle selections, including make and model, model year, and sampling temperatures. Dilution tunnel blanks were also examined and treated as a background check. Finally, all sampled air volumes (1.73 ± 0.12 m3) and dilution ratios were virtually identical throughout emissions testing.
Analytical chemical procedures
Multiple studies have shown that methanol extracts aerosol OC at higher efficiencies than water, and that a large fraction of light absorption in the near-UV and visible ranges is ascribed to water-insoluble OC23, 32, 37. Hence, methanol was used for sample extractions. For prescribed and laboratory BB samples, a QF filter punch (1.5 cm2) was extracted with 5 mL methanol (HPLC grade) in a tightly closed amber vial, sonicated for 15 min, and then filtered (National Scientific Company, 30 mm diameter. ×0.2 μm pore size, polytetrafluoroethylene (PTFE)) using a glass syringe. The light absorption of filtered extracts was measured with a UV-Vis spectrometer at λ = 200–900 nm and a resolution of 0.2 nm (V660, Jasco Incorporated, Easton MD). The wavelength accuracy and repeatability were checked monthly to ensure the quality of the data being collected. The wavelength accuracy was less than ±0.3 nm; the wavelength repeatability was less than ±0.05 nm. A reference cuvette containing methanol was used to eliminate the impact of solvent absorption. The UV-Vis absorption of background air samples was negligible (greater than 1 order of magnitude lower) compared to prescribed burn samples but used for correction nonetheless. This study focused on λ = 300–550 nm, where most of the BrC absorption has been observed32.
All BB QF samples were analyzed for OC and elemental carbon (EC) content using a thermal-optical instrument (Sunset Laboratory, Portland, OR) and modified National Institute of Occupational Safety and Health (NIOSH), Method 504044. Instrument blanks and calibration check standards (sucrose solution) were run at the beginning of each day to ensure valid measurements. Only trace concentrations of OC were observed in background air samples, accounting for less than 1% of the average OC concentration in BB samples, and were used for correction. The amount of OC extracted was calculated as the difference between OC on the un-extracted QF and OC in the air-dried residual QF following extraction. The OC extraction efficiency was calculated as the ratio of extracted OC to OC on the un-extracted filter multiplied by 100%.
Analytical procedures for gasoline vehicle emissions samples were virtually identical to the BB samples, the only difference being that the three QFs corresponding to each phase of the LA92 cycle were composited and analyzed. In other words, one punch of each of the three QF filters in every selected run was combined (three punches in total) and extracted for spectroscopic measurement. The OC and EC were also measured (three punches together) prior to and after filter extraction. The background air in the testing warehouse was impacted by residual vehicle emissions, so the light absorption, OC and EC content of dilution tunnel blank samples were provided separately and not subtracted for correction. The extraction efficiency of OC was also calculated.
The light absorption measured by the UV-Vis spectrometer is expressed as:
where A λ is the light absorbance at a given wavelength (λ); I 0 and I are the intensity of the incident and transmitted light, respectively.
The A λ value of each sample extract is converted to a light absorption coefficient (Abs λ , Mm−1) by ref. 20
where A 700 is referenced to account for systematic baseline drift45, V l (m3) is the volume of methanol (5 mL) used for extraction, V a (m3) is the volume of the sampled air represented by the extracted filter punches, and L (0.01 m) is the optical path length of the quartz cuvette in the UV-vis spectrometer. The bulk mass absorption coefficient (MAC λ , m2 g−1C) could be used to describe the absorption efficiency of extracted OC and the value at 365 nm was typically used as a measure of BrC20. The MAC λ was calculated as45:
where C OC is the mass concentration of extracted OC in PM (μg m−3). Here, the solution MAC λ is different from the widely known term “mass absorption cross-section” (α abs), which is attributed to carbonaceous components in particles suspended in the air. The α abs is empirically parameterized as12:
where K is a fitting parameter including aerosol mass concentrations, and Å abs is the absorption Ångstrӧm exponent, a measure of the λ dependence of aerosol light absorption. In this work, the Å abs of methanol extract is determined by the linear regression of log10(Absλ) vs. log10(λ) over the λ range of 300 and 550 nm, which is used to represent the characteristics of BrC (Å abs much bigger than 1). All OC and EC measurements and calculations of EC/OC ratio, extraction efficiency, MAC365 and Å abs for BB and gasoline vehicle emissions samples are provided in supplementary Tables S1 and S2, respectively.
Data used in the writing of this manuscript can be obtained upon request to Amara Holder (firstname.lastname@example.org).
Results and Discussion
Analysis of BB samples
Compared with field-based prescribed burns, Table 2 shows that the fire simulations produce systematically higher EC/OC ratios in the filter PM irrespective of biomass fuel species. In tandem with the higher Modified Combustion Efficiency (MCE) — a measure of a fire’s flaming versus smoldering combustion — observed for the fire simulations (MCE > 0.9539). One explanation is that our laboratory simulations were run in an enclosure under very controlled conditions which produced a relatively stable emissions stream and were only able to partially mimic field conditions. These results imply that the simulations produce flaming combustion synonymous with higher burning temperatures. Combining the field measurements, which exhibited lower MCEs and lower EC/OC ratios, with the laboratory simulations results in a range of combustion conditions for the same fuel types. EC/OC ratios determined for the aerostat filter samples are generally higher than ground-level determinations. Presumably, the ground-level samples depict higher smoldering combustion contributions or higher dilution aloft partly vaporizes the semivolatile OC39. The extraction efficiency of OC from the BB emissions was consistently 90% or greater, similar to the results of Chen and Bond32. The sampling site and fuel and fire type variables show slight if any effect on the extraction efficiency. Table 2 also provides the light absorption properties of extractable OC. For ease of analysis, the bulk mass absorption coefficient of extracted OC at 365 nm (MAC365) was used to measure BrC, because the light absorption at this wavelength is representative and has been successfully used to study BrC in past studies20, 27, 37, 45. Mean values (EC/OC, extraction efficiency, MAC365 and Å abs) are reported with standard deviations. For tests with N < 3, only the mean value is provided.
Figure 1a shows characteristic MAC spectra within the wavelength (λ) range of 300–550 nm. The spectra exhibit a strong λ dependence and Å abs > 2. Although the absorption is greater over the λ < 350 nm region, absorption at visible wavelengths (>400 nm) is taken as evidence of BrC15. The average MAC365 and Å abs values determined for aerostat, ground and OBTF test samples for each fuel type are listed in Table 2. The methanol extracts of PM from the laboratory fire simulations show relatively high MAC365 and low Å abs values, suggesting that the higher temperature flaming combustion that dominates the fire simulations preferentially generates OC with strong light absorption. In this work, the MAC365 ranged from 0.90 to 2.22 m2 g−1C across all samples (including aerostat, ground and OBTF); the Å abs range is 4.43–8.67 with an average of 7.01 ± 0.90, and the correlations between log10(Absλ) and log10(λ) are greater than 0.98 (p < 0.01). The average MAC365 (1.27 ± 0.34 m2 g−1C) measured in this study is comparable to the methanol extracts for ambient aerosols from the LA basin (MAC365 1.58 m2 g−1C, Å abs 4.82)45 and Beijing (MAC365 1.45 ± 0.26 m2 g−1C, Å abs 7.10 ± 0.45)23, but greater than those from three sampling sites in Georgia (MAC365, 0.27–0.41 m2 g−1C, Å abs 4.02–5.89)37. The absorption of methanol-extractable OC measured in the Beijing study was strongly correlated with levoglucosan – a biomass burning tracer, indicating an influence from BB23. However, in the LA basin study, BrC was attributed mainly to anthropogenic emissions and associated formation of secondary organic aerosol45. The low absorption of aerosol extracts in Georgia was attributed primarily to biogenic secondary emissions46. The average Å abs (7.01 ± 0.90) in this work is comparable to the extractable OC from burning of corn stalks (7.7)47 and wood (6.9–7.8)32.
Light absorption and EC/OC ratio
Instead of MCE, which has shown only moderate correlation with optical properties48, the EC/OC ratio is used here as an indicator of fire conditions. Recent studies comparing MCE and EC/OC have shown that EC/OC is key to understanding aerosol optical properties18, 38. Figure 2a shows the MAC365 vs. EC/OC and Å abs vs. EC/OC relationships for all the BB samples (regardless of fuel types and sampling method). The data clearly show that the light absorption of OC from BB is dependent on burn conditions as measured by EC/OC, consistent with previous studies14, 18. However, the scatter and low MAC365 and EC/OC correlation (r = 0.24, p > 0.05) suggest that something other than fire conditions may influence the light-absorbing properties of OC from BB.
Previous laboratory studies of BrC from BB have observed that optical properties depend on burning conditions but not on fuel type14, 38. However, these studies14, 38 are limited in that there were few replicates per fuel type and the replicates tended to reflect similar burning conditions. Thus, a limited range of EC/OC values was observed per fuel type, and the Å abs and MAC365 relationships could therefore not be adequately characterized by fuel type. To compare with Saleh et al.14, we pooled all OBTF samples together (Fig. 3a) and compared to only the forest fuels (Fig. 3b), which had the greatest sample population (N = 9) of the laboratory burn simulations and the widest EC/OC range. When the OBTF results are pooled, the MAC365 vs. EC/OC (r = 0.07, p > 0.05) and Å abs vs. EC/OC (r = −0.29, p > 0.05) linear correlations are not statistically significant. When limited to just the forest fuels, the regressions for MAC365 and Å abs with EC/OC become statistically significant (p < 0.05; Fig. 3b). The uncertainties in EC/OC ratio, MAC365 and Å abs were estimated by replicate analysis of select filter samples to determine if measurement uncertainty impacts the MAC365 and Å abs dependence on EC/OC. While the potential variability intrinsic to the combustion system was not addressed. Details of the uncertainty analysis are provided in the Supplementary Information and Tables S3 and S4. The uncertainty was around 5% for the EC/OC ratio and less than 5% for MAC365 and Å abs. Therefore, the linear relationship and overall trends observed for MAC365 vs. EC/OC and Å abs vs. EC/OC in Fig. 3b are unaffected by measurement uncertainty, further confirming the importance of burning conditions and biomass fuel type on the light absorption of OC from BB.
In addition, Figure S1 shows MAC365 vs. EC/OC and Å abs vs. EC/OC by fuel type for all sampling methods (aerostat, ground and OBTF) fit to a linear regression (“Grass burn” data are removed because sample number N = 2). All correlations are significant (p < 0.05) except for Å abs vs. EC/OC (r = −0.49, p > 0.05, Figure S1c) for the “Wheat” fires. The weak correlation observed for “wheat” fires may be due to the limited sample population (N = 5), although the MAC365 and EC/OC correlation for “Wheat” is significant (r = 0.95, 0.01 < p < 0.05). In Figure S1, the field data points have little variation in MAC365 and Å abs, suggesting similar burn conditions during filed burns. Except “Grass burn”, the aerostat samples had consistently higher average EC/OC ratio and MAC365, and lower Å abs than ground samples (Table 2), which might also indicate the dependence of light absorption on burn condition. Among the four biomass fuels in Figure S1, MAC365 and Å abs of the “Wheat + herbicide” burns show the highest sensitivity to the EC/OC ratio (slope, 9.87 and −19.5), while the “Wheat” and “Forest burn” tests are the least sensitive (slope < 1), suggesting that fuel type influences the optical properties of OC from BB. However, how biomass fuel type affects the light absorption of OC from BB is not clear and warrants further study. In this work, due to the small sample populations for laboratory simulated burns using “KBG”, “Wheat” and “Wheat + Herbicide”, and the relatively narrow EC/OC ratio and MAC365 and Å abs ranges for the field measurements, future studies are needed to verify the relationships of MAC365 vs. EC/OC and Å abs vs. EC/OC for specific biomass fuel types.
Saleh et al.14 evaluated the OC light absorption on a direct particle measurement basis, which may in part be influenced by BC absorption. In our study, the OC component is extracted and isolated from EC, thus there is no EC influence or lensing effect (enhancement of EC absorption by OC coatings). These different approaches may have impacted the relationship between fuel type and BrC, which may partly explain the differences between this study and that of Saleh et al.14. Additionally, Saleh et al.14 analyzed emissions from a different fuel species set compared with the current study. To date, few studies have investigated the influence of burning conditions and fuel types on BrC from BB emissions14, 18, 32, which is necessary to predict the impact of BB aerosols on radiative forcing12.
Analysis of gasoline vehicle emissions samples
To date, a majority of studies propose BB as a major BrC source, which has led to relatively limited testing of anthropogenic sources for BrC content. An objective of the present study is to examine the potential BrC contribution due to petroleum-powered vehicles. Supplementary Table S2 provides pertinent vehicle and emissions test information by study trial as well as the OC and EC concentrations, EC/OC ratios, OC extraction efficiency, MAC365 and Å abs. The OC and EC concentrations are reported as μg m−3 and potentially reflect the emission strength because the total sampling and dilution volumes are similar for all tests. Due to sample availability, the pre-1981 and 1981–1990 vehicle groups are combined and compared with the 1991–1995 and 1996–2005 vehicle groups. Emissions from all tested vehicles were combined for data trend analysis and data visualization.
The OC and EC concentrations (μg m−3), EC/OC ratios, and OC extraction efficiency results by vehicle group and season are given in Supplementary Figure S2. As expected, OC and EC emissions increase in winter and with vehicle age. Schauer et al.49 found that motor vehicles emitted substantially more carbonaceous particle matter at low temperatures (~0 °C) than at regular temperatures (~24 °C). Similar trends with season and vehicle age were observed previously for PM emissions42, 43. EC/OC ratios are greater in the summer, contrasting with the extraction efficiency of OC, perhaps owing to increased volatilization of SVOCs and faster catalyst and engine warm-up times. EC/OC ratios and OC extraction efficiency correlate negatively (r = −0.52, p < 0.01) for all vehicle test data. Presumably, the EC in PM strongly adsorbs OC, in turn reducing the extraction efficiency.
In Fig. 1b, typical MAC spectra over the 300–550 nm λ range are shown for gasoline vehicle emissions. Similar to BB, light absorption is observed in both the UV and short visible regions, and spectra exhibit strong wavelength dependence (Å abs > 2). Figure 4 shows the MAC365 and Å abs values by season for the vehicle groups. The median and average MAC365 values were higher in winter (median 0.51–0.66 m2 g−1C, average 0.61 ± 0.34–1.10 ± 0.66 m2 g−1C) than in summer (0.15–0.38 m2 g−1C, 0.27 ± 0.30–0.46 ± 0.46 m2 g−1C), while Å abs values exhibited an opposite seasonal variation (winter average 6.29 ± 2.25–6.93 ± 1.53, summer average 9.81 ± 1.50–10.18 ± 1.27). Unlike the OC and EC emissions, the median and average MAC365 did not show a consistent trend across vehicle model year. These results suggest that gasoline vehicles could generate stronger light-absorbing OC emissions under colder conditions, although the season had less of an effect on the light-absorbing properties of OC from vehicles with newer model years (1996 to 2005).
Compared with the BB, the MAC365 values for gasoline vehicle emissions are generally lower (average 0.62 m2 g−1C) and more variable (range, 0.016–4.88 m2 g−1C). However, the average or median MAC365 values of these sources are of similar magnitude. Hence, gasoline vehicle emissions may represent a substantial contribution to BrC in urban regions affected by vehicle emissions. Interestingly, the EC/OC ratio may not be an adequate proxy for understanding the light absorption of methanol extractable OC in gasoline vehicle emissions. Neither the MAC365 nor the Å abs correlate to EC/OC (r = 0.06, p > 0.05 and r = 0.20, p > 0.05; Fig. 2b). This observation is valid even when isolating samples by season (winter and summer), vehicle type (truck and car), or model year. Therefore, the BrC from gasoline vehicles may be compositionally different than BrC from BB. The extraction efficiency of OC from gasoline vehicle emissions (75.9 ± 9.42%) is lower than the extraction efficiency of OC from BB (>90%), and the light absorption of the residual OC is uncertain. Chen and Bond32 found that higher BB temperatures can generate more light-absorbing OC and suggest that macromolecules containing both conjugated aromatic rings and functional groups are responsible for the light absorption. Di Lorenzo and Young50 compared the contributions of high- and low-molecular weight compounds to light absorption using aged BB aerosols and observed large molecular weight (>1000 Da) components as the dominant contributors. Thermodenuder measurements performed to characterize light-absorbing OC in BB aerosols as a function of volatility also demonstrated that extremely low volatility OC contributed most to light absorption14. The non-extracted OC fraction in gasoline vehicle emissions is likely hydrophobic or high molecular weight compounds with conjugated double-bonded carbon structures (e.g., PAHs). Their light absorption properties require further study.
Imaginary part of the complex refractive index
In this study, the k value of extractable organic matter — another measure of BrC — from BB and gasoline vehicle emissions was calculated based on the spectroscopic data measured in this study. The calculation method and resulting k values are given in the Supplementary Information and Table S5, respectively. The median k values of BB samples at wavelengths of 365, 405 and 550 nm are 0.026, 0.014 and 0.0020, respectively, and of the same magnitude as those k values estimated by Lack et al.51 (404 nm, 0.009) and Li et al.47 (400 nm, 0.041; 550 nm, 0.005) but 5–10 times lower than the values from Saleh et al.14 (550 nm, ~0.01–0.03). Li et al.47 calculated the k value using the same method as this study (solvent extracts based); Lack et al.51 and Saleh et al.14 performed optical closure with Mie theory calculations to retrieve effective k values. The optical closure method has large uncertainties since the real particle morphology may greatly deviate from the idealized spherical Mie model. The discrepancies between these studies in k estimation might be caused by the difference in both method and BB (biomass fuel and burn conditions). The median k values of gasoline vehicle emissions at 365, 405 and 550 nm are 0.013, 0.0086 and 0.0015 in winter, respectively, and approximately two times the values in summer. Therefore, treating organic aerosol as non-absorbing particles would underestimate the radiative effect of organic aerosols, especially in urban areas where motor vehicle emissions are a substantial fraction of the aerosol.
This study measured the light absorption of methanol-extractable OC derived from BB and gasoline vehicle emissions, which exhibited strong wavelength dependence with Åabs values much higher than 2. The OC generated during BB under high temperature or flaming combustion shows strong light absorption; the biomass fuel type may also play a role in the light-absorbing properties of OC generated from BB. However, how biomass fuel type affects the light absorption of OC from BB is uncertain and merits further study. Gasoline vehicles tend to emit stronger light-absorbing OC in winter than in summer. Compared to BB, the light absorption of OC from gasoline vehicle emissions was of the same magnitude but weaker, suggesting the importance of gasoline vehicle emissions as a BrC source in urban regions. Non-extractable OC accounted for a substantial part (~25%) of the total OC from gasoline vehicle emissions, and further study to measure its potential light-absorbing properties is warranted.
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This work was funded by the U.S. Environmental Protection Agency. We thank B. Gullett and J. Aurell for assistance with field and laboratory biomass burning sampling, and R. Baldauf for assistance with motor vehicle emission sampling. The views expressed in this article are those of the authors and do not necessarily represent the views or policies of the U.S. Environmental Protection Agency.
The authors declare that they have no competing interests.
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Xie, M., Hays, M.D. & Holder, A.L. Light-absorbing organic carbon from prescribed and laboratory biomass burning and gasoline vehicle emissions. Sci Rep 7, 7318 (2017). https://doi.org/10.1038/s41598-017-06981-8
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