Journal topic
Atmos. Chem. Phys., 20, 1105–1129, 2020
https://doi.org/10.5194/acp-20-1105-2020
Atmos. Chem. Phys., 20, 1105–1129, 2020
https://doi.org/10.5194/acp-20-1105-2020

Research article 28 Jan 2020

Research article | 28 Jan 2020

# Molecular composition and photochemical lifetimes of brown carbon chromophores in biomass burning organic aerosol

Molecular composition and photochemical lifetimes of brown carbon chromophores in biomass burning organic aerosol
Lauren T. Fleming1, Peng Lin2,a, James M. Roberts3, Vanessa Selimovic4, Robert Yokelson4, Julia Laskin2, Alexander Laskin2, and Sergey A. Nizkorodov1 Lauren T. Fleming et al.
• 1Department of Chemistry, University of California, Irvine, Irvine, CA 92697, USA
• 2Department of Chemistry, Purdue University, West Lafayette, IN 47907, USA
• 3Chemical Sciences Division, Earth System Research Laboratory, National Oceanic and Atmospheric Administration, Boulder, CO 80305, USA
• 4Department of Chemistry, University of Montana, Missoula, MT 59812, USA
• anow at: California Air Resources Board, El Monte, CA 91731, USA

Correspondence: Sergey A. Nizkorodov (nizkorod@uci.edu)

Abstract

1 Introduction

Forests have naturally occurring wildfire cycles that maintain the forest ecosystem, but global climate change is altering the cycles with unpredictable consequences (Shvidenko and Schepaschenko, 2013; Weber and Stocks, 1998). In addition to the impacts of wildfires on ecosystems, biomass burning plumes have pronounced effects on atmospheric chemistry and climate (Boulanger et al., 2014; Moriondo et al., 2006; Shvidenko and Schepaschenko, 2013; Wotton et al., 2010; Wotton and Flannigan, 1993). Wildfire plumes contain a complex mixture of greenhouse gases (carbon dioxide and methane), multiple non-methane organic compounds (NMOCs), and carbonaceous and ash particles. The effects arising from biomass burning organic aerosol (BBOA) are not well understood because BBOA composition and optical properties may depend on many factors, such as the type of fuel burned and combustion conditions (Chen and Bond, 2010; Jen et al., 2019; Kirchstetter et al., 2004), wind speed, heading or backing fires (Surawski et al., 2015), and fuel moisture content (Tihay-Felicelli et al., 2017). Global climate models are starting to include contributions from light-absorbing organic carbon, termed brown carbon (BrC), because treating BBOA as purely scattering leads to incorrect predictions of climate forcing (Bond et al., 2011; Laskin et al., 2015; Ma et al., 2012). One of the first studies incorporating BrC into models was by Feng et al. (2013), who found that in areas where primary BrC emissions are high the absorbing component of BBOA can dominate over the scattering component, switching net radiative forcing by organic aerosols from negative (cooling) to positive (warming) at the top of the atmosphere. Other modeling studies have demonstrated that BrC can have large positive effects on the radiative forcing (Bahadur et al., 2012; Chung et al., 2012; Laskin et al., 2015; Ramanathan et al., 2007). However, field measurements to date indicate that BrC has a short lifetime of ∼10 h, which would considerably reduce its impact if included in models (Forrister et al., 2015; Selimovic et al., 2019). Light absorption by BrC can also result in a significant decrease in the photolysis rates of photochemically active gases, such as HONO and NO2, which affect the mixing ratios of atmospheric oxidants (Jiang et al., 2012; Li et al., 2011). To better quantify the effect of BrC on climate, the chemical composition and lifetimes of individual BrC chromophores, as well as the effect of photochemical aging on the optical properties of BrC particles, should be studied. Further, for a comprehensive understanding, we should consider the diversity of BrC, spanning nonpolar to polar molecules, and BBOA from a range of sources.

Previous studies have identified important classes of BBOA chemical components that contribute to light absorption. A major class includes lignin-pyrolysis products, which are typically substituted aromatics with a high degree of unsaturation, such as coniferaldehyde (Budisulistiorini et al., 2017; Fleming et al., 2018; Simoneit et al., 1993). Another class is nitroaromatics, such as nitrocatechols, which are readily produced in the presence of NOx and absorb strongly, with a λmax around 340 nm (Iinuma et al., 2010; Lin et al., 2017). Polycyclic aromatic hydrocarbons (PAHs) have long been known to be emitted from incomplete combustion processes, and large PAHs can be significantly light-absorbing at the near-UV and visible wavelengths (Simoneit, 2002). Budisulistiorini et al. (2017) observed sulfur-containing species from fern and peat pyrolysis, and suggested that they are formed via acid-catalyzed heterogeneous reactions. Tar balls are largely externally mixed spheres or spherical aggregates produced from smoldering combustion or through multiphase secondary chemistry (Sedlacek et al., 2018; Tóth et al., 2014). In terms of their chemical composition, tar balls are thought be comprised primarily of oxygenated organic compounds, similar to that of BBOA (Chakrabarty et al., 2010; Girotto et al., 2018; Li et al., 2019; Pósfai et al., 2004; Sedlacek et al., 2018).

The photochemical aging of actual mixtures of BBOA compounds, not just surrogates, was also reported in the literature. For example, Tomaz et al. (2018) found that aqueous BBOA mixtures from the 2016 FIREX lab intensive decayed rapidly, with most having lifetimes due to aqueous OH oxidation mimicking clouds of a half a day or less. The decay of compounds such as catechol, benzoic acid, and methylfurfural lead to the formation of oxalate, which made up 13 %–16 % of total dissolved organic carbon after 150 h. Saleh et al. (2013) burned pocosin pine and oak, and diluted smoke was irradiated with UV lights in a smog chamber. Aerosol optical properties were monitored with an aethalometer at seven wavelengths. They found that aged emissions were more absorbing than fresh emissions at 370 and 470 nm after 1 h. Zhong and Jang (2014) tracked the absorption coefficients of BBOA during solar exposure in a smog chamber, and observed an increase of 11 %–54 % in the integrated mass absorption cross section (280–600 nm) in the first half of the day, followed by decrease in the afternoon. In Lin et al. (2016), BBOA collected from ponderosa pine and Indonesian peat burns were dissolved in a 50 % by volume water/acetonitrile solvent and irradiated with actinic wavelengths. They found that, regardless of the fuel type, the half-life of the absorbance at 300 nm was roughly 16 h under sunlight for soluble BBOA. Wong et al. (2017) found that irradiated BBOA water extracts lost water-soluble organic carbon (WSOC) when irradiated with 300–400 nm light. Simultaneously, the absorption coefficients at 365 and 400 nm first increased, in the latter case to about 0.035 m2 g−1 after 20 min of illumination time, and then decreased to nearly 0 in 60 min. Size-exclusion chromatography showed that low-molecular-weight BrC chromophores (<400 Da) were quickly formed and photo-degraded, giving yield to a photo-enhancement due to the formation of high-molecular-weight species (>400 Da). They concluded that this high-molecular-weight fraction was responsible for long-lived light absorption. In Sumlin et al. (2017), BBOA produced from burning Alaskan peat were aged by reactions with OH in an oxidation flow reactor (OFR), and light absorption coefficients of aged and unaged BBOA were measured by an integrated photoacoustic nephelometer. They found that the mass absorption coefficient at 375 nm deceased roughly 45 % after an equivalent of 4.5 d of photochemical aging.

To summarize the literature survey above, much work has been done in terms of characterizing optical properties of photochemically aged BBOA and surrogates, but a consensus on what drives the photobleaching and photo-enhancement of chromophores in BBOA and the relative importance of these processes on atmospherically relevant timescales has not been reached. This study aims to better understand the molecular composition of BrC for different fuel types and combustion conditions as it may be essential to understanding the optical properties of BBOA and predicting their evolution during photochemical aging.

2 Experimental methods

## 2.1 Sample collection and information

BBOA particle samples were collected during the FIREX Fall 2016 lab intensive at the Missoula Fire Lab (https://www.esrl.noaa.gov/csd/projects/firex/firelab/, last access: 1 May 2019). One of the BBOA samples used in this study was from a “stack” burn and the other samples were from “room” burns. Selimovic et al. (2018) explains room and stack burns and fuels in detail. Briefly, the combustion of forest fire fuels lasted 5–20 min and during stack burns emissions were collected from a constant, diluted flow of entrained emissions by way of the stack. In room burns, the smoke from the fire was allowed to mix in the room during sample collection, and BBOA was collected during both the burn and mixing periods. Smoke was purged from the room by clean air between burns. Fuels were collected from different US regions and brought to the Missoula Fire Lab for test burns. This paper focuses on 12 fires covering gymnosperm or conifers, including ponderosa pine (Pinus ponderosa), lodgepole pine (Pinus contorta), Engelmann spruce (Picea engelmannii), Douglas fir (Pseudotsuga menziesii), juniper (Juniperus), longleaf pine (Pinus palustris), and subalpine fir (Abies lasiocarpa). Angiosperm forest fire fuels included Montana sagebrush and two types of chaparral, i.e., manzanita (Arctostaphylos) and chamise (Adenostoma fasciculatum). In some test burns, a representative “ecosystem” mix of biomass was used, including canopy, duff, litter, herbaceous, and shrub components. In other test burns, single biomass components of the ecosystem were used, such as rotten log samples. Information for each fire is provided in Table S1 in the Supplement.

Copper tubing with a PM2.5 cyclone inlet was placed in the combustion room, while the pump and filter were located in an adjacent room. The pump was operating at a flow of 16.7 L min−1 with the aid of a critical orifice, and BBOA particle samples were collected on PTFE filter substrates (FGLP04700, Millipore, 47 mm diameter, 0.2 µm pore size) during both of the combustion and smoke-mixing stages of the room burns. Loaded filters were stored at −18C until they were analyzed for BrC chromophores no more than 2 months after sampling. The room burn protocols allowed for long collection times and therefore higher aerosol mass loading, which is desirable for the analysis described below.

## 2.2 HPLC–PDA–HRMS

The molecular identity and relative abundance of BrC chromophores were determined using the HPLC–PDA–HRMS platform described by Fleming et al. (2018) and Lin et al. (2018). Segments of the filter were extracted into a mixture of organic solvents composed of 2.0 mL dichloromethane, 2.0 mL acetonitrile, and 1.0 mL of hexanes, which was shown to optimize the extraction efficiency (Lin et al., 2017). The extraction occurred overnight on a platform shaker. Extracts were filtered with polyvinylidene fluoride (PVDF) syringe filters (Millipore, Duropore, 13 mm, 0.22 µm) to remove undissolved suspended particles. Water (50 µL) and dimethyl sulfoxide (DMSO; 100 µL) were added to the extracts, which were then concentrated under a flow of N2 until the volume was reduced to roughly 150 µL, which signified that the extracting solvent evaporated and (mostly) water and DMSO remained in the solution. For photolyzed BBOA, DMSO (30 µL) was exclusively added to the extract, and evaporated to a volume of 30 µL. Visual inspection confirmed that the extracted material did not precipitate out of solution.

The HPLC utilized a reverse-phase column (Luna C18, 2×150 mm, 5 µm particles, 100 Å pore size, Phenomenex, Inc.). The injection volume was 5.0 µL for unphotolyzed or 10 µL for extractions of post-irradiated samples, with the latter providing more analyte mass since only a quarter of the filter was used in irradiation experiments. The mobile phase consisted of 0.05 % formic acid in liquid chromatography–mass spectrometry (LC–MS) grade water (A) and LC–MS grade acetonitrile (B). Gradient elution was performed with the A–B mixture at a flow rate of 200 µL min−1: 0–3 min hold at 90 % A, 3–62 min linear gradient to 10 % A, 63–75 min hold at 10 % A, 76–89 min linear gradient to 0 % A, 90–100 min hold at 0 % A, then 101–120 min hold at 90 % A. The electrospray ionization (ESI) settings of the Orbitrap HRMS were as follows: 4.0 kV spray potential, 35 units of sheath gas flow, 10 units of auxiliary gas flow, and 8 units of sweep gas flow. The solutions were analyzed in both positive and negative ion ESI-HRMS modes.

The HPLC–PDA–HRMS data were acquired and first analyzed using Xcalibur 2.4 software (Thermo Scientific). Possible exact masses were identified based on the corresponding LC retention time using the open-source software toolbox MZmine version 2.23 (http://mzmine.github.io/, last access: 28 July 2017) (Pluskal et al., 2010). Chemical formulas were assigned from exact mz values using the Formula Calculator v1.1. More details about experimental procedures and data processing can be found elsewhere (Lin et al., 2015b, 2016, 2018).

## 2.3 Condensed-phase photochemistry experiments

A quarter of the filter was directly irradiated by either an ultraviolet light-emitting diode (LED, Thorlabs M300L4) or a filtered xenon arc lamp. The LED was used in experiments aimed at estimating lifetimes of individual chromophores. The LED emission spectrum was centered at 300 nm with a full width at half maximum (FWHM) of 20 nm. This wavelength was chosen because it corresponds to the most energetic UV photons available in the lower troposphere. It is common practice in photochemical experiments to use narrow band UV sources, as opposed to a broadband simulator, as it limits sample heating and evaporation (Calvert and Pitts, 1966). The LED was fixed half a centimeter away from the filter, resulting in an incident power density of 11 mW cm−2. Irradiation times for these experiments are given in Table S2. After the irradiation step, the photolyzed BBOA were extracted and analyzed using HPLC–PDA–HRMS as described in the previous section.

The irradiation time using the LED was converted into an equivalent time under sunlight by calculating the ratio of the 290–350 nm integrated spectral flux of the Sun and the 300 nm LED, given in Eq. (1). This conversion assumes that photochemistry is limited to the <350 nm range, consistent with the photochemistry of many organic molecules, which exhibit a sharp drop in the photochemical quantum yields at longer wavelengths (Turro et al., 2009). Because the radiation source does not replicate the solar spectrum, the lifetimes calculated from the formula below should be regarded as estimates.

$\begin{array}{}\text{(1)}& {\mathit{\tau }}_{\mathrm{atm}}={\mathit{\tau }}_{\mathrm{LED}}×\frac{{\int }_{\mathrm{290}\phantom{\rule{0.125em}{0ex}}\mathrm{nm}}^{\mathrm{350}\phantom{\rule{0.125em}{0ex}}\mathrm{nm}}{F}_{\mathrm{LED}}\left(\mathit{\lambda }\right)\mathrm{d}\mathit{\lambda }}{{\int }_{\mathrm{290}\phantom{\rule{0.125em}{0ex}}\mathrm{nm}}^{\mathrm{350}\phantom{\rule{0.125em}{0ex}}\mathrm{nm}}{〈{F}_{\mathrm{solar}}\left(\mathit{\lambda }\right)〉}_{\mathrm{24}\phantom{\rule{0.125em}{0ex}}\mathrm{h}}\mathrm{d}\mathit{\lambda }}\end{array}$

The spectral flux density for the LED and the Sun as a function of wavelength is shown in Fig. 1. The solar flux density was estimated every hour and averaged over a 24 h period for Los Angeles, CA (34 N, 118 W), on 20 June 2017 from the quick Tropospheric Ultraviolet Visible (TUV) calculator (Madronich et al., 2002) using the following parameters: 300 DU overhead ozone column, 0.1 surface albedo (0–1), and ground elevation of 0 km with default outputs for aerosols and clouds. The procedure for calculating the spectral flux density of the LED is described in the Supplement. The maximum possible spectral flux density from the Sun was also calculated at a solar zenith angle (SZA) of 0 using the TUV calculator. The equation for calculating the equivalent atmospheric lifetime at an SZA of 0 is the same as Eq. (1), except that the 24 h averaged flux density is replaced by the peak flux density at SZA = 0. The SZA = 0 comparison represents the lower limit of BrC absorption lifetimes.

Figure 1Spectral flux density (photons cm−2 s−1 nm−1) approximated for a solar zenith angle of 0 (orange), as well as the 24 h average for the latitude and longitude of Los Angeles (34 N, 118 W) on 20 June 2017 (red). The spectral flux density for the 300 nm LED (blue) and the filtered Xe arc lamp (green) are also shown.

In a separate series of experiments, filter samples were irradiated by the filtered radiation from a xenon arc lamp to determine the characteristic lifetime for the photobleaching of the overall absorption by BrC molecules. A quarter of a PTFE filter sample was exposed to filtered light emitted from a xenon arc lamp (Newport 66902). Broadband light was reflected at a 90 angle using a dichroic mirror, then filtered through a 295 nm long-pass filter (Schott WG295), and finally passed through a UV bandpass filter (Schott BG1), ultimately transmitting light in the range of 290–400 nm. The incident overall power density was 196 mW cm−2. Particles were irradiated for ∼12 h to 1.8 d; the exact time varied from sample to sample depending on the offline transmission spectra. Transmission spectra were acquired directly from the PTFE filter without any material extraction using a Jasco V-670 absorption spectrometer, with a blank PTFE filter used as a reference. Four to six transmission spectra were collected at each time point as the filter was rotated, to minimize the effect of the filter orientation. The filter was then returned to the irradiation setup for further irradiation. When there was no longer any change in the transmission spectrum due to irradiation, the filter was extracted into an organic solvent mixture of 10 mL methanol, 5.0 mL acetonitrile, and 2.0 mL of hexane in a scintillation vial using a vortex mixer. While dichloromethane would be a better solvent for BBOA material, methanol was used for these experiments, since dichloromethane absorbs at longer wavelengths in the UV (up to 240 nm) and could interfere with the measurement. The solution was then evaporated down to 5 mL in order to increase the analyte concentration. For comparison, an un-irradiated quarter of the filter was prepared identically in a separate vial, and solution-phase transmission spectra of both solutions were recorded using a dual beam UV–Vis spectrometer (Shimadzu UV-2450). Sample filter-based and solution-phase spectra are shown in Fig. S2, with the y axis converted to effective base-10 absorbance, $A=-\mathrm{log}\left(T\right)$, where T is the wavelength-dependent transmittance through the filter or the cuvette. For filter-based transmission spectra, the baseline was manually corrected by assuming the absorbance at 850 nm was zero for BrC.

In all UV irradiation experiments, the integrated absorbance from 300 to 700 nm was calculated and normalized to the starting integrated absorbance before the UV exposure. The decay constants and corresponding lifetimes were calculated as described in Fig. S1. The linear regression trend line was constrained to have a y intercept of zero. Error bars were calculated from the standard error of the slope of the linear trend line, the first-order rate constant. It should be noted that lifetimes of BrC absorption and chromophores given in this paper are lower-limit estimates since there are uncertainties due to scattering by the Teflon substrate (Presser et al., 2014).

3 Results and discussion

## 3.1 BrC chromophores

Table 1 summarizes BrC chromophores observed in two or more fires or fuel types. The table numbers BrC chromophores by their ascending retention time on the HPLC column, i.e., with smaller, more polar compounds appearing first. Each entry includes the absorption spectrum recorded by the PDA detector, the chemical formula(s) corresponding to the detected characteristic masses at that retention time, and a potential structure based on a spectra acquired from standards or observations in previous studies. All PDA chromatograms were integrated over 300–700 nm and normalized to the maximum integrated absorbance. Chromophores in Table 1 are binned with respect to their normalized PDA absorbance as M – major (75 %–100 %); I – intermediate (25 %–75 %); or W – weak (5 %–25 %). Abundance and absorption cross sections of BrC chromophores both factor into their assigned absorbance bin, as absorbance was not mass normalized with standards. It is possible that the chromophores labeled as “M” are present in small concentrations but have a large absorption coefficient. Compounds making up less than 5 % of the normalized absorbance are not included in the table.

Table 1Chromophores common among multiple fuel types are listed by their HPLC retention times, absorption spectra, assigned elemental formulas, and examples of possible structures. The absorbance by each chromophore is binned by integrated photodiode array absorbance normalized to the highest absorbance in each chromatogram: M – major (75 %–100 %); I – intermediate (25 %–75 %); or W – weak (5 %–25 %). The absorption spectra of the standard (blue) may not fully match the absorption spectra of the eluents because the separation is not complete and more than one compound may elute at any given time. The shown absorption spectra are baseline-corrected by subtracting the spectrum at a nearby retention time where the PDA absorbance is low.

Lin et al. (2018)

Lignin pyrolysis products make up one group of BrC chromophores observed. Lignin is a large, heterogeneous biopolymer that is a significant component of wood, along with cellulose and hemicellulose. Lignin monomer units vary depending on the class of the plant but generally possess phenolic moieties that are largely preserved during pyrolysis (Simoneit et al., 1993). Sinapaldehyde (8) and coniferaldehyde (9) are known lignin pyrolysis products derived from the corresponding lignin monomer units, sinapyl and coniferyl alcohol, respectively. However, they are detected in varying abundance depending on the lignin monomer units of the plant class. Sinapaldehyde and coniferaldehyde are separated by the column but elute only 0.3 min apart, as shown in Fig. 2. Sinapaldehyde is a major BrC chromophore for nearly all angiosperm or flowering fuel types, including ceanothus, chamise, and sagebrush, while coniferaldehyde is a major BrC chromophore largely among conifers or soft wood species such as subalpine fir duff, longleaf pine, juniper, and ponderosa pine litter. Coniferaldehyde has one fewer methoxy ring substituent compared to sinapaldehyde, and its PDA intensity is generally anticorrelated to that of sinapaldehyde. In other words, for fuel types with low sinapaldehyde absorbance, we observe coniferaldehyde as a major BrC chromophore and vice versa. This is consistent with the composition of lignin monomers for angiosperms and gymnosperms (Sarkanen and Ludwig, 1971; Simoneit et al., 1993).

Figure 2The lignin pyrolysis products sinapaldehyde (C11H12O4) and coniferaldehyde (C10H10O3) elute at slightly different retention times, roughly 18.1 and 18.4 min, respectively.

Other BrC chromophores cannot be classified as lignin pyrolysis products but are clearly lignin-derived. Vanillic acid (1) elutes at 10.07–10.29 min as the first, shared chromophore across multiple fuel types that is notable in terms of absorption. It is observed in three fires as a weak chromophore, including subalpine fir duff, ponderosa pine rotten log, and Engelmann spruce duff. All three fires are dominated by smoldering combustion and have the lowest modified combustion efficiencies (MCEs) of all fires (Table S1). This evidence suggests that vanillic acid is a product of smoldering combustion. Further, it also has the coniferyl moiety observed for softwoods. Salicylic acid (3) is an intermediate-absorbing BrC chromophore produced during lodgepole pine burning, and weakly absorbing among other softwoods and duffs. Veratraldehyde (4) is another lignin-derived BrC chromophore, which appears in nearly all BBOA samples of this study, regardless of whether they are gymnosperm or angiosperm fuels.

There are other BrC chromophores with CxHyOz composition that can be explained as distillation products, or the volatilization of molecules originating in plants as secondary metabolites (Agati et al., 2012; Iranshahi et al., 2009). Found in plants, coumarins such as umbelliferone (5) and nodakenetin (13) have been researched because of their positive pharmacological properties (Venugopala et al., 2013). The absorption spectrum for nodakenetin has not been reported; however, the molecule has previously been detected in plant tissues (Lee et al., 2003; Wang et al., 2014) and is a major or intermediate BrC chromophore in smoke from all fuel types except chamise and ceanothus. Another type of distillation product is flavonoids, which give leaves, flowers, and fruits their color, protecting the plant from solar UV radiation, and are antioxidants, guarding the plant from reactive oxygen species (Agati et al., 2012). Flavones and flavonols have the backbone structure of 2-phenyl-1-benzopyran-4-one, and flavonols additionally require a hydroxy substituent on the only available carbon of the pyranone ring. BrC chromophores 11, 14, and 16 could have flavonoid structures based on their chemical formulas. Interestingly, tentatively assigned kaempferol (11) and diosmetin (14) are observed in only conifer species, such as lodgepole pine and longleaf pine. On the other hand, 7-hydroxy-3',4'-dimethoxyflavone (16) is only observed in angiosperm BBOA: ceanothus, chamise, and sagebrush. The former two plants appear to be related as they have the order Rosales in common, which could explain the same flavone detected in both. Coumarins and flavonoids were distillation products observed across fuel types, although the observation of specific BrC chromophores depends on the plant class, i.e., angiosperm or gymnosperm.

Nitroaromatics are a strongly absorbing class of BrC chromophores that are formed from the reaction of aromatics with NOx in plumes (Harrison et al., 2005). This class of compounds is represented in Table 1 with nitropyrogallol (2), nitrocatechol (6), hydroxynitroguaiacol (7), and methyl nitrocatechol (10). Xie et al. (2019) suggest that chromophore (12) with the chemical formula C11H13NO5 is not a nitroaromatic compound but rather a compound containing a different nitrogen-containing functional group, such as a nitrile group. We did not observe this group of chromophores for fires with low NOx levels, such as duff, as qualitatively indicated by the peak NO level (Table S1). Nitrocatechol and methyl nitrocatechol are tracers for BBOA emissions formed from the photooxidation of phenol or m-cresol, toluene, and other aromatic compounds in the presence of NOx (Iinuma et al., 2010, 2016; Lin et al., 2015a). These chromophores are most prominent in BBOA from chamise and sagebrush burns. Those two fires exhibited the highest NO mixing ratios in the entire study – 3.79 ppmv (82 % of total N emissions) and 1.62 ppmv (57 % of total N emissions) peak NO values, respectively. Nitropyrogallol (2) has an additional hydroxy group and is likely formed in the same way as nitrocatechol and methyl nitrocatechol but is more oxidized. A compound with the same formula as nitropyrogallol (2) was observed during the photooxidation of nitrocatechol in the lab (Hems and Abbatt, 2018). This is an intermediate or major BrC chromophore detected in BBOA samples from longleaf pine, manzanita, and ponderosa pine litter fires. Hydroxynitroguaiacol (7) was observed in 10 of the 12 fires and is most prominent in ponderosa pine log BBOA despite this fire having the lowest NO levels. However, it may still form through photooxidation of guaiacol in the presence of NOx (Hems and Abbatt, 2018). Nitrocatechol and methyl nitrocatechol are often used as biomass burning tracers in aged plumes (Al-Naiema and Stone, 2017; Iinuma et al., 2010; Li et al., 2016). However, in addition to these, we observed more oxidized versions of these nitroaromatic species with varying abundance depending on the BrC chromophore and test fire. This suggests that the BBOA markers nitrocatechol and methyl nitrocatechol become more functionalized on relatively short timescales (less than 2 h) due to photooxidative aging.

Polycyclic aromatic hydrocarbons (PAHs) are known to be products of incomplete combustion, and they have the potential to be long-lived BrC chromophores despite their reactivity (Keyte et al., 2013). PAHs have been observed in pristine environments, and it has been suggested that this is due to phase separation of particles and slow diffusivity of PAHs to surfaces where they react with atmospheric oxidants (Fernández et al., 2002; Keyte et al., 2013; Macdonald et al., 2000; Sofowote et al., 2011; Zhou et al., 2012, 2019). In addition to its climatic effects, PAHs are mutagenic and carcinogenic as their metabolites, diol epoxides, bind to guanidine nucleobases in DNA, effectively leading to mutations (Finlayson-Pitts and Pitts, 2000; Moorthy et al., 2015; Wood et al., 1984; Xue and Warshawsky, 2005; Zhou et al., 2017). Various PAHs (17–25, Table 1) were observed in only ceanothus, chamise, and sagebrush BBOA. PAHs in Table 1 are detected from positive ion mode ESI, and although positive mode ESI is not optimal for observing PAHs, larger PAHs are still detectable by this method (Cha et al., 2018). The same PAHs were previously observed by Lin et al. (2018) for sagebrush using atmospheric pressure photoionization (APPI) coupled with HPLC–PDA–HRMS, which is more sensitive for the detection of nonpolar aromatic compounds. In general, individual PAH chromophores are binned as “weak” in Table 1 based on their contribution to optical absorption, but, for BBOA sampled from flaming sagebrush and chamise burns, they make up a significant fraction of the overall light absorption by BrC.

Table 2Chromophores appreciably found in only one fuel type, listed by their HPLC retention time, absorption spectra, assigned elemental formulas, and examples of possible structures. The absorbance by each chromophore is binned by integrated photodiode array absorbance normalized to the highest absorbance in each chromatogram: M – major (75 %–100 %); I – intermediate (25 %–75 %); or W – weak (5 %–25 %).

Table 2 presents abundant BrC chromophores observed only in a single type of biomass fuel emissions. It should be noted that compounds making up less than 5 % of the normalized PDA absorbance (integrated from 300 to 700 nm) are not included in the tables. Due to this constraint, chromophores in Table 2 may also be present in other fires but at very low PDA absorbance values. Despite BrC chromophores in Table 2 being observed significantly for only one fuel type, they belong to the same compound classes as the BrC chromophores in Table 1. For example, a coumarin known as scopoletin (26) was observed from sagebrush BBOA. Previously we discussed that these coumarins are possible distillation products, along with flavonoids, which we also observe as a product (40) from the ceanothus fire. These distillation products (26 and 40) are among the most strongly absorbing of the BrC chromophores, characterized as intermediate or “I” in Table 2.

## 3.2 Aging by condensed-phase photochemistry

Gymnosperm (lodgepole pine) and angiosperm (ceanothus) BBOA particle samples were selected for the initial condensed-phase photochemistry experiments. BBOA filter samples from a lodgepole pine burn were irradiated for 6 h by an LED centered around 300 nm (which corresponds to approximately 33 h of irradiation from 24 h average solar flux density; see Eq. 1). BBOA from the ceanothus burn were irradiated by the same LED for 16 h (equivalent to 88 h of 24 h averaged atmospheric sunlight). The burning of gymnosperm (lodgepole pine) and angiosperm (ceanothus) resulted in different distributions of BrC chromophore classes. However, the same compound classes, lignin-derived and flavonoid compounds, were photo-resistant in both samples.

Figure 3BrC chromophores present in the BBOA sample before (a) and after (b) 300 nm irradiation for a conifer fuel: lodgepole pine.

Figure 4BrC chromophores present in the BBOA sample before (a) and after (b) 300 nm irradiation for an angiosperm fuel: ceanothus.

Most chromophores from the lodgepole pine burn sample experienced complete photobleaching during this exposure, but six of them remained observable, including coniferaldehyde (C10H10O3, 80 % decrease), salicylic acid (C7H6O3, 70 % decrease), veratraldehyde (C9H8O3, 90 % decrease), flavonoids (C15H10O6 and C16H12O6, both 70 % decrease), and nodakenetin (C14H14O4, 90 % decrease), as shown in Fig. 3. Figure 4 shows five chromophores from the ceanothus burn sample that remained observable under these conditions, including sinapaldehyde (C11H12O4, 90 % decrease), a lignin-derived chromophore (C18H16O6, 80 % decrease), and flavonoids (C16H12O5, C17H14O6, and C17H14O5, all 80 % decrease), some of which were observed exclusively in this fire. These comparatively resilient species are aromatic, which helps them be more resistant to photodegradation.

Figure 5Approximate atmospheric lifetimes for select individual BrC chromophores due to UV irradiation in BBOA from chamise, manzanita, and lodgepole pine fires (the irradiation times are listed in Table S2). These lifetimes are shorter than those calculated for overall BrC absorption.

The same chromophores were found to decay at different rates depending on the fuel/fire type (Fig. 5). For example, very different equivalent atmospheric lifetimes due to UV irradiation were obtained across fuel types for veratraldehyde (no. 4 in Table 1, C9H8O3), a BrC chromophore common to all three fires. One explanation is that there are multiple chromophores co-eluting at this retention time, and therefore the calculation is an average lifetime for multiple compounds. A more interesting explanation is that the surrounding matrix could affect the rate of condensed-phase photochemical transformations for individual chromophores by several possible mechanisms. First, different matrices could quench the electronic excitation in the chromophores to a different extent. Another possibility is that photodegradation of BrC chromophores could be not due to direct photolysis but rather occurring through condensed-phase photosensitized reactions (Malecha and Nizkorodov, 2017; Monge et al., 2012), in which case the rate of decomposition would depend on concentration of photosensitizers in the samples as well as viscosity of the material (Hinks et al., 2016; Kaur et al., 2019). Lastly, other absorbing species, such as black carbon, could be shielding BrC chromophores from irradiation, altering the amount of radiation absorbed by BrC chromophores. Given the different mechanisms, the potential contributions from each are difficult to distinguish in this study. The particle matrix is different for all three BBOA particle samples and could contribute to the very different equivalent atmospheric lifetimes of individual BrC chromophores observed in Fig. 5.

Table 3Lifetimes for the loss of the measured integrated absorbance from 300 to 700 nm. The results are expressed in equivalent days of solar exposure to either time-averaged solar flux in Los Angeles (middle column) or peak solar flux at SZA = 0 (right column). The lifetimes were calculated from the transmission spectra measured for particles on PTFE filters. The irradiation was done in the condensed phase on the filter for all samples.

Once there was no further significant change in the transmission spectrum, the filter was extracted for the solution-phase UV–Vis measurement, in order to compare the spectra obtained from the filter and in the solution. The reduction in absorbance in the solution-phase spectra was comparable to that observed in the filter transmission spectra (Fig. S2). However, there were differences in the shape of the spectra – there was no measurable absorbance above 550 nm in the extracted samples, but filter samples absorbed even at these long wavelengths (Fig. S2). It is likely that the extraction from the filter was not complete, and some of the absorbers remained on the filter after the extraction. The latter is another advantage of doing these experiments with filter samples as opposed to their solvent extracts.

BBOA from subalpine fir (litter and other components) had the shortest equivalent absorption lifetime at 10 d, and ponderosa pine (litter and canopy) had the next shortest equivalent absorption lifetime at 17 d. Different ecosystem biomass components were burned in the longleaf pine fire, such as duff, litter, and canopy, and had the next longest absorption lifetime of 25 d. The longest living BrC absorbance, at 41 d, was observed for the sample from juniper (canopy only) burn. Fuel components appear to affect BrC absorption lifetimes, as it does seem that non-canopy fuel components, such as litter and duff, lower the BrC absorption lifetimes. However, it is difficult to correlate the BrC absorption lifetimes with quantitative measures such as NO levels or MCE (Table S1). Table S1 shows that the peak NO level was lower for longleaf pine (0.67 ppmv) compared to juniper (1.72 ppmv) and ponderosa pine (1.61 ppmv), suggesting less flaming combustion may have occurred for the longleaf pine fire (although this is not reflected in the MCE trends). Regardless, the data suggest that BrC absorption can be long-lived from direct photodegradation.

In general, the lifetimes for the loss of the absorbance integrated over 300–700 nm (Table 3) are much longer than those of individual chromophores (Fig. 5). There are two likely reasons for that. First, the photochemical transformation of individual chromophores creates product(s) that may also absorb in the same wavelength range. The integrated BrC absorption (300–700 nm) may significantly decrease only after the compounds go through several successive stages of photodegradation, finally resulting in products that no longer absorb above 300 nm. The results of both UV irradiation experiments is consistent with work by Di Lorenzo et al. (2017) and Wong et al. (2017), which show that during aging, high-molecular-weight BrC chromophores are formed after lower-molecular-weight chromophores are photo-degraded. The high-molecular-weight fraction of BrC chromophores persists even at long aging times and are referred to as the recalcitrant fraction. This theory is one explanation for the short lifetimes of low-molecular-weight BrC compounds, while observing longer overall BrC absorption lifetimes. Second, Eq. (1), which we use to estimate lifetimes, does not take into account photochemical quantum yields, which tend to increase greatly at shorter wavelengths. The LED, which was used in measurements of lifetimes of individual chromophores, has a higher density of higher-energy photons compared to the Xe lamp (Fig. 1), which could accelerate the observed photodegradation rate.

The lifetimes for BrC photobleaching due to UV irradiation (10 to 41 d) are longer than what other studies have observed or approximated for other aging mechanisms. Lin et al. (2016) found that peat and ponderosa pine BBOA had similar half-lives of around 16 h based on absorption coefficients at 300 nm. However, in Lin et al. (2016), BBOA was extracted and irradiated in solution where photodegradation could occur more rapidly due to molecular diffusion (Lignell et al., 2014). Forrister et al. (2015) collected filter samples in the plumes of wildfires with different transport times during the SEAC4RS campaign and found that the BrC absorbance lifetime at 370 nm was 9–15 h. Similarly, Selimovic et al. (2019) found a significant decrease in the absorption Angstrom exponent after 10 h of daytime aging during a wildfire event in the northwestern US. Sumlin et al. (2017) aged smoldering peat BBOA in an OFR and reported a decrease of ∼40 %–50 % in the aerosol mass absorption coefficients at 375 and 405 nm after 4.5 equivalent aging days. They attributed this decrease to fragmentation of BrC chromophores due to photooxidation (oxidation by gaseous OH). Based on the comparison of these observations, photooxidation could be a more important aging mechanism affecting BrC absorption lifetimes than the UV-induced photochemical processes inside the particles.

4 Conclusions and implications

Samples of BBOA particles from laboratory burns of 12 forest fire fuels collected around the United States were analyzed for BrC chromophores. Biomass fuels spanned plant types (gymnosperm versus angiosperm) and ecosystem components (duff, litter, canopy, etc.). BrC chromophores were grouped among classes, including lignin pyrolysis products, lignin-derived products, distillation products (coumarins and flavonoids), nitroaromatics, and PAHs. While most BrC chromophore classes were observed in all burns, regardless of fuel type, there were specific BrC chromophores that were divided across angiosperm (flowering) and gymnosperm (conifer) lines. For example, sinapaldehyde was mainly observed in BBOA when angiosperm fuels were burned, and coniferaldehyde was mainly observed when gymnosperm fuels were burned. Additionally, there were flavonoids specific to conifers, tentatively kaempferol and diosmetin (Table 1, chromophores 11 and 14), and unique to angiosperms such as chromophore 16. PAHs are largely angiosperm BrC chromophores, showing up mainly for sagebrush, chamise, and ceanothus fuels. There are some BrC chromophores that are only appreciably observed in a single fuel type or burn; many of these are likely distillation or lignin-derived products. The most absorbing of these BrC chromophores are components of the angiosperm BBOA (Table 2).

UV irradiation of BBOA from different fuels directly on filters removes some BrC chromophores but some appear to be photo-stable, specifically, lignin-derived compounds (including lignin-pyrolysis products) and flavonoids. Interestingly, individual BrC chromophore lifetimes varied based on the fuel burned and perhaps the underlying combustion conditions, rather than just the structure of the chromophore. Part of the reason is that co-elution of chromophores with different stabilities complicates measurements of individual chromophore lifetimes. In addition, indirect photochemical mechanisms, such as photosensitized reactions, energy loss to neighboring molecules, and shielding of light by other absorbing molecules could change depending on the specific BBOA material. The BrC chromophores of chaparral fuels had shorter equivalent photochemical lifetimes compared to BBOA generated from the canopies of conifer fuel types. On the whole, these results suggest that some of the primary BrC chromophores may be destroyed by UV irradiation after several hours.

Despite the rapid change in the absorbance of individual chromophores, the overall integrated BrC absorbance from 300 to 700 nm decayed with a much longer lifetime of 10 to 41 d. These observations contrast with individual chromophores in particles that decayed on the timescale of 0.4 to 1.6 d. Taken together, the two types of UV irradiation experiments suggest that the absorption by the complete pool of BrC compounds persists during irradiation longer than the individual BrC chromophores detected. Our findings also show that ecosystem components, and the combustion conditions they create, could influence the apparent BrC absorption lifetimes. BrC from the subalpine fir mix burned with more smoldering combustion and had the shortest equivalent lifetime of 10 d, while BBOA from the juniper and lodgepole canopy fuels had longer BrC absorption lifetimes of 25–41 d. The canopy fuels contributed to more flaming combustion. These fairly long BrC absorption lifetimes suggest that the that optical properties of BrC particles change slowly under UV-irradiated conditions and that other chemical aging mechanisms such as OH oxidation may be more important under atmospheric conditions. Based on these results, climate modelers should first focus on chemical aging mechanisms other than condensed-phase photochemistry, such as heterogeneous oxidation by OH.

Data availability
Data availability.

All data used in this study are listed within the paper.

Supplement
Supplement.

Author contributions
Author contributions.

LTF, PL and AL collected and analyzed particulate matter samples. JMR, VS and RY analyzed gaseous composition. JL, AL and SAN assisted with interpretation of mass spectrometry data. LTF did the photochemistry experiments and wrote the paper. All co-authors provided edits and critical feedback for the paper.

Competing interests
Competing interests.

The authors declare that they have no conflict of interest.

Acknowledgements
Acknowledgements.

The chemical analysis portion of this work by were supported by NOAA-CPO grant no. NA16OAR4310102 (Lauren T. Fleming and Sergey A. Nizkorodov) and NOAA-CPO grant no. NA16OAR4310101 (Peng Lin, Julia Laskin and Alexander Laskin). Vanessa Selimovic and Robert Yokelson were supported by NOAA-CPO grant no. NA16OAR4310100. The photochemistry portion of this work was supported by NSF grant no. AGS-1853639. We thank the USFS Missoula Fire Sciences Laboratory for their help in conducting these experiments. This work was also supported by NOAA's Climate Research and Health of the Atmosphere Initiative. The HRMS measurements were performed at the W.R. Wiley Environmental Molecular Sciences Laboratory (EMSL) – a national scientific user facility located at PNNL – and sponsored by the Office of Biological and Environmental Research of the U.S. DOE. PNNL is operated for the U.S. DOE by the Battelle Memorial Institute under contract no. DE-AC06-76RL0 1830.

Financial support
Financial support.

This research has been supported by the National Oceanic and Atmospheric Administration, Climate Program Office (grant nos. NA16OAR4310100, NA16OAR4310101, and NA16OAR4310102) and the National Science Foundation (grant no. AGS-1853639).

Review statement
Review statement.

This paper was edited by Ryan Sullivan and reviewed by three anonymous referees.

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