Chemical composition and light absorption of carbonaceous aerosols emitted from crop residue burning: influence of combustion efficiency
- 1State Key Joint Laboratory of Environmental Simulation and Pollution Control, College of Environmental Sciences and Engineering, Peking University, Beijing 100871, China
- 2Collaborative Innovation Center of Atmospheric Environment and Equipment Technology, Nanjing University of Information Science & Technology, Nanjing, China
- 3Key Laboratory for Urban Habitat Environmental Science and Technology, School of Environment and Energy, Peking University Shenzhen Graduate School, Shenzhen, China
- 4Beijing Innovation Center for Engineering Sciences and Advanced Technology, Peking University, Beijing 100871, China
Correspondence: Min Hu (firstname.lastname@example.org)
Biomass burning is one of the major sources of carbonaceous aerosols, which affects air quality, the radiation budget and human health. Field straw residue burning is a widespread type of biomass burning in Asia, while its emissions are poorly understood compared with wood burning emissions. In this study, lab-controlled straw (wheat and corn) burning experiments were designed to investigate the emission factors and light absorption properties of different biomass burning organic aerosol (BBOA) fractions, including water-soluble organic carbon (WSOC), humic-like substances (HULIS) and water-insoluble organic carbon (WISOC). The influences of biofuel moisture content and combustion efficiency on emissions are comprehensively discussed. The emission factors of PM2.5, organic carbon (OC) and elemental carbon (EC) were 9.3±3.4, 4.6±1.9 and 0.21±0.07 g kg−1 for corn burning and 8.7±5.0, 3.9±2.8 and 0.22±0.05 g kg−1 for wheat burning, generally lower than wood or forest burning emissions. Though the mass contribution of WISOC to OC (32 %–43 %) was lower than WSOC, the light absorption contribution of WISOC (57 %–84 % at 300–400 nm) surpassed WSOC due to the higher mass absorption efficiency (MAE) of WISOC. The results suggested that BBOA light absorption would be largely underestimated if only the water-soluble fractions were considered. However, the light absorption of WSOC in the near-UV range, occupying 39 %–43 % of the total extracted OC absorption at 300 nm, cannot be negligible due to the sharper increase of absorption towards shorter wavelengths compared with WISOC. HULIS were the major light absorption contributors to WSOC, due to the higher MAE of HULIS than other high-polarity WSOC components. The emission levels and light absorption of BBOA were largely influenced by the burning conditions, indicated by modified combustion efficiency (MCE) calculated by measured CO and CO2 in this study. The emission factors of PM2.5, OC, WSOC, HULIS and organic acids were enhanced under lower MCE conditions or during higher moisture straw burning experiments. Light absorption coefficients of BBOA at 365 nm were also higher under lower MCE conditions, which was mainly due to the elevated mass emission factors. Our results suggested that the influence of varied combustion efficiency on particle emissions could surpass the differences caused by different types of biofuels. Thus, the burning efficiency or conditions should be taken into consideration when estimating the influence of biomass burning. In addition, we observed that the ratios of and increased under higher MCE conditions due to the enhancement of potassium and chlorine released under higher fire temperatures during flaming combustion. This indicates that the potassium ion, as a commonly used biomass burning tracer, may lead to estimation uncertainty if the burning conditions are not considered.
Biomass burning emissions, as a major primary source of carbonaceous aerosols, have significant effects on air quality, human health and the regional or global radiation budget (Bond, 2004; Chen et al., 2017a; Reid et al., 2005; Saleh et al., 2015). Biomass burning could contribute one-third of the black carbon (BC) budget and two-thirds of the primary organic aerosol budget on the global scale (Bond, 2004; Bond et al., 2013). In recent years, biomass burning organic aerosols (BBOA) also attracted much attention due to their substantial contribution to light-absorbing organic aerosols, known as brown carbon (BrC) (Andreae and Gelencsér, 2006; Laskin et al., 2015; Lin et al., 2016; Saleh et al., 2014; Washenfelder et al., 2015; Yan et al., 2018). Emission factors (EFs) of BrC ranged from 1.0 to 1.4 g kg−1 biomass, comparable to those of BC (Aurell and Gullett, 2013). The majority of BrC aerosol mass was associated with biomass burning emissions in the rural southeast United States (Washenfelder et al., 2015). Regional radiative forcing effects of BrC could be comparable to those of BC over major areas dominated by biomass burning and biofuel combustion, such as South and East Asia (Feng et al., 2013).
Emission factors, chemical compositions and light absorption properties of biomass burning aerosols could be obviously influenced by different types of biomass, biofuel structures, moisture contents and especially varied burning conditions (Chen and Bond, 2010; Holder et al., 2016; Reisen et al., 2018). The emissions of particulate organics could span several orders of magnitude depending on different burning conditions (Chen et al., 2017a; Jen et al., 2019). In general, higher levels of particulate matter (PM) and organic aerosols were emitted during less efficient biomass burning, due to prolonged incomplete or smoldering combustion (Holder et al., 2016; Jen et al., 2019; Reisen et al., 2018). Open biomass burning, especially smoldering combustion, dominates the organic carbon (OC) emissions in many regions of the world on an annual-average basis (Bond, 2004). The light absorption of biomass burning aerosols is also largely dependent on the combustion conditions (Cheng et al., 2016a; Liu et al., 2014; Pokhrel et al., 2016; Saleh et al., 2014). The contribution of BrC to aerosol light absorption at near-UV wavelength was reported to be higher for more smoldering combustion compared with more flaming combustion (Holder et al., 2016). The reported variation trends of BBOA absorption properties as a function of combustion conditions, however, are not consistent among different studies. High variability in reported emission factors and optical properties of BBOA from different burning conditions complicates their treatment in climate models (Liu et al., 2014; Saleh et al., 2014) and indicates the importance of further investigations on biomass burning emissions, especially the influence of burning conditions.
Unlike the well-understood BC, the light-absorbing OC or BrC comprises a wide range of poorly characterized organic compounds, which exhibit highly variable chemical and light absorption properties (Andreae and Gelencsér, 2006; Laskin et al., 2015; Lin et al., 2016; Saleh et al., 2014; Washenfelder et al., 2015; Yan et al., 2018). Previous studies have suggested that methanol-extracted BrC was usually more light-absorbing than water extracts for BBOA or ambient aerosols (Chen and Bond, 2010; Liu et al., 2013). More than 92 % of the light-absorbing OC emitted from solid fuel pyrolysis could be extracted by methanol, compared with 73 % for water-extracted compounds (Chen and Bond, 2010). Alkaline- or methanol-extracted OC fractions were also observed with higher mass absorption efficiency (MAE) at 365 nm than water-soluble organic carbon (WSOC) for residential coal combustion (Li et al., 2018). Only considering the water-soluble BrC would result in underestimation of BrC absorption and radiative forcing (Cheng et al., 2016b, 2017). Different light absorption properties of organic fractions could be attributed to the varied chemical compositions and structures (Chen et al., 2016a, b, 2017b). However, few studies have been conducted to gain a comprehensive understanding of the influence of combustion conditions on the chemical composition and light absorption of different BBOA fractions from agricultural residue burning.
Field open burning of agriculture waste or crop residues is a widespread type of biomass burning in Asia (IARI, 2012; Bond, 2004; Streets et al., 2003). Open crop residue burning during the harvest season results in severely adverse impacts on regional air quality and human health (Chen et al., 2017a; Li et al., 2014; Lin and Yu, 2011; Streets et al., 2003; Zhang et al., 2010). The PM emission factors from agricultural waste burning range from 1.7 to 17.8 g kg−1 (Bond, 2004). Source apportionment results showed that ∼50 % of carbonaceous aerosols in Beijing were associated with biomass burning, with crop residue combustion being a major source (Cheng et al., 2013). Straw residue burning could contribute as high as 51 % of PM and 76 % of OC during harvest seasons in the agriculture regions in China (Li et al., 2014). Considering the large contribution of straw residue burning, the chemical compositions and light absorption properties of BBOA in Asia may differ from other regions whose major type of biomass burning is wood burning. However, the understanding of field straw residue burning emissions is still limited. A better characterization of the emission levels and optical properties of straw burning aerosols is required to quantify their effects on air quality and regional radiation forcing in agriculture areas (Hungershoefer et al., 2008). Laboratory simulation experiments have been suggested as a good way to study biomass burning emissions due to their advantage in quantifying emission factors and controlling combustion conditions within well-defined limits. In this study, a series of lab burning experiments were designed to systematically investigate the emission factors, chemical compositions and light absorption properties of both water-soluble and water-insoluble carbonaceous aerosols emitted from straw residue burning. The influence of biofuel moisture contents, burning conditions and combustion efficiency on the BBOA emission levels and light absorption properties is comprehensively discussed.
2.1 Simulation and sampling of biomass burning aerosols
Lab-controlled burning experiments were conducted in the Laboratory of Biomass Burning Simulation at Peking University Shenzhen Graduate School. The simulation system was designed and optimized on the basis of the one used in He et al. (2010), which included a combustion system, dilution system, sampling system and data acquisition system (Fig. S1 in the Supplement). During each experiment, about 1–2 kg biomass fuel was ignited on the combustion pan. The emitted smoke was collected by the hood above the fire and diluted by zero air (21 mol % O2 and 79 mol % N2) before being collected on filters or monitored by online instruments. Smoke aerosols were collected on both Teflon (Whatman Inc.) and quartz fiber (Whatman Inc.) filters, using a PM2.5 cutoff with a sampling flow rate of 16.7 L min−1. During each burning experiment, CO and CO2 were measured continuously by CO and CO2 analyzers (Thermo Scientific Inc., Bremen, Germany). The burning efficiency, calculated based on the online CO and CO2 data, was monitored continuously during each experiment (Table S1 in the Supplement). The variation of fire temperatures during each experiment was also measured by a sensor above the fire (Fig. S1).
In this study, the burning of corn and wheat, two kinds of primary grain crops in China, was simulated to represent the straw residue burning in China. To investigate the influence of biofuel moisture contents on burning emissions, straw with different levels of moisture contents was burned, including low (13 %) and high (18 %) levels for corn burning experiments and low (7 %–9 %), medium (18 %–22 %) and high (27 %–33 %) levels for wheat burning experiments (Table S1). The moisture content was measured by weighing the fuels before and after drying the biofuels in the oven at 105 ∘C for 24 h. Straw residues with different moisture contents were prepared by mixing weighed biofuels with weighed pure water in a plastic box and shaking until the water was absorbed. Each experiment condition was repeated three times. All the conducted experiment conditions as well as burning conditions are summarized in Table S1.
2.2 Isolation of carbonaceous aerosols
Quartz fiber filters were used to extract different carbonaceous aerosol fractions, including water-insoluble organic carbon (WISOC), WSOC and the carbon component of humic-like substances (HULISC). The filter samples were firstly extracted twice in an ultrasonic bath using 10 mL ultrapure water each time, for 30 min each. The extracts were then combined and filtered with a 0.45 µm pore size syringe filter (Gelman Sciences) to obtain the WSOC solutions. After removing the WSOC fraction on filters, the WISOC fractions were then extracted twice in an ultrasonic bath using 5 mL methanol each time, for 30 min each. The extracts then were combined and filtered using a 0.25 µm syringe filter. The HULIS fraction was isolated from the WSOC solutions via solid phase extraction (SPE), with the majority of low-molecular-weight organic acids (with relatively higher polarities) and sugars removed from the water solutions. Details about the HULIS extraction procedures were described in our previous paper (Wang et al., 2017). The WSOC fraction that excluded HULIS was high-polarity WSOC (WSOC-h) in this study.
2.3 Quantification and light absorption measurements of carbonaceous aerosols
The total OC abundance was analyzed by a thermal/optical carbon analyzer (Sunset Laboratory). The concentrations of water-soluble carbonaceous aerosol fractions, including WSOC and HULISC, were measured using a total organic carbon (TOC) analyzer (AnalytikJena multi N/C 3100). The WISOC concentrations were obtained by the difference between total OC and WSOC. The light absorption of the extracted solutions (WSOC, HULISC and WISOC) was measured by a UV–Vis spectrometer (UV-1780, Shimadzu) over the wavelength range of 300–700 nm. The absorptions of WSOC and WISOC were added up to represent the absorption of the total extracted OC. The absorption coefficients (Absλ, M m−1) and mass absorption efficiency (MAEλ) of isolated solutions at a wavelength λ were calculated as follows (Cheng et al., 2011, 2016b):
where Aλ and A700 represent the measured absorbance at wavelength λ and 700 nm. Aλ is referenced to the A700 to account for systematic baseline drift (Xie et al., 2019; Zhang et al., 2013). Vsol is the volume of extracted solutions, and Vair is the volume of air sampled through the filter punch. The optical path length (L) is 1 cm in the present experiments. ln (10) is used to convert from a common logarithm to a natural logarithm. C corresponds to the concentrations of OC, WISOC, WSOC or HULISC fractions. It is noted that the total OC was used to represent the concentration of total extracted OC, which may lead to an underestimation of MAE of WISOC. Previous studies suggested that 92 %–99.7 % of BBOA could be extracted by methanol (Chen and Bond, 2010; Xie et al., 2019); thus the residue OC un-extracted by methanol was relatively small compared with the extracted fraction. The wavelength dependence of light absorption is described using the absorption Ångström exponent (AAE), which is calculated by a linear regression fit of log (Absλ) versus log (λ) in the wavelength range of 300–450 nm.
The radiation effects of different BrC fractions (WSOC, HULIS and WISOC) relative to elemental carbon (EC, f) were estimated using a simplified model (Kirillova et al., 2014; Wu et al., 2020):
where MAEBrC, 365 and MAEEC, 870 represent the MAE of different BrC fractions at 365 nm and MAE of EC at 870 nm. AAE is the AAE value of different BrC fractions obtained in this study, and the AAE of EC is set to 1. CBrC and CEC are the concentrations of BrC and EC, and hABL is the height of the atmospheric boundary layer (1000 m). I0(λ) represents the clear-sky Air Mass 1 Global Horizontal solar irradiance (Levinson et al., 2010).
Water-soluble K+ and Cl− and low-molecular-weight organic acids (acetic acid, formic acid, succinic acid, oxalic acid, propionic acid and methanesulfonic acid) were analyzed by an ion chromatograph (DIONEX, ICS2500/ICS2000), following the procedures described in Guo et al. (2010).
3.1 Burning conditions and combustion efficiency
The burning conditions and combustion efficiency of the simulation experiments, calculated by measured CO and CO2 concentrations, are shown in Fig. 1 and Table S1. Modified combustion efficiency (MCE), defined as ), is used to indicate the burning conditions during a fire (Akagi et al., 2011; Andreae and Merlet, 2001). The burning conditions in this study varied for different fires, with the MCE ranging from 0.68 to 0.88 and an average value of 0.77. The amount and compositions of substances emitted from a given fire are determined to a large extent by the burning conditions or the ratio of flaming to smoldering combustion, which is often expressed as “combustion efficiency”. Higher MCE (>0.9) indicates more flaming combustion, and lower MCE indicates more smoldering conditions. A previous study suggested that pure flaming has an MCE near 0.99, and the MCE of most smoldering combustion is around or lower than 0.8 (Akagi et al., 2011). The burning experiments were generally dominated by smoldering combustion in the present study. Smoldering-dominated conditions, with an expected MCE<0.9 or even lower, have been widely observed during the combustion of agricultural residues in the field (IARI, 2012; Wang et al., 2017); thus the results in this study are applicable to field or related model studies.
The biomass fuels with lower moisture contents are generally burned more efficiently, with relatively higher MCE values (Table S1, Fig. S2 in the Supplement), which suggested a higher proportion of flaming combustion during the fire. The MCE of higher moisture biomass burning was generally lower, and prolonged smoldering combustion was observed (Figs. 1 and S2). Previous lab-controlled burning experiments also reported a similar phenomenon that higher fuel moisture lowers the combustion efficiency, shortens the flaming phase and introduces prolonged smoldering combustion (Chen et al., 2010). The relative proportion of flaming versus smoldering phases can vary considerably as a function of fuel moisture. A similar MCE was also observed among wheat burning experiments with different levels of moisture contents (Table S1). This was because the MCE is not only influenced by biofuel moisture contents but also the variations of biofuel structures (e.g. size), burning temperatures or ambient conditions (Chen and Bond, 2010; Lu et al., 2009; Sanchis et al., 2014). We cannot completely exclude the differences of other factors between each parallel experiment, which was the reason for repeating each condition three times in our experiment (Table S1).
Figure 1 displays variations of the monitored parameters (CO, CO2, ΔCO∕ΔCO2 and fire temperature) during two selected burning experiments (low-moisture biomass burning with MCE=0.83 and high-moisture biomass burning with MCE=0.68). Different burning conditions dominate during different periods of a fire, and the length of each period varied by experiment (Fig. 1). Actually, flaming and smoldering phases occur simultaneously during a fire, and the proportions of different combustion types vary over time (Akagi et al., 2011; Andreae and Merlet, 2001). For example, the initial period of the low-moisture biomass burning experiment (Fig. 1a) is dominated by flaming, wherein CO2 increased rapidly to the highest level and ΔCO∕ΔCO2 ratios were lower (MCE was higher) compared with the smoldering-dominated period. The fire temperatures were very high during this initially high-efficiency burning period. During the later period, smoldering dominated the burning conditions. The burning efficiency and fire temperatures decreased during this period, and ΔCO∕ΔCO2 ratios were higher than the first period. Previous ground-based and aircraft measurements of wildfire emissions also observed gradually decreased combustion efficiency of a fire over time (Collier et al., 2016). For the high-moisture biomass burning, smoldering combustion dominated the fire types during the whole period (Fig. 1b). In higher moisture fuel burns, some energy released from the combustion is first used to dry up the higher moisture of the biofuels; thus the fire temperatures and burning efficiency were lower than those of the low-moisture biomass burning.
3.2 Emission factors of carbonaceous aerosols
The average emission factors of PM2.5, OC and EC were 9.3±3.4, 4.6±1.9 and 0.21±0.07 g kg−1 for corn burning and 8.7±5.0, 3.9±2.8 and 0.22±0.05 g kg−1 for wheat burning (Fig. 2). The measured emission factors in this study fall within the range of previous straw burning experiments (4.7–12.9, 1.2–8.9 and 0.17–1.2 g kg−1 for PM2.5, OC and EC, respectively) (Akagi et al., 2011; Hays et al., 2005; Li et al., 2007). The estimated EFs from crop residue burning were generally lower than wood or forest burning emissions (Akagi et al., 2011; Aurell and Gullett, 2013; Jen et al., 2019). However, open crop residue burning in the field could result in severe air pollution during the harvest season, especially in agricultural areas in China and South Asia (IARI, 2012; Li et al., 2014; Streets et al., 2003; Venkataraman et al., 2006). This type of biomass burning cannot be neglected in these regions.
Organic matter (OM), calculated by multiplying OC by 1.3 (Li et al., 2007), was the dominant component of straw burning aerosols, which accounted for ∼64 % and ∼55 % of the PM2.5 emitted from corn and wheat burning, respectively (Fig. 2). Around 57 % and 68 % of the OC from corn and wheat burning is water-soluble, and HULISC represents 53 % and 46 % of the WSOC. Though the mass contributions of WISOC were lower than WSOC in straw burning aerosols (Fig. 2), the WISOC fractions cannot be neglected, especially when considering the light absorption properties of BBOA (see Sect. 3.4). Previous studies also suggested a large portion of WISOC in ambient aerosols, which are an important contributor of light-absorbing BrC (Cheng et al., 2016b, 2017).
The average EFs of water-soluble acetic acid, formic acid, succinic acid and oxalic acid were respectively 13.3±13.9, 4.1±3.3, 8.8±10.6 and 2.2±1.1 mg kg−1 for corn burning and 13.0±14.5, 4.7±5.3, 9.9±13.5 and 3.1±1.9 mg kg−1 for wheat burning (Fig. 2). Propionic acid and methanesulfonic acid in most samples were below the instrument detection limits in this study, and their emissions were not taken into consideration in the following discussion. The quantified water-soluble low-molecular-weight acids averagely accounted for 0.84 % (0.16 %–1.6 %) and 0.88 % (0.24 %–1.8 %) of the water-soluble OM (WSOM) emitted from corn and wheat burning. A previous study has suggested that low-molecular-weight organic acids represented an important fraction of WSOC in BBOA, and oxalic acid was a dominant short dicarboxylic (C2–C6) acid (Falkovich et al., 2005). The estimated emission factors of acetic acid and formic acid in this work were lower than those emitted from eucalypt forest fires, which were reported to be 17 and 26 mg kg−1 for flaming combustion and 104 and 94 mg kg−1 for smoldering combustion based on ground-based field measurements (Reisen et al., 2018). The difference could be attributed to different biofuels and burning conditions as well as experimental methods conducted.
Figure 2 compares the emission factors of PM2.5, carbonaceous aerosols and low-molecular-weight organic acids from straw residue burning under different levels of moisture contents. The EFs of fine particles and organic carbonaceous aerosols from high-moisture biomass burning were obviously higher than those from low-moisture biomass burning. Substantial particulate carbonaceous aerosols could be generated from the burning of higher moisture biofuels, which is mainly associated with the prolonged smoldering phases and less efficient combustion (Fig. 1, Table S1). Similar variation trends were also reported in previous biomass burning studies (Chen et al., 2010; Sanchis et al., 2014). Different levels of biofuel moisture contents will actually influence the burning conditions and thus impact the emission levels and compositions of particulate matter.
3.3 Influence of combustion efficiency on emission factors
As shown in Fig. 3, the emission factors of PM2.5 and organic carbonaceous components increased with decreasing MCE. Particle emissions were obviously enhanced under less efficient burning conditions. The emission factors of PM2.5, OC, WSOC and HULISC from the most smoldering combustion experiment were about 3.4, 4.3, 3.8 and 2.8 times those from the most flaming combustion condition, regardless of the biomass type. Similar to the emission of OC or WSOC, the emission factors of low-molecular-weight organic acids also showed increasing trends with decreasing combustion deficiency (Fig. S3 in the Supplement). These trends are generally in agreement with previous studies (Dhammapala et al., 2006; Holder et al., 2016; Jen et al., 2019; Reisen et al., 2018; Wang et al., 2013). Under the same burning conditions, the emission factors of particles or organic aerosols from corn burning were slightly higher than those from wheat burning (Fig. 3). This was mainly due to the different pyrolysis temperatures and combustion efficiency of different biofuels, which influence the burning processes (Khan et al., 2009; Zanatta et al., 2016). Our results suggested that the influence of varied burning conditions or combustion efficiency on particle emissions could surpass the differences between the two types of straw residue burning measured in this study (Fig. 3). Thus, the burning efficiency or conditions should be taken into consideration when simulating or estimating the influence of biomass burning emissions in future models.
Different from organic compounds, the emission factors of EC under different combustion efficiency remain relatively consistent (Fig. 3e). Holder et al. (2016) summarized the results from lab and field studies and also found that the black carbon emission factors from different studies are relatively constant, despite the differences in plume dilution or measurement methods (Holder et al., 2016). Some studies, however, reported an increasing trend in EC or BC emission levels with the increasing of combustion efficiency in wildfires or forest burns in the United States (Aurell and Gullett, 2013; Jen et al., 2019). As the conducted experiments were mostly dominated by smoldering combustion (MCE=0.68–0.88) in this study, we cannot exclude the possibility that the EC emissions may be higher under flaming-dominated combustion (e.g. MCE>0.9). Though the EC emission factors did not show obvious variation trends as a function of MCE, a positive correlation between ratios and combustion efficiency was observed (Fig. 3g). Due to the obvious dependence of EC ∕ OC or ratios on burning efficiency, these ratios could be employed to indicate different burning conditions when the emitted CO and CO2 data are not available, which have been used in previous studies (Xie et al., 2018, 2019).
To further investigate the influence of burning conditions on the chemical compositions of biomass burning aerosols, mass ratios of WSOC ∕ OC, HULISC ∕ OC, and as a function of burning efficiency are plotted in Fig. 4. The WSOC ∕ OC and HULISC ∕ OC mass ratios ranged from 0.52 to 0.78 and 0.16 to 0.54 among different burning experiments. The HULISC ∕ OC ratios were comparable to those (0.26–0.44, with an average of 0.34) reported in field or controlled chamber combustion experiments (Lin et al., 2010). We did not observe obvious variation trends of WSOC ∕ OC or HULISC ∕ OC ratios with MCE (Fig. 4), which indicated relative constant BBOA chemical compositions under different combustion conditions. However, the and ratios showed consistent variation trends under different MCE conditions, which increased from <0.1 under the more smoldering condition to >0.5 under the more flaming condition for and from 0.05 to >0.5 for (Fig. 4). The highest (0.64) and (0.61) ratios were observed in a low-moisture wheat burning experiment with an MCE of 0.79. This is because the K and Cl emissions from combustion are highly affected by fire temperatures and burning conditions. Lab-controlled experiments suggested that the proportions of released potassium and chlorine from the biomass fuels increase with the applied combustion temperatures (Jensen et al., 2000; Knudsen et al., 2004). Much higher fire temperatures were observed for the flaming combustion (with higher MCE) than the smoldering combustion (with lower MCE) (Fig. 1). Though the emission levels of particles or organic aerosols decreased during higher efficiency burning (Fig. 3), elevated proportions of potassium and chlorine were released into smoke during the flaming combustion phase under this condition (Fig. 4b). The two wheat burning experiments (moisture content=7 %) with higher and ratios (>0.5) than others were related to the higher combustion temperatures during the initial flaming periods of the burning experiments (Fig. S4 in the Supplement). The potassium ion is a commonly used tracer to indicate the biomass burning emissions. However, our results revealed that K+ cannot correctly indicate the emission levels of biomass burning aerosols under obviously different burning conditions, which may lead to large uncertainty in estimating burning emissions if the combustion conditions are not considered.
3.4 Light absorption of BBOA
The light absorption of straw burning organic aerosols decreased sharply from near-UV to visible wavelengths (Fig. 5), indicating their properties as biomass-burning-generated BrC. The absorption of WISOC, WSOC and HULISC at 300 nm was as high as 4.5, 15.2 and 11.2 times those at 400 nm for corn burning emissions and 4.8, 9.2 and 10.6 times those for wheat burning emissions. The wavelength dependence property of BBOA light absorption was described by AAEs derived from the absorption in the range of 300–450 nm. The AAEs of WISOC, WSOC and HULISC were respectively 5.8–5.9, 8.6–11.3 and 8.9–10.2 for corn burning aerosols and 5.7–6.0, 8.1–9.0 and 9.0–10.5 for wheat burning aerosols, and the averaged values are also shown in Fig. 5. The water-soluble BBOA fractions (WSOC and HULIS) showed stronger wavelength dependence than the water-insoluble fractions. The estimated AAE values of straw burning organic aerosols in this study are comparable to those of BBOA (5.3–8.1) and biomass burning-influenced atmospheric aerosols (5.2–9.4) reported in previous studies (Hecobian et al., 2010; Hoffer et al., 2006; Wu et al., 2018, 2019; Xie et al., 2017, 2019; Zhu et al., 2018). The strong light absorption of biomass-burning-generated BrC in the near-UV range leads to an increase in aerosol light absorption and radiative forcing efficiency (Chakrabarty et al., 2010).
The WISOC was the most important light-absorption fraction among straw burning organic aerosols, which contributed 61 %–84 % and 57 %–72 % of the light absorption (at 300–400 nm) by extracted BrC emitted from corn and wheat burning (Fig. 5). In the wavelength range of 300–400 nm, HULISC and other high-polarity WSOC (WSOC-h=WSOC-HULISC) respectively contribute to 16 %–28 % and 1 %–10 % of the total BBOA absorption for corn burning and 17 %–29 % and 12 %–15 % for wheat burning. Though the mass contribution of WISOC was lower than WSOC (Fig. 2), the light absorption of WISOC surpassed WSOC due to the higher light absorption capability of water-insoluble BBOA, indicated by the higher MAE of WISOC (Fig. 6). Meanwhile, the light absorption of water-soluble BBOA in the near-UV range cannot be neglected due to their sharper increase of absorption towards shorter wavelengths compared with WISOC (Fig. 5). The light absorption contribution of WSOC to extracted BrC increased substantially from 16 %–28 % at 400 nm to 39 %–43 % at 300 nm. Among the water-soluble BBOA, HULIS were the major contributors of light absorption, which occupied 74 % and 68 % of the WSOC absorption at 300 nm for corn and wheat burning emissions, respectively. This was due to the higher light absorption capability of HULIS than other high-polarity WSOC fractions (Fig. 6), though their mass contributions were comparable in straw burning aerosols (Fig. 2).
The light absorption capabilities of different BBOA fractions are compared in Fig. 6. The estimated MAE365 values of straw-burning-generated BrC in this study are comparable to those reported in previous studies (Fan et al., 2018; Xie et al., 2017). The MAEs of WISOC are higher than water-soluble BBOA (WSOC and HULIS) among the measured wavelength ranges for both corn and wheat burning aerosols. The MAE300 of WISOC was 1.6 and 1.7 times that of WSOC emitted from corn and wheat burning and comparable to that of HULIS (Fig. 6). Due to the slower decrease of WISOC absorption towards visible wavelengths than the water-soluble fractions (Fig. 5), the MAE365 of WISOC was as high as 2.5 and 2.2 times that of WSOC from corn and wheat burning emissions and 1.7 and 1.6 times that of HULIS. Though the mass contribution of WISOC among BBOA could be smaller than WSOC, their contribution to light absorption cannot be neglected due to the higher MAE of water-insoluble BBOA. The solar energy absorbed by biomass burning-emitted WISOC relative to EC (25 %) among the wavelength range of 300–700 nm was higher than that of WSOC (10 %) or HULIS (4 %). The light absorption of BBOA would be largely underestimated if only the water-soluble fractions are considered. Previous studies also reported a large proportion of WISOC absorption in BBOA and ambient aerosols (Cheng et al., 2016b, 2017; Park et al., 2018; Sengupta et al., 2018).
Figure 7 clearly shows the dependence of the BBOA absorption coefficient (Abs365) on burning conditions. A higher Abs365 of biomass-burning-generated BrC was observed under less efficient burning conditions for both corn and wheat burning experiments. This is mainly due to the elevated BBOA emission factors as MCE decreases (Fig. 3). We did not observe obvious dependence of MAE365 on the combustion efficiency for either water-soluble fractions or WISOC (Fig. 7d–f). Previous lab and field studies suggested that the optical properties of biomass burning aerosols are more dependent on burning conditions other than fuel types (Liu et al., 2014; Xie et al., 2017). The MAE365 of BBOA emitted from flaming combustion was reported to be higher than that from smoldering combustion based on lab-controlled burning experiments (Xie et al., 2019). Another lab experiment also suggested the dependence of MAE365 of methanol-extracted BBOA on burning conditions, while the variation trends are different regarding different fuel types or sampling methods among different experiments (Xie et al., 2017). It is noted that a limited sample population was selected to conduct the light absorption measurements and that smoldering dominated the burning conditions in this study, which could be the reasons that we did not observe an obvious dependence of MAE on combustion conditions. More lab experiments, involving larger numbers of experiments and more variable burning conditions, are required to address the influence of combustion efficiency on the light absorption capability of biomass burning-emitted carbonaceous aerosols in future studies.
The emission factors of PM2.5, OC and EC were 9.3, 4.6 and 0.21 g kg−1 for corn burning and 8.7, 3.9 and 0.22 g kg−1 for wheat burning, generally lower than wood or forest burning emissions. Around 57 % and 68 % of the OC emitted from corn and wheat burning is WSOC, among which HULISC represents 53 % and 46 % of the WSOC mass concentrations. Though the mass contribution of WISOC was lower than WSOC, the light absorption contribution of WISOC (57 %–84 % at 300–400 nm) surpassed WSOC due to the higher MAE of WISOC. The BBOA light absorption would be largely underestimated if only the water-soluble fractions were considered. Meanwhile, the light absorption of WSOC in the near-UV range, occupying 39 %–43 % of extracted OC absorption at 300 nm, cannot be neglected due to their sharper increase of absorption towards shorter wavelengths compared with WISOC. HULIS were the major light absorption contributors to WSOC, and their light absorption capability was higher than other high-polarity WSOC components.
The emission levels, compositions and light absorption of BBOA were influenced by the burning conditions. The combustion conditions varied in different burning experiments, with the MCE ranging from 0.68 to 0.88. The emission factors of PM2.5 and organic carbonaceous aerosols were obviously enhanced under less efficient burning conditions (lower MCE). The emission factors of PM2.5, OC, WSOC and HULISC from the most smoldering combustion experiment were about 3.4, 4.3, 3.8 and 2.8 times those from the most flaming combustion condition, regardless of the biofuel type employed in this study. The emission factors of PM2.5 and carbonaceous aerosols from high-moisture straw burning were obviously elevated compared with those from low-moisture straw burning experiments. This is mainly due to the prolonged smoldering and incomplete combustion period during high-moisture biomass burning.
The ratios showed a positive correlation with MCE, though EC emission factors remain relative constant under different combustion conditions. Thus, it is reasonable to employ EC ∕ OC or EC ∕ (EC+OC) ratios as an indicator of biomass burning conditions. The mass ratios of WSOC ∕ OC or HULISC ∕ OC did not display obvious variation trends under different combustion efficiency. However, the and ratios showed continuous increasing trends during higher efficiency burning, from <0.1 under the more smoldering condition to >0.5 under the more flaming condition for K+∕OC and from 0.05 to >0.5 for ratios. This is mainly attributed to the elevated proportions of released potassium and chlorine from biofuels under the higher fire temperatures during flaming combustion. Our results indicate that the potassium ion, as a commonly used biomass burning tracer, may lead to large uncertainty in estimating biomass burning emission levels if the combustion conditions are not considered.
A higher absorption coefficient (Abs365) of straw-burning-generated BrC, including WSOC, HULIS and WISOC, was observed under less efficient burning conditions for both corn and wheat burning. This is mainly attributed to the higher BBOA emission factors as MCE decreases. Our results suggested that the influence of varied combustion efficiency on the emission levels of BBOA could surpass the differences between biofuel types. Thus, the burning efficiency or combustion conditions should be taken into consideration when estimating the influence of biomass burning.
The data presented in this article are available from the authors upon request (email@example.com).
The supplement related to this article is available online at: https://doi.org/10.5194/acp-20-13721-2020-supplement.
MH, ZW, XH and LH organized the project. YW conducted the simulation experiments. YW, NX and YQ analyzed the samples. YW wrote the manuscript with input from all co-authors. All authors contributed to discussing the results and commenting on the manuscript.
The authors declare that they have no conflict of interest.
We thank Song Guo for his helpful suggestions for this study.
This research has been supported by the National Natural Science Foundation of China (grant nos. 91844301 and 91544214) and the China Postdoctoral Science Foundation (grant no. 2019M650354).
This paper was edited by Kelley Barsanti and reviewed by two anonymous referees.
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