Saccharides Emissions from Biomass and Coal Burning in Northwest China and Their Application in Source Contribution Estimation

Saccharides are important tracers in aerosol source identification but results in different areas varied significantly. In this study, six saccharides (levoglucosan, arabitol, glucose, mannitol, inositol, and sucrose) were determined for their emission factors and diagnostic ratios from domestic combustion of typical biomass and coal fuels in Northwest China. Three types of coal (i.e., anthracitic coal, bituminous coal, and briquettes) and five types of biomass (i.e., maize straw, wheat straw, corn cob, wood branches, and wood block) collected from regional rural areas were selected. Overall, the ranking of the fuel types in terms of the emission factor of particulate matter less than 2.5 μm in diameter (PM2.5) was coal < firewood fuel < straw fuel, with a range of 0.14–36.70 g/kg. Furthermore, the emission factor (e.g., organic carbon (OC) levels) of traditional stove-Heated Kang in the Guanzhong Plain differed significantly from that of wood stoves burning the same fuel, which is attributable to differences in the combustion conditions. The combined diagnostic ratios of levoglucosan (LG)/OC and arabitol/elemental carbon can be used to accurately distinguish the source contribution from coal and biomass combustion to atmospheric PM. Estimation of the biomass burning (BB) contribution to PM2.5 had an uncertainty of −2.7% to 41.0% and overestimation of 9.9–28.2% when LG was used as the sole tracer, despite its widespread use in other studies; thus, these estimation methods are inadequate and require improvement. The results also revealed that specialized emission control and clean energy strategies are required for both residential BB and non-BB sources on a regional scale.


Introduction
Although many areas in China have implemented clean energy transformation plans in recent years, coal and biomass are still major sources of energy for domestic cooking and heating purposes in most rural and suburban areas [1][2][3]. Combustion activities produce a large amount of particulate matter (PM), the constituent elements of which (e.g., organic carbon (OC), elemental carbon (EC), ions, and saccharides) affect global air quality and human health [4][5][6][7][8]. OC has both primary and secondary origins and includes components, such as polycyclic aromatic hydrocarbons with possible mutagenic and carcinogenic effects [9,10]. EC is formed from the incomplete combustion of carbon-based fuels; its strong light absorption affects the atmospheric chemical reaction process [11,12]. The optical properties and physical and chemical processes of the atmosphere are also affected by ion concentrations [13,14]. Saccharides are a major class of water-soluble organic compounds in atmospheric aerosols, which affect the hygroscopic properties of particles. Some saccharides, such as levoglucosan (LG), can be used as tracer because of its source (cellulose or hemicelluloses thermal degradation) and relatively stability in The samples were collected in rural field studies, with the sampling points located in the east, west, and middle of the Guanzhong Plain. These locations contained typical fuels used in rural areas of Northwest China. Eight selected fuels were categorized into two groups, namely coal (anthracitic coal, bituminous coal, and briquettes) and biomass (corn cob, maize straw, wheat straw, wood branches, and wood blocks). The briquettes used in this study were mostly made from anthracitic coal. These fuels were further subjected to proximate analysis to determine their moisture level, ash content, volatile matter content, and heat value, which are listed in Table 1 (on an as-received basis). Both biomass and coal fuel come from the local users for heating and cooking, and are representative. The combustion conditions in this study were the real usage conditions of the materials by local residents and could be divided into coal (coal stove) and biomass (wood stove and Heated Kang) groups. The sampling information and combustion conditions are listed in Appendix A Table A1. The traditional stove-Heated Kang is used for heating and has a long history of usage in rural areas of the Guanzhong Plain; a detailed structure of this stove is provided in Figure 1, and its characteristics are described in our previous publication [39]. The air inlet was limited to the small hole in the feed inlet which was aimed to extend the combustion time and, thus, get a slow-release effect of heat for space heating, and the oxygen supply is, thus, insufficient. local residents and could be divided into coal (coal stove) and biomass (wood stove and Heated Kang) groups. The sampling information and combustion conditions are listed in Appendix A Table A1. The traditional stove-Heated Kang is used for heating and has a long history of usage in rural areas of the Guanzhong Plain; a detailed structure of this stove is provided in Figure 1, and its characteristics are described in our previous publication [39]. The air inlet was limited to the small hole in the feed inlet which was aimed to extend the combustion time and, thus, get a slow-release effect of heat for space heating, and the oxygen supply is, thus, insufficient.

Sample Collection
A dilution sampling system was used for flue gas collection in this study, in which the dilution ratio could be adjusted 5-50 times. This device was designed and manufactured by the Desert Research Institution (Reno, NV, USA), and the specific structure is depicted in Figure 2.

Sample Collection
A dilution sampling system was used for flue gas collection in this study, in which the dilution ratio could be adjusted 5-50 times. This device was designed and manufactured by the Desert Research Institution (Reno, NV, USA), and the specific structure is depicted in Figure 2. PM 2.5 samples were collected from three parallel channels located downstream of the residence chamber at a flow rate of 5 L/min. Two channels equipped with 47-mm quartz filters (Whatman, Maidstone, Kent, UK) and another equipped with a 47-mm Teflon filter (Pall Life Sciences, Ann Arbor, MI, USA) were used. The filters were weighed before and after sampling on a microbalance (±1 µg precision, Sartorius AG MC5; Göttingen, Germany) to obtain the PM 2.5 mass. Equal gas velocity in sampling probe and stack were set initially and the vertical arrangement of sampling probe and chimney ( Figure 2) both guaranteed isokinetic conditions in this study. The extraction velocity was monitored by a flowmeter (TSI 3031, Shoreview, MN, USA). The dilution air has been dried and filtrated to guarantee a dry and clean condition; and a dilution ratio over 10 in this study could guarantee an acceptable humidity (<40%) and temperature (<25°C) for the final exhaust. The PM 2.5 sample collection efficiency was based on the design of PM 2.5 impactor (Airmetrics, Eugene, OR, USA), which has been widely employed in this field. A standard flow rate would technically guarantee the PM 2.5 cutting efficiency. The mass concentration PM2.5 samples were collected from three parallel channels located downstream of the residence chamber at a flow rate of 5 L/min. Two channels equipped with 47-mm quartz filters (Whatman, Maidstone, Kent, UK) and another equipped with a 47-mm Teflon filter (Pall Life Sciences, Ann Arbor, MI, USA) were used. The filters were weighed before and after sampling on a microbalance (±1 μg precision, Sartorius AG MC5; Göttingen, Germany) to obtain the PM2.5 mass. Equal gas velocity in sampling probe and stack were set initially and the vertical arrangement of sampling probe and chimney ( Figure 2) both guaranteed isokinetic conditions in this study. The extraction velocity was monitored by a flowmeter (TSI 3031, Shoreview, MN, USA). The dilution air has been dried and filtrated to guarantee a dry and clean condition; and a dilution ratio over 10 in this study could guarantee an acceptable humidity (<40%) and temperature (<25 ℃) for the final exhaust. The PM2.5 sample collection efficiency was based on the design of PM2.5 impactor (Airmetrics, Eugene, OR, USA), which has been widely employed in this field. A standard flow rate would technically guarantee the PM2.5 cutting efficiency. The mass concentration of each sample filter was obtained through subtraction from the field blank to eliminate any passive gas adsorption artifacts.

Chemical Analysis
OC/EC analysis: OC and EC were quantified on the basis of a punch (0.526 cm 2 ) from the quartz-fiber filter through the use of the thermal optical reflectance technique with a thermal/optical carbon analyzer (DRI Model, 2001; Atmoslytic, Calabasas, CA, USA) and the IMPROVE_A protocol (TC = EC + EC, OC = OC1 + OC2 + OC3 + OC4 + OP, EC = EC1 + EC2 + EC3-OP) [40]. The punch (0.526 cm 2 ) is heated in an oxygen-free pure He environment, setting the heating gradient to 140 ℃ (OC1), 280 ℃ (OC2), 480 ℃ (OC3), and 580 ℃ (OC4). In this process, the particulate organic carbon on the filter is burned to generate CO2; the second stage of the sample is heated in an environment of 2% oxygen and helium, and the heating gradient is 580 ℃ (EC1), 740 ℃ (EC2), and 840 ℃ (EC3). At this time, elemental carbon is oxidized to CO2 in this process. The CO2 generated under various temperature gradients is reduced to methane by MnO2 in the reduction furnace, and its concentration can be detected by the flame ion detector. Due to the coking effect produced during the heating process of the sample, some organic carbon will undergo a cracking reaction to form Pyrolysis Organic Carbon (OP). It is necessary to use a He/Ne laser with

Chemical Analysis
OC/EC analysis: OC and EC were quantified on the basis of a punch (0.526 cm 2 ) from the quartz-fiber filter through the use of the thermal optical reflectance technique with a thermal/optical carbon analyzer (DRI Model, 2001; Atmoslytic, Calabasas, CA, USA) and the IMPROVE_A protocol (TC = EC + EC, OC = OC1 + OC2 + OC3 + OC4 + OP, EC = EC1 + EC2 + EC3-OP) [40]. The punch (0.526 cm 2 ) is heated in an oxygen-free pure He environment, setting the heating gradient to 140°C (OC1), 280°C (OC2), 480°C (OC3), and 580°C (OC4). In this process, the particulate organic carbon on the filter is burned to generate CO 2 ; the second stage of the sample is heated in an environment of 2% oxygen and helium, and the heating gradient is 580°C (EC1), 740°C (EC2), and 840°C (EC3). At this time, elemental carbon is oxidized to CO 2 in this process. The CO 2 generated under various temperature gradients is reduced to methane by MnO 2 in the reduction furnace, and its concentration can be detected by the flame ion detector. Due to the coking effect produced during the heating process of the sample, some organic carbon will undergo a cracking reaction to form Pyrolysis Organic Carbon (OP). It is necessary to use a He/Ne laser with a wavelength of 633 nm to irradiate the sample under test. When the intensity change of the reflected light and transmitted light of the filter film returns to the initial value, the starting point of elemental carbon oxidation can be determined, that is, OP is returned to the OC part, and the organic carbon and elemental carbon concentration values are finally determined. The EC and OC concentrations in the sample sets were all above the detection limit (0.01 and 0.39 µg cm −2 , respectively).
Saccharides analysis: One-half of each quartz-fiber filter was extracted with highpurity dichloromethane and methanol (2:1, v/v) under ultrasonication for 15 min. The procedure was repeated three times to ensure complete extraction. The solution was then passed through Pasteur pipettes filled with sodium sulfate (Na 2 SO 4 ) and glass wool to remove water and debris from the combined extracts. A rotary evaporator under vacuum was used to concentrate the extracts to 1 mL. Aliquots of the extracts were reacted with Atmosphere 2021, 12, 821 5 of 14 N,O-bis-(trimethylsilyl)trifluoroacetamide (BSTFA) containing 1% trimethylchlorosilane and pyridine at 70 • C for 3 h. After the solution is cooled, add 40 µL internal standard (hexamethylbenzene, 1.512 ng. µL −1 ), mix well, and place in the refrigerator for testing. The silanization reaction of BSTFA can convert polar groups, such as hydroxyl groups of sugars into non-polar groups, which can be detected by gas chromatography/mass spectrometer (GC/MS) (7890A/5975C; Agilent Technologies, Santa Clara, CA, USA). One microliter of the reactant was injected into a GC/MS. The extract was injected through a GC injection port at 275 • C in an auto-sampler, and the GC separation made use of a DB-5MS fused-silica capillary column (30 m × 0.25 mm i.d., 0.25 µm film thickness, Agilent Technology). The MS was operated in the selective ion monitoring mode (SIM) with two ions monitored for each compound and dwell times ranging between 25 and 50 ms. The GC oven was programmed to increase from room temperature to 50 • C in 2 min, ramped to 120 • C (at a rate of 15 • C min −1 ), then to 300 • C (at 5 • C min −1 ), and, finally, held at 300 • C for 16 min. The target compounds were identified by comparison of their retention times and ratios of qualifier ions with those in standards. An Internal standard (IS) was added into the samples to qualify the actual amounts of the target compounds. In this study, the detection method was designed to measure saccharides, n-alkanes, and PAHs at the same time [42], resulting in pretty busy peaks in the GC/MS curve. In addition, the relatively great gap between LG and MA (GA) concentrations makes it hard to identify the small peaks of GA and MA. Therefore, these two species of saccharides were rarely detected in this study. The recoveries of organic compounds ranged from 70 to 130%, and all concentrations reported in this study were recovery and blank corrected. In addition, the concentration of LG and arabitol in source can be calculated based on their EF and stove volume (15-25 L), and details can be found in the Support Information. The concentration of LG and arabitol in stove was far greater than that in ambient [30]; thus, the ambient background can be ignored.

Data Processing
The EF is defined as the amount of pollutants emitted from a unit weight of fuel burned (on an as-received basis) [43,44] and is calculated as follows [45]: where V Total-chimney is the total volume of exhaust flowing through the chimney during the experiment (m 3 ) at a standard temperature and pressure, m fuel is the mass of the burned fuel (kg), m filter is the mass of pollutants collected on the filter (g), Q is the sampling volume through the filter (m 3 ), and DR is the dilution rate of the dilution sampling system. DR can be calculated as follows: Because the dilution channel used in the field experiment does not have real-time CO 2 concentration monitoring, its dilution factor was calculated from the flow rate of the three nodes, namely the flue gas intake Q in , the dilution gas volume Q di , and the diluted total gas volume Q t (Q t = Q in + Q di ).

General Description of PM 2.5 EFs
The statistical results of PM 2.5 and main component EFs collected from biomass and coal in different combustion conditions are presented in Table 2. Overall, the ranking of the fuel types in terms of their EFs of PM 2.5 was coal < firewood fuel < straw fuel, with a range of 0.14-36.70 g/kg. The EF of PM 2.5 in bituminous coal was an exception, with an almost 200 times higher EF than that of anthracitic coal, which can be attributed to the high volatile content in bitumite [46,47]. The difference in the PM 2.5 EFs between anthracitic coal and briquettes was nonsignificant because the main material of briquettes used in this study was anthracitic coal. The maize straw burning in the Heated Kang yielded the highest PM 2.5 EF (36.70 ± 4.12 g/kg), which was an order of magnitude higher than that recorded in the literature (2.45-8.18 g/kg) on account of its unique combustion conditions [48][49][50]. The stove structure also affects the combustion conditions [51], and Figure 1 depicts the oxygen supply in Heated Kang; it is deficient because of the windshield structure with small holes; thus, combustible PM cannot be fully oxidized before discharge [39,52]. In addition, a result of oxygen-deficient combustion, the OC emissions from straw in Heated Kang were significantly higher than those from the other fuel-stove combinations. The EFs of OC reached 20.65 ± 1.14 g/kg and 10.43 ± 1.79 g/kg for maize straw and wheat straw, respectively, which were also higher than those reported in the literature (0.85-3.21 g/kg) [53]. The EFs of PM 2.5 and OC in a firewood stove were lower than those in Heated Kang, but the EFs of EC exhibited a reverse sequence, likely due to the better ventilation and higher combustion temperature in firewood stoves than in Heated Kang [52]. Similar to their ranking in terms of EFs of PM 2.5 , the fuel types were ranked as follows according to their EFs of water-soluble ions: coal < firewood fuel < straw fuel, though with much lower concentrations (2.93-8.94%) compared with the concentrations of total carbon (32.56-71.71%). These results are consistent with those reported in the literature [54,55], indicating that the PM 2.5 emitted from household solid fuel combustion is primarily from carbon-containing substances, especially the high proportion of organic matter. Among the measured ions, that with the highest EF in coal was SO 4 2− , with a range of 3.22-300.08 mg/kg, and the anion and cation ions in biomass with the highest EFs were Cl − and K + , respectively. Measurements of Cl − and K + were higher in herbaceous fuels (corn cob, maize straw, and wheat straw) than in woody fuels (wood branches and wood blocks) [56], which could explain the different EFs of these two ions in straw and wood burning.
The EFs of saccharides, including LG, arabitol, glucose, mannitol, inositol, and sucrose, are listed in Table 2. The range of saccharide EFs for straw fuel was 315.50-434.68 mg/kg, which was higher than that for firewood fuel (104.92-274.70 mg/kg), both of which were three orders of magnitude higher than that of the saccharide EFs from coal combustion. The proportion of LG and arabitol in saccharides were the highest, collectively contributing more than 90% of the total saccharides. In terms of the high OC emission from biomass fuels, we further explored the concentrations of saccharides in OC ( Table 3). The saccharide concentration in OC for coal was 0.04‰-14.33‰ and for biomass was 21.05‰-62.00‰. Considering the large consumption of bituminous coal, the total saccharide emission from coal combustion was nonnegligible. Furthermore, the proportion of LG in the OC for coal was 0.02‰-5.33‰, and for biomass was 12.55‰-27.12‰. It is noticed that arabitol was also highly abundant in BB derived PM 2.5 which proportions in OC showed even significant difference between biomass and coal. Solid fuel combustion sources (e.g., biomass, coal, etc.) existed in the atmosphere when the proportion of LG (arabitol) in PM 2.5 OC was greater than zero. In addition, the BB contribution could be deduced, when the ratios of LG/OC and arabitol/OC were greater than 14.58‰ and 8.20‰, respectively. Considering that other saccharides may be hydrolyzed or converted from other effects (e.g., photosynthesis), LG is still undeniably an accurate indicator of saccharides in the initial inference of source, although studies have determined that LG is not solely derived from biomass and coal. However, arabitol has not yet been widely used in source identification. Note: ND denotes not detected. TC: total carbon. The data are shown as mean ± standard deviation. * denotes the sum of levoglucosan, arabitol, glucose, mannitol, inositol, and sucrose.

Comparison of Diagnostic Ratios of PM 2.5 between BB and CC
To better systematically distinguish between different sources of PM 2.5 , the proportions of specific PM 2.5 components were calculated, as detailed in Table 4. The use of specific markers and diagnostic ratios of selected individual components is a common method for source identification and apportionment [31]. The OC/EC ratio is a common diagnostic ratio used in PM 2.5 research to determine basic information regarding its main sources [49,57]. The OC/EC ranges of coal, straw fuel, and firewood fuel in this study were 0.70-6.00, 1.78-14.90, and 1.24-5.26, respectively, and were slightly higher than those previously reported in the literature [53,58,59]. The OC/EC ratios in anthracite (1.50) and briquettes (6.00) were far greater than that in bituminous coal (0.70), indicating that coal form and quality influence OC and EC emissions [60]. The OC/EC ratio in Heated Kang was higher than that in firewood stoves because of the greater production of OC in oxygen-deficient environments. In addition, because of their relatively low combustion temperatures, Heated Kang tended to generate less EC than did firewood stoves [39]. The SO 4 2− /K + ratio in straw fuel and firewood was 0.06-0.99 and 0.25-1.12 and was much smaller than that in coal (3.81-10.73). This is because biomass combustion emits a large concentration of K + but less SO 4 2− , resulting in a significantly lower ratio than in CC and other sources (e.g., firework burning: 2.1-4.8); therefore, the SO 4 2− /K + ratio can be used to identify biomass combustion sources [61]. The difference in K + /OC ratio between biomass fuel and coal was not significant, but a difference was observed in the order of magnitude of emissions between Heated Kang (0.01-0.03) and wood stoves (0.10-0.13), indicating that different ventilation conditions affected the diagnostic ratio of K + /OC. The K + /EC ratio exhibited obvious differences between coal (0.01-0.05) and biomass fuel (0.06-0.38), especially the K + /EC ratio of wheat straw in Heated Kang, which was significantly greater than that for other fuels. This phenomenon can be attributed to straw containing more K + than firewood and coal, which can be used as a key parameter in distinguishing the emissions of straw, firewood, and coal combustion [54,62,63]. Both biomass burning and coal combustion produced saccharides; thus, the ratio of some saccharides to certain components was calculated to identify the different sources. To ensure a more comparative result, we increased the ratio of saccharides to other components by a factor of 1000. The LG/OC ratio in coal was 0.02-5.33, which was almost one-tenth of that in the biomass fuel (12.55-27.12); thus, the LG/OC ratio is a reliable indicator and distinguisher. Although the difference in LG/EC ratio between coal (0.01-17.00) and biomass (18.03-236.49) was also large, their scope too close to distinguish between these two sources. Similarly, the ranges of the arabitol/OC ratio in coal (0.02-8.00) and biomass (8.20-34.85) almost overlapped, but the difference in arabitol/EC ratio between coal (0.01-12.00) and biomass (26.87-234.29) reveals the potential of the arabitol/EC ratio for distinguishing between the combustion sources of coal and biomass. An extreme ratio was observed in K + /LG, SO 4 2− /LG, and NO 3 − /LG due to the combination of extremely high ion emissions and low LG emissions; therefore, they could act as potential tracers of bituminous coal among numerous fuels. High K + /LG ratios were generally associated with low LG/TC ratios, possibly because LG can be broken down under high temperatures but K + cannot [62]. Thus, a higher K + /LG ratio may indicate the predominance of a burning condition.

Assessment of Present BB Source Contribution Estimation Methods
In addition to clarifying the factors and specific ratios of biomass and coal fuels, some saccharide molecular markers, such as LG, are often used to estimate the contribution of specific sources to the aerosol particle mass [24][25][26][27][28]. Because LG forms in relatively large amounts, is sufficiently stable, and is specific to cellulose-containing substances, it serves as an ideal molecular marker for BB. Notably, the relative contribution of LG to the PM and OC concentrations was dependent on combustion conditions and the fuel itself. In this study, taking the ambient data of Xi'an in 2015 as an example [30], we calculated the contribution of BB to ambient PM 2.5 by using equations, such as the following: The ratios of LG to PM 2.5 emitted from BB were 0.007-0.228 in the literature and 0.007 in this study ( Table 5). The results indicated that the contribution of BB to PM 2.5 was significantly different (1.4-45.1% and 42.4%, respectively) when different source data were used along with the same environmental data. Inducing uncertainty in the BB activity data, EF also varied considerably under different combustion conditions and fuel types. Therefore, selecting an appropriate source ratio, such as the local source ratio, is paramount for reducing this uncertainty and enhancing the accuracy of the BB contribution results. An increasing number of studies have proposed that LG originates not only from BB but also from municipal solid waste burning, firework burning, meat cooking, and coal burning [32,64], drawing attention to the clear overestimation of a single source that has long been overlooked in other studies. Using coal as an example, LG may be detected in coal combustion emissions and coal is the main fuel for energy supply in China. This study demonstrated that the concentration of LG in CC-derived PM 2.5 was low; however, considering its large consumption of coal in China, the contribution of CC to LG emissions cannot be ignored. We estimated respective LG emissions on the basis of the usage of coal and biomass listed in the 2020 Statistical Yearbook of Shaanxi Province, China. The total consumption of biomass fuels for burning was calculated as where M b is the dry mass of the biomass used in residential combustion (in t), P is the total production of crops (in t), R is the residue-to-crop ratio, D is the dry fraction of crop residue, H is the harvest residue fraction, and C is the ratio of the fuel consumed through residential combustion. Specific biomass parameters were detailed by Sun et al. [

Conclusions
In this study, typical biomass and coal fuels were selected to investigate emission characteristics and diagnostic ratios. We evaluated the widely used source apportionment method that considers BB as the sole source of LG and identified a high level of uncertainty in its veracity. Overall, the fuel types were ranked as follows according to their EFs of PM 2.5 : coal < firewood fuel < straw fuel. Fuel types and combustion conditions both strongly affected the EFs of PM 2.5 and the main chemical components. The LG/OC and arabitol/EC ratios can serve as suitable indicators to distinguish sources of CC and BB; however, these diagnostic ratios also varied under different combustion conditions. Other studies have typically used LG to estimate the contribution of BB to PM 2.5 and OC contents in urban sites. Uncertainties remain in BB factors, leading to large deviations (−2.7% to 41.0%) in estimates of the contribution of BB to PM 2.5 . However, studies have demonstrated that LG also has non-BB sources. On the basis of the data obtained in this study and the reported levels of coal and biomass consumption in Shaanxi Province in 2019, LG emissions were carefully estimated. The contribution of BB in Xi'an to ambient PM 2.5 was overestimated by 9.9-28.2% when non-biomass sources are considered. The results indicated that existing methods often overestimate LG emissions from BB and that the contribution from non-BB sources should not be ignored. Therefore, future studies must reevaluate the potential emission sources of LG and their ramifications for the original method of estimating the contribution of BB.

Highlights
The diagnostic ratios of levoglucosan /OC and arabitol/EC varied greatly in different fuel.
Different sources had an obvious impact on BB contribution estimation.

Appendix B. The Concentration of LG and Arabitol in Stove Calculated Method
The concentration of LG and arabitol in source can be calculated based on their EF and stove volume (15-25 L). Take LG as an example, and LG concentration can be calculated as follows: where Con LG is the concentration of LG (ng/m 3 ), EF is the emission factor of fuel (ng/kg), mfuel is the mass of the burned fuel (kg), and V is the stove volume (m 3 ).
In the previous study, we measured levoglucosan and arabitol in ambient PM 2.5 samples during summer and winter in Xi'an city, northwestern China. The results indicated that the mean concentration of levoglucosan and arabitol in winter is 268.5 ng/m 3 and 8.9 ng/m 3 , respectively. Take anthracite as an example, and the stove volume is 20 L, the estimated LG concentration in fume is 6896 ng/m 3 , which is much larger than the natural background.