Contribution of Biomass Burning to Ambient Particulate Polycyclic

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Letter

The Contribution of Biomass Burning to Ambient Particulate Polycyclic Aromatic Hydrocarbons at a Regional Background Site in East China Shuduan Mao, Jun Li, Zhineng Cheng, Guangcai Zhong, Kechang Li, Xiang Liu, and Gan Zhang Environ. Sci. Technol. Lett., Just Accepted Manuscript • DOI: 10.1021/acs.estlett.8b00001 • Publication Date (Web): 30 Jan 2018 Downloaded from http://pubs.acs.org on January 30, 2018

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Title: The Contribution of Biomass Burning to Ambient Particulate Polycyclic Aromatic Hydrocarbons at a Regional Background Site in East China

Authors: Shuduan Mao, Jun Li, Zhineng Cheng, Guangcai Zhong, Kechang Li, Xiang Liu and Gan Zhang

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The Contribution of Biomass Burning to Ambient Particulate Polycyclic Aromatic

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Hydrocarbons at a Regional Background Site in East China

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Shuduan Mao†,‡, Jun Li †, Zhineng Cheng †, Guangcai Zhong †, Kechang Li †, Xiang Liu † and Gan

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Zhang *,†

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Academy of Sciences, Guangzhou 510640, China

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Supporting Information

State Key Laboratory of Organic Geochemistry, Guangzhou Institute of Geochemistry, Chinese

University of Chinese Academy of Sciences, Beijing 100049, China

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ABSTRACT: Biomass burning has a significant impact on regional air quality, public health, and

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climate change. It is an important source of particulate polycyclic aromatic hydrocarbons (PAHs),

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which are a major class of toxic air pollutants. To estimate the contribution of biomass burning to

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ambient particulate PAH concentrations, fifteen PAHs and three anhydrosugars (levoglucosan,

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galactosan, and mannosan) were analyzed in particulate samples collected at a background site in east

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China from August 2012 to August 2015. Higher concentrations of all species were observed in fall

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and winter. Indoor biofuel combustion in north China was considered to be the major contributor to

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the high concentrations of anhydrosugars in fall and winter, because there were few fires detected on a

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fire count map for this period. A tracer-based approach, using the ratio of PAHs to levoglucosan

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(PAHs/Lev) in fresh biomass burning aerosols, was proposed and used to estimate the contribution of

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biomass burning to PAHs. The results showed that biomass burning contributed nearly 11% of the

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total particulate PAHs. The estimation of the contribution from biomass burning using PAHs/Lev

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agreed well with the results obtained from an independent positive matrix factorization (PMF)

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analysis.

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INTRODUCTION

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Biomass burning in both open field fires and domestic biofuel combustion can emit large

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amounts of greenhouse gases, trace gases and particulate matter, which can affect air quality, public

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health, and climate change.1, 2 Studies of ambient volatile organic compounds (VOCs) at a receptor site

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in Pearl River Delta during October-November 2008 have revealed that biomass burning accounts for

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9–37% of the mixing ratios of selected VOC species, with the figure being > 30% for aromatics,

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formaldehyde, and acetaldehyde.3 Model- and observation-based estimations have indicated that open

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biomass burning accounts for 37% of PM2.5 in the Yangtze River Delta during the harvest period in

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summer 2011.4 Radiocarbon (14C)-based source apportionment studies at south of Hainan Island from

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May 2005 to August 2006 and at Gosan, Korea from April 2013 to April 2014 have shown that

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biomass burning could account for > 30% of the organic carbon (OC) concentrations in China.5, 6

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Among the trace substances emitted from biomass burning, there are also polycyclic aromatic

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hydrocarbons (PAHs), an important class of persistent organic pollutants (POPs).7,

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generated by the incomplete combustion of biomass and fossil fuels.9 They are ubiquitous in the

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atmosphere and are considered to be a major class of toxic air pollutant.10, 11 They can cause serious

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health effects due to their carcinogenicity and mutagenicity. In recent decades, PAHs have attracted

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considerable public and scientific attention, especially in China where high PAH concentrations are

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frequently reported.11, 12 Efforts have been made to estimate PAH emissions. An emission inventory in

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2004 indicated that China was one of the largest PAH emitters in the world, and that biomass

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combustion and coke ovens were the most important sources.13 Latterly, an updated global PAHs 3

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PAHs are

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emission inventory for a period from 1960 to 2008 suggested that biomass fuels were the globally

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major PAH sources.12 Due to economic considerations and the promotion of coal consumption

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reduction policies, biomass fuel has become a popular alternative energy source to fossil fuels in

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households, and manufacturing and service industries in rural regions.14, 15 Therefore, assessment of

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the contribution of biomass fuels to ambient PAH levels is of great significance. Molecular markers,

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especially levoglucosan (lev), can be used to quantify the contribution of biomass burning to

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atmospheric pollutants, such as particulate matter and OC aerosol.16, 17 A lev-based approach may

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therefore also have the potential to quantify the contribution of biomass burning to PAH

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concentrations.

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A biomass burning plume not only has a local impact, but also has effects at the regional scale

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through long range transport.18 As one of the most economically developed regions in China, east

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China experiences serious air pollution. Although it is not a high emission intensity area for PAHs

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from biomass burning, the outflow flux of PAHs from north China has resulted in elevated

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concentrations of atmospheric PAHs in this region.19 Additionally, it is reported that most PAHs were

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transported out of China through the eastern boundary.19 Therefore, Ningbo Atmospheric Environment

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Observatory (NAEO, 29°40.8′N, 121°37′E, 550 m ASL) in east China, which is a key site on the

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outlet transport route for aerosols from the Chinese continent to the Pacific Ocean, was selected as a

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regional background site to monitor PAHs in this study (Figure S1). The sampling site has been

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described in previous report.20 The aim of this study was to apportion the sources of PAHs and

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estimate the contribution of biomass burning to particulate PAHs in east China.

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MATERIALS AND METHODS

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Sampling. Since the year 2012, successive 24 h total suspended particle samples were collected

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once a week at NAEO by high volume air samplers fitted with quartz microfiber filters (QFFs) (Grade

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GF/A, 20.3 × 12.7 cm; Ahlstrom Munktell, Falun, Sweden) operating at 300 L/min. The QFFs were

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baked at 450°C for 6 h before sampling and then sealed and stored at -20°C after collection. A total of

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73 QFF samples, i.e., 1 from each fortnight from August 2012 to August 2015, were used in this study.

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Sample Pretreatment and Analysis. Details of the sample treatment and analytical method can

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be found in Text S1 in the Supporting Information. Briefly, a section of each filter sample was spiked

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with perdeuterated PAHs as surrogates and extracted in a Soxhlet apparatus for 24 h with

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dichloromethane (DCM). The extracts were further purified on a multilayer neutral silica gel column.

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15 PAHs were then quantified by gas chromatography–mass spectrometry (GC-MS), with a DB-5MS

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capillary column (30 m × 0.25 mm × 0.25 µm, model 7890/5975; Agilent, Santa Clara, CA, USA):

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acenaphthene(Ace), acenaphtylenc(Acy), fluorene (Flu), phenanthrene (Phe), anthracene (Ant),

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fluoranthene (Fla), pyrene (Pyr), benzo[a]anthracene (BaA), chrysene (Chr), benzo[b]fluoranthene

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(BbF), benzo[k]fluoranthene (BkF), benzo[a]pyrene (BaP), dibenzo[a,h]anthracene (DahA),

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benzo[g,h,i]perylene (BghiP) and indeno[1,2,3-c,d]pyrene (IcdP).

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A section of each sample was spiked with

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C labeled lev as a recovery standard and Soxhlet

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extracted for 24 h with DCM/methanol (40:3 by volume) to analyze anhydrosugars. The extracts were

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anhydrated with an anhydrous sodium sulfate column, spiked with methyl-β-L-xylanopyranoside

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(m-XP) as an internal standard and then dried completely by a gentle nitrogen stream. Finally, a

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derivatization reagent (a mixture of N,O-Bis(trimethylsilyl) trifluoroacetamide (1% trimethylsilyl

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chloride) and pyridine) was added for the sequent reaction (70°C, 1 h). The resulting solution was then

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immediately analyzed by GC-MS.

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A punch of each filter was analyzed to determine the organic carbon (OC) and elemental carbon

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(EC) concentrations by a DRI Model 2015 Thermal/Optical Carbon Analyzer (Atmoslytic Inc.,

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Calabasas, CA). Details of analytical method can be found in Text S1.

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Quality Control. Laboratory and field blank filters were analyzed. The method detection limit

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(MDL) was defined as the average of all blanks plus three times the standard deviation. The MDLs of

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each target compound are listed in Table S1. The average recoveries were 75 ± 15%, 91 ± 12%, 101 ±

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14%, 100 ± 19%, and 95 ± 14% for acenapthene-d10, phenanthrene-d10, chrysene-d12, perylene-d12,

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and 13C labeled lev, respectively. All reported values were corrected for recovery in this study.

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Air Mass Back Trajectories. Five-day back trajectories were calculated at 6 h intervals for the

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campaign period using the HYSPLIT model (http://ready.arl.noaa.gov/HYSPLIT.php). All individual

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trajectories were clustered for each season, as shown in Figure S1. The air mass mostly originated

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from the west Pacific and the South China Sea in summer, and passed over the continental regions in

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Mongolia and north China during other seasons.

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RESULTS AND DISCUSSION

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Temporal Variations and Correlations between Lev and Particulate PAHs. The

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concentrations of 15 particulate PAHs, 3 anhydrosugars, OC and EC are listed in Table S2. The

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composition of PAHs in this study was dominated by high molecular weight PAHs, with low vapor

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pressures. Anhydrosugars were composed primarily of levo (91 ± 4.4%), followed by mannosan (6.1 ±

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3.3%), and galactosan (3.3 ± 1.7%). A time-series of particulate PAHs, three anhydrosugars, OC and

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EC from August 2012 to August 2015 is shown in Figure S2. The average concentrations of each

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species in different seasons are listed in Table S3. Seasonal characteristics were observed for each

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species, with the highest average concentrations being in winter (December to February) and fall

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(September to November), and the lowest in summer (June to August).

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Five-day backward trajectories showed that air masses passed over north China in winter, where

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biofuel and fossil fuel are typically used for household heating. During summer, the air masses

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originated from the west Pacific or the South China Sea. The low abundance of components at this

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time was mostly attributed to clean-air-masses originating from marine areas. According to fire count

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maps for each season (Figure S3), produced by the satellite based Moderate Resolution Imaging

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Spectroradiometer (MODIS), few wild fires occurred in China during winter and fall when the highest

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concentration of lev was observed. Moreover, air masses passed over north China during winter and

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fall. These results suggested that high concentrations of 3 anhydrosugars were mostly attributed to

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indoor biofuel combustion in north China (such as domestic heating by biomass and combustions of

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agricultural crops and wood in domestic stoves), which could not be detected by satellites.

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Correlations between lev (a well-known biomass burning tracer) and individual selected

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particulate PAH compounds were estimated and the Person correlation coefficients (r) are displayed in

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Table 1. The correlation coefficients (r) were above 0.75 for 71 samples with each particulate

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compound. The strong correlations between lev and particulate PAH congeners, as showed in Table 1,

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would suggest a strong association of the PAHs to particulate, from source/origin to atmospheric

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processes.

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Table 1. Correlations between lev and individual particulate PAH compounds during the whole sampling

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campaign Lev vs. particulate PAHs

N

r

P

Lev vs.Phe

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0.75