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Effect of Organic Coatings, Humidity and Aerosol Acidity on Multiphase Chemistry of Isoprene Epoxydiols Matthieu Riva, David M. Bell, Anne-Maria Kaldal Hansen, Greg Drozd , Zhenfa Zhang, Avram Gold, Dan Imre, Jason Douglas Surratt, Marianne Glasius, and Alla Zelenyuk Environ. Sci. Technol., Just Accepted Manuscript • DOI: 10.1021/acs.est.5b06050 • Publication Date (Web): 13 May 2016 Downloaded from http://pubs.acs.org on May 17, 2016
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Effect of Organic Coatings, Humidity and Aerosol Acidity on Multiphase Chemistry of
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Isoprene Epoxydiols
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Matthieu Riva†, David M. Bell‡, Anne-Maria Kaldal Hansen§, Greg T. Drozd♯, Zhenfa
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Zhang†, Avram Gold†, Dan Imre&, Jason D. Surratt†, Marianne Glasius§,*, Alla Zelenyuk ‡,*
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† Department of Environmental Sciences and Engineering, Gillings School of Global Public
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Health, The University of North Carolina at Chapel Hill, Chapel Hill, NC, USA
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‡ Pacific Northwest National Laboratory, Richland, WA, USA
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§ Department of Chemistry, Aarhus University, Aarhus, Denmark
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♯ Department of Environmental Science, Policy, and Management, University of California,
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Berkeley, CA, USA
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&
Imre Consulting, Richland, WA, USA
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* Corresponding Authors:
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Email:
[email protected]; 3335 Innovation Blvd., Richland, WA 99354 USA
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Phone: (1) 509-371-6155; Fax: (1) 509-371-6139
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Email:
[email protected]; Langelandsgade 140, DK-8000 Aarhus C, Denmark
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Phone: (45) 8715-5923 ; Fax : (45) 8619 6199
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Keywords: IEPOX, secondary organic aerosol, heterogeneous chemistry, single particle mass
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spectrometer
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TITLE RUNNING HEAD: Multiphase chemistry of IEPOX
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ABSTRACT
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Multiphase chemistry of isomeric isoprene epoxydiols (IEPOX) has been shown to be the
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dominant source of isoprene-derived secondary organic aerosol (SOA). Recent studies have
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reported particles composed of ammonium bisulfate (ABS) mixed with model organics
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exhibit slower rates of IEPOX uptake. In the present study, we investigate the effect of
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atmospherically-relevant organic coatings of α-pinene (AP) SOA on the reactive uptake of
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trans-β-IEPOX onto ABS particles under different conditions and coating thicknesses. Single
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particle mass spectrometry was used to characterize in real-time particle size, shape, density,
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and quantitative composition before and after reaction with IEPOX. We find that IEPOX
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uptake by pure sulfate particles is a volume-controlled process, which results in particles with
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uniform concentration of IEPOX-derived SOA across a wide range of sizes. Aerosol acidity
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was shown to enhance IEPOX-derived SOA formation, consistent with recent studies. The
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presence of water has a weaker impact on IEPOX-derived SOA yield, but significantly
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enhanced formation of 2-methyltetrols, consistent with offline filter analysis. In contrast,
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IEPOX uptake by ABS particles coated with AP-derived SOA is lower compared to that of
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pure ABS particles, strongly dependent on particle composition, and therefore on particle
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size.
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INTRODUCTION
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Isoprene (2-methyl-1,3-butadiene, C5H8) is the most abundant non-methane
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hydrocarbon emitted into the atmosphere with annual emissions estimated from 500 to 750
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Tg.1 Isoprene reacts primarily with hydroxyl radicals (OH) in the troposphere,2-6 but can also
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be oxidized by nitrate radicals (NO3) or ozone (O3).7-9 Although formation of secondary
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organic aerosol (SOA) from isoprene oxidation was previously considered negligible,10,11
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research over the last decade identified a large number of highly oxidized compounds (e.g., 2-
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methyltetrols, C5-alkene triols, and organosulfates) arising from the atmospheric oxidation of
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isoprene.5-7,9,12,13 High abundance of these compounds within fine organic aerosol (PM2.5,
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aerosol with aerodynamic diameter ≤ 2.5 µm) collected from isoprene-rich regions indicates
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that isoprene could be an important SOA precursor, thereby providing a stimulus to
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understanding the pathways from isoprene to SOA.12,13
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SOA formation from isoprene oxidation is now recognized as one of the major sources
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of SOA in the atmosphere.14 Laboratory studies over the last decade have revealed the critical
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role of aerosol acidity in forming SOA from the atmospheric oxidation of isoprene.9,15-18
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Recent studies have demonstrated significant formation of SOA from the reactive uptake of
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isomeric isoprene epoxydiols (IEPOX) in the presence of acidified sulfate aerosol and
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identified a large number of highly oxidized compounds within the aerosol phase, including
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organosulfates, 2-methyltetrols, C5-alkene-triols, and oligomers.17,19-21 IEPOX has been
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shown to be an important secondary oxidation product,22 and has a key role in SOA formation
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from the oxidation of isoprene.17,19 Formation of IEPOX has been identified from the
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photooxidation of isoprene under both low- and high-NOx conditions;22,23 however, the yield
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of IEPOX is greater under low-NOx conditions. Although gas-phase OH oxidation of IEPOX
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could occur, removal of IEPOX from the gas phase is likely dominated by acid-catalyzed
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uptake reactions onto acidic sulfate aerosols.24-27 Recent field campaigns have demonstrated
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the importance of IEPOX-derived SOA products in fine organic aerosol, especially in the
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southeastern U.S. where IEPOX-derived SOA tracers can represent up to 40% of the total fine
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organic aerosol mass.28-32
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Prior studies on SOA formation have utilized primarily polydisperse ‘pure’ inorganic
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seed aerosols. However, given that atmospheric sulfate particles often contain organic
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compounds, their presence could have an impact on the multiphase chemical processes of
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IEPOX.25 It is therefore important to investigate this aspect of the IEPOX chemistry. Indeed,
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recent studies indicate that coatings composed of model oligomeric organics significantly
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reduce the uptake rate of IEPOX by sulfate particles.21,25 However, as of yet, the effect of
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atmospherically relevant SOA coatings on IEPOX heterogeneous chemistry has not been
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studied. Additionally, the relationship between particle size and the reactive uptake rate of gas
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phase molecules like IEPOX provides mechanistic information on the processes involved.
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However, particle-size effect studies on multiphase chemistry of IEPOX have not been
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explicitly conducted. The relative rates between gas-phase mass transfer and particle surface
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controlled reactive uptake govern the evolution of particle size during IEPOX uptake by
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sulfate seed particles. If diffusion kinetics or the mass accommodation rate is the limiting
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factor, the size evolution will be surface area controlled, whereas when the chemical reaction
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kinetics is the limiting step, it means the size evolution will be volume controlled. While
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some recent studies suggest that IEPOX uptake kinetics on laboratory-generated inorganic
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aerosols is a volume controlled process,25,33 results from application of Henry's law constants
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to ambient aerosols vary by order of magnitude.29
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In the present work, we investigate the effect of particle acidity and relative humidity
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(RH) on reactive uptake of trans-β-IEPOX, which is the predominant IEPOX isomer,34 onto
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sulfate seed particles. We then expand on this work with a study of the IEPOX uptake into
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acidic sulfate particles containing SOA produced from α-pinene ozonolysis. In all cases, the
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reactions are characterized as function of particle sizes. Two single particle mass
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spectrometers (miniSPLAT and SPLAT II)35 were used to characterize in-situ and in real time
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size, composition, density, and shape of individual particles before and after the uptake
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reaction, and follow the changes in particle size and mass spectral peak intensities as function
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of reaction time.
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From the data, we estimate the density of the organic moiety of IEPOX products and
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determine the weight fraction of the IEPOX-derived SOA ( ) as a function of particle
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size. Note that isoprene-derived SOA density used in air quality models is derived from
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isoprene photooxidation experiments performed under low-NOx conditions in the absence of
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sulfate particles under dry conditions.5 However, under these conditions the reactive uptake of
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IEPOX does not occur or is significantly slower25,26 than other atmospheric sinks (e.g., OH
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oxidation or deposition).33,35 Therefore, the density of SOA produced from the multiphase
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chemistry of IEPOX and acidic seeds remains unknown.
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In addition to online single particle multidimensional analysis, aerosol bulk chemical
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composition was analyzed by offline ultra-performance liquid chromatography/electrospray
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ionization, high-resolution quadrupole time-of-flight mass spectrometry (UPLC/ESI-
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QTOFMS), and gas chromatography/electron ionization-mass spectrometry (GC/EI-MS)
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analysis.
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EXPERIMENTAL SECTION
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Chamber Experiments. Experiments were conducted under wet (50-60% RH) or dry ( 99%) ozonolysis prior to IEPOX injection. In these
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experiments approximately 300 ppb of ozone was added after ABS seed injection, then 2 or 5
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0.15 µL injections of AP were made to achieve thin (~20 nm) and thick (~40 nm) coating
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thickness, respectively. Nucleation of AP ozonolysis products was prevented by multiple
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injections of AP.39 At the end of each experiment particles were collected onto Teflon
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membrane filters (47 mm diameter, 1.0 µm pore size; Pall Life Science) at a flow rate of ~ 10
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L min−1 for 70-80 min. Filters were then stored in scintillation vials in the dark at −20 °C until
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analysis.
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Single Particle Characterization. For all experiments, miniSPLAT and SPLAT II were used
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to characterize the size, density, shape, and chemical compositions of individual particles
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during the IEPOX uptake into the seed aerosol. Both instruments have been previously
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described in detail.35,40-42 Briefly, single particles are sampled through a 100 µm flow-
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calibrated critical orifice at a flow rate of 0.1 L min-1 and focused into a collimated particle
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beam in the aerodynamic lens inlet before transmission to the sizing region. Each particle is
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detected by light scattering at two optical detection stages to yield individual particle velocity,
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which is used to determine particle vacuum aerodynamic diameter (dva) with precision better
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than 0.5%.35,41 The two detection events are also used to time the triggering of a pulsed
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desorption/ionization excimer laser, operated at 193 nm with an output energy of 1.5-2.0 mJ
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per pulse, and acquire individual particle mass spectra. Each data point reported in this work
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represents the analysis of ~ 2000 individual particle mass spectra.
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In addition to sampling of the polydisperse particle flow, miniSPLAT and SPLAT II
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were used to characterize dva and mass spectra of mobility- and mass-selected particles to
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yield quantitative information on particle density or effective density, shape, and composition
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as described in detail elsewhere.41,43-45 In addition, characterization of mobility- and mass-
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selected particles over a wide range of sizes and masses makes it possible to evaluate the
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relationship between particle size and reactivity. Measurements on classified particles were
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performed at the end of each step: injection of seed particles, AP-derived SOA coating
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process, and IEPOX reactive uptake. In all the experiments conducted at elevated RH,
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particles were dried by passing through two inline diffusion dryers prior to classification and
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characterization.
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Filter Extraction and Chemical Analysis. Chemical characterization of SOA from IEPOX
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uptake was also performed by UPLC/ESI-QTOFMS (6520 Series, Agilent) operated in both
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negative and positive ion modes and by GC/EI-MS. Operating conditions have been described
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in detail elsewhere.21 Particles collected from experiments were extracted from filters with 22
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mL of high-purity methanol (LC-MS CHROMASOLV-grade, Sigma-Aldrich) by 45 min of
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sonication. Methanol extracts were then blown dry under a gentle N2(g) stream at room
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temperature. Dried extracts were reconstituted in 2 mL methanol, divided into two equal
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portions and then blown dry.
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For UPLC/ESI-QTOFMS analysis, one dried extract was reconstituted with 150 µL of
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a 50:50 (v/v) solvent mixture of methanol (LC-MS CHROMASOLV-grade, Sigma-Aldrich)
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and high-purity water (Milli-Q, 18.2 MΩ). 5 µL and 10 µL aliquots were injected onto the
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UPLC column (Waters ACQUITY UPLC HSS T3 column, 2.1 × 100 mm, 1.8 µm particle
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size) and eluted at a flow rate of 0.3 mL min-1 with a solvent mixture of methanol containing
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0.1% acetic acid or 0.1% ammonium acetate (LC-MS CHROMASOLV-grade, Sigma-
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Aldrich) and water containing 0.1% acetic acid or 0.1% ammonium acetate (LC-MS
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CHROMASOLV-grade, Sigma-Aldrich) for negative and positive mode, respectively. A
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mixture of 2-methyltetrol sulfate esters (C5H11O7S−) was synthesized in-house for use as an
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authentic standard.29
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The second portion of dried filter extract was trimethylsilylated by addition of 100 µL
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N,O-Bis(trimethylsilyl)trifluoroacetamide (BSTFA) + trimethylchlorosilane (99:1 (v/v),
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Supleco) and 50 µL pyridine (Sigma-Aldrich, 98%, anhydrous). The mixture was heated for 1
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h at 70 °C and analyzed within 24 hours following trimethylsilylation. Analyses were
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performed by GC/EI-MS at 70 eV (Hewlett 5890 Packard Series II Gas Chromatograph
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interfaced to a HP 5971A Series Mass Selective Detector, Econo-CapTM-ECTM-5 column,
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30 m × 0.25 mm × 0.25 µm). Operating conditions and temperature program of the GC/MS
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were as described previously.17 Authentic 2-methyltetrols and cis- and trans- 3-
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methyltetrahydrofuran-3,4-diols (3-MeTHF-3,4-diols) were synthesized in-house and used to
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quantify identified products.19,29
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RESULTS AND DISCUSSION
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In this study we investigate reactive uptake of trans-β-IEPOX by sulfate aerosol of
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varying acidity, and by ABS seed particles coated with AP-derived SOA of different effective
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coating thicknesses. Experiments were carried out under wet and dry conditions. Table S1
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summarizes the different experimental conditions, which were chosen to be consistent with
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those used in previous chamber experiments.21,26
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We begin by examining results from IEPOX uptake into ABS particles under dry
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conditions. Figure 1 displays a mass spectrum of IEPOX-derived SOA obtained by
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subtracting ABS mass spectral peaks from the mass spectrum of reacted ABS particles. The
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inset in Figure 1 presents the time series of the relative mass spectral intensities of the
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identified characteristic fragment ions (m/z=31 (CH3O+), 59 (C3H7O+), 61 (C3H9O+), 71
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(C4H7O+), 75 (C3H7O2+), 83 (C5H7O+), 87 (C4H7O2+), 101 (C5H9O2+), and 105 (C4H9O3+)).
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Some fragment ions have been previously observed using other types of mass spectrometers
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operated in positive ion mode in field studies and laboratory IEPOX uptake
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experiments.19,21,28,46 For example, Lin et al.21 observed the same major fragment ions as those
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shown in Figure 1 (m/z 83, 101, 105) using ESI-MS operated in the positive ion mode. Figure
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1 shows that while the relative intensity of the mass-spectral peak at m/z 87 attains a
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maximum value nearly instantaneously, the intensity of the peak at m/z 101 increases at the
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slowest rate. The different temporal evolutions suggest that fragment ions at m/z 87 and 101
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originate from different molecules. The rapid increase in the relative intensity of the ion at m/z
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87 is often followed by a decrease, suggesting it could be a fragment of IEPOX that is
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reacting in the particle, consistent with the mass spectrum of the authentic IEPOX standard
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(Figure S1). Formation of IEPOX-derived SOA is also apparent in the changes in particle
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size, an example of which is illustrated in Figure S2, showing that the particles mean mobility
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diameter (dm) increases with time (half-life of the rise of ~15 min) in response to the addition
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of IEPOX, consistent with previous observations.19,26 Filter measurements reveal the presence
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of the known IEPOX-derived SOA tracers (2-methyltetrols, C5-alkene triols, organosulfates,
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dimers, and trimers), which have been previously observed and reported from reactive uptake
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of IEPOX.17 Relative contributions of each tracer from all experiments (Table S1 and Figure
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2) reveal that experimental conditions, such as humidity, strongly impact relative
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concentrations of the identified tracers.47 The differences will be discussed in more detail in
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the following sections.
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Determination of dva of either mobility- or mass-selected particle yields information on
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the particle shape (sphericity/asphericity) and density, or effective density.41 Figure 3a
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illustrates the changes in dva distributions of mobility-selected particles (at 80, 116 and 151
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nm) due to the reaction of ABS particles with IEPOX. It shows that addition of IEPOX-
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derived SOA to the ABS seed particles results in significant decrease of dva for particles with
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the same dm, indicating a decrease in particle density. The narrow line widths of all the dva
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distributions shown in Figure 3a indicate that the particles are spherical before and after the
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reaction, and therefore that these data provide direct information on particle density.41,45
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Figure 3b shows that the density of ABS particles after the reaction with IEPOX under dry
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conditions is 1.48 ± 0.02 g cm-3, independent of particle size suggesting volume-controlled
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reactive uptake of IEPOX. It should be noted that ABS particles, even at extremely low RHs,
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are not crystalline,40 which explains their high reactivity with IEPOX under dry
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conditions.17,25-27 The measured densities of the ABS particles before and after the reaction
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with IEPOX (Figure 3b) together with the observed changes in particles size due to the
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addition of IEPOX-derived SOA (Figure S1) make it possible to estimate density of IEPOX-
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derived SOA and calculate the weight fraction of IEPOX-derived SOA in reacted sulfate
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aerosol.44 The data indicate that prior to the addition of IEPOX, ABS particles had a mean
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diameter of 122 nm (Figure S1) and a density of 1.77 ± 0.02 g cm-3 (Figure 3b). After the
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addition of IEPOX, particle mean diameter became 155 nm and the particle density decreased
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to 1.48 ± 0.02 g cm-3 (Figure 3b). Assuming volume additivity, we calculate a density of 1.2 g
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cm-3 for IEPOX-derived SOA, which then can be used to calculate the weight fraction of
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IEPOX-derived SOA = 0.41 ± 0.01 for all particle sizes.
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To evaluate the limiting reaction parameters (IEPOX and sulfate) on the reactive
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uptake of IEPOX, multiple IEPOX injections were performed. Each addition of IEPOX
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results in a decrease in particle density and with it a decrease in dva for mobility- or mass-
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selected particles (Figure S3a). Here, as well, the dva distributions of mobility- and mass-
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selected particles indicate that all particles are spherical and the density of particles, and
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therefore their composition, is independent of their size. We find that after three identical and
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successive injections of IEPOX, the weight fraction of IEPOX-derived SOA in particles
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gradually increases from of 0.41 to 0.54, with only a negligible change following the
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fourth IEPOX addition (Figure S3b). In other words, after the first IEPOX injection, a fraction
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of sulfate aerosol remains unreacted, indicating competition between kinetics of IEPOX
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reactive uptake on ABS particles and IEPOX wall loss.
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The impact of RH on IEPOX reactive uptake was evaluated by conducting the
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experiment under wet (~50% RH) conditions. Particle density and weight fraction of IEPOX-
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derived SOA were determined in the same manner as in the experiments conducted under dry
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conditions. In all experiments under wet conditions, particles were sent through a diffusion
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drier before they were characterized by the single particle mass spectrometers to avoid
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potential measurement artifacts from water.48 The data indicate that the density of particles
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reacted under wet conditions is slightly lower (1.42 ± 0.02 g cm-3) than that under dry
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conditions (1.48 ± 0.02 g cm-3). Here, as well we find that particle density, and therefore
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composition, is independent of particle size (Figure S4), suggesting volume-controlled
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reactive uptake of IEPOX. As before, particle density is used to calculate the weight fraction
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of IEPOX-derived SOA under wet conditions: = 0.49 ± 0.01, which is slightly higher
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than under dry conditions (0.41 ± 0.01). Gaston et al.25 and Riedel et al.26 reported a slight
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decrease in the reactive uptake coefficient (γ) of IEPOX uptake under comparable conditions,
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which was attributed to dilution of acidity by additional particle water. Kinetics does not
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likely explain the difference in . Moreover, the composition of IEPOX-derived SOA
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in the dry and wet experiments is found to be noticeably different. As shown in Figure 2, 2-
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methyltetrol formation is significantly enhanced in the presence of water, consistent with the
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known acid-catalyzed epoxide ring-opening mechanisms.17,47 Similarly, composition analysis
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by single particle mass spectrometry indicates that relative intensity of peaks at m/z 75 and
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105, characteristic of 2-methyltetrols (Figure S2), are ~ 3 times higher in the mass spectra of
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IEPOX-derived SOA produced under wet conditions.
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Experiments with non-acidified deliquesced ammonium sulfate (AS) seed aerosol
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under wet conditions were performed to investigate the effect of acidity on IEPOX uptake. As
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reported in Table S1, aerosol acidity differs significantly between experiments performed
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with ABS and AS seed aerosol. Unlike ABS particles, AS particles are crystalline below 35%
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RH,40 therefore in these experiments we start with wet AS particles generated at nearly 100%
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RH and reduce the RH down to ~50% RH to assure that during exposure to IEPOX the AS
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seed particles are liquid. As reminder, we note that before characterization by miniSPLAT or
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SPLAT II wet particles are always dried by passing through two inline diffusion dryers. The
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data show that following IEPOX uptake onto liquid AS seeds and subsequent drying, the
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reacted particles are spherical and have density of 1.54 ± 0.02 g cm-3 for all particle sizes
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(Figure S5). In sharp contrast, when pure AS particles are dried they effloresce to form
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aspherical crystalline AS particles, whose effective density decreases with particle size, as
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their dynamic shape factor increases with size (Figure S5), consistent with previous studies.48
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The weight fraction of IEPOX-derived SOA in this case is lower = 0.31 ± 0.01,
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which is consistent with the slower IEPOX uptake kinetics. Under comparable conditions,
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Riedel et al.26 have reported a γ two orders of magnitude lower than the γ determined from
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IEPOX uptake on wet acidified AS seed aerosol (6.5 ± 6.4 × 10-4 vs 1.9 ± 0.2 × 10-2,
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respectively). This is also consistent with previous work demonstrating that aerosol acidity
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significantly enhances IEPOX-derived SOA yields.19,21,27 Comparison of the time profiles of
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characteristic ions presented in Figures 1 and S6 shows that formation of fragment ions is
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approximately 3 times slower for AS seed. Loss of IEPOX to the walls could explain the
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lower IEPOX-derived SOA content in the particles due to slower uptake kinetics on the AS
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particles. In addition, we find that the relative intensities of peaks at m/z 87 and 101 in the AS
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seed experiments increase at nearly the same rates (Figure S6), in contrast to their temporal
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evolution observed for ABS seed aerosol (Figure 1).
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The largest mass fraction of atmospheric sub-micron aerosol is comprised of organic
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compounds that are dominated by SOA formed from the gas-phase oxidation of volatile
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organic compounds (VOCs).49 While recent studies have shown that the presence of organic
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coatings in the aerosol phase suppresses the uptake and multiphase kinetics of IEPOX,21,25
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they utilized model organics, which are not found in the atmosphere. In contrast, in the
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present study we use SOA produced from ozonolysis of α-pinene (AP-derived SOA) as a
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representative biogenic SOA commonly found in the atmosphere. ABS particles were
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exposed to oxidation products arising from AP ozonolysis prior to injection of IEPOX into
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chamber. In separate experiments, two different quantities of AP-derived SOA were deposited
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onto the ABS particles to vary the organic coating thickness (Table S1). A typical mass
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spectrum of AP-derived SOA (Figure S7) is dominated by fragment ions at m/z 43, 59 and 73.
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It should be noted that the main IEPOX-derived SOA fragment ions (m/z 75, 83, 87 and 101)
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are observed here in very low abundance. The density of AP-derived SOA coated ABS
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particles, and therefore weight fraction of AP-SOA ( ), depends on particle size (Figure
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S8). In the experiment with thinly coated ABS particles, the decreases from ~ 75 % for
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80 nm particles to ~ 15% for 500 nm particles (Figure S8b). Alternatively, the AP-derived
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SOA particle content can be expressed as an equivalent coating thickness.44 Note that since
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the exact morphology of these particles has not been established, we use the term “equivalent
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coat thickness” as a convenient measure of how much AP-SOA is present. The thin coating
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case yields 18 ± 2 nm for all particle sizes. In other words, while the coating thickness
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remains constant at 18 nm, the rapidly decreases with particle size.
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After exposure to IEPOX, the average particle mass spectrum of AP-derived SOA
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coated ABS particles exhibits high intensities of the IEPOX-derived SOA marker fragment
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ions at m/z 87 and 101 (Figure S9). The inset in Figure S9 shows the time-series of different
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fragment ions identified from reactive uptake of IEPOX onto coated acidified AS. Although
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the curves of the temporal evolution of the fragment ions are qualitatively similar to those
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observed using AS particles (Figure S6), formation of IEPOX-derived SOA is approximately
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2 times faster on the thinly AP-derived SOA-coated ABS particles. However, compared to
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experiments performed using pure ABS particles (Figure 1), both the kinetics and the
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temporal evolution curves are different, demonstrating that AP-derived SOA coatings impact
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IEPOX reactive uptake kinetics (Figure S9). After IEPOX injection, the changes in particle
339
density exhibit strong size dependence, with the particle density of the smallest particles
340
remaining unchanged, while the density of larger particles decreases significantly (Figure
341
S10a). This size-dependent pattern indicates that the IEPOX-derived SOA content increases
342
with particle size. Similarly, the relative intensities of IEPOX-derived SOA fragment ions
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also clearly show that the concentrations of the IEPOX-derived SOA products increase with
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particle size (Figure S10b). The measured particle densities can be used to calculate the
345
and as function of particle size presented in Figure 4a. This figure shows that
346
the of the smallest particles appears negligible, increasing to ~ 20% for larger
347
particles.
348
In order to compare these results with those from the pure ABS particles, the
349
with respect to ABS seed was also calculated (Figure 4b). It increases rapidly from 0 to 30%,
350
as the ABS seed aerosol diameter increases from 60 to 100 nm, and then remains nearly
351
constant at ~30% for diameters > 100 nm. As discussed above, the data on pure ABS particles
352
show that ABS core size has no effect on the reactive uptake of IEPOX, suggesting that the
353
reactive uptake of IEPOX by the coated particles is affected by the quantity of organic present
354
in the particle.
355
Figure S11 displays plotted as a function of with respect to ABS seed
356
particle. The data show that once drops below ~ 50 %, the remains constant at
357
~ 30 % with respect to ABS seed particle. Similar experiments with AP-derived SOA coated
358
ABS particles were also performed under wet conditions. As before, ABS particles were
359
coated by AP-derived SOA to form an equivalent coating thickness that was determined to be
360
22 ± 3 nm. The coated particles were then exposed to IEPOX. Both, particle density and mass
361
spectral data indicate that while smaller particles contain undetectable amounts of IEPOX-
362
derived SOA, the reaches ~ 35 % with respect to ABS seed particle when
363
drops below ~ 50 % (Figure S12), which is very similar to experiment performed under dry
364
conditions presented above. These findings imply that when particle organic content increases
365
under either dry or wet conditions, reactive uptake of IEPOX could be significantly limited
366
compared to pure ABS particles.
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Finally, ABS particles were coated with a larger quantity of AP-derived SOA to
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produce a thicker (38 ± 2 nm) organic coating (Table S1). Figure S13 shows the measured
369
densities of both AP-derived SOA coated ABS particles prior to the addition of IEPOX and
370
after the reaction, yielding that are higher than 50% for particles smaller than ~ 300 nm.
371
When these particles are exposed to IEPOX, their average mass spectra indicate very low
372
intensities for fragment ions of IEPOX-derived SOA products. Similarly, the densities of
373
these particles before and after exposure to IEPOX are nearly indistinguishable, with small
374
differences observed only for the largest particles (Figure S13), indicating that a 40 nm
375
coating of AP-derived SOA virtually halts the reactive uptake of IEPOX. Here again, IEPOX
376
uptake occurred only when dropped below ~ 50 % with respect to ABS seed particle,
377
which is consistent with other experiments described above. We conclude that the amount of
378
organics on the ABS particles plays a key role on reactive uptake of IEPOX.
379
Presence of organics on ABS particles could lead to a liquid-liquid phase separation,
380
especially at high organic loadings, as recently demonstrated.50-53 Phase separation can
381
significantly affect overall physical and chemical aerosol properties, and decrease the rate of
382
heterogeneous chemistry. For instance, organic coatings on aqueous aerosols can suppress
383
heterogeneous reactions, such as N2O5 reactive uptake.54 Similarly, semi-solid or glassy-phase
384
organics can inhibit or significantly slow down the partitioning of semivolatile products.55
385
Changes in particle composition and morphology in the presence of high amounts of organics,
386
such as phase separation, have previously been shown to have strong effects on the uptake
387
and heterogeneous chemistry of epoxides.25,56 In the present study we showed that IEPOX
388
uptake by pure inorganic particles, both AS and ABS, is a volume-controlled process, which
389
results in particles with uniform composition across a wide range of sizes. In contrast, IEPOX
390
uptake by ABS particles coated with AP-derived SOA exhibits strong dependence on the
391
, and therefore on particle size. As shown in Figure 4 and discussed above, IEPOX
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uptake occurred only when the of thin or thick coatings of AP-derived SOA on sulfate
393
aerosol dropped below ~ 50 % under both dry and wet conditions, effectively limiting IEPOX
394
uptake to larger particles with lower . Similarly to the laboratory-generated particles used
395
in this study, atmospheric particles composed of SOA and sulfates often exhibit size
396
dependent composition, with small particles being dominated by SOA.57,58 It should be also
397
noted that liquid-liquid phase separation within organic coatings is highly impacted by the
398
oxidation state of aerosol components, i.e. oxygen-to-carbon (O:C) ratios.51 In general, phase
399
separation occurred for O:C < 0.5-0.6 and not for O:C ratios above 0.8. In the intermediate
400
regime (0.6-0.8), liquid-phase separation depends on composition and organic functional
401
groups.59 Ozonolysis of AP produces SOA with O:C ratios from 0.3 to 0.4 60 and liquid-liquid
402
phase separations most likely occurred in the present study, which was already reported in
403
previous studies.
404
the key role of organic coatings on SOA formation arising from reactive uptake of IEPOX.
405
However, further studies are needed to fully resolve the impacts of varying organic coatings
406
and phase separation on IEPOX uptake and multiphase chemistry. Indeed, gas-phase
407
oxidation of other SOA precursors, such as isoprene or aromatic compounds, yield SOA with
408
O:C ratios higher than 0.6.60 Therefore, organic coatings resulting from the oxidation of the
409
other SOA precursors could adversely impact IEPOX reactive uptake, and may need to be
410
considered in explicit models of IEPOX-derived SOA formation.61, 62
51-53
This work provides new insight on isoprene SOA chemistry, showing
411 412
Supporting Information Available
413
The table provides a summary of experimental conditions. Figures show typical temporal
414
evolution of particle mean diameter during IEPOX uptake; typical particle mass spectra; time
415
evolution of the relative intensity of the major fragment ions from IEPOX uptake on seed
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particles; measured density of seed and reacted particles as a function of particle size;
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calculated weight fraction of organics and IEPOX-derived SOA as function of particle size
418
and AP-derived SOA weigh fraction. This material is available free of charge via the Internet
419
at http://pubs.acs.org/.
420 421
ACKNOWLEDGMENTS
422
The authors wish to thank the Camille and Henry Dreyfus Postdoctoral Fellowship Program
423
in Environmental Chemistry for their financial support. The authors wish also to thank Joel
424
Thornton (University of Washington) for useful discussions. This work is also funded in part
425
by the National Science Foundation under grants CHE 1404644, the Carlsberg Foundation
426
and the Centre of Excellence Cryosphere-Atmosphere Interactions in a Changing Arctic
427
Climate (CRAICC) funded by NordForsk. Work by A. Z. and the development of the
428
advanced single particle analysis methods (A.Z.) were supported by the US Department of
429
Energy, Office of Science, Office of Basic Energy Sciences (BES), Division of Chemical
430
Sciences, Geosciences & Biosciences. The part of the research was performed using EMSL, a
431
DOE Office of Science User Facility sponsored by the Office of Biological and
432
Environmental Research and located at Pacific Northwest National Laboratory.
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REFERENCES
435
1. Guenther, A. B.; Jiang, X.; Heald, C. L.; Sakulyanontvittaya, T.; Duhl, T.; Emmons, L.
436
K.; Wang, X. The Model of Emissions of Gases and Aerosols from Nature version 2.1
437
(MEGAN2.1): an extended and updated framework for modeling biogenic emissions.
438
Geosci Model Dev., 2012, 5, 1471-1492.
439 440
2. Atkinson, R. Gas-phase tropospheric chemistry of volatile organic compounds: 1. Alkanes and alkenes. J. Phys. Chem. Ref. Data 1997, 26 (2), 215-290.
441
3. Edney, E.O.; Kleindienst, T.E.; Jaoui, M.; Lewandowski, M.; Offenberg, J.H.; Wang,
442
W.; Claeys, M. Formation of 2-methyltetrols and 2-methylglyceric acid in secondary
443
organic aerosol from laboratory irradiated isoprene/NOX/SO2/air mixtures and their
444
detection in ambient PM2.5 samples collected in the eastern United States. Atmos.
445
Environ. 2005, 39 (29), 5281-5289.
446
4. Kroll, J.H.; Ng, N.L.; Murphy, S.M.; Flagan, R.C.; Seinfeld, J.H. Secondary organic
447
aerosol formation from isoprene photooxidation under high-NOx conditions. Geophys.
448
Res. Lett. 2005, 32 (18), L18808.
449
5. Kroll, J.H.; Ng, N.L.; Murphy, S.M.; Flagan, R.C.; Seinfeld, J.H. Secondary organic
450
aerosol formation from isoprene photooxidation. Environ. Sci. Technol. 2006, 40 (6),
451
1869-1877.
452
6. Surratt, J.D.; Murphy, S.M.; Kroll, J.H.; Ng, N.L.; Hildebrandt, L.; Sorooshian, A.;
453
Szmigielski, R.; Vermeylen, R.; Maenhaut, W.; Claeys, M.; Flagan, R.C.; Seinfeld,
454
J.H. Chemical composition of secondary organic aerosol formed from the
455
photooxidation of isoprene. J. Phys. Chem. A 2006, 110 (31), 9665-9690.
456
7. Ng, N.L.; Kwan, A.J.; Surratt, J.D.; Chan, A.W.H.; Chhabra, P.S.; Sorooshian, A.;
457
Pye, H.O.T.; Crounse, J.D.; Wennberg, P.O.; Flagan, R.C.; Seinfeld, J.H. Secondary
ACS Paragon Plus Environment
19
Environmental Science & Technology
Page 20 of 34
458
organic aerosol (SOA) formation from reaction of isoprene with nitrate radicals (NO3).
459
Atmos. Chem. Phys. 2008, 8 (14), 4117-4140.
460
8. Kleindienst, T.E.; Lewandowski, M.; Offenberg, J.H.; Jaoui, M.; Edney, E.O. Ozone-
461
isoprene reaction: Re-examination of the formation of secondary organic aerosol.
462
Geophys. Res. Lett. 2007, 34 (1), L01805.
463
9. Riva, M., S. H. Budisulistiorini, Z. Zhang, A. Gold, and J. D. Surratt. Chemical
464
characterization of secondary organic aerosol constituents from isoprene ozonolysis in
465
the
466
doi:http://dx.doi.org/10.1016/j.atmosenv.2015.06.027.
presence
of
acidic
aerosol,
Atmos
Environ,
2016,
130,
5-13,
467
10. Kamens, R.M.; Gery, M.W.; Jeffries, H.E.; Jackson, M.; Cole, E.I. Ozone-isoprene
468
reactions: product formation and aerosol potential. Int. J. Chem. Kinet. 1982, 14 (9),
469
955-975.
470
11. Pandis, S.N.; Paulson, S.E.; Seinfeld, J.H.; Flagan, R.C. Aerosol formation in the
471
photooxidation of isoprene and β-pinene. Atmos. Environ. Part A 1991, 25 (5-6), 997-
472
1008.
473
12. Claeys, M.; Graham, B.; Vas, G.; Wang, W.; Vermeylen, R.; Pashynska, V.; Cafmeyer,
474
J.; Guyon, P.; Andreae, M.O.; Artaxo, P.; Maenhaut, W. Formation of secondary
475
organic aerosols through photooxidation of isoprene. Science 2004, 303 (5661), 1173-
476
1176.
477
13. Wang, W.; Kourtchev, I.; Graham, B.; Cafmeyer, J.; Maenhaut, W.; Claeys, M.
478
Characterization of oxygenated derivatives of isoprene related to 2-methyltetrols in
479
Amazonian aerosols using trimethylsilylation and gas chromatography/ion trap mass
480
spectrometry. Rap. Commun. Mass Spectrom. 2005, 19 (10), 1343-1351.
ACS Paragon Plus Environment
20
Page 21 of 34
481 482
Environmental Science & Technology
14. Carlton, A.G.; Wiedinmyer, C.; Kroll, J.H. A review of secondary organic aerosol (SOA) formation from isoprene. Atmos. Chem. Phys. 2009, 9 (14), 4987–5005.
483
15. Surratt, J.D.; Kroll, J.H.; Kleindienst, T.E.; Edney, E.O.; Claeys, M.; Sorooshian, A.;
484
Ng, N.L.; Offenberg, J.H.; Lewandowski, M.; Jaoui, M.; Flagan, R.C.; Seinfeld, J.H.
485
Evidence for organosulfates in secondary organic aerosol. Environ. Sci. Technol. 2007,
486
41 (2), 517-527.
487
16. Surratt, J.D.; Lewandowski, M.; Offenberg, J.H.; Jaoui, M.; Kleindienst, T.E.; Edney,
488
E.O.; Seinfeld, J.H. Effect of acidity on secondary organic aerosol formation from
489
isoprene. Environ. Sci. Technol. 2007, 41 (15), 5363-5369.
490
17. Surratt, J.D.; Chan, A.W.H.; Eddingsaas, N.C.; Chan, M.; Loza, C.L.; Kwan, A.J.;
491
Hersey, S.P.; Flagan, R.C.; Wennberg, P.O.; Seinfeld, J.H. Reactive intermediates
492
revealed in secondary organic aerosol formation from isoprene. Proc. Natl. Acad. Sci.
493
2010, 107 (15), 6640-6645.
494
18. Wong, J.P.S.; Lee, A.K.Y.; Abbatt, J.P.D. Impacts of sulfate seed acidity and water
495
content on isoprene secondary organic aerosol formation. Environ. Sci. Technol., 2015,
496
49 (22), 13215-13221.
497
19. Lin, Y.-H.; Zhang, Z.; Docherty, K.S.; Zhang, H.; Budisulistiorini, S.H.; Rubitschun,
498
C.L.; Shaw, S.L.; Knipping, E.M.; Edgerton, E.S.; Kleindienst, T.E.; Gold, A.; Surratt,
499
J.D. Isoprene epoxydiols as precursors to secondary organic aerosol formation: acid-
500
catalyzed reactive uptake studies with authentic compounds. Environ. Sci. Technol.
501
2012, 46 (1), 250-258.
502
20. Nguyen, T.B.; Coggon, M.M.; Bates, K.H.; Zhang, X.; Schwantes, R.H.; Schilling,
503
K.A.; Loza, C.L.; Flagan, R.C.; Wennberg, P.O.; Seinfeld, J.H. Organic aerosol
ACS Paragon Plus Environment
21
Environmental Science & Technology
Page 22 of 34
504
formation from the reactive uptake of isoprene epoxydiols (IEPOX) onto non-acidified
505
inorganic seeds. Atmos. Chem. Phys. 2014, 14 (7), 3497-3510
506
21. Lin, Y.-H.; Budisulistiorini, S.H.; Chu, K.; Siejack, R.A.; Zhang, H.; Riva, M.; Zhang,
507
Z.; Gold, A.; Kautzman, K.E.; Surratt, J.D. Light-absorbing oligomer formation in
508
secondary organic aerosol from reactive uptake of isoprene epoxydiols. Environ. Sci.
509
Technol. 2014, 48 (20), 12012-12021.
510
22. Paulot, F.; Crounse, J.D.; Kjaergaard, H.G.; Kroll, J.H.; Seinfeld, J.H.; Wennberg, P.O.
511
Isoprene photooxidation: New insights into the production of acids and organic
512
nitrates. Atmos. Chem. Phys. 2009, 9 (4), 1479-1501.
513
23. Jacobs, M.I.; Burke, W.J.; Elrod, M.J. Kinetics of the reactions of isoprene-derived
514
hydroxynitrates: Gas phase epoxide formation and solution phase hydrolysis. Atmos.
515
Chem. Phys. 2014, 14 (17), 8933-8946.
516
24. Jacobs, M.I.; Darer, A.I.; Elrod, M.J. Rate constants and products of the OH reaction
517
with isoprene-derived epoxides. Environ. Sci. Technol. 2013, 47 (22), 12868-12876.
518
25. Gaston, C.J.; Riedel, T.P.; Zhang, Z.; Gold, A.; Surratt, J.D.; Thornton, J.A. Reactive
519
uptake of an isoprene-derived epoxydiol to submicron aerosol particles. Environ. Sci.
520
Technol. 2014, 48 (19), 11178-11186.
521
26. Riedel, T.P.; Lin, Y.-H.; Budisulistiorini, S.H.; Gaston, C.J.; Thornton, J.A.; Zhang,
522
Z.; Vizuete, W.; Gold, A.; Surratt, J.D. Heterogeneous reactions of isoprene-derived
523
epoxides: reaction probabilities and molar secondary organic aerosol yield estimates.
524
Environ. Sci. Technol. Lett. 2015, 2 (2), 38-42.
525
27. Liu, Y.; Kuwata, M.; Strick, B.F.; Geiger, F.M.; Thomson, R.J.; McKinney, A.;
526
Martin, S.T. Uptake of epoxydiol isomers accounts for half of the particle-phase
ACS Paragon Plus Environment
22
Page 23 of 34
Environmental Science & Technology
527
material produced from isoprene photooxidation via the HO2 pathway. Environ. Sci.
528
Technol., 2015, 49 (1), 250-258.
529
28. Budisulistiorini, S.H.; Canagaratna, M.R.; Croteau, P.L.; Marth, W.J.; Baumann, K.;
530
Edgerton, E.S.; Shaw, S.L.; Knipping, E.M.; Worsnop, D.R.; Jayne, J.T.; Gold, A.;
531
Surratt, J.D. Real-time continuous characterization of secondary organic aerosol
532
derived from isoprene epoxydiols in downtown Atlanta, Georgia, using the aerodyne
533
aerosol chemical speciation monitor. Environ. Sci. Technol. 2013, 47 (11), 5686-5694.
534
29. Budisulistiorini, S.H.; Li, X.; Bairai, S.T.; Renfro, J.; Liu, Y.; Liu, Y.J.; McKinney,
535
K.A.; Martin, S.T.; McNeill, V.F.; Pye, H.O.T.; Nenes, A.; Neff, M.E.; Stone, E.A.;
536
Mueller, S.; Knote, C.; Shaw, S.L.; Zhang, Z.; Gold, A.; and Surratt, J.D. Examining
537
the effects of anthropogenic emissions on isoprene-derived secondary organic aerosol
538
formation during the 2013 Southern Oxidant and Aerosol Study (SOAS) at the Look
539
Rock, Tennessee, ground site. Atmos. Chem. Phys., 2015, 15 (15), 8871–8888.
540
30. Hu, W.W.; Campuzano-Jost, P.; Palm, B.B.; Day, D.A.; Ortega, A.M.; Hayes, P.L.;
541
Krechmer, J.E.; Chen, Q.; Kuwata, M.; Liu, Y.J.; de Sá, S.S.; Martin, S.T.; Hu, M.;
542
Budisulistiorini, S.H.; Riva, M.; Surratt, J.D.; St. Clair, J.M.; Isaacman-Van Wertz,
543
G.; Yee, L.D.; Goldstein, A.H.; Carbone, S.; Artaxo, P.; de Gouw, J.A.; Koss, A.;
544
Wisthaler, A.; Mikoviny, T.; Karl, T.; Kaser, L.; Jud, W.; Hansel, A.; Docherty, K.S.;
545
Canagaratna, M.R.; Paulot, F.; Jimenez, J.L. Characterization of a Real-Time Tracer
546
for Isoprene Epoxydiols-Derived Secondary Organic Aerosol (IEPOX-SOA) from
547
Aerosol Mass Spectrometer Measurements. Atmos. Chem. Phys., 2015, 15 (20),
548
11807-11833.
549
31. Chen, Q.; Farmer, D.K.; Rizzo, L.V.; Pauliquevis, T.; Kuwata, M.; Karl, T.G.;
550
Guenther, A.; Allan, J.D.; Coe, H.; Andreae, M.O.; Pöschl, U.; Jimenez, J.L.; Artaxo,
ACS Paragon Plus Environment
23
Environmental Science & Technology
Page 24 of 34
551
P.; Martin, S.T. Submicron particle mass concentrations and sources in the Amazonian
552
wet season (AMAZE-08). Atmos. Phys. Chem., 2015, 15 (7), 3687-3701.
553
32. Xu, L.; Guo, H.; Boyd, C.M.; Klein, M.; Bougiatioti, A.; Cerully, K.M.; Hite, J.R.;
554
Isaacman-VanWertz, G.; Kreisberg, N.M.; Knote, C.; Olson, K.; Koss, A.; Goldstein,
555
A.H.; Hering, S.V.; De Gouw, J.; Baumann, K.; Lee, S.-H.; Nenes, A.; Weber, R.J.;
556
Ng, N.L. Effects of anthropogenic emissions on aerosol formation from isoprene and
557
monoterpenes in the southeastern United States. Proc. Natl. Acad. Sci. 2015, 112 (1),
558
37-42.
559
33. Eddingsaas, N.C.; Vandervelde, D.G.; Wennberg, P.O. Kinetics and products of the
560
acid-catalyzed ring-opening of atmospherically relevant butyl epoxy alcohols. J. Phys.
561
Chem. A 2010, 114 (31), 8106-8113.
562
34. Bates, K.H.; Crounse, J.D.; St. Clair, J.M.; Bennett, N.B.; Nguyen, T.B.; Seinfeld,
563
J.H.; Stoltz, B.M.; Wennberg, P.O. Gas phase production and loss of isoprene
564
epoxydiols. J. Phys. Chem. A 2014, 118 (7), 1237−1246.
565
35. Zelenyuk, A.; Imre, D.; Wilson, J.; Zhang, Z.; Wang, J.; Mueller, K. Airborne single
566
particle mass spectrometers (SPLAT II & miniSPLAT) and new software for data
567
visualization and analysis in a geo-spatial context. J. Am. Soc. Mass Spectr., 2015, 26
568
(2), 257-270.
569
36. Clegg, S.L.; Brimblecombe, P.; Wexler, A.S. Thermodynamic Model of the System
570
H+−NH4+−Na+−SO42−−NO3−−Cl−−H2O at 298.15 K. J. Phys. Chem. A 1998, 102 (12),
571
2155−2171.
572
37. Wexler, A.S.; Clegg, S.L. Atmospheric aerosol models for systems including the ions
573
H+, NH4+, Na+, SO42−, NO3−,Cl−, Br−, and H2O. J. Geophys. Res.: Atmos. 2002, 107
574
(D14), ACH 14-1−ACH 14-14.
ACS Paragon Plus Environment
24
Page 25 of 34
Environmental Science & Technology
575
38. Zhang, Z.; Lin, Y.-H.; Zhang, H.; Surratt, J. D.; Ball, L. M.; Gold, A. Technical note:
576
Synthesis of isoprene atmospheric oxidation products: Isomeric epoxydiols and the
577
rearrangement products cis and trans-3-methyl-3,4-dihydroxytetrahydrofuran. Atmos.
578
Chem. Phys. 2012, 12 (18), 8529−8535.
579 580
39. Lee, S.; Kamens, R.M. Particle nucleation from the reaction of α-pinene and O3 Atmos. Environ. 2005, 39 (36), 6822-6832.
581
40. Vaden, T. D., Imre, D., Beranek, J. and Zelenyuk, A. Extending the Capabilities of
582
Single Particle Mass Spectrometry: I. Measurements of Aerosol Number
583
Concentration, Size Distribution, and Asphericity. Aerosol Sci Tech. 2011, 45:113-124.
584
41. Zelenyuk, A.; Juan, Y.; Chen, S.; Zaveri, R.A.; Imre, D. A new real-time method for
585
determining particles' sphericity and density: application to secondary organic aerosol
586
formed by ozonolysis of α-pinene. Environ. Sci. Technol., 2008, 42 (21), 8033-8038.
587
42. Zelenyuk, A.; Yang, J.; Choi, E.; Imre, D. SPLAT II: An aircraft compatible, ultra-
588
sensitive, high precision instrument for in-situ characterization of the size and
589
composition of fine and ultrafine particles. Aerosol Sci. Tech. 2009, 43 (5), 411-424.
590
43. Zelenyuk, A.; Imre, D. Beyond single particle mass spectrometry: multidimensional
591
characterisation of individual aerosol particles. Int. Rev. Phys. Chem., 2009, 28 (2),
592
309-358.
593
44. Zelenyuk, A.; Yang, J.; Song, C.; Zaveri, R. A.; Imre, D. "Depth-profiling" and
594
quantitative characterization of the size, composition, shape, density, and morphology
595
of fine particles with SPLAT, a single-particle mass spectrometer. J Phys Chem A,
596
2008, 112 (4), 669-677.
597 598
45. Beranek, J.; Imre, D.; Zelenyuk, A. Real-time shape-based particle separation and detailed in situ particle shape characterization. Anal. Chem. 2012, 84 (3), 1459-1465.
ACS Paragon Plus Environment
25
Environmental Science & Technology
Page 26 of 34
599
46. Robinson, N.H.; Hamilton, J.F.; Allan, J.D.; Langford, B.; Oram, D.E.; Chen, Q.;
600
Docherty, K.; Farmer, D.K.; Jimenez, J.L.; Ward, M.W.; Hewitt, C.N.; Barley, M.H.;
601
Jenkin, M.E.; Rickard, A.R.; Martin, S.T.; McFiggans, G.; Coe, H. Evidence for a
602
significant proportion of secondary organic aerosol from isoprene above a maritime
603
tropical forest. Atmos. Chem. Phys. 2011, 11 (3), 1039–1050.
604
47. Riedel, T.P.; Lin, Y.-H.; Zhang, Z.; Chu, K.; Thornton, J.A.; Vizuete, W.; Gold, A.;
605
Surratt, J.D. Constraining condensed-phase formation kinetics of secondary organic
606
aerosol components from isoprene epoxydiols. Atmos. Chem. Phys. Discuss., 2015, 15
607
(20), 28289-28316.
608
48. Zelenyuk, A.; Cai, Y.; Imre, D. From Agglomerates of Spheres to Irregularly Shaped
609
Particles: Determination of Dynamic Shape Factors from Measurements of Mobility
610
and Vacuum Aerodynamic Diameter. Aerosol Sci. Technol. 2006, 40 (3), 197-217.
611
49. Kanakidou, M.; Seinfeld, J.H.; Pandis, S.N.; Barnes, I.; Dentener, F.J.; Facchini,
612
M.C.; Van Dingenen, R.; Ervens, B.; Nenes, A.; Nielsen, C.J.; Swietlicki, E.; Putaud,
613
J.P.; Balkanski, Y.; Fuzzi, S.; Horth, J.; Moortgat, G.K.; Winterhalter, R.; Myhre,
614
C.E.L.; Tsigaridis, K.; Vignati, E.; Stephanou, E.G.; Wilson, J. Organic aerosol and
615
global climate modelling: A review. Atmos. Chem. Phys. 2005, 5 (4), 1053-1123.
616
50. Ciobanu, V.G.; Marcolli, C.; Krieger, U.K.; Weers, U.; Peter, T. Liquid-liquid phase
617
separation in mixed organic/inorganic aerosol particles. J. Phys. Chem A 2009, 113
618
(41), 10966-10978.
619
51. Bertram, A.K.; Martin, S.T.; Hanna, S.J.; Smith, M.L.; Bodsworth, A.; Chen, Q.;
620
Kuwata, M.; Liu, A.; You, Y.; Zorn, S.R. Predicting the relative humidities of liquid-
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liquid phase separation, efflorescence, and deliquescence of mixed particles of
622
ammonium sulfate, organic material, and water using the organic-to-sulfate mass ratio
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of the particle and the oxygen-to-carbon elemental ratio of the organic component.
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Atmos. Chem. Phys. 2011, 11 (21), 10995-11006.
625
52. Renbaum-Wolff, Song, L.M.; Marcolli, C.; Zhang, Y.P.; Liu, F.; Grayson, J.W.;
626
Geiger, F.M.; Martin, S.T.; Bertram, A.K. Observations and implications of liquid–
627
liquid phase separation at high relative humidities in secondary organic material
628
produced by α-pinene ozonolysis without inorganic salts. Atmos. Chem. Phys. Discuss.
629
2015, 15 (22), 33379-33405.
630
53. Smith, M.L.; Kuwata, M.; Martin, S.T. Secondary Organic Material Produced by the
631
Dark Ozonolysis of α-Pinene Minimally Affects the Deliquescence and Efflorescence
632
of Ammonium Sulfate. Aerosol Sci. Technol. 2011, 45, 244-261.
633
54. Gaston, C.J.; Thornton, J.A.; Ng, N.L. Reactive uptake of N2O5 to internally mixed
634
inorganic and organic particles: The role of organic carbon oxidation state and inferred
635
organic phase separations. Atmos. Chem. Phys., 2014, 14 (11), 5693-5707.
636
55. Zhou, S.; Shiraiwa, M.; McWhinney, R.D.; Pöschl, U.; Abbatt, J. Kinetic limitations
637
in gas-particle reactions arising from slow diffusion in secondary organic aerosol.
638
Faraday Discuss. 2013, 165, 391-406.
639
56. Drozd, G.T.; Woo, J.L.; McNeill, V.F. Self-limited uptake of α-pinene oxide to acidic
640
aerosol: The effects of liquid-liquid phase separation and implications for the
641
formation of secondary organic aerosol and organosulfates from epoxides. Atmos.
642
Chem. Phys. 2013, 13 (16), 8255-8263.
643
57. Vaden, T.D.; Imre, D.; Beránek, J.; Shrivastava, M.; Zelenyuk, A. Evaporation
644
kinetics and phase of laboratory and ambient secondary organic aerosol. Proc. Natl.
645
Acad. Sci. 2013, 108 (6), 2190-2195.
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58. Zaveri, R.A.; Shaw, W.J.; Cziczo, D.J.; Schmid, B.; Ferrare, R.A.; Alexander, M.L.;
647
Alexandrov, M.; Alvarez, R.J.; Arnott, W.P.; Atkinson, D.B.; Baidar, S.; Banta, R.M.;
648
Barnard, J.C.; Beranek, J.; Berg, L.K.; Brechtel, F.; Brewer, W.A.; Cahill, J.F.; Cairns,
649
B.; Cappa, C.D.; Chand, D.; China, S.; Comstock, J.M.; Dubey, M.K.; Easter, R.C.;
650
Erickson, M.H.; Fast, J.D.; Floerchinger, C.; Flowers, B.A.; Fortner, E.; Gaffney, J.S.;
651
Gilles, M.K.; Gorkowski, K.; Gustafson, W.I.; Gyawali, M.; Hair, J.; Hardesty, R.M.;
652
Harworth, J.W.; Herndon, S.; Hiranuma, N.; Hostetler, C.; Hubbe, J.M.; Jayne, J.T.;
653
Jeong, H.; Jobson, B.T.; Kassianov, E.I.; Kleinman, L.I.; Kluzek, C.; Knighton, B.;
654
Kolesar, K.R.; Kuang, C.; Kubátová, A.; Langford, A.O.; Laskin, A.; Laulainen, N.;
655
Marchbanks, R.D.; Mazzoleni, C.; Mei, F.; Moffet, R.C.; Nelson, D.; Obland, M.D.;
656
Oetjen, H.; Onasch, T.B.; Ortega, I.; Ottaviani, M.; Pekour, M.; Prather, K.A.; Radney,
657
J.G.h, Rogers, R.R.; Sandberg, S.P.; Sedlacek, A.; Senff, C.J.; Senum, G.; Setyan, A.;
658
Shilling, J.E.; Shrivastava, M.; Song, C.; Springston, S.R.; Subramanian, R.; Suski,
659
K.; Tomlinson, J.; Volkamer, R.; Wallace, H.W.; Wang, J.; Weickmann, A.M.;
660
Worsnop, D.R.; Yu, X.-Y.; Zelenyuk, A.; Zhang, Q. Overview of the 2010
661
Carbonaceous Aerosols and Radiative Effects Study (CARES). Atmos. Chem. Phys.,
662
2012, 12 (16), 7647-7687.
663
59. Song, M.; Marcolli, C.; Krieger, U.K.; Zuend, A.; Peter, T. Liquid-liquid phase
664
separation in aerosol particles: Dependence on O:C, organic functionalities, and
665
compositional complexity. Geophys. Res. Lett. 2012, 39 (19), L19801.
666
60. Chhabra, P.S.; Ng, N.L; Canagaratna, M.R.; Corrigan, A.L.; Russell, L.M.; Worsnop,
667
D.R.; Flagan, R.C.; Seinfeld, J.H. Elemental composition and oxidation of chamber
668
organic aerosol. Atmos. Chem. Phys. 2011, 11 (17), 8827-8845.
669
61. McNeill, V.F.; Woo, J.L.; Kim, D.D.; Schwier, A.N.; Wannell, N.J.; Sumner, A.J.;
670
Barakat, J.M. Aqueous-phase secondary organic aerosol and organosulfate formation
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in atmospheric aerosols: A modeling study. Environ. Sci. Technol., 2012, 46 (15),
672
8075-8081.
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62. Pye, H.O.T.; Pinder, R.W.; Piletic, I.R.; Xie, Y.; Capps, S.L.; Lin, Y.-H.; Surratt, J.D.;
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Zhang, Z.; Gold, A.; Luecken, D.J.; Hutzell, W.T.; Jaoui, M.; Offenberg, J.H.;
675
Kleindienst, T.E.; Lewandowski, M.; Edney, E.O. Epoxide pathways improve model
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predictions of isoprene markers and reveal key role of acidity in aerosol formation.
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Environ. Sci. Technol., 2013, 47 (19), 11056-11064.
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Figure 1. Mass spectrum of IEPOX-derived SOA formed as a result of IEPOX uptake onto
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ABS seed aerosols under dry conditions. Inset shows the temporal evolution of the relative
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intensities of the characteristic mass-spectral peaks, including two major peaks at m/z 87 (red)
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and 101 (blue). t=0 min indicates the injection of IEPOX into the chamber.
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Figure 2. Relative contributions (% by mass) of IEPOX-derived SOA tracers by both GC/EI-
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MS and UPLC/ESI-QTOFMS in filters collected from different experiments. ABS
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corresponds to the experiment performed using ammonium bisulfate seed particle under dry
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(< 5%) and wet conditions (~ 50-55%). AS represents experiments performed using
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ammonium sulfate seed particles under wet conditions. AP-thin and AP-thick correspond to
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experiments using α-pinene (AP)-derived SOA with 18 ± 2 nm and 38 ± 2 nm equivalent
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coatings on ABS seed particles, respectively.
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Figure 3. (a) The dva distributions of ABS seed particles (blue) and ABS + IEPOX particles
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(red) classified at dm=80 nm. Note that multiply charged particles are also present. The dva of
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ABS + IEPOX particles with the same dm are smaller because of their lower density; (b) The
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measured densities of ABS seed particles (blue) and ABS + IEPOX particles (red) as a
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function of particle size.
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Figure 4. (a) The calculated weight fractions for α-pinene (AP)-derived SOA ( , green),
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the organic moiety of IEPOX-derived SOA ( , red), and total organics (
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as a function of particle size; (b) The calculated weight fractions of AP-derived SOA (green)
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and the organic moiety of IEPOX-derived SOA (red) with respect to (wrt) the ammonium
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bisulfate (ABS) seed vs. the ABS seed diameter. Open and solid circles represent repeated
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experiments.
, yellow)
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TOC Art 84x47mm (300 x 300 DPI)
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