Modeling organic aerosol over Europe in summer conditions with the VBS-GECKO parameterization: sensitivity to secondary organic compound properties and IVOC (intermediate-volatility organic compound) emissions

The VBS-GECKO (volatility basis set – Generator for Explicit Chemistry and Kinetics of Organics in the Atmosphere) parameterization for secondary organic aerosol (SOA) formation was integrated into the chemistry-transport model CHIMERE. Concentrations of organic aerosol (OA) and SOA were simulated over Europe for the July–August 2013 period. Simulated concentrations with VBS-GECKO were compared to results obtained with the former H2O parameterization implemented in CHIMERE and to observations from EMEP, ACTRIS and other observations available in the EBAS database. The model configuration using the VBS-GECKO parameterization slightly improves the performances compared to the model configuration using the former H2O parameterization. The VBS-GECKO model configuration performs well for stations showing a large SOA concentration from biogenic sources, especially in northern Europe, but underestimates OA concentrations over stations close to urban areas. Simulated OA was found to be mainly secondary (∼ 85 %) and from terpene oxidation. Simulations show negligible contribution of the oxidation of monoaromatic compounds to SOA production. Tests performed to examine the sensitivity of simulated OA concentrations to hydro-solubility, volatility, aging rates and NOx regime have shown that the VBS-GECKO parameterization provides consistent results, with a weak sensitivity to changes in the parameters provided by the gas-phase mechanism included in CHIMERE (e.g., HOx or NOx concentrations). Different scenarios considering intermediate-volatility organic compound (IVOC) emissions were tested to examine the contribution of IVOC oxidation to SOA production. At the continental scale, these simulations show a weak sensitivity of OA concentrations to IVOC emission variations. At the local scale, accounting for IVOC emissions was found to lead to a substantial increase in OA concentrations in the plume from urban areas. This additional OA source remains too small to explain the gap between simulated and measured values at stations where anthropogenic sources are dominant. Published by Copernicus Publications on behalf of the European Geosciences Union. 4906 V. Lannuque et al.: Modeling organic aerosol over Europe in summer conditions


Introduction
For the past 20 years, fine particulate matter or PM 2.5 (particles with diameters smaller than 2.5 µm) has been regulated due to its health impacts and the resulting costs (e.g., Lim et al., 2012;WHO Regional Office for Europe and OECD, 2015). Furthermore, fine particles degrade visibility (e.g., Han et al., 2012) and influence climate change (e.g., Boucher et al., 2013). Organic aerosol (OA) represents a large fraction of the total fine particle mass (e.g., Jimenez et al., 2009). This OA is either primary (directly emitted into the atmosphere) or secondary (formed by gas-particle partitioning of low volatility and/or highly soluble species produced during the oxidation of gaseous organic compounds) (e.g., Carlton et al., 2009;Kroll and Seinfeld, 2008). The secondary organic aerosol (SOA) dominates the primary organic aerosol (POA) in most environments (e.g., Gelencsér et al., 2007;Jimenez et al., 2009).
Chemistry-transport models (CTMs) are used to investigate and identify air quality regulation policies. Parameterizations are developed and used in CTMs to represent SOA formation. Different approaches have been followed to describe SOA formation as the two-product model (e.g., Odum et al., 1996;Schell et al., 2001), the molecular approach (e.g., Pun et al., 2002Pun et al., , 2003, the volatility basis set (VBS) approach (e.g., Donahue et al., 2006Donahue et al., , 2012 or the statistical oxidation model (SOM) (e.g., Cappa and Wilson, 2012;Jathar et al., 2015). Parameterizations are constantly improved and additional processes were included in the parameterizations to improve the simulations of SOA concentrations, such as gas-phase aging of organic species (e.g., Rudich et al., 2007) and more comprehensive emissions and multiphase chemistry. Robinson et al. (2007) have indeed shown that POA provided in emission inventories is in part composed of semivolatile organic compounds (SVOCs) (existing both in particle and gas phases) and that a fraction of emitted organic compounds were missing from these inventories: the intermediate-volatility organic compounds (IVOCs) (forming SOA after several oxidation stages) (e.g., Ots et al., 2016;Robinson et al., 2007;Woody et al., 2015). Numerous experimental and modeling studies have since explored the volatility distribution of SVOCs from POA emissions and of IVOC emissions depending on the emission source (e.g., Akherati et al., 2019;Grieshop et al., 2009;Hatch et al., 2018;Jathar et al., 2017;Louvaris et al., 2017;Lu et al., 2018;May et al., 2013a, b, c;Woody et al., 2016).
Most of these SOA parameterizations are optimized and built on the basis of atmospheric chamber data. Experiments are, however, limited in number and are usually performed under conditions that differ from the atmosphere. In addition, SOA formation experiments can be subject to potential artifacts from chamber wall surfaces, such as aerosol and gaseous compound wall losses (e.g., La et al., 2016;Matsunaga and Ziemann, 2010;McMurry and Grosjean, 1985). Considering or not these artifacts for the parameterization development directly impacts SOA representation in air quality models (e.g., Cappa et al., 2016).
The development of the VBS-GECKO (volatility basis set -Generator for Explicit Chemistry and Kinetics of Organics in the Atmosphere) parameterization explores another track using the results of an explicit model to represent the organic gas-phase chemistry and gas-particle mass transfer instead of atmospheric chamber data. The VBS-GECKO parameterization for SOA formation (Lannuque et al., 2018a) is a VBS-type parameterization with gaseous aging. VBS-GECKO was optimized based on box modeling results using explicit oxidation mechanisms generated with the Generator for Explicit Chemistry and Kinetics of Organics in the Atmosphere (GECKO-A) modeling tool (Aumont et al., 2005;Camredon et al., 2007). Lannuque et al. (2018a) have shown that the VBS-GECKO parameterization is coherent compared to the explicit GECKO-A chemical mechanism. The reliability of the VBS-GECKO parameterization is by design directly linked to the accuracy of the GECKO-A mechanisms. The accuracy of the GECKO-A mechanisms to represent SOA formation has been evaluated against around 50 chamber experiments (Denjean et al., 2015;La et al., 2016;McVay et al., 2016;Valorso et al., 2011). Some processes relevant for SOA formation in the atmosphere can, however, be misrepresented in the GECKO-A mechanisms or are just not included (such as gaseous autoxidation reactions or the reactivity in the condensed phase). The reliability of the VBS-GECKO parameterization to represent SOA formation observed in the atmosphere has thus to be evaluated.
The objectives of this study are (i) to evaluate the behavior of the VBS-GECKO parameterization in the CTM CHIMERE (Menut et al., 2013;Mailler et al., 2017) by comparison with field measurements and previous simulations obtained with the H 2 O parameterization (Couvidat et al., 2012) already implemented in CHIMERE, (ii) to explore the sensitivity of simulated SOA concentrations to organic compound properties (volatility, solubility, aging rates or NO x regime) and (iii) to test the sensitivity of OA concentrations to the uncertainties in IVOC emission fluxes from traffic. The setup of the CHIMERE model and the implementation of VBS-GECKO in the CTM are described in Sect. 2. In Sect. 3, the VBS-GECKO, and is evaluated over Europe for a 2-month summer period, the sensitivity to organic compound properties is explored in Sect. 4, and the sensitivity to the uncertainties in IVOC emission fluxes from traffic is investigated in Sect. 5. Finally, results on simulated OA sources and concentrations are discussed in Sect. 6.

The CHIMERE chemical transport model
The evaluation of the VBS-GECKO parameterization and the exploration of SOA sensitivity were performed using the CHIMERE 2017 β version. This version is based on the CHIMERE 2013 version (Menut et al., 2013), which was modified to improve the representation of particles with the implementation of a new aerosol module. Details of the CHIMERE 2017 β version and its evaluation are given in Couvidat et al. (2018).
Briefly, the CHIMERE 2017 β version uses the MEL-CHIOR2 gas-phase chemical scheme, involving 44 species reacting according to 120 reactions. MELCHIOR2 is a reduced version of the MELCHIOR1 mechanism, obtained by the Carter's surrogate molecule method (Carter, 1990). In CHIMERE, the aerosol evolution is described by a sectional aerosol module (e.g., Bessagnet et al., 2004Bessagnet et al., , 2009Schmidt et al., 2001). The size distribution of aerosol particles is here represented using nine bins, ranging from 10 nm to 10 µm. Aerosol formation is represented in the model by nucleation for sulfuric acid (Kulmala et al., 1998), coagulation between particles (e.g., Debry et al., 2007;Jacobson et al., 1994) and condensation/evaporation via absorption according to the "bulk equilibrium" approach (e.g., Pandis et al., 1993). For inorganic species, the gas-particle equilibrium concentrations are calculated using the ISORROPIA v2.1 (Fountoukis and Nenes, 2007) thermodynamic module. For organic species, the equilibrium concentrations are calculated using the SOAP (Secondary Organic Aerosol Processor) thermodynamic module (Couvidat and Sartelet, 2015). The gaseous formation of secondary organic species able to partition be-tween the gas and the condensed phases (so leading to SOA formation) are represented in the CHIMERE β version using the H 2 O mechanism. Here, the VBS-GECKO parameterization was also implemented. The H 2 O and VBS-GECKO organic aerosol modules are described hereafter.
The chemical speciation of emitted nonmethane volatile organic compounds (NMVOCs) is taken from Passant (2002) as described in Menut et al. (2013). POA from emission inventories are considered SVOC. A factor of 5 is applied to residential POA emissions, as wood burning emissions are underestimated in emission inventories (e.g., Denier Van Der Gon et al., 2015). This factor was shown to give satisfactory results on OA estimations (Couvidat et al., 2012(Couvidat et al., , 2018. Biogenic emissions are computed with the Model of Emissions of Gases and Aerosols from Nature MEGAN 2.1 algorithm (Guenther et al., 2012). Dry deposition for gaseous organic species is described using the Wesely (1989) parameterization and according to their Henry's law constants, as described by Bessagnet et al. (2010).

The organic aerosol modules
The purpose of the comparison between the H 2 O and GECKO-VBS mechanisms for SOA formation is to evaluate the reliability of the VBS-GECKO parameterization. The simulations performed with CHIMERE were therefore setup using the same configuration of the model (meteorological data, emissions, deposition, inorganic and organic gaseous chemical mechanism, inorganic and organic gasparticle partitioning, etc.) but implementing either the H 2 O or the GECKO-VBS parameterizations. The implementation of a given parameterization for SOA formation induces anyway some differences related to the primary compounds considered and/or the processes taken into account in the parameterization. The differences between the H 2 O and VBS-GECKO are mentioned in the following parameterization presentation sections.

The H 2 O reference mechanism
The H 2 O mechanism, described in detail by Couvidat et al. (2018), considers SOA formation from the partitioning of hydrophilic species (condensing on an aqueous phase and an organic particulate phase) and hydrophobic species (condensing only on an organic particulate phase owing to their low affinity with water). Distinction between hydrophobic and hydrophilic compounds is based on their octanol/water coefficient (Pun et al., 2006b) or their partitioning between the organic and aqueous phases (Couvidat and Seigneur, 2011). H 2 O considers the formation of hydrophilic and/or hydrophobic species from the gaseous oxidation of isoprene, monoterpenes (α-pinene, β-pinene, the limonene and ocimene), sesquiterpenes (humulene) and mono-aromatic precursors (toluene and xylenes). Note that in H 2 O, limonene mechanism is used as a surrogate mech-anism for ocimene (ocimene having its own OH, NO 3 and O 3 reaction rates). Each emitted SOA precursor is linked to a species of the H 2 O mechanism. POA provided by emissions inventories are split into three emitted SVOCs having different volatilities (saturation vapor pressures at 298 K of 8.9×10 −11 , 8.4×10 −9 and 3.2×10 −7 atm, respectively) with a fraction that follows the volatility distribution of POA emissions given by Robinson et al. (2007). In H 2 O, gaseous oxidation of these three compounds with OH leads to hydrophobic species with a lower volatility. No gaseous oxidation is considered for hydrophilic and hydrophobic species in H 2 O. Activity coefficients for the H 2 O species are computed with the thermodynamic model UNIFAC (UNIversal Functional group Activity Coefficient; Fredenslund et al., 1975). H 2 O has been evaluated over Europe (Couvidat et al., 2012(Couvidat et al., , 2018 and the Paris area (Couvidat et al., 2013;Zhu et al., 2016a, b). The H 2 O reference mechanism is presented in Table S1 of the Supplement.

The VBS-GECKO parameterization
The VBS-GECKO parameterization is described in detail in a previous paper by Lannuque et al. (2018a). Briefly, VBS-GECKO is a volatility basis set (VBS) type parameterization that represents SOA formation from the partitioning of organic compounds having a low volatility onto an organic aerosol phase. The VBS-GECKO parameterization takes into account for the oxidation of a precursor k (precu k ) (1) the formation of 7 VB k,i , where i is the number of the volatility bin (1 being the most volatile and 7 the less volatile) (Reactions R1, R2 and R3), (2) the gas-phase aging of the VB k,i (except for the lowest volatility bin 7) with OH redistributing the matter between the VB k,i (Reaction R4) and by photolysis leading to a loss of carbon matter (Reaction R4) and (3) the gas-particle partitioning of the precursor k (Reaction R6) and of the VB k,i (Reaction R7). The VBS-GECKO follows this structure for a given precursor k: In VBS-GECKO, the production and gaseous aging of the VB k,i for a precursor k are adjusted by stoichiometric coefficients (a k,RRR,i , b k,RRR,i , c k,RRR,i , d k,RRR,i , for Reactions R1 to R4, respectively), which depend on the NO x regime. The formation of more volatile and less volatile bins can be assimilated to fragmentation and functionalization processes, respectively. The stoichiometric coefficients depend on the NO x according to the reaction rate ratio (RRR) of RO 2 with NO: where k RO 2 +NO (set to 9.0×10 −12 cm 3 molec. −1 s −1 according to Jenkin et al., 1997 at 298 K) and k RO 2 +HO 2 (set to 2.2×10 −11 cm 3 molec. −1 s −1 according to Boyd et al., 2003, assuming a large carbon skeleton for RO 2 at 298 K) are the rate constants for the reactions of the peroxy radicals with NO and HO 2 , respectively, and [NO] and [HO 2 ] are the concentration of the radicals. The entire RRR range is covered by linear interpolation of the coefficients between the two closest tabulated values. The photolysis is considered a limiting process for SOA formation, leading to a loss of matter. The photolysis rates of the VB k,i are based on the acetone one multiplied by an optimized factor ϕ k , different for each precursor k. Precursors and VB k,i condense on an organic particulate phase according to an equilibrium between the gas and the organic particulate phase that follows the Raoult's law (Reactions R6 and R7). The properties of the 7 VB k,i were considered to be independent of the precursor k and set for each volatility bin i to the mean values simulated with explicit GECKO-A simulations. Table 1 gives the molar weights (Mw), saturation vapor pressures (P sat ) at 298 K, effective Henry's law constants (H eff ) at 298 K and vaporization enthalpies ( H vap ) used for each VB k,i VBS-GECKO species. The stoichiometric coefficients and factors ϕ k were optimized on explicit GECKO-A simulations of gas-phase oxidation and SOA formation. The stoichiometric coefficients were optimized for five RRR values: 0, 0.1, 0.5, 0.9 and 1 (Lannuque et al., 2018a). Precursors considered in the current VBS-GECKO parameterization are mono-aromatic compounds (benzene; toluene; and o-, m-, and p-xylenes) and n-alkanes (decane, tetradecane, octadecane, docosane and hexacosane) reacting with OH and monoterpenes (α-pinene, β-pinene and limonene) and linear 1-alkenes (decene, tetradecene, octadecene, docosene and hexacosene) reacting with OH, O 3 and NO 3 . Note that (1) the parameterization does not represent SOA formation from the partitioning of hydrophilic species, (2) recently identified chemical processes, such as autoxidation reactions or acid-catalyzed pathways, not included in the GECKO-A mechanisms, are thus not considered in the VBS-GECKO parameterization and (3) the high value of the reaction rate of the VB k,i (k OH = 4 × 10 −11 cm 3 molec. −1 s −1 ) was fixed before optimization and is compensated by lower or higher values of optimized coefficients (see details in Lannuque et  For SOA production from NMVOC oxidation, the former H 2 O parameterization in CHIMERE was replaced by the VBS-GECKO parameterization for terpenes and monoaromatic compounds. The VBS-GECKO mechanisms were also implemented in CHIMERE for SOA formation from C 10 to C 13 alkanes and alkenes, gaseous species usually not considered in 3D models as SOA precursors. Each emitted SOA precursor not present in the VBS-GECKO was linked to a VBS-GECKO species. As in the H 2 O mechanism, the VBS-GECKO parameterization for limonene was used as a surrogate mechanism for ocimene. The VBS-GECKO parameterizations for benzene; toluene; and o-, m-, and p-xylenes were also used as surrogate mechanisms for other emitted mono-aromatic compounds according to their SOA yield and reactivity with OH. The n-dodecane and tetradecane VBS-GECKO species were used to lump emitted alkanes with 10 to 13 atoms of carbon, according to their carbon chain length. The VBS-GECKO mechanism for 1-decene was applied for all emitted C 10 alkenes. The lumping scheme between emitted NMVOCs and VBS-GECKO species is given in Table 2. The current VBS-GECKO version does not represent SOA production from the oxidation of isoprene and sesquiterpenes. The H 2 O parameterizations for isoprene and humulene were therefore left unchanged in CHIMERE to account for this SOA production. For SOA production for SVOC oxidation distributed from POA emissions, the H 2 O approach was kept unchanged (i.e., distribution of POA emissions into three SVOC species and representation of their SOA production using the H 2 O mechanism). In CHIMERE, RRR is calculated in each box at each chemical time step following Eq. (1). Activity coefficients for the condensation of the VBS-GECKO species into the aerosol particulate phase are fixed to 1 (i.e., ideality of the organic particulate phase is considered). This implementation of the VBS-GECKO in CHIMERE was selected here as the reference configuration Table 2. Distribution of the NMVOC emission in the VBS-GECKO species.

Simulation setup and field measurements
The model was run to simulate the concentrations of OA over Europe (from 25 • W to 45 • E in longitude and from 30 to 70 • N in latitude) with a horizontal resolution of 0.25 • × 0.25 • during the July-August 2013 period, SOA formation being expected to be important during summertime. Meteorology was obtained from the Integrated Forecasting System (IFS) model of the European Centre for Medium-Range Weather Forecasts (ECMWF). This meteorology has been evaluated in Bessagnet et al. (2016) for the model intercomparison project EURODELTA-III. ECMWF-IFS in the EURODELTA-III project has been shown to be one of the most reliable models to represent meteorological conditions over Europe. Anthropogenic emissions of gases and particles were taken from the European Monitoring and Evaluation Programme (EMEP) inventory (methodology described in Vestreng, 2003) and boundary conditions were generated from the Model for OZone And Related chemical Tracers (MOZART v4.0;Emmons et al., 2010). Wildfire emissions were not considered.
The VBS-GECKO mechanism was evaluated by comparing the simulated results to the H 2 O mechanism and particulate-phase measurements available in the EBAS database (http://ebas.nilu.no/, last access: 20 April 2020). EBAS is a database hosting observation data of atmospheric chemical composition and physical properties in support of a number of national and international programs ranging from monitoring activities to research projects. EBAS is developed and operated by the Norwegian Institute for Air Research (NILU). This database is populated, for example, by the EMEP measurements (Tørseth et al., 2012) or the Aerosols, Clouds and Trace gases Research Infrastructure (ACTRIS; http://www.actris.eu/, last access: 20 April 2020) ones. The 48 rural background stations provide measurements for fine particulate matter and were thus selected here for a statistical evaluation: 36 stations for PM 2.5 , 13 for OC PM 2.5 (organic carbon in PM 2.5 , obtained by filter calcinations) and 6 for OM PM 1 (organic matter in PM 1 , obtained with aerosol chemical speciation monitors (ACSMs)). For the comparisons with OC measurements, the OM : OC ratio of the VBS-GECKO volatility bins were assumed to be equal to 1.8, in agreement with typical observed values given by Canagaratna et al. (2015). The location of the selected stations is shown in Fig. 1a. Among these stations, seven stations were used for time series comparisons: the Cabauw (NL0644R, the Netherlands), Melpitz (DE0044R, Germany) and Palaiseau (FR0020R, SIRTA, France) rural background stations, located in areas dominantly impacted by anthropogenic air masses (see Fig. S1 presenting the mean of the simulated ratios between toluene and α-pinene emission fluxes for the studied period).
These seven stations were selected among the 48 background station, because the measurements at the stations provide (1) direct information on the organic fraction of fine particles, i.e., OM PM 1 and OC PM 2.5 measurements, and (2) enough data over the studied period to perform time series comparisons. The location of the seven selected stations is shown in Fig. 1b. Various statistical indicators were computed to evaluate the VBS-GECKO mechanism, including the root mean square error (RMSE), the correlation coefficient, the mean fractional error (MFE) and the mean fractional bias (MFB). MFB and MFE are calculated as where c mod i and c obs i are the simulated and observed, respectively, concentrations of the studied component at the time i and N being the number of available in situ measurement values. Boylan and Russell (2006) defined two criteria to evaluate the performances of a model. The model performance criteria (described as the level of accuracy that is considered to be acceptable for modeling applications) is reached when MFE ≤ 75 % and |MFB| ≤ 50 %, whereas the performance goal (described as the level of accuracy that is considered to be close to the best values a model can be expected to achieve) is reached when MFE ≤ 50 % and |MFB| ≤ 30 %. These criteria are currently used to evaluate the reliability of the models (e.g., Ciarelli et al., 2017;Couvidat et al., 2018;Lecoeur and Seigneur, 2013;Mircea et al., 2019). Figure 2a shows the mean OA mass concentrations simulated with the ref-VBS-GECKO version for the July-August 2013 period. The simulated mean OA concentrations range from ∼ 0 µg m −3 in remote oceanic areas to ∼ 12 µg m −3 around the Adriatic Sea and in northern Italy, and they are coherent with the expected orders of magnitude and spatial distributions over Europe (Aksoyoglu et al., 2011;Crippa et al., 2014). Figure 2b presents the relative difference between mean OA mass concentrations simulated with ref-VBS-GECKO and with H 2 O. The ref-VBS-GECKO produces more OA than H 2 O, with a mean OA mass concentration around 30 % higher on average over Europe. The increase is particularly important over northern Europe, with maximum differences reaching around +60 %.  (Bergström et al., 2012;Ciarelli et al., 2017) or USA (Ahmadov et al., 2012;Murphy et al., 2017). For daily averaged measurements of PM 2.5 , the correlation is smaller (0.42). This lower correlation for PM 2.5 has already been highlighted in summertime during the EURODELTA-III intercomparison campaign (Bessagnet et al., 2016). MFE and   results, the simulated daily averaged PM 2.5 concentrations over the 36 stations appear to be weakly sensitive to the SOA formation mechanism used in the model.

Sensitivity to the parameterization properties
Sensitivity tests were performed to assess the VBS-GECKO parameterization, evaluate the consistency of the modeling results and examine some hypotheses that may explain the gaps between measurement and simulated values. Sensitiv- ities to hydro-solubility, gaseous aging, NO x regimes and volatility were studied comparing results to the nonmodified ref-VBS-GECKO version.

Sensitivity tests to hydro-solubility and H eff
SOA formation from the gas-particle partitioning of hydrosoluble organic compounds into an aqueous phase is now well recognized (e.g., Bregonzio-Rozier et al., 2016;Carlton et al., 2009;Knote et al., 2014). The effective Henry's law constant (H eff ) is the key parameter which controls this hydrophilic partitioning. Hydro-soluble organic compounds can also be lost at the surface by dry deposition. In CHIMERE, and according to the deposition scheme of Wesely (1989), the stomatal resistance of organic compounds depends on H eff . To analyze the sensitivity of the simulated OA to hydrophilic partitioning and values of H eff , the following two simulations were run: -Hydro-VBS-GECKO. In this model configuration, VB k,i can condense both on organic and aqueous phases of particles. Aqueous-phase partitioning is computed according to Henry's law, assuming the particle phase behaves as an ideal well-mixed homogeneous aqueous phase. Deposition of VB k,i was already taken into account in the reference model configuration and was kept unchanged.    Table 4 shows no significant modification in the statistical results for this simulation. The values of H eff set to each volatility bin increase when the volatility decreases (see Table 1), meaning that the less volatile species are also more prone to condense into the aqueous phase. Adding a hydrophilic partitioning does therefore not increase substantially the concentrations of organic species in the condensed phases. The Hydro-VBS-GECKO-high configuration increases the mean simulated OA concentrations by ∼ 10 %, with a maximal increase reached over the Belgium-the-Netherlands-Luxembourg area (called Benelux hereafter, around +20 %; see Fig. 5b). The contribution of the deposition and the partitioning processes are shown in Fig. 5c and d, respectively. Changes due to deposition appear negligible (below ±0.2 %) compared to the changes due to the aqueous partitioning (∼ +10 %). According to the Wesely (1989) parameterization used for deposition, water solubility contributes to the surface resistance only. Knote et al. (2014) have shown that deposition is not limited by the surface resistance for H eff greater than 10 8 mol L −1 atm −1 . In ref-VBS-GECKO, this threshold corresponds to the VB k,(3-7) nominal H eff values, i.e., to the volatility bins partitioning mainly to OA. OA concentrations are therefore not sensitive to an increase in the H eff values. The increase in H eff by a factor of 100 makes possible hydrophilic partitioning of the most volatile bins that would not have condensed otherwise, and it leads to an increase in simulated OA concentrations. The maximum relative changes simulated over Benelux are mainly linked to the high relative humidity encountered in this area and the low simulated OA concentrations (see Fig. 2a). This model configuration improves slightly the RMSE, MFB and MFE calculated on OM PM 1 (−4.58 %, −0.06 and −0.05, respectively) and OC PM 2.5 (−0.65 %, −0.05 and −0.03, respectively) mass concentrations (see Table 4). According to these tests, SOA production due to the hydrophilic partitioning of the various VB k,i of the VBS-GECKO parameterization is expected to be a minor process.

Sensitivity test to gaseous aging rates and OH radical concentrations
In the VBS-GECKO parameterization, the same rate constant is set for the VB k,i reactions with OH (k OH = 4.0 × 10 −11 cm 3 molec. −1 s −1 ). The timescale for gaseous aging is therefore driven by the OH concentrations simulated by the CTM. Simulated OH concentrations depend on the gas-phase chemical mechanisms used in the CTM, with differences in OH concentrations reaching up to 45 % between mechanisms (Sarwar et al., 2013). Two simulations were run with modified k OH to examine the sensitivity of SOA production to the rate of chemical aging: k OH -VBS-GECKO-low. In this model configuration, the VB k,i +OH rate constants are divided by a factor 2, i.e., k low OH = 2.0 × 10 −11 cm 3 molec. −1 s −1 . k OH -VBS-GECKO-high. In this model configuration, the VB k,i +OH rate constants are multiplied by a factor 2, i.e., k high OH = 8.0 × 10 −11 cm 3 molec. −1 s −1 . The relative difference in the simulated mean OA concentrations between k OH -VBS-GECKO-low (respectively k OH -VBS-GECKO-high) and ref-VBS-GECKO is given Fig. 6a (respectively Fig. 6b). A slight variation of simulated OA concentrations is found (lower than ±10 %), with simulated OA concentrations decreasing with the decrease in aging rates and vice versa. This result highlights that the gas-phase aging of volatility bins in the VBS-GECKO parameterization promotes functionalization (formation of less volatile bins) rather than fragmentation (formation of more volatile bins), as already shown with tests conducted in a box model (Lannuque et al., 2018a). The highest relative differences are located over the Mediterranean Sea and northern Africa, i.e., areas showing high OH and low OA concentrations (below 4 µg m −3 ; see Fig. 2a). The k OH -VBS-GECKO-high configuration improves statistics, due to an overall increase in the simulated OA concentrations (and contrariwise for the k OH -VBS-GECKO-low configuration) (see Table 4). However, the sensitivity of SOA to the gas-phase aging of the VBS-GECKO volatility bins remains weak, and aging rates are likely not a major source of uncertainty.

Sensitivity test to the NO x regime
Similar to the OH discussion above, simulated HO 2 and NO concentrations in CTMs are linked to the gas-phase chemical mechanism used. The concentrations of these two species determine the value of the RRR ratio and therefore drive the aging of the various VB k,i (Lannuque et al., 2018a). A sensitivity test was performed to examine the sensitivity of the simulated OA to the chemical regime. HO 2 or NO concentrations can hardly be modified without changing all the simulation conditions. Here, two simulations were run modifying the k RO 2 +HO 2 value used to calculate the RRR.
-RRR-VBS-GECKO-low. In this model configuration, RRR ratio is calculated with k RO 2 +HO 2 multiplied by 2, i.e., k RRRlow RO 2 +HO 2 = 4.4 × 10 −11 cm 3 molec. −1 s −1 . -RRR-VBS-GECKO-high. In this model configuration, RRR ratio is calculated with k RO 2 +HO 2 divided by 2, i.e., k RRRhigh RO 2 +HO 2 = 1.1 × 10 −11 cm 3 molec. −1 s −1 . Figure 7 presents the mean RRR ratio during the 2-month period for both RRR-VBS-GECKO-low (Fig. 7a) and RRR-VBS-GECKO-high model configurations (Fig. 7b). The entire range of RRR ratio (from remote NO x conditions to high NO x conditions) is covered over Europe with the both model configuration. As expected, the urban, industrial and intense shipping transport areas such as Paris, the Channel, Benelux, northern Italy or Moscow are systematically in the high NO x regime (RRR close to 1), whereas remote areas over the seas (away from shipping tracks) are systematically in the remote NO x regime (RRR close to 0). Between these two extremes, the RRR ratio depends on the environmental and meteorological conditions at the location and, in this sensitivity study, on the model configuration for the RRR calculation. Current parameterizations for SOA formation only consider two extreme regimes corresponding to a high-NO x and a low-NO x condition. Criteria used to define high and low NO x differ from a study to another one but the parameterizations are usually optimized at NO x values typical of rural conditions for low NO x (corresponding to a RRR ratio of ∼ 0.6) and typical of urban conditions for high NO x (corresponding to a RRR ratio of ∼ 1) (e.g., Hodzic et al., 2014;Lane et al., 2008). The range of RRR between 0.0 and 0.6 is therefore not considered in most of the parameterizations, although substantial changes in SOA formation were found within this range of RRR (Lannuque et al., 2018a).
The relative difference in the simulated mean OA concentrations between RRR-VBS-GECKO-low (respectively RRR-VBS-GECKO-high) and ref-VBS-GECKO is given Fig. 8a (respectively Fig. 8b). Results show variations in simulated mean OA concentrations smaller than ∼ 15 %. In agreement with previous studies, an increase (decrease) of RRR ratio leads to a decrease (increase) of the simulated OA concentrations (e.g., Donahue et al., 2005;Lannuque et al., 2018a;Ng et al., 2007). As expected, the variation is weaker over areas having either an RRR ratio close to 0 or 1, the NO x regime remaining unchanged among the model configurations. The highest relative differences on OA are found over continental rural areas, i.e., areas showing the largest variation in RRR among the model configurations. Large relative differences are also found over the Mediterranean Sea, owing in part to the low simulated OA concentrations. Similar to the k OH sensitivity tests, the RRR-VBS-GECKO-low configuration increases the overall OA concentrations and improves statistical indicators, and contrariwise for the RRR-VBS-GECKO-high configuration. Sensitivity on RRR values appears weak enough to likely not be a major source of uncertainty for the VBS-GECKO parameterization.

Sensitivity test to volatility and P sat
In the explicit GECKO-A simulations used for the VBS-GECKO optimization, the saturation vapor pressure, P sat , of secondary organic compounds was estimated using structure activity relationships (SAR) (see Lannuque et al., 2018a). Estimated P sat can typically vary within 1 order of magnitude according to the SAR used (e.g., Valorso et al., 2011). Two  simulations were run to examine the sensitivity of SOA to the uncertainties in P sat : -P sat -VBS-GECKO-low. In this model configuration, the nominal P sat values of VB k,i are divided by 10.
-P sat -VBS-GECKO-high. In this model configuration, the nominal P sat values of VB k,i are multiplied by 10.
As OA concentration directly contributes to the partitioning, these two simulations can also be considered a sensitivity test to the simulated OA concentrations. The relative difference in the simulated mean OA concentrations between P sat -VBS-GECKO-low (respectively P sat -VBS-GECKO-high) and ref-VBS-GECKO is given Fig. 9a (respectively Fig. 9b). Shifting the volatility of the VB k,i by 1 order of magnitude leads to an overall change in the simulated mean OA concentrations of about −25 % (+25 %) when P sat is increased (decreased). A weaker sensitivity is observed over urban areas, such as Paris or Moscow. This behavior is mainly linked to the simulated volatility of OA in the ref-VBS-GECKO simulations. Figure 10 shows the mean volatility of OA over Europe for the reference configuration. Simulated OA contributors are mainly low-volatility species (with mean P sat 298 K between 10 −10 and 10 −14 atm), with the highest values being found over urban areas (less aged OA) and the lowest values found over areas close to the boundaries of the domain (linked to a boundary effect in the model). A shift in volatilities over these two types of site has a lower impact on OA concentrations, as OA mean volatilities being either too high (mean P sat 298 K ≈ 10 −10 atm, upon urban areas) or too low (mean P sat 298 K ≈ 10 −14 atm, upon boundary areas) for a change in P sat to substantially impact the partitioning. The largest effect is typically observed over central Europe where OA contributors show intermediate mean volatilities (mean P sat 298 K ≈ 10 −12 atm). Statistically, the P sat -VBS-GECKO-low configuration is the only configuration matching the performance goal for all the simulated OA concentrations (OC PM 2.5 and OM PM 1 ) (see Table 4). For OC PM 2.5 , RMSE is, however, higher than in the reference configuration. Simulated OA concentrations appear to be sensitive to uncertainties in the estimated saturation vapor pressures of the numerous OA contributors considered during the development of the VBS-GECKO parameterization.

Sensitivity to IVOC emission fluxes from traffic and transport sources
IVOCs have been shown to be a substantial source of SOA in the plume of megacities (e.g., Hodzic et al., 2010;Tsimpidi et al., 2010). Even if several recent studies have been performed to identify the IVOC speciation of different individual emission sources (e.g., Akherati et al., 2019;Grieshop et al., 2009;Hatch et al., 2018;Jathar et al., 2017;Louvaris et al., 2017;Lu et al., 2018;May et al., 2013a, b, c;Woody et al., 2016), a comprehensive inventory is still not available to represent IVOC emissions by activity sector (gathering several individual emission sources). A large fraction of these IVOCs is thus still not considered in emission inventories. In this section, only IVOC emissions from traffic and transportation sources are treated. Robinson et al. (2007) assumed that IVOC emissions for small off-road diesel engines were equal to 150 % of POA emissions, consistent with the Schauer et al. (1999) emission data for 1995 medium-duty diesel vehicles. Recent studies have measured IVOC emissions from (i) exhausts of light-duty gasoline vehicles and (ii) exhausts of both heavy-duty and medium-duty diesel vehicles (Zhao et al., 2015(Zhao et al., , 2016. Experiments on gasoline exhausts were processed on 42 vehicles and experiments on diesel vehicles on 6 vehicles, with the selected vehicles being representative of the transportation fleet in North America. In both cases, Zhao et al. (2015Zhao et al. ( , 2016 have shown that a stronger correlation can be found between IVOC and NMVOC emissions (R 2 equal to 0.92 and 0.98 for gasoline and diesel exhausts, respectively) than between IVOC and POA emissions (R 2 equal to 0.76 and 0.61 for gasoline and diesel exhausts, respectively). Zhao et al. (2015Zhao et al. ( , 2016 have estimated that IVOC emissions represent about 4 % of NMVOC emissions in cold-start cycle to about 16 % in hot-start cycle for light-duty gasoline vehicles and about 60 ± 10 % of NMVOC emissions for heavyduty and medium-duty diesel vehicles. In this study, the VBS-GECKO parameterization was used to examine the sensitivity of SOA to IVOC emissions from road traffic (SNAP 7) and other mobile sources and machinery (SNAP 8). The following five model configurations, based on different IVOC emission fluxes, were designed for that purpose.
-IVOC 150POA : in this model configuration, IVOC emissions are set to 150 % of the semivolatile POA emissions, based on Robinson et al. (2007).
-IVOC 4VOC : in this configuration, IVOC emissions are set to 4 % of NMVOC emissions, based on Zhao et al. (2016) for gasoline vehicles in cold-start cycle.
-IVOC 16VOC : in this configuration, IVOC emissions are set to 16 % of NMVOC emissions, based on Zhao et al. (2016) for gasoline vehicles in hot-start cycle.
-IVOC 30VOC : in this configuration, emissions are set to 30 % of NMVOC emissions, assuming a mixing of diesel and gasoline vehicle fleets.
-IVOC 65VOC : in this configuration, IVOC emissions are set to 65 % of NMVOC emissions, based on Zhao et al. (2015) for diesel vehicles.
As in the reference model configuration, POA species are considered SVOC in these sensitivity tests for traffic and transport emissions. Primary SVOCs and IVOCs (S/IVOCs) constitute a complex mixture of linear, branched, and cyclic alkanes; alkenes; and aromatics (Fraser et al., 1997;Gentner et al., 2012;Lu et al., 2018;Schauer et al., 1999Schauer et al., , 2002. The molecular composition of S/IVOCs emitted in the atmosphere by fossil fuel combustion is, however, still poorly documented. S/IVOCs at emission were thus considered to be distributed into the nine volatility bins given by Robinson et al. (2007), with the provided fraction of primary SVOCs in each SVOC volatility bin, and of estimated primary IVOCs in each IVOC volatility bin. The VBS-GECKO parameterizations for C 14 , C 18 , C 22 and C 26 1-alkenes and n-alkanes were used as surrogate mechanisms for S/IVOCs (C 14 and C 18 for IVOCs and C 18 , C 22 and C 26 for SVOCs). The C 14 to C 26 VBS-GECKO's n-alkanes and 1-alkenes were distributed according to their volatility into the nine volatility bins of Robinson et al. (2007). Correspondences are shown in Fig. 11 for the example of the IVOC 150POA model configuration. The distribution of alkanes and alkenes was estimated based on (i) the EMEP guidebook (https://www.eea. europa.eu/publications/emep-eea-guidebook-2016, last access: 20 April 2020), providing speciation data for emissions for various types of vehicles, and (ii) the COPERT4 software (Ntziachristos et al., 2009) providing data for a vehicle fleet. Data are only available for light compounds and are here extrapolated to the heavy ones for the needs of the study. Thus, 75 % of the primary S/IVOCs are here assumed to be alkanes and 25 % alkenes. The primary SVOC total emissions and distributions over volatility bins are unchanged between each simulation. The distribution of IVOCs among volatility bins is also unchanged but the total IVOC emissions are modulated according to the five IVOC emission scenarios described before (i.e., IVOC 150POA , IVOC 4VOC , IVOC 16VOC , IVOC 30VOC and IVOC 65VOC ). Table 5 gives the speciation of VBS-GECKO species for the various model configurations and the VBS-GECKO mechanism for S/IVOCs presented in Table S3. Figure 12 shows the mean OA mass concentrations simulated for the five IVOC emission configurations and the absolute and relative differences with the ref-VBS-GECKO simulation without IVOC emissions. Table 6 presents the statistical results calculated on daily averaged concentrations (RMSE, Pearson's correlation coefficient, MFE and MFB) for the different IVOC emission configurations and their difference with those of the ref-VBS-GECKO configuration. As discussed previously, the highest concentrations are simulated over northern Italy (see Fig. 2). For this area, accounting for IVOC emissions increases the simulated concentrations of OA up to 3 µg m −3 with the IVOC 65VOC model configuration. As expected, OA concentration increases when IVOC emissions over Europe are taken into account during the simulated period, with an overall mean increase of about 12 %, 2 %, 5 %, 10 % and 20 % for the IVOC 150POA , Figure 11. Distribution of the VBS-GECKO species into the S/IVOC volatility bins by Robinson et al. (2007). Normalized emission factors by POA emissions for IVOCs are used for the IVOC 150POA model configuration.
IVOC 4VOC , IVOC 16VOC , IVOC 30VOC and IVOC 65VOC configurations, respectively. The relative differences show large increases of OA concentrations (reaching +40 %) over a wide area including the North Sea and Benelux for the IVOC 65VOC configuration, owing to the low simulated OA concentrations with the ref-VBS-GECKO configuration. The IVOC 150POA configuration leads to mean OA mass concentrations lying between the IVOC 16VOC and the IVOC 30VOC configurations. Areas showing substantial changes in simulated OA are, however, different between these model configurations. In the IVOC 150POA configuration, the largest OA concentration increase is simulated over the Channel and Gibraltar's Detroit (up to +80 %). These results were expected for this model configuration based on POA emissions. Indeed, ships are one of the most important sources of POA but emit a relatively small amount of NMVOCs. For example, the EMEP inventory for 2013 estimates an average NMVOC/POA emission ratio of ∼ 4 for road traffic in Europe and ∼ 0.4 for shipping in the studied domain.
Taking into account SOA formation from IVOC precursors improves the statistical indicators for the simulated concentrations of OM PM 1 . As discussed previously, the ref-VBS-GECKO configuration underestimates OM PM 1 . Including IVOC emission increases the mean OM PM 1 concentrations at the stations of about 5 %, 2 %, 5 %, 7 % or 13 % for the IVOC 150POA , IVOC 4VOC , IVOC 16VOC , IVOC 30VOC or IVOC 65VOC configuration, respectively. Increasing IVOC emissions provide better statistical indicators for OM PM 1 , with MFE and MFB significantly closer to the performance goal (MFE decreases by 0.06 and |MFB| decreases by 0.09 between IVOC 4VOC and IVOC 65VOC configurations; see Table 6). For OC PM 2.5 , however, the opposite trend is observed with a degradation of the statistical indicators (Table 6). The ref-VBS-GECKO configuration leads to a slight overestimation of OC PM 2.5 concentrations over some stations (e.g., Iskrba; see Fig. 3) and adding the SOA source from IVOCs strengthens the deviation (up to about +30 % of RMSE for the IVOC 65VOC configuration), even if the correlation is not significantly modified. IVOC oxidation appears to be a significant SOA source at some locations (e.g., the Cabauw station), especially in the IVOC 30VOC and IVOC 65VOC configuration. However, the re-sulting OA increase remains too weak to fill in the gaps between observations and simulated data (maximum increase around +40 %). For example, time series presented in Fig. 13 show that adding IVOC emission increases systematically the simulated OA concentrations, but it is not enough to explain the OA peaks recorded at the anthropogenic stations  (see Fig. 13b). Moreover, accounting for IVOC emission strengthens the disagreement of the simulated concentrations with observations over other areas (e.g., at Iskrba station). The various IVOC emission configurations are aimed to answer the following question: with constant POA and NMVOC emissions for the traffic, do IVOC emissions typi-cal of diesel vehicles (upper limit) or gasoline vehicles (lower limit) significantly change OA concentrations in Europe, and in particular in anthropogenic areas? At a local scale where anthropogenic sources are dominant, IVOC emissions from traffic and transportation sources appear to be a significant source of OA and simulated OA concentrations are depen-dent to the IVOC emission configuration (∼ +3 µg m −3 in northern Italy for IVOC 65VOC against IVOC 4VOC ). At a continental scale outside anthropogenic areas, the low variations observed on simulated OA concentrations between the different IVOC emission configurations suggest that IVOCs from traffic and transportation sources are likely not a major source of SOA.
6 Tracking OA sources Apportionment of OA sources is investigated in this section. The study takes into account OA formation from IVOC oxidation and is based on the IVOC 30VOC model configuration. Figure 14 shows the contribution of the various OA sources to the simulated OA concentrations during the July-August 2013 period and the mean daily profiles at two stations located in areas dominantly impacted by anthropogenic air masses (Cabauw and Palaiseau) and two stations located in areas dominantly impacted by biogenic air masses (Birkenes II and Iskrba). SOA constitutes the main fraction of OA whatever the environment. This secondary fraction typically grows from anthropogenically impacted areas (about 70 % at Palaiseau station) to remote areas (about 95 % at Iskrba station). This trend is in agreement with what is usually observed or simulated for summertime periods (e.g., Aksoyoglu et al., 2011;Belis et al., 2013). For the remote stations Birkenes II and Iskrba, respectively 82 % and 67 % of the simulated OA concentrations come from a biogenic source. Contrariwise, anthropogenic sources are the major OA contributors at anthropogenically impacted stations (65 % and 60 % of OA at the Cabauw and Palaiseau stations, respectively).
Among OA biogenic sources, terpene oxidation is clearly found as the major contributor of OA during the summer period, contributing from 35 % (at anthropogenic impacted stations) to 80 % (at remote stations) of the total OA mass. The 60 % increase in OA mass concentration observed in northern Europe between H 2 O and VBS-GECKO parameterizations (see Fig. 2) is also mainly related to SOA formation from terpene, especially ocimene and limonene. In our simulation, SOA produced by isoprene oxidation does not represent a substantial fraction of OA at the selected measurement stations. The major contribution of isoprene SOA to OA reaches about 5 % (see Fig. 14h) and is observed at the Iskrba station during diurnal conditions.
The anthropogenic fraction of OA is found to be dominated by residential biomass burning OA sources (BBOA). Indeed, according to the temporal factors used in CHIMERE (based on GENEMIS; Ebel et al., 1997;Friedrich, 2000), 4 % of annual emissions of residential BBOA occurs during July-August, leading to a non-negligible amount of residential BBOA during summer. This result remains, however, subject to caution, owing to the large uncertainties in the temporalization of biomass burning emissions in the model. The primary organic fraction (i.e., condensed primary SVOCs) from traffic emissions is found to be substantial in the OA budget only at night in urban areas. On the other hand, the secondary organic fraction produced by traffic emissions can represent about 50 % of diurnal anthropogenic OA at stations near urban areas (i.e., Palaiseau and Cabauw). OA formed by the oxidation of mono-aromatic species is found to be negligible over Europe (less than 0.025 µg m −3 on average over the studied domain). Figure 15 shows the contribution of traffic emission to the simulated OA concentrations for the July-August 2013 period for three categories of precursors: SVOCs, IVOCs and mono-aromatic compounds. As mentioned above, the OA concentrations from monoaromatic compound oxidation are negligible compared to concentrations from traffic S/IVOC oxidation. Globally, in our study over Europe, OA concentrations produced from traffic S/IVOC oxidation are of the same order of magnitude. OA from primary SVOCs is locally more important close to sources (i.e., northern Italy, Moscow, Paris, Gibraltar, etc.). OA from IVOC is globally higher far away from the sources, with a higher dispersion over Europe (Fig. 15). This higher dispersion is expected owing to the larger timescale required to produce low-volatility species via multistep oxidation processes in the plumes of high emission areas.
The distributions of OA within the volatility bins (given in Fig. S2) show similar features from one station to another. The results suggest that OA over Europe has relatively low volatility during summertime. Indeed, the VBS-GECKO contributors to OA have very low volatility: ∼ 80 % of the OA contributors from VBS-GECKO are volatility bins 7 to 5 (VB k,7 , VB k,6 and VB k,5 species), i.e., having saturation vapor pressure at 298 K of 10 −14 , 10 −12 and 10 −11 atm, respectively.

Conclusions
The VBS-GECKO parameterization for SOA production was developed based on explicit mechanisms generated with the GECKO-A tool. The VBS-GECKO parameterization was fitted using box modeling results for a selected set of parent compounds including terpenes, mono-aromatic compounds, linear alkanes and alkenes and for various environmental conditions, including different NO x regimes, temperatures, and OA loads (Lannuque et al., 2018a). In this study, the VBS-GECKO parameterization was evaluated in the CHIMERE β 2017 CTM over Europe during summertime.
The VBS-GECKO parameterization shows good performances to simulate OA concentrations over Europe in the summer. Calculated mean fractional biases and mean fractional errors on PM 2.5 , OC PM 2.5 and OM PM 1 satisfy the performance criteria of Boylan and Russel (2006). The model configuration including the VBS-GECKO parameterization yields to higher OA concentrations compared to the former Figure 14. Evolution of simulated OA concentrations and distribution function of sources with the IVOC 30VOC model configuration. Panels (a), (c), (e) and (g) present evolutions of daily averaged concentrations during the July-August 2013. Panels (b), (d), (f) and (h) present mean daily profiles. Results are shown at two stations influenced by anthropogenic sources in the Netherlands (Cabauw, a, b) and in France (Palaiseau, c, d) and at two stations influenced by biogenic sources in Norway (Birkenes II, e, f) and Slovenia (Iskrba, g, h). Primary and secondary BBOA include compounds from biomass burning. Traffic SVOC includes C 14 to C 26 VBS-GECKO alkanes and alkenes and SOA from traffic SVOC+IVOC oxidation includes their oxidation products. SOA from terpenes includes all species produced by α-pinene, β-pinene, limonene, ocimene and humulene oxidation. reference configuration including the H 2 O parameterization. The deviations between the two configurations are especially marked over northern Europe, with an increase factor of ∼ 60 %. Outside this area, the OA increases obtained with the VBS-GECKO configuration are slight. Statistically, the use of the VBS-GECKO improves the overall MFB, MFE and RMSE and does not modify significantly correlation coefficients. Tests performed to examine the sensitivity of simulated OA concentrations to hydro-solubility, volatility, aging rates and NO x regimes have shown that the VBS-GECKO parameterization provides consistent results that are not subject to large deviations induced by parameters provided by the gas-phase mechanism included in the CTM (e.g., HO x or NO x concentrations). However, the OA concentrations remain underestimated with the VBS-GECKO model configuration, especially in areas with a significant contribution of anthropogenic sources (e.g., reaching a factor of 2.5 for OC PM 2.5 at the NL0644R station in the Netherlands). None of the conducted sensitivity tests leads to OA variations large enough to fill the gaps between measurements and simulated concentrations at the anthropogenic stations.
The analysis of simulated OA shows that, during summertime, the main fraction is made of secondary matter which represents ∼ 85 % of the total mean OA concentration. A 4924 V. Lannuque et al.: Modeling organic aerosol over Europe in summer conditions Figure 15. Mean simulated anthropogenic OA mass concentration formed by the partitioning of species produced from the oxidation of emitted traffic SVOCs (a), traffic IVOCs (b) and monoaromatic compound (c) for July-August 2013 over Europe (data from IVOC 30VOC simulation). large fraction of the simulated OA comes from biogenic sources (between 30 % and 85 % of the total OA), especially from terpene oxidation which represents ∼ 95 % of these biogenic sources. For the conditions examined in this study, OA formed by the oxidation of mono-aromatic compounds appears to be negligible with maximum mean concentrations of 0.025 µg m −3 over the North Sea and Benelux. Note that ignoring SOA production from these precursors in the model would substantially reduce the number of VB k,i species currently considered in the VBS-GECKO parameterization. The simulated OA was found to be made of species having low and extremely low volatilities in remote areas but also of SVOCs closer to major anthropogenic sources.
Finally, IVOC oxidation was added to examine the contribution of this additional source to the SOA budget. Five model configurations with distinct IVOC emissions from traffic were tested and compared using the VBS-GECKO parameterization in CHIMERE. As expected, considering the emission of IVOCs by traffic and transport sources was found to globally increase background OA concentrations. Although SOA production from traffic IVOC oxidation can locally be significant (up to ∼ +3 µg m −3 in northern Italy, assuming IVOC emissions represents 65 % of NMVOC emissions), this additional OA source remains too small to explain the gap between simulated and measured values at stations where anthropogenic sources are dominant. This first application of this new VBS-GECKO parameterization has been shown to provide consistent results. This outcome creates motivation to extend the exploration to wintertime conditions and to expand the list of parent compounds considered, in particular to include SOA formation from oxidation of isoprene, sesquiterpenes or organics species emitted by residential biomass burning, a prerequisite to extend the evaluation and analysis to wintertime when this source is dominant. This is the subject of ongoing studies. The VBS-GECKO is a heavy parameterization in term of species number. Calculation time is multiplied by 2 using the complete VBS-GECKO scheme with IVOCs compared to H 2 O. This study has shown that the number of species can be optimized. For example, because of the low influence on OA concentrations, the representation of the SOA formed by the oxidation of monoaromatic species can be highly simplified and C 10 precursors even removed.
Data availability. Daily averages and mean day profiles for the 17 model configurations presented in this article have been made available on Zenodo: https://doi.org/10.5281/zenodo.1654297 (Lannuque et al., 2018b).
Author contributions. VL implemented the parameterization in the air quality model, conducted the simulations and the sensitivity tests, and wrote the article. FC conducted the reference simulation. VL, FC, MC, BA and BB contributed to design the research, develop the parameterization, interpret the data and revise the article.
Competing interests. The authors declare that they have no conflict of interest.