Optical and hygroscopic properties of black carbon influenced by particle microphysics at the top of the anthropogenically polluted boundary layer
Aerosols at the top of the planetary boundary layer (PBL) could modify its atmospheric dynamics by redistributing the solar radiation and start to be activated to form low-level cloud at this layer. Black carbon (BC), as an aerosol component efficiently absorbing solar radiation, can introduce heating and positive radiative effects at this sensitive layer, especially in the polluted PBL over the continent. This study presents continuous measurements of detailed BC properties at a mountain site located at the top of the polluted PBL over the North China Plain, during seasons (3 and 4 weeks of data during winter and summer, respectively) with contrasting emission structure and meteorology. The pollution level was persistently influenced by local surface anthropogenic emission on a daily basis through daytime convective mixing, but the concentration was also enhanced or diluted depending on air mass direction, defined as a neutral, polluted and diluted PBL, respectively. Winter was observed to have a higher BC mass fraction (4 %–8 %) than summer (2 %–7 %). By resolving the detailed particle size-resolved mixing state of BC in optical and hygroscopic models, we found an enhanced BC mass absorption cross section (MACBC) for the polluted PBL (up to 13 m2 g−1 at λ = 550 nm), which was 5 % higher during summer than winter due to a smaller BC core size. The higher BC mass fraction in winter corresponded to a lower single-scattering albedo by 0.03–0.09 than summer, especially the lowest for the diluted winter PBL (0.86 ± 0.02). The water supersaturation (SS) required to activate half the number of BC decreased from 0.21 % ± 0.08 % to 0.1 % ± 0.03 % for the winter diluted and polluted PBL and from 0.22 % ± 0.06 % to 0.17 % ± 0.05 % for summer. Notably, at the top of the anthropogenically polluted PBL in both seasons, the enlarged BC with enhanced absorption capacity could also be efficiently droplet activated; e.g. winter (summer) BC with an MAC of 9.84 ± 1.2 (10.7 ± 1) m2 g−1 could be half activated at SS = 0.13 % ± 0.06 % (0.18 % ± 0.05 %). This BC at the top of the PBL can more directly interact with the free troposphere and be transported to a wider region, exerting important direct and indirect radiative impacts.
Black carbon (BC) aerosol is strongly shortwave absorbing, wielding an important climate warming impact on the regional and global scales (Bond et al., 2013; Bond and Bergstrom, 2006). The emission of BC has large regional heterogeneity with a higher impact over polluted regions (Ramanathan and Carmichael, 2008). The impacts due to BC heating are importantly determined by its vertical distribution in the atmospheric column, which could lead to a more stable or convective planetary boundary layer (PBL) (Ding et al., 2016; Koch and Del Genio, 2010); e.g. an enhanced heating at a higher level will depress the development of the layer below (Chung et al., 2002; Ramanathan et al., 2005; Hansen et al., 2005), while the heating can promote the convection above (Mcfarquhar and Wang, 2006; Rudich et al., 2003); e.g. BC was found to account for 43 % of the total aerosol radiative forcing at the atmosphere in South Asia due to heating (Raju et al., 2020). Therefore, the properties of BC at the top of the PBL are important, which may result in contrasting impacts in perturbing atmospheric dynamics. In addition, surface emissions could serve regular cloud condensation nuclei (CCN) on a daily basis through daytime convective mixing in the PBL (Bretherton and Wyant, 1997; Wood and Bretherton, 2004). Aerosols can be uplifted to the top of the PBL and subsequently activated to incorporate into clouds. However, the way of BC from surface sources to be activated, after the PBL processing during vertical transport, is yet to be explicitly understood.
Ground measurements of BC have been intensively conducted over the polluted North China Plain (NCP) region in the last decades (Han et al., 2009; Cheng et al., 2011; Ji et al., 2018; Liu et al., 2019a); e.g. the seasonal variation of elemental carbon in urban Beijing during 2005/06 and 2012/13 (Han et al., 2009; Ji et al., 2018), the size-resolved mixing state of BC and the aging mechanism at a suburban site in the NCP (Cheng et al., 2011), and the contrasting physical properties in urban Beijing between winter and summer (Liu et al., 2019a) were investigated in these studies, but these results were not able to represent the BC properties at the top of the PBL. Additionally, recently conducted series of aircraft measurements provided comprehensive information about vertical distributions of BC over this region (Zhao et al., 2019; Ding et al., 2019a), but the manner of the aircraft measurement could not capture the variation of BC at a certain level at sufficient time resolution. The nature of the diurnal pattern of the PBL means that not only is the surface concentration of pollutants influenced by the daily evolution of the PBL, but that the pollutants at the top of the PBL will also have diurnal variation which needs stable measurements to be characterized. This is particularly the case if the top of the PBL was continuously influenced by surface emissions. However, such information is lacking at the top of the PBL over the polluted NCP region, and many models still rely on surface measurements to estimate the conditions at higher levels (Guleria et al., 2014; Srivastava et al., 2012a).
Microphysical properties of BC importantly determine its optical and hygroscopic properties. For example, the presence of coatings associated with refractory BC (rBC) may enhance its absorbing capacity (Liu et al., 2017) and also enhance its hygroscopicity (Liu et al., 2013) and particle size, thereby modifying the potential to be droplet activated (Chuang et al., 2002; Panicker et al., 2016; Ding et al., 2019b). This study for the first time characterizes the detailed BC microphysics at a mountain site located at the top of the PBL, influenced by surface emission on a daily basis over the NCP region. We have conducted the experiments with intensive measurements lasting for 1 month for each of the representative seasons. We investigated the optical and hygroscopic properties of BC at this level, as influenced by microphysical properties. Such information will help to constrain the impacts of BC in influencing the PBL dynamics and low-level cloud formation over this anthropogenically polluted region.
Experiments in this study were performed in winter (February–March) and summer (June–July) of 2019 at a mountain site (115.78∘ E, 40.52∘ N; 1344 m), located north of Taihang ridge to the northwest of central Beijing, shown in Fig. 1a. The site is away from any local primary emissions, but the only sources of pollutants are contributed by lower-level surface emissions and regional transport (the follow-up discussions).
Backward trajectories at the site are analysed using the HYSPLIT 4.0 model (Draxler and Hess, 1998) for every 6 h during the experimental period. The meteorological field uses the 1∘ × 1∘, 3-hourly GDAS1 reanalysis product, and trajectories back to 48 h are calculated. The backward trajectories are used for further cluster analysis to group the backward trajectories with a similar transport pathway, whereby the homogeneity of trajectories is maximized in each cluster; meanwhile, the heterogeneity among different clusters is maximized (Makra et al., 2011). This is achieved by analysing the spatial variance of each trajectory and the total variance in each pre-defined cluster. The iteration next simultaneously calculates and assigns the trajectories to the eventually merged clusters. This analysis has been widely used to identify the main transport pathways of air mass (Markou and Kassomenos, 2010; Philipp, 2009; Jorba et al., 2004; Grivas et al., 2008) and is performed using the built-in module in the HYSPLIT model software.
All aerosol measurements were performed behind a PM2.5 impactor (BGI SCC1.829) and were dried by a Nafion tube prior to the sampling of the instruments. BC was measured by a single-particle soot photometer (SP2) (DMT Inc. USA). This instrument uses a laser-induced technique to incandesce BC-containing particles (Schwarz et al., 2006; Liu et al., 2010). The measured incandescence signal of an individual BC particle can be converted to a refractory BC (rBC) mass, which was calibrated using the Aquadag® BC particle standard (Acheson Inc.), and a factor of 0.75 was applied to correct for the ambient rBC mass (Laborde et al., 2012). The core size (Dc) of BC is calculated from the measured rBC mass by assuming a material density of BC of 1.8 g cm−3 (Bond and Bergstrom, 2006). The scattering cross section of BC is derived by the leading edge only (LEO) method (Gao et al., 2007) on the measured scattering signal of an individual BC particle. The entire particle size of a BC-containing particle (Dp) including coatings is determined by matching the measured scattering cross section with the modelled one based on a core-shell assumption using a Mie lookup table (Liu et al., 2014; Taylor et al., 2015). This assumption is mostly valid for BC with thick coatings (Liu et al., 2017) but does not consider the scenario in which BC may be attached to dust particles (Srivastava et al., 2018), given that no dust event was observed in this study. The bulk coating thickness (Dp∕Dc) in a given time window is calculated as the cubic root of the total volume of BC-containing particles weighted by the total volume of rBC (Liu et al., 2014):
where Dp,i and Dc,i are the diameters for the ith single particle, respectively. The count (or mass) median diameter (CMD or MMD) is derived from a number (or mass) size distribution, below and above which size the number (or mass) concentration is equal. The modelled mass absorption cross section (MAC) of an individual BC-containing particle is calculated by applying Mie theory (Bohren, 1998) with a core-shell mixing state assumption. The bulk MAC for a given time window can then be determined by the total MAC of each BC particle divided by the total rBC mass, expressed as
where MACi and mrBC,i are the MAC and rBC mass for each particle, respectively. An example to calculate the MAC from single-particle information is shown in Fig. 5f. The absorption coefficient kabs (in M m−1) is calculated as the MAC (m2 g−1) multiplying the rBC mass concentration (µg m−3) in each size bin and then integrated throughout the size distribution:
where m (log Dc,i) is the BC mass concentration at each Dc bin.
The volume ratio between coating and rBC could be obtained from Dc and Dp of individual BC:
where εcoating and εrBC are the volume fraction within a BC particle. The hygroscopicity parameter of BC (κBCc) could be calculated with known κcoating and κrBC = 0, based on the Zdanovskii–Stokes–Robinson (ZSR) rule (Stokes and Robinson, 1966), expressed as
In this study, the main focus is the coating abundance distribution across all BC size distributions, but the variation of coating composition is of less importance; thus, a constant κcoating = 0.3 is used to represent a typical environment containing aged aerosols (Pringle et al., 2010). An example to calculate κrBC from single-particle information is shown in Fig. 5g.
Total aerosol size distribution was measured by a Scanning Mobility Particle Sizer (SMPS, TSI Inc., model 3936) at mobility diameter 15–700 nm. The total particle mass below diameter 1 µm (PM1) is derived from the SMPS size distribution by assuming a mean particle density of 1.45 g cm−3 (Liu et al., 2015; Cross et al., 2007). The scattering cross section σsc (µm2) of a particle at all sizes is calculated by applying Mie calculation assuming a refractive index (RI) of 1.48+0i (Liu et al., 2009) (a positive imaginary RI considering the BC mass fraction is tested to have a minor influence on total scattering within 3 %), thereby calculating the scattering coefficient ksca (in M m−1) of all aerosols:
where n (log Di) represents the particle number concentration at the ith size bin. Single-scattering albedo (SSA) is derived as the quotient of scattering coefficient (ksca) divided by extinction coefficient (kabs+ksca).
4.1 Classification of the PBL
Clustered air masses for both seasons are shown in Fig. 2, and three clusters are classified for each season. For both seasons, cluster 1 (C1) represents the air masses from the most intensive anthropogenically influenced regions according to the BC emission inventory (Fig. 1b). The seasonal difference is that the winter pollution was transported from the west over Shanxi and Hebei provinces and was southerly in summer mainly from the North China Plain over Hebei province. Cluster 2 (C2) passed over similar regions in both seasons from the cleaner north. Cluster 3 (C3) had a longer transport than both other clusters, from northwest and northeast in winter and summer, respectively. The diurnal variations of PBL height (PBLH) corresponding to periods of each cluster are shown in Fig. 2d and h, with a pronounced diurnal pattern. Apart from C3, winter had a lower PBLH than summer; i.e. the mountain site was slightly above or below the well-developed PBL top in winter and summer, respectively. The consistent diurnal variation of the PBL means the mountain site was persistently influenced by the surface sources through daytime convective mixing, when pollutants were transported in the polluted PBL. However, the actual concentration will depend on whether the site had contributions by additional sources or dilution (Fig. 1c).
Figure 3 shows the temporal evolution of BC mass and PM for both seasons classified by air mass clusters, with panels g to 1 showing the frequency under each cluster. Figure 4 shows their diurnal variations. For all experimental periods, the concentration level of BC mass was generally positively correlated with the PM mass, both indicating the pollution levels. Among the three clusters, C2 had the medium mass concentration, with over 85 % frequency of the air masses contributed by local regions (± 1∘ around the measurement site), and additional air masses were from the cleaner northerly direction, similar for both seasons (Fig. 2). It is likely that this cluster was mainly contributed by local emission and occasionally diluted to some extent by the air mass from a less polluted region. Here this cluster is defined as the “neutral PBL” to distinguish it from the other two clusters. In winter C2 showed clear diurnal variation of BC and PM1 concentrations, with significant enhancement in the daytime (Fig. 4b and e) with a fully developed PBL (Fig. 2d), with the diurnal pattern consistent with a previous study conducted in the Indian Himalayan foothills (Srivastava et al., 2012b). This diurnal pattern on the mountain was in contrast with the usual surface measurement, when the daytime PBL development could dilute the concentration (Liu et al., 2019a; Han et al., 2009). This opposite trend on the mountain site was consistent with the fully developed PBLH at 12:00–16:00 (Fig. 2d) when the top of the PBL reached the mountain site at this time, and pollutants were transported through convective mixing from the surface sources (Fig. 1c). At midnight, the nocturnal depressed PBL trapped the surface pollution towards the mountain, and the subsiding cleaner air in the free troposphere may have diluted the concentration of pollutants on the mountain site (Sullivan et al., 1998; Bennett et al., 2010). The enhanced concentration from midday in summer was also observed (on the mean, Fig. 4a) but was not as pronounced as in winter, probably due to some wet removal during the daytime vertical transport from the surface, given the high relative humidity (RH) in the summer (Fig. S1 in the Supplement).
Consistent with the combined back-trajectory and emission analysis above, C1 had for both seasons the highest BC (1.0 ± 0.5 and 0.4 ± 0.2 µg m−3 for winter and summer, respectively) and the highest PM mass (23.8 ± 10.3 and 13.4 ± 9.5 µg m−3). Compared to C1, for C2, the concentration of BC mass was enhanced by a factor of 2.8 (1.7) higher than that in C2 for winter (summer), with winter having a mass concentration frequently exceeding 1 µg m−3. C1 clearly shows the diminished diurnal variation compared to the neutral PBL of C2, but all increased throughout the day and night (Fig. 4a and d), particularly for winter. This is because besides the persistent influence of daytime convective mixing as the neutral cluster in C2, C1 had an additional contribution from wider polluted regions, here defined as “polluted PBL” (Fig. 1c). This contribution by regional transport was not related to a diurnal pattern. The lower concentration in the summer mountain may also result from the lower surface emission in the season.
C3 had the lowest pollution level among all air mass clusters, with a lower BC (0.09 ± 0.03 µg m−3) and PM1 mass (1.8 ± 0.4 µg m−3) than C2 by a factor of 2–4, within a similar range of a previous study in the western and central Himalayas (Nair et al., 2013). C3 represented the air masses from regions with low emissions (Fig. 1b). In addition, the faster transport (shown as the longest path for back trajectories among clusters, Fig. 2c) and the highest PBLH (Fig. 2d) in C3 could efficiently dilute the pollution in the PBL, here termed “diluted PBL”. Compared to C2, C3 can efficiently disperse and reduce the pollutants being vertically transported to the mountain site from the surface, thus with no apparent diurnal pattern of pollution concentrations either (Fig. 4c).
BC mass fraction in PM1 was overall higher in winter than summer, on average at 5.1 % ± 1.7 % and 3.6 % ± 2.3 %, respectively, with both seasons showing a frequency distribution skewed to higher values up to 10 % (Fig. 3k and l). Note that in summer the BC mass fraction among clusters had no discernible differences, with only C2 shown to be slightly higher. The overall higher BC mass fraction in winter may result from the seasonal variation in emission structure that the additional primary emissions from heating activities may have introduced more fractions of BC (Chow et al., 2011; Liu et al., 2018). However, the lowered BC mass fraction for the polluted PBL in winter (with a significant reduction for fraction > 7 %) may result from the enhanced secondary formation in a polluted environment (Volkamer et al., 2006; Hallquist et al., 2009). The comparable BC mass fraction between C1 and C3 in summer (but all lower than neutral PBL) may result from the dominant process of enhanced secondary formation (reducing PM1) and particle scavenging (reducing BC) for polluted and diluted PBL, respectively. There was a notably higher BC mass fraction at 6.7 % ± 1.5 % for the diluted PBL in winter, suggesting a much reduced secondary aerosol in a less polluted environment, and the removal process of BC had been less efficient than other substances (Koch and Del Genio, 2010).
4.2 Particle microphysics of BC
BC core size showed no variation among all PBL types in both seasons. The mass (count) median diameter of the BC core is 203 ± 12 nm (106 ± 7 nm) and 167 ± 11 nm (85 ± 5 nm) for winter and summer, respectively. The BC core size could be used to discern emission sources, such as BC from solid fuel burning that tended to have a larger MMD compared to those from traffic sources (Liu et al., 2014). The larger MMD in winter than summer was consistent with previous observation over this region (Ding et al., 2019a; Hu et al., 2020), which may indicate additional sources from residential solid fuel burning for heating in the cold season.
The coatings relative to BC, as reflected by Dp∕Dc, were positively correlated with the pollution level of the PBL (represented by PM1 mass loading) in winter (Fig. 5a) and in summer from a neutral to polluted PBL (Fig. 5b). The polluted PBL in winter had the highest Dp∕Dc (1.76 ± 0.3), in line with the most polluted condition. For both neutral and diluted PBLs, winter had higher BC coatings than summer. Apart from some periods in summer, the diluted PBL occasionally showed higher Dp∕Dc up to 1.8, comparable with the high end of that for the polluted PBL.
The warmer temperature in summer may have caused a more likely tendency for some semi-volatile particle species to evaporate, thereby reducing coatings on BC in winter even at the same pollution level, which is consistent with previous ground studies over this region (Liu et al., 2019a). The highest coatings were associated with the most polluted condition, implying that the regional transport of air mass from a wider polluted region may have advected both primary emissions and gas precursors when some gas-partitioning processes may have occurred on BC during transport and caused the high coatings. In a clean environment, summer showed remarkably higher coatings than winter, which may result from more intense solar radiation received at the mountain site in summer, where photochemical reactions may have caused significant formation of secondary particulate matter (Xu et al., 2017; Bao et al., 2018; Liu et al., 2019b).
The detailed size distributions of uncoated and coated BC are shown in Fig. 5c and e. Here three typical examples are chosen to represent the polluted and diluted PBLs in winter (case 1 and case 2) and the polluted PBL in summer (case 3). Comparing between case 1 and case 2, it showed that the polluted period had caused increased size for all particles from peak diameter (d) less than d = 30 nm to the accumulation mode of d = 120 nm. Coated BC diameter peaked from 150 to 220 nm. This means the condensation process had occurred on all particles and enlarged their sizes, including BC. The coated BC in the most polluted PBL significantly extended its coated size up to d = 400–700 nm. Note that for the clean PBL in winter, the coated BC was populated at d = 150 nm, leading to a higher BC number fraction of 22 % at this size. For the polluted PBL in summer, the peaking diameter of all particles (d = 450 nm) was lower than winter, and coated BC also peaked at a smaller size (d = 153 nm). Figure S3 shows almost consistent coated BC sizes in summer (120–130 nm), which was smaller than winter because of the smaller core size (though with a higher Dp∕Dc).
Detailed core-size-resolved mixing states, expressed in a space of coated vs. uncoated BC diameter, are shown in Fig. 5f–h, corresponding to the three cases above. Dp = Dc indicates no coatings on BC and coating increases when Dp is larger than Dc. For the polluted PBL in winter, most BC populations lay between 100–200 nm core diameter and 200–300 nm coated diameter, in contrast to the diluted PBL with a significant fraction of uncoated BC and a coated diameter at 100–140 nm. The summer polluted PBL showed a reduced fraction of bare BC but a range of coating thickness for coated BC. Such analysis in mapping the size-resolved mixing state of a single BC particle on the space of uncoated–coated size can resolve the optical (contour in Fig. 5f) and hygroscopic (contour in Fig. 5g) properties that BC particle microphysics could influence, which will be discussed next.
4.3 Optical properties of BC
Figures 6a and b and S4 in the Supplement show the mass absorption cross section (MAC) of uncoated and coated BC for different PBL types in both seasons. Summer showed systematically higher MAC (7.2 ± 0.1 m2 g−1) than winter (6.6 ± 0.3 m2 g−1) for uncoated BC, because the BC core was smaller in summer than winter (Figs. S2 and S3 in the Supplement). The MAC for coated BC was largely modulated by coatings, showing positive correlation with PM1 in winter (MACBC,coated = 0.09 ⋅ PM1 + 8.7, r = 0.79) and summer (MACBC,coated = 0.12 ⋅ PM1 + 9.5, r = 0.5), corresponding to the diluted to polluted PBL types. The enhanced absorption efficiency of coated BC with increased pollution level was consistent with previous studies over this region (Zhang et al., 2018; Ding et al., 2019a). The mean MACBC,coated for the polluted PBL in summer (11 ± 1 m2 g−1) was higher than that in winter (10.7 ± 0.9 m2 g−1) by 2 %. The neutral and diluted PBL also had a higher MAC in summer than winter (by 8 % and 22 %, respectively). The overall higher absorption efficiency of BC in summer (especially in the diluted PBL) was due to the smaller core size, leading to a higher baseline MAC for uncoated BC by 10 % than winter. This effect prevailed over the even lower coating amount and associated absorption enhancement in summer (Fig. 5b). Notably, the MACBC for the diluted summer PBL had been enhanced by both reduced BC core size and increased coatings (Fig. 5b), reaching an almost equivalent MAC compared to the winter neutral PBL. This means that at the top of the clean PBL in summer there was a BC layer with high absorbing capacity (in contrast to winter with a much lower MAC), which may efficiently absorb the strong solar radiation.
The single-scattering albedo at λ = 550 nm (SSA550) in winter was systematically lower for all PBL types (Figs. 6c and d and S4) by 0.06, 0.05 and 0.08 than summer for the diluted, neutral and polluted PBLs, respectively. The decreased SSA550 was in line with the increased BC mass faction (Fig. 3) and also influenced by the absorbing efficiency, as it was reported that the SSA of elemental carbon (EC) particles was as low as 0.25 (Srivastava et al., 2020). Our winter results here were comparable to previous aircraft measurements over the Beijing region in the cold season of 2016, with SSA ranging from 0.8 to 0.98 from the clean to heavily polluted periods in the PBL (Tian et al., 2020). For the diluted PBL in winter, SSA550 could reach as low as 0.86 ± 0.02 when BC mass fraction reached 7 % ± 1.5 % (Fig. 3k). This was within the range of that study in the clean period at SSA = 0.8–0.85 in the PBL, and the neutral and polluted PBLs were within a similar range in transition and the fully polluted PBL at SSA = 0.85–0.98, suggesting the clusters here may represent different development stages of pollution events. The lower SSA in the winter PBL than summer tended to induce radiative effects towards a more positive effect (Hansen et al., 1981; Haywood and Ramaswamy, 1998) at the top of the PBL, in particular for the clean winter PBL.
4.4 Hygroscopic properties of BC
The droplet activation of BC is determined by the particle size and hygroscopicity, where the coatings play roles in enlarging the entire BC size (Dusek et al., 2006a, b) and increasing its hygroscopicity (Liu et al., 2013). Both factors can be obtained by our observation of size-solved mixing state of BC. The coated BC diameter based on number concentration (coated CMD) is shown in Fig. 7a and b. The CMD of coated BC in the winter polluted PBL was 0.19 ± 0.05 µm, which was the largest among PBL types. Generally, the coated BC CMD was in positive correlation with the PM, in winter fitted as CMD = 0.003 × PM1 + 0.14 (r = 0.69) and in summer as CMD = 0.001 × PM1 + 0.11 (r = 0.73). The coated BC CMD in winter PBL was larger than summer by 14, 35 and 56 nm for diluted, neutral and polluted PBLs, respectively.
The hygroscopicity parameter of the BC-containing particle (κBCc) at the size of the CMD is positively correlated with coating content. In winter κBCc was at 0.15 ± 0.02, 0.20 ± 0.03 and 0.24 ± 0.03 for the diluted, neutral and polluted PBLs, respectively, while the corresponding values were 0.19 ± 0.03, 0.20 ± 0.03 and 0.22 ± 0.03 in summer, consistent with the reduced Dp∕Dc from the polluted PBL to the diluted PBL for both seasons. κBCc could be fitted as κBCc = 0.003 × PM1 + 0.17 (r = 0.77) and κBCc + 0.004 × PM1 + 0.17 (r = 0.49) for winter and summer, respectively. Note that the summer-diluted PBL had a significantly higher κ (0.19 ± 0.03) than winter for the same PBL type.
After obtaining the CMD of coated BC and the corresponding κBCc, a critical water superstation (SS) could be derived from the Kölher model (Fig. S5 in the Supplement) for BC at the size of the CMD to be activated. By assuming that all of the population larger than the CMD could also be consequently activated (because of the larger particle size and higher hygroscopicity), the SS obtained above is thus the lower estimate for half of the number population of BC to be activated, termed SShalf. In line with the increased coated BC size and particle hygroscopicity, SShalf decreased with increased pollution level, from 0.21 % ± 0.08 % to 0.1 % ± 0.03 % for the winter-diluted to polluted PBL and from 0.22 % ± 0.06 % to 0.17 % ± 0.05 % for summer. This highlights the lowest possible SS required to activate BC in the polluted winter PBL, and for the same PBL type, summer will need a higher SS, apart from occasionally some lower SShalf for the summer-diluted PBL. This potential CCN ability of BC is derived from the physical properties of BC itself, but the actual activation of BC depends on the ambient superstation condition which is determined by the size distribution of existing droplets and other aerosols competing with CCN (Pruppacher et al., 1998; McFiggans et al., 2006). The results here generally consistent with a previous surface measurement of BC CCN activation in urban Nanjing as constrained by size-resolved compositions (Wu et al., 2019) when an activation fraction of 33 % at SS = 0.1 % was found. A previous study using flight measurements over the NCP region (Ding et al., 2019a) found a SS = 0.08 % required to activate half of the BC number in heavy pollution conditions, consistent with the polluted PBL here.
By performing continuous measurement on a mountain site located at the top of the planetary boundary layer (PBL) over the North China Plain region in winter and summer, the optical and hygroscopic properties of BC were investigated. We identified three types of PBLs, all persistently influenced by surface anthropogenic emission on a daily basis through daytime convective mixing, but which could be either enhanced or diluted subject to received air masses. By investigating the detailed microphysical properties of BC, this study provides a clear picture of optical and hygroscopic characteristics of BC at the top of anthropogenically influenced PBL. Highlighted information includes higher BC mass fractions in winter than summer, corresponding to a lower single-scattering albedo by 0.05–0.08, especially the lowest for the diluted winter PBL (0.86 ± 0.02); both mass absorbing efficiency and CCN ability of BC are positively correlated with the pollution level of the PBL due to enhanced coating content under a more polluted environment; e.g. from the diluted to polluted PBL, coating content increased by 39 % (11 %), absorbing efficiency increased by 31 % (10 %), and the water supersaturation in activating half number of BC decreased by 53 % (26 %) for winter and summer, respectively. It clearly demonstrates that BC with higher coating content could be efficiently incorporated into liquid clouds, and meanwhile this BC had a high absorbing capacity, which means this highly absorbing BC may have great potential for in-cloud heating (Jacobson, 2012; Nenes and et al., 2002).
Compared to surface measurement, the results here are more directly linked to the aerosol properties closer to the condensation level which is subsequently CCN-activated. BC located at this layer more importantly determines its heating impacts due to receiving stronger solar radiation. Rather than being subject to significant scavenging processes of low-level emissions, BC transported to the lower free troposphere may be transported to a wider region (Weinzierl, 2008; Yang et al., 2018; Govardhan et al., 2017), exerting regional direct and indirect radiative impacts.
The data in this study are available from the corresponding author upon request (firstname.lastname@example.org).
The supplement related to this article is available online at: https://doi.org/10.5194/acp-21-681-2021-supplement.
DL, DZ and DD led and designed the study. SD, DL, DZ, KH, PT, RL, YC, FW, HH and MH set up and conducted the experiment. SD, DL and KH contributed to the data analysis. SD and DL wrote the paper.
The authors declare that they have no conflict of interest.
This research was supported by the National Key Research and Development Program of China (2016YFA0602001) and the National Natural Science Foundation of China (41875167). Part of this work is supported by the National Center of Meteorology, Abu Dhabi, UAE, under the UAE Research Program for Rain Enhancement Science.
This research has been supported by the National Key Research and Development Program of China (grant no. 2016YFA0602001) and the National Natural Science Foundation of China (grant no. 41875167).
This paper was edited by James Allan and reviewed by Atul Kumar Srivastava and one anonymous referee.
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