Measurement report: Optical properties and sources of water-soluble brown carbon in Tianjin, North China – insights from organic molecular compositions

. Brown carbon (BrC) aerosols exert vital impacts on climate change and atmospheric photochemistry due to their light absorption in the wavelength range from near-ultraviolet (UV) to visible light. However, the optical properties and formation mechanisms of ambient BrC remain poorly understood, limiting the estimation of their radiative forcing. In the present study, ﬁne particles (PM 2 . 5 ) were collected during 2016–2017 on a day/night basis over urban Tianjin, a megacity in northern China. Light absorption and ﬂuorescence properties of water extracts of PM 2 . 5 were investigated to obtain seasonal and diurnal patterns of atmospheric water-soluble while of apportionments using organic same set and


Introduction
Brown carbon (BrC) is light-absorbing organic carbon (OC) in the atmosphere, which can absorb radiation in the range from near-ultraviolet (UV) to the visible and show strong wavelength dependence (Andreae and Gelencsér, 2006;Bahadur et al., 2012). Although its light-absorbing ability is generally weaker than that of black carbon (BC), BrC exerts considerable impacts on atmospheric radiative balance and global climate due to its large abundance and strong light absorption in the near-UV spectrum (Feng et al., 2013;Kirillova et al., 2014;Lu et al., 2015;Zhang et al., 2017;. In addition, BrC can efficiently affect the atmospheric photochemistry processes, formation of secondary organic aerosol (SOA), and, thus, regional air quality by influencing the photolysis rates of atmospheric radicals Moise et al., 2015;Mok et al., 2016;Baylon et al., 2018). Since the last decade, plenty of studies on BrC aerosols have been performed to explore their optical properties and estimate their environmental and climatic effects (Hecobian et al., 2010;Huang et al., 2018;Shamjad et al., 2018;Choudhary et al., 2021;Yue et al., 2022).
However, it is quite a challenge to understand the extremely complex chemical composition, sources, and formation and evolution mechanisms of BrC Yan et al., 2018;Wu et al., 2021). On the one hand, atmospheric BrC is derived from the incomplete combustion of carbonaceous materials, such as fossil fuels, biomass, and biofuel (Chakrabarty et al., 2010;Lack et al., 2012;Sun et al., 2017;Lei et al., 2018;Hettiyadura et al., 2021). On the other hand, BrC can be formed through gas phase, aqueous phase, or heterogeneous reactions from both biogenic and anthropogenic precursors (Lin et al., 2015;. Furthermore, optical properties and chemical compositions of BrC aerosols will undergo significant changes when they are experiencing atmospheric physical and chemical processes such as photochemical aging and hygroscopic growth Forrister et al., 2015;Sumlin et al., 2017;Wong et al., 2017;Dasari et al., 2019;Kasthuriarachchi et al., 2020;Palm et al., 2020;Ni et al., 2021). Therefore, despite the progresses reported in recent years, it is necessary to further characterize the sources and formation mechanisms of atmospheric BrC, particularly from the perspectives of chromophore and molecular composition Yan et al., 2018).
To identify the chromophores in BrC will be beneficial for probing the sources, dynamic optical properties, and aging processes of atmospheric BrC Yan et al., 2018). However, to our best knowledge, until now it is still challenging to conduct a comprehensive analysis of the chromophores of atmospheric BrC. One great difficulty is to distinguish the absorbing chromophores from a majority of nonchromophoric components. The threedimensional excitation-emission matrix (EEM) fluorescence spectroscopy is a powerful tool for revealing the chemical compositions, sources, and chemical reactions of complex chromophores in different environments, since each chromophore has its own specific excitation-emission peak in the EEM maps (Coble, 1996(Coble, , 2007Murphy et al., 2013). In recent years, the fluorescence technique has been used to investigate the characteristics and potential sources of chromophores in aerosols (Mladenov et al., 2011;Fu et al., 2015;Chen et al., 2016Chen et al., , 2020Qin et al., 2018;Tang et al., 2020;Wang et al., 2020). With the fluorescence technique, some categories of chromophores, such as humic-like and protein-like chromophores, could be identified in atmospheric aerosols. However, applications of the fluorescence technique in the atmospheric BrC aerosols were comparatively limited so far .
The North China Plain (NCP), with a regional population contribution of approximately 25 %, is the second-largest plain in China. The NCP is also one of the most developed city clusters in China and contains several megacities, such as Beijing, Tianjin, and Shijiazhuang. Due to the rapid economic development and intensive anthropogenic activities, the NCP has been suffering from severe regional air pollution in the recent years, which has attracted worldwide concern (Zhao et al., 2013;Guo et al., 2014;Huang et al., 2017;Gao et al., 2018;Ge et al., 2018;Zhang et al., 2021). Despite numerous studies on chemical compositions, source apportionment, and formation mechanisms of atmospheric aerosols, the current understanding of the optical properties and sources of BrC aerosols over the NCP are still inadequate. Nevertheless, the limited studies focusing on BrC aerosols are mostly conducted in Beijing (Cheng et al., 2011;Du et al., 2014;Yan et al., 2015Yan et al., , 2020, while the BrC-related studies in other cities in this hotspot region are quite scarce and, therefore, deserve more attention. Located adjacent to Beijing and the Bohai Sea, Tianjin is the largest industrial city and secondlargest megacity in North China. Previous studies have found that Tianjin experienced serious aerosol pollution, with large contributions from anthropogenic activities, including coal combustion, industrial, and vehicular emissions Gao et al., 2018). Abundances and molecular compositions of organic aerosols were investigated, and the contributions of primary emission sources and secondary formation to organic aerosols were also evaluated (Y. . However, optical properties and formation mechanisms of BrC in Tianjin are still unclear.
In the present study, field measurements of water-soluble BrC in ambient fine aerosols were performed in urban Tianjin. Seasonal and diurnal variations in the optical properties of BrC in the water extract were investigated, and direct radiative effects by water-soluble BrC aerosols were also estimated. The fluorescence technique was adopted to further explore the components and possible chromophores in BrC. The impacts of various sources and photooxidation on atmospheric BrC were unveiled by analyzing the relationships of BrC with chemical compositions and the organic molecular markers of aerosols. This study provides a comprehensive view on the temporal variability in optical properties and sources of water-soluble BrC, thereby helping to deepen the understanding in its climatic effects.

Sample collection
PM 2.5 (particulate matter with an aerodynamic diameter of < 2.5 µm) sampling was performed using a high-volume sampler (TE-PM 2.5 HVP-BL; Tisch Environmental) at a flow rate of 1.05 m 3 min −1 . The air sampler was installed on the rooftop (∼ 20 m above ground level) of a building on the Weijin Lu Campus of Tianjin University (39.11 • N, 117.17 • E) in urban Tianjin. The sampling site is close to a commercial and residential region, and there is no obvious industrial emission around the site. Field campaigns were conducted from 10 November to 23 December 2016 (winter) and from 22 May to 22 June 2017 (summer). Daytime samples were collected from 08:00 to 20:00 LT, and nighttime samples were collected from 20:00 to 08:00 LT on the next day. Aerosols were collected onto quartz fiber filters with a size of 20.3 × 25.4 cm (Pallflex 2500QAT-UP), which were preheated at 450 • C for 6 h in a muffle furnace to remove potential contamination from organics. In total, 84 winter samples and 60 summer samples were collected during this campaign. Field blank filters were also collected during both seasons by keeping a blank filter in the sampler for 5 min without air flow. After collection, the samples were stored in the dark at −20 • C until analysis.

Chemical analysis
Then, two pieces of quartz filters with diameter of 14 mm were punched and extracted with 25 mL ultrapure water (> 18.2 M cm). The extracts were under ultrasonication for 20 min and then filtered through a poly tetra fluoroethylene (PTFE) syringe filter (0.22 µm) to remove water-insoluble compounds. Concentrations of water-soluble organic carbon (WSOC) in the water extracts were determined with a total organic carbon (TOC) analyzer (TOC-VCPH; Shimadzu, Japan). The rest of the extracts were used for the light absorption and fluorescence measurement. Major water-soluble inorganic ions (e.g., SO 2− 4 , NO − 3 , Cl − , NH + 4 , and K + ) were analyzed with ion chromatography (ICS 5000+; Thermo Fisher Scientific, USA). A punch of a quartz filter, with an area of ∼ 2.3 cm 2 , was cut to measure the elemental carbon (EC) and organic carbon (OC) concentrations in aerosol samples by using a thermal-optical carbon analyzer (model RT-4; Sunset Laboratory, USA), following the National Institute for Occupational Safety and Health (NIOSH) protocol. Secondary organic carbon (SOC) concentration was estimated with the EC tracer method, which assumed that, in all samples, the OC/EC ratio for the primary sources affecting the site remains constant as follows (Castro et al., 1999): where (OC/EC) min is the minimum value of OC/EC ratios in each season. The measurements of molecular markers in organic aerosols have been reported in detail in our previous study  and are briefly described here. First, a filter aliquot was extracted with dichloromethane / methanol (2 : 1; v/v) under ultrasonication for 10 min and repeated three times. The extracts were then concentrated with a rotary evaporator and dried with pure nitrogen gas. After that, 50 µL of N,O-Bis(trimethylsilyl)trifluoroacetamide (BSTFA) with 1 % trimethylsilyl chloride and 10 µL pyridine was added to the extracts to react at 70 • C for 3 h. After the polar groups were derivatized into the trimethylsilyl (TMS) esters and ethers, the derivatives were added to 40 µL of n-hexane-containing internal standards (C 13 n alkane; 1.43 ng µL −1 ) before gas chromatography/mass spectrometry (GC/MS) analysis. GC/MS analysis was performed using an Agilent model (7890 GC) coupled to a (5975c) massselective detector to identify and quantify the organic compound classes. The GC was equipped with a split/splitless injector and a DB-5MS fused silica capillary column (30 m × 0.25 mm internal diameter; 0.5 µm film thickness). The samples in the fused silica capillary column were analyzed using a specific GC temperature program with the carrier gas of helium. The MS was operated on electron impact (EI) mode at 70 eV, scanning from 50 to 650 Da. Data processes were performed with Agilent ChemStation software. The results were corrected by field blanks, which were treated as the real samples. Temporal variations in the concentrations of carbonaceous species and some molecular markers in PM 2.5 , including sugars and SOA tracers, are plotted in Figs. S1, S2, and S3 in the Supplement, and seasonal average concentrations are summarized in Table S1 in the Supplement.

Light absorption analysis
The light absorbance (A λ ) of the water extracts at the wavelength (λ) spectra between 200 and 700 nm was measured with a UV-Vis spectrophotometer (UV-2700; Shimadzu). The light absorption coefficient Abs λ (Mm −1 ) of the dissolved organic matter (DOM) at the wavelength λ can be calculated as follows: where V l is the volume of the extracts, V a is the volume of the punched and extracted air, and L is the optical path length (0.01 m in this study). A λ are referenced to the A 700 to account for any baseline drift (Hecobian et al., 2010). In this study, light absorption coefficients of water-soluble organics at 365 nm (Abs 365 ) are used as a proxy of BrC, in accordance with previous studies . The mass absorption efficiency (MAE, in m 2 gC −1 ) of water-soluble BrC can be derived as follows: where [WSOC] (µgC m −3 ) represents the mass concentration of WSOC. The wavelength dependence of light absorption fits a power law as follows: where C is a concentration-and composition-related constant, and AAE is the absorption Ångström exponent, depending on the types of chromophores. In this study, AAE was fitted at the range of 300-450 nm. The particle refractive index (m = n + ki) is a key optical parameter in a climate model that expresses the light extinction ability of ambient aerosols. The imaginary part k represents light absorption and can be estimated as follows (Liu et al., 2013): where ρ (g m −3 ) is the particle density and set as 1.5.

Determination of direct radiative absorption by BrC
The direct radiative forcing of water-soluble BrC in Tianjin was assessed with the simple forcing efficiency (SFE). The SFE (W g −1 ) represents the energy added to the Earthatmosphere system per unit of mass aerosol (Bond and Bergstrom, 2006). The wavelength-dependent SFE of BrC can be calculated as follows (Chen and Bond, 2010): where dS(λ)/dλ is the wavelength-dependent solar irradiance, τ atm is the atmospheric transmission (0.79), F c is the cloud fraction (0.6), α s is the surface albedo (0.19 for global average), β is the backscatter fraction, and MSE and MAE are the mass scattering and absorption efficiency of BrC, respectively. Direct radiative forcing due to aerosol scattering can be ignored when estimating the radiative effects of BrC light absorption. Therefore, the absorption radiative forcing in a given spectral range was calculated by integrating the SFE values per nanometer with the simplified Eq. (6) as follows: In addition, the relative direct climate warming effects due to BrC light absorption were also estimated by comparing the direct radiative forcing of BrC with that of BC (Bosch et al., 2014;Kirillova et al., 2014). Relative radiative forcing of BrC (f BrC ) is calculated with the method as follows: where I 0 (λ) is the solar emission spectrum estimated using the clear sky Air Mass 1 Global Horizontal (AM1GH) irradiance model (Levinson et al., 2010). MAE BC, 550 is the mass absorption efficiency for BC at 550 nm, which is set to 7.5 m 2 g −1 , and the AAE for BC is set to 1, based on Bond and Bergstrom (2006) and Kirillova et al. (2014).
[BC] is the mass concentration of BC. The height of the atmospheric boundary layer (h ABL ) is adopted as 1000 m because it has little impact on the calculated ratio in the range of 200-3000 m .

Fluorescence analysis
The EEM fluorescence spectra of the extracts were measured using a fluorometer (Aqualog; HORIBA). The excitation wavelength range was 240-550 nm (3 nm interval), and the emission wavelength range was 246-828 nm (∼ 2.4 nm interval). The measured EEM spectra were calibrated by instrument calibration, internal filter correction, and Raman correction (Murphy et al., 2013). The EEM spectra of all samples were corrected by subtracting the blank sample. The fluorescence intensities were further divided by the amount of water used for the extraction and the air volume of each filter sample to convert the fluorescence unit to Raman units per cubic meter (RU m −3 ). The fluorescence properties of the extracts were determined through humification index (HIX), biological index (BIX), and fluorescence index (FI). The FI was determined by the ratio of emission intensity of 450 to 500 nm under the excitation wavelength of 370 nm, BIX was determined by the ratio of emission intensity of 380 to 430 nm under the excitation wavelength of 310 nm, and HIX was determined by the ratio of the integrated fluorescence emission intensity in the range of 435-480 to 300-345 nm under the excitation wavelength of 255 nm (Battin, 1998;McKnight et al., 2001). With the fully corrected and treated EEM fluorescence spectra data, the parallel factor analysis (PARAFAC) model was adopted to identify the fluorescent components of BrC (Murphy et al., 2013). PARAFAC is a mathematical method to separate the chemically independent but spectrally overlapping fluorescent components based on the assumption that EEM spectra are independent, linear related, and additive (Murphy et al., 2011). During re-cent years, the PARAFAC model has been used to investigate the fluorescence properties of aerosol WSOC (Pöhlker et al., 2012;Matos et al., 2015;Chen et al., 2016Chen et al., , 2020G. Wu et al., 2019Dey et al., 2021). The PARAFAC modeling was performed with the software package Solo (Eigenvector Research Inc.).

Source apportionment of BrC
Positive matrix factorization (PMF; version 5.0), a receptor model developed by the United States Environmental Protection Agency (US EPA), was adopted to carry out the source apportionment of BrC. The PMF model is a multivariate factor analysis tool that decomposes a measured sample matrix into two matrices, including factor profiles and factor contributions (Paatero and Tapper, 1994). PMF can provide, as model outcome, both the source profiles and contributions of various sources, without inputting source profiles. In this study, the measurement data of BrC (i.e., Abs 365 ) and chemical species of the aerosol samples, including OC, WSOC, and major inorganic ions, were selected as inputs of PMF model. Especially, the organic molecular markers (i.e., sugars and biogenic and anthropogenic SOA compounds) were implemented to the PMF model to constrain the sources of BrC. Separating and identifying different source factors with molecular markers species enables more accurate and finer results of source apportionment of organic aerosols Al-Naiema et al., 2018;.

Light absorption properties of BrC
The variations in the light absorption coefficients of watersoluble BrC with a wavelength in the spectral range of 300-600 nm in winter and summer in Tianjin are presented in Fig. S4. The absorption spectrums showed an evident feature of BrC, since they were highly wavelength dependent and decreased remarkably from the ultraviolet to the visible ranges. BrC light absorption was more wavelength dependent in winter than in summer, since the winter average AAE of BrC was 5.4 ± 0.4, about 10 % higher than the summer average (4.9 ± 0.6; Table 1). However, AAE in summer varied in a relatively wider range (3.2-6.5) compared with that in winter (4.3-6.1; Fig. 1a). The gap between AAE values in different seasons indicate that the distinct chemical composition of BrC resulted from various sources and atmospheric formation/aging processes. BrC in winter may be significantly affected by primary emissions of fossil fuel combustion, since high AAE coefficients are often associated with biomass burning (Desyaterik et al., 2013) and coal combustion (Li et al., 2019). In contrast to the significant seasonal variations, there were no evident diurnal variation in AAE because daytime AAE values (4.8 ± 0.6 in summer and 5.4 ± 0.4 in winter) were comparable with nighttime AAE values (4.9 ± 0.6 in summer and 5.4 ± 0.3 in winter). The t test results also showed that the day/night differences in AAE values were not significant. It indicates that chemical compositions of BrC in daytime and nighttime may be similar.
Water-soluble BrC light absorption (at 365 nm; i.e., Abs 365 ) in Tianjin experienced obvious day-to-day variations in both winter and summer (Fig. 1b). Exhibiting remarkable seasonal variations, Abs 365 values were much larger in winter than in summer, similar to the concentrations of WSOC and OC (Table S1). Abs 365 was in the range of 2.0-53.7 Mm −1 in winter and 0.5-6.1 Mm −1 in summer. The average Abs 365 was 14.1 ± 8.5 Mm −1 in winter, ∼ 6.7 times higher than the summer average (2.1 ± 1.0 Mm −1 ; Table 1). Generally, there are no significant differences between daytime and nighttime Abs 365 , with the daytime averages of 14.4 ± 10.3 Mm −1 (winter) and 2.0 ± 0.8 Mm −1 (summer) and nighttime averages of 13.9 ± 6.3 Mm −1 (winter) and 2.1 ± 1.1 Mm −1 (summer). Temporal variations in BrC light absorption are closely related to both the abundance and absorption capacity of BrC.
MAE can be used to describe the light-absorbing ability of BrC aerosols. MAE 365 values of water-soluble BrC in winter and summer were in the ranges of 1.06-2.58 and 0.36-1.50 m 2 gC −1 , respectively (Fig. 1c). Average MAE 365 in winter (1.54 ± 0.33 m 2 gC −1 ) was ∼ 1.8 times higher than that in summer (0.84 ± 0.22 m 2 gC −1 ), suggesting the much higher light absorption capacity of BrC in winter than in summer (Table 1). The imaginary refractive index, k, is a vital parameter representing the light-absorbing ability used in a climate model to assess direct radiative forcing of aerosols (Andreae and Gelencsér, 2006;Shamjad et al., 2016). The k 365 for water-soluble BrC in Tianjin were in the range of 0.052-0.127 in winter and 0.018-0.074 in summer, with the seasonal averages of 0.076 ± 0.016 and 0.041 ± 0.011, respectively ( Table 1). The obvious seasonal variations in both MAE 365 and k 365 also suggest the distinct sources and formation mechanisms of BrC chromophores in different seasons. For example, in the summer aerosols, the larger contributions from biogenic SOA, which are not or less light absorbing, will lower the MAE. In contrast, although the nighttime lightabsorbing ability was slightly stronger than in the daytime in both seasons, diurnal differences were not statistically significant between daytime and nighttime MAE 365 (and k 365 ), as revealed by t test, also indicating the similar chemical compositions of BrC in daytime and nighttime. MAE 365 values in Tianjin were comparable with those in Beijing in North China , higher than those in the USA (Xie et al., 2019) and Europe (Moschos et al., 2018), and lower than those in New Delhi and Kanpur in India (Dasari et al., 2019;Choudhary et al., 2021).

Direct radiative absorption by BrC
Radiative forcing efficiency of water-soluble BrC was estimated by integrating the wavelength-dependent SFE from 300 to 700 nm (i.e., SFE 300−700 ). Because BrC mainly absorb solar radiation in the UV spectral region, the BrC absorption radiative forcing efficiency in the 300-400 nm range (i.e., SFE 300−400 ) was also calculated. Figure 1d illustrates the temporal variations in the radiative forcing efficiencies of BrC at the two spectra. In summer, SFE 300−400 and SFE 300−700 varied from 0.6 and 2.4 to 1.7 and 10.5 W g −1 , respectively. By comparison, variations in the forcing efficiencies were slightly larger in winter, and SFE 300−400 and SFE 300−700 varied from 1.6 and 3.6 to 3.3 and 13.4 W g −1 .
Average BrC forcing efficiency in winter (summer) were 6.2 ± 2.0 W g −1 (4.6 ± 1.7 W g −1 ) over the entire solar spectrum and 2.4 ± 0.5 W g −1 (1.4 ± 0.4 W g −1 ) in the UV range (Table 1). SFE 300−400 and SFE 300−700 were ∼ 71 % and ∼ 35 % larger in winter than summer, respectively, indicating that the more abundant BrC with stronger light-absorbing capacity resulted in a remarkable increase in direct radiative forcing by BrC. It should be noted that SFE 300−400 accounted for 22.4 %-57.4 % (40.3 ± 6.4 %) and 21.0 %-52.0 % (30.7 ± 5.8 %) of SFE 300−700 in winter and summer, respectively, suggesting that radiative forcing in the UV range plays a vital role in radiative forcing by BrC absorption. In comparison with the limited literature calculating with the same method, the BrC forcing efficiency in Tianjin was slightly larger than that in Hong Kong (4.4 W g −1 in winter; Q. Zhang et al., 2020), while much smaller than that in Xi'an in northwestern China (11.7 W g −1 in winter, Q. Zhang et al., 2020) and Kanpur in India (19.2 W g −1 in winter and 12.3 W g −1 in monsoon; Choudhary et al., 2021). Direct radiative forcing by BrC absorption was also evaluated by calculating solar radiative effect of water-soluble BrC relative to BC in the 280-4000 nm range (i.e., f 280−4000 ). The relative radiative effect of BrC in the UV spectral region (i.e., f 300−400 ) was also calculated. f 280−4000 was in the ranges of 4.5 %-25.3 % and 4.8 %-25.6 % (Fig. 1e), with the comparable averages of 13.5 ± 4.1 % and 12.5 ± 4.5 % in winter and summer (Table 1), respectively, indicating that water-soluble BrC is a non-negligible contributor to the climate warming by absorbing solar radiation. Although BrC light absorption was much stronger in winter than summer, relative direct radiative effects of BrC at the entire solar spectrum were comparable in the two seasons. It can be attributed to the enhanced direct radiative effect by BC absorption due to the sharp increase in BC concentration in winter (Table S1). Relative direct radiative effect in the UV range (f 300−400 ) was in the ranges of 19.0 %-96.1 % and 17.4 %-76.6 % in winter and summer, respectively. f 300−400 exhibited obvious seasonal variations with a much larger value in winter (54.3 ± 16.9 %) than in summer (44.6 ± 13.9 %).
The much larger f 300−400 compared with f 280−4000 suggested that although BC still dominated the radiative effect by light-absorbing carbonaceous aerosols, BrC played a far more important role in the shorter wavelength in comparison to the entire spectrum. The large contributions of BrC light absorption in the UV spectral range deserve more attentions due to its potential impact on atmospheric photochemistry and ozone formation (Mok et al., 2016;Baylon et al., 2018). Relative direct radiative effects of water-soluble BrC in Tianjin were comparable to those in the High Arctic (13 ± 7 %; Yue et al., 2019a) and much larger than those in other urban locations in China such as Beijing (5.7 ± 2.5 % in summer and 10.7 ± 3.0 % in winter; Yan et al., 2015), and Xi'an (2 ± 1 % in summer and 10 ± 4 % in winter; Huang et al., 2018). It is stressed that the estimated effects in the present work only represent the direct radiative effects of water-soluble fractions of BrC, and they should be less than the actual effects of aerosol BrC, since the water-insoluble species in BrC were not considered in the calculation. Be-sides, these predicted radiative effects are for water-soluble BrC measured in the extract and do not accurately reflect the actual effects of atmospheric BrC aerosols. The discrepancies between the BrC light absorption of particle-phase BrC and extracted BrC have been found in previous studies (Liu et al., 2013;Cheng et al., 2021;Zeng et al., 2022) and will not discussed here. In addition, due to the lack of vertical measurements of aerosols in the upper air, these estimated radiative effects reflect the solar spectrum integrated relative absorbance of water-soluble BrC and BC for a ground-level situation and do not accurately represent actual impact of aerosol BrC on top-of-atmosphere radiative forcing. This assumption will lead to some uncertainty, although most of the column aerosols over the NCP are distributed within 1.5 km above the ground, while light absorption by aerosols over 4 km above ground is much smaller .

Fluorescence indices of BrC
Fluorescence indices originally developed as indicators of the type and source of the fluorescent DOM in aquatic systems, and soils have been applied to investigate the sources and aging processes of organic aerosols, including primary biological aerosol particles, for a decade (Mladenov et al., 2011;Lee et al., 2013;Fu et al., 2015;Qin et al., 2018;Yue et al., 2019b;Huang et al., 2021;Tang et al., 2021;Wu et al., 2021). HIX is a proxy for the aromaticity of DOM, and an increased HIX value is usually accompanied a higher polycondensation degree, C/H ratio, and aromaticity of DOM (Zsolnay et al., 1999;McKnight et al., 2001;Birdwell and Engel, 2010). HIX values in this study were 2.22 ± 0.54 (1.17-3.51) and 2.73 ± 0.51 (1.64-3.96) during winter and summer, respectively ( Fig. 1f and Table 1), suggesting that water-soluble organic aerosols were less aromatic compared with aquatic or soil DOM, which might be attributed to the lower molecular weight and smaller contributions from aromatic organics (Qin et al., 2018). HIX values of Tianjin aerosols were comparable to those of aerosols in Mount Tai Tang et al., 2021), and the high Arctic (0. 69-5.24, 2.93;Fu et al., 2015), and higher than those in Lanzhou, China (1.2 in winter and 2.0 in summer); Qin et al., 2018), suggesting the moderate aromaticity degree of water-soluble BrC in Tianjin. Similar to previous research in Lanzhou, northwestern China (Qin et al., 2018), HIX values in Tianjin experienced obvious seasonal variations, with higher values in summer than winter, suggesting that water-soluble BrC in summer had a higher aromaticity degree or increasing polycondensation in chemical structure (Zsolnay et al., 1999). Low HIX values were probably associated with freshly introduced primary organic aerosols and fresh secondary organic aerosols (SOA); however, HIX values would significantly increase during the aging processes of organic aerosols Tang et al., 2021). Therefore, HIX values indicated that BrC in Tianjin was significantly affected by primary emissions and less aged in winter, while more aged in summer due to the strong photooxidation and secondary chemical processes.
FI and BIX were both adopted to assess the relative contributions from biological sources to DOM. The fluorophore is often associated with higher aromaticity if FI is low and vice versa (McKnight et al., 2001;Fu et al., 2015). High BIX usu-ally corresponds to the predominant biological or microbial materials, while low BIX indicates few biological organics (Huguet et al., 2009). For water-soluble BrC in Tianjin, BIX values were 1.32 ± 0.14 (1.08-1.73) and 1.19 ± 0.13 (0.92-1.45) in winter and summer, and the corresponding FI values were 1.71±0.06 (1.60-1.88) and 1.61±0.10 (1.32-1.82), respectively ( Fig. 1g-h and Table 1). The slightly lower summer values of BIX and FI indicate that BrC fluorophores in summer had higher aromaticity degrees, in accordance with the HIX results. The lower FI values in summer may be a result of the photobleaching of fluorescent DOM, since fluorescent DOM absorbing light at higher wavelengths would be removed due to photochemical processes (McKnight et al., 2001;Xie et al., 2016). Another possible reason for the higher BIX and FI values in winter is that primary aerosols from coal combustion and biomass burning had high FI and BIX values (Tang et al., 2021). Table 1 also shows that in both seasons BIX and FI values were slightly lower during the daytime compared with nighttime, suggesting that fluorophores in aerosols at daytime were more aged due to photobleaching and thus had higher aromaticity. Figure 1 presents an obvious seesaw relationship between HIX and BIX (or FI) in winter. HIX showed significantly negative correlations with both FI (r = −0.803; p < 0.01; Fig. 2a) and BIX (r = −0.927; p < 0.01; Fig. 2b) in winter, indicating the quite similar factors controlling the aromaticity and biological contribution of organic aerosols. Actually, the elevated aromaticity in winter was mainly led by the increased aromatic compounds (e.g., polycyclic aromatic hydrocarbons -PAHs), which were mostly emitted from anthropogenic sources. Therefore, higher aromaticity degrees were generally associated with larger contributions from anthropogenic sources, while there were smaller contributions from biological activities. However, in summer, correlations of HIX with FI (r = −0.207; p > 0.05) or and (r = −0.130; p > 0.05) were not significant, suggesting the different influencing factors of aromaticity and biological contribution during the period. For example, secondary formation and aging processes play an important role in the hot season due to the stronger radiation and higher temperature, which may result in increases in both HIX and BIX, although the influences on BIX are relatively small . A comparison of HIX as a function of FI and BIX for Tianjin aerosols, together with aerosol samples in the literature, is summarized in Fig. 2c and d, respectively. HIX values for Tianjin aerosols are mainly concentrated in the region where freshly emitted aerosols (Mladenov et al., 2011) and fresh SOA  are located, but they were much lower than HIX values for aged SOA  and aged dust aerosols experiencing long-range transport (Mladenov et al., 2011). BIX and FI values of aerosols in Tianjin were mainly located within the region where the primary aerosols from biomass burning, coal combustion, and vehicle emissions were concentrated (Tang et al., 2021). Therefore, the fluorescence indices together indicated water-soluble BrC in Tianjin prominently contained freshly emitted and less aged aerosol, especially in winter. However, since the influencing mechanisms of fluorescence properties of atmospheric organic compounds are extremely complicated and still unclear, further studies on fluorescence indices are needed .

Compositions of BrC identified by fluorescence analysis
To explore the possible sources of fluorophores in watersoluble BrC, correlations of fluorescent intensities with light absorption and chemical compositions of aerosols were examined. Generally, fluorescent intensities were strongly correlated with Abs 365 in both winter (r = 0.863; p < 0.01) and summer (r = 0.882; p < 0.01), suggesting that the sources and influencing mechanisms of light absorption and fluorescent properties were much similar (Fig. S5a). The strong correlations of fluorescent intensities with EC (r = 0.743-0.841; p < 0.01; Fig. S5b) and SOC (r = 0.484-0.820; p < 0.01; Fig. S5c) suggested that BrC fluorophores were from both the combustion-related and secondary formation processes. Note that fluorescent intensities even showed a stronger correlation with SOC than EC in winter, indicating that the dominant source of BrC fluorophores might be secondary formation rather than primary emissions from combustion in this season. Levoglucosan, the tracer of biomass burning (Simoneit, 2002), is also strongly correlated with fluorescent intensities (Fig. S5d), suggesting that biomass burning was an important source of BrC fluorophores. The contribution of biomass burning to fluorophores in aerosols has also been suggested by previous studies (Qin et al., 2018;Dey et al., 2021). Figure 3a presents typical EEM fluorescence spectra of water-soluble BrC in PM 2.5 samples in winter and summer in Tianjin, respectively. PARAFAC analysis on the basis of EEM spectra was conducted to provide more knowledge of the chemical composition and source of BrC. In total, five independent fluorophores in water-soluble BrC were identified by PARAFAC model with the total explained variance of 99.65 % within the whole sampling period (Fig. 3b). Figure 3c presents the emission and excitation spectra of each BrC fluorophore at the peak emission and excitation wavelengths. The fluorescent intensities of water-soluble BrC with relative abundances of each fluorophore varied for different samples (Fig. S6), suggesting that the chemical compositions of BrC were highly variable. The fluorophore C 1 presents a primary fluorescent peak at an excitation/emission (Ex/Em) of ∼ 250 nm/395 nm and a secondary peak at Ex/Em of ∼ 315 nm/395 nm. C 1 can be classified as a humic-like fluorophore because the bimodal distribution of fluorescence spectra is typically associated with humic-like substances (HULISs; Coble, 2007;Murphy et al., 2011;Yu et al., 2015). The second peak at the high excitation wavelength suggests there are plenty of condensed aromatic moi-eties, conjugated bonds, and nonlinear ring systems (Matos et al., 2015). The fluorophore C 2 exhibiting a peak at Ex/Em of ∼ 250 nm/465 nm is also a humic-like fluorophore. The longer wavelength of C 2 suggests that, compared with C 1 , C 2 is more aromatic with higher molecular weight, containing more conjugated and unsaturated chemical structures due to condensation reactions (Matos et al., 2015;Dey et al., 2021). C 3 , showing a peak at Ex/Em of ∼ 250 nm/385 nm, is also a humic-like fluorophore (X. J. Li et al., 2020a). Based on previous research, it is inferred that C 1 and C 3 both contain less oxygenated organic species, and C 1 is more oxidized than C 3 ; however, C 2 is associated with more oxygenated structures (Elcoroaristizabal et al., 2014;Chen et al., 2016).
Different from the humic-like fluorophores, C 4 and C 5 are identified as protein-like fluorophores due to their short emission wavelengths (Coble, 1996(Coble, , 2007. C 4 , showing a fluorescence peak at Ex/Em of ∼ 250 nm/340 nm, is often associated with tryptophan-like fluorophore (Murphy et al., 2011(Murphy et al., , 2013. C 5 , with a peak at Ex/Em of ∼ 275 nm/305 nm, is generally regarded as a typical tyrosine-like fluorophore (Stedmon and Markager, 2005;Murphy et al., 2011). The significant correlations between BIX and C 4 (r = 0.583; p < 0.01) or C 5 (r = 0.369; p < 0.01) may support the possible contributions of bioaerosols to the protein-like fluorophores ( Fig. S7a and b). It should be noted that, due to the similar fluorescence spectra, the two fluorophores are also probably related to some PAHs-like or phenol-like species from fossil fuel combustion and biomass burning, which is particularly so in the case of urban aerosols (Elcoroaristizabal et al., 2014;Matos et al., 2015;Chen et al., 2020). For example, to a certain extent, the spectrum of C 4 is overlapped with that of naphthalene, an aromatic compound from fossil fuel combustion (Mladenov et al., 2011;Wu et al., 2019). More evidence supporting the likely impacts of fossil fuel combustion activities on the two protein-like fluorophores in BrC is the strong correlations of low molecular weight n alkanes with both C 4 (r = 0.880; p < 0.01) and C 5 (r = 0.842; p < 0.01; Fig. S7c and d), since low molecular weight n alkanes were mainly derived from emissions of incomplete combustion of fossil fuels (Xie et al., 2009). Furthermore, C 5 produces spectra similar to the fluorophore, which may be related to non-nitrogen-containing species (Chen et al., 2016).
Correlation coefficients were further obtained between fluorescent intensities of each fluorophore and chemical compositions used to identify the potential sources of different fluorophores. During the sampling periods, EC showed significantly strong correlations with all the fluorophores, except C 5 in summer ( Fig. 4a1 and b), again providing support for the influence of primary emissions from combustionrelated sources on BrC fluorophores. Similarly, the relationships between levoglucosan and BrC fluorophores suggest that biomass burning contributed to the formation of all the humic-like and protein-like fluorophores, except C 5 in summer ( Fig. 4c and d). The correlation between C 5 and EC in summer was weak (r = 0.198; p < 0.01) and between C 5 and SOC was comparatively stronger (r = 0.326; p < 0.01), indicating that combustion processes were not the dominant sources of C 5 in summer, and secondary formation even played a more important role. The considerable impacts of secondary formation on BrC fluorophores were indicated by the significant correlations between SOC and all the fluorophores, especially in winter ( Fig. 4e and f). It is noted that C 2 presented the strongest correlation with SOC among the humic-like fluorophores, followed by C 1 and C 3 . This finding supported the hypothesis that C 2 is associated with more oxygenated structures, while C 3 is less oxidized than the less oxygenated component C 1 . Figure 5 illustrates the average relative contributions of the fluorophores for water-soluble BrC in different periods. On average, the humic-like fluorophores together contributed 73.4 % and 68.7 % to the fluorescence intensity in winter and summer, respectively, suggesting that humic-like fluorophores played a dominant role in fluorescence properties of water-soluble BrC in Tianjin. Generally, for winter samples, the less oxygenated fluorophores C 1 (27.5 %) and C 3 (24.4 %) both made considerable contributions, followed by the more oxygenated fluorophore C 2 (21.5 %). By contrast, in summer, the relative contribution made by the least oxidized fluorophore C 3 decreased remarkably to 8.6 %. Meanwhile, C 1 presented much more abundantly (35.8 %), and C 2 also increased slightly (24.3 %). The larger relative contributions of more oxygenated fluorophores in summer might partly be attributed to the reason that the less oxygenated fluorophores would be photodegraded through exposure to the strong summer solar radiation and then convert into more oxygenated fluorophores through the oxygenation reaction pathways. This can further support the results that BrC were more aged in summer than in winter, which were previously revealed by the fluorescent indices. In addition, this photoinduced mechanism can also explain the diurnal variations in relative abundances of humic-like fluorophores, which was characterized by a smaller contribution of the less oxygenated fluorophore C 3 and a larger contribution of the more oxygenated fluorophore C 2 in daytime than nighttime in both seasons. Protein-like fluorophores were also vital components for BrC fluorophores since, together, they accounted for 26.6 % and 31.3 % of the total fluorescence intensities in winter and summer, respectively (Fig. 5). One possible reason for the larger contribution of proteinlike fluorophores during summertime is the higher relative abundances of bioaerosols from fungal spores and plant debris due to the enhanced biological activities in summer, which can be supported by our previous research (Y. . C 4 , the fluorophore significantly influenced by combustion sources, made a much smaller contribution in summer (12.4 %) compared with winter (20.7 %). However, C 5 contributed 18.9 % in summer, an amount more than 3 times greater than in winter (5.9 %). This is not surprising, since C 5 had fluorescent spectra similar to that of a photochemically formed fluorophore . Therefore, the larger contribution of C 5 was likely due to the excessive oxidation and decomposition processes in summer, and this was particularly the case in daytime.

Sources of BrC
Relationships between BrC light absorption and carbonaceous species of aerosols were examined to investigate the sources of BrC in Tianjin (Fig. 6a-d). The temporal pattern of Abs 365 was quite similar to that of WSOC (Fig. S1a) and OC (Fig. S1b). The strongly positive correlations between  Abs 365 and WSOC (r = 0.837-0.947; p < 0.01; Fig. 6a) and OC (r = 0.851-0.956; p < 0.01; Fig. 6b) indicate that the sources of BrC were similar to those of WSOC and OC. Abs 365 also correlated well with EC (r = 0.695-0.789; p < 0.01; Fig. 6c), suggesting that the combustion-related processes were important sources of ambient BrC in both seasons, since EC is mainly from the incomplete combustion of biomass and fossil fuels. We have found that biomass burning was one of the most abundant sources of OC in Tianjin, especially in winter (Y. . Abs 365 was significantly correlated with levoglucosan (r = 0.498-0.665; p < 0.01), the typical organic molecular tracer of biomass burning, indicating that a considerable fraction of BrC aerosols was associated with biomass burning activities in both winter and summer (Fig. 6e). This is in accordance with previous findings that biomass burning is an important source of atmospheric BrC (Lack et al., 2012;Lin et al., 2016). Levoglucosan concentration in winter (252 ± 145 ng m −3 ) was more than 10 times larger than that in summer (23.6±34.4 ng m −3 ), suggesting the much larger contribution of biomass burning to winter OC and BrC (Table S1). The influences of biomass burning on BrC can also be supported by the strong linear correlations of Abs 365 with K + (r = 0.784-0.789; p < 0.01; Fig. 6f), since K + is another tracer of biomass burning. However, the relatively weaker correlation between Abs 365 and levoglucosan in winter in comparison with that in summer indicates that the relative contribution of biomass burning might be smaller in winter. It is not surprising because the combustion of fossil fuels, such as coal and petroleum, played a more important role in winter BrC formation due to the intense anthropogenic activities (e.g., heating) in the cold season. This can be supported by the much stronger linear correlations of Abs 365 with SO 2− 4 (r = 0.812; p < 0.01; Fig. 6g) and NO − 3 (r = 0.769; p < 0.01; Fig. 6h) in winter, since the precursors of NO − 3 (e.g., NO x ) and SO 2− 4 (e.g., SO 2 ) are mainly emitted from fossil fuel combustion. Such results coincide with previous studies, which found that fossil fuel combustion made great contributions to winter aerosols in Tianjin Gao et al., 2018).
Relationships between Abs 365 and molecular markers of organic aerosols from other specific emission sources were analyzed to investigate the potential sources of atmospheric BrC. Besides primary emissions from combustions, bioaerosols, which contain various particle types such as bacteria, algae, pollen, fungal spores, plant debris and biopolymers, are also important sources of BrC aerosols (Andreae and Gelencsér, 2006;Pöhlker et al., 2013). With the number and mass concentration in the size range, with diameters > 1 µm, bioaerosols make significant contributions to atmospheric aerosols (Fröhlich-Nowoisky et al., 2016). Although many bioaerosols are water insoluble, some bioaerosolrelated components (or biological markers) are water soluble and light absorbing (i.e., water-soluble BrC), such as some proteins and amino acids. For example, due to being emitted from biogenic sources or degraded from proteinaceous substances, atmospheric amino acids account for a large fraction of water-soluble organic nitrogen compounds in aerosols . Many sugar compounds are emitted persistently from biological sources and have been viewed as tracers of primary bioaerosols . For example, arabitol and mannitol are the major species in fungi and, therefore, used as the tracer for airborne fungal spores (Bauer et al., 2008). Glucose is predominantly derived from terrestrial vegetative fragments such as pollen, fruit, and debris (Pacini, 2000). Trehalose, a metabolite of many microorganisms, is also frequently recognized as fungal carbohydrates (Simoneit et al., 2004). Xylose, a monosaccharide, is the main component of hemicellulose in biomass and comes from different sources such as bacteria, vegetation, microbiota, and biomass burning . Therefore, the significant correlations of Abs 365 with arabitol (r = 0.419-0.494; p < 0.01; Fig. 6i), mannitol (r = 0.407-0.422; p < 0.01; Fig. 6j), glucose (r = 0.347-0.401; p < 0.01; Fig. 6k), trehalose (r = 0.306-0.489; p < 0.01; Fig. 6l), and xylose (r = 0.476-0.773; p < 0.01; Fig. 6m) suggest that bioaerosols also contributed to water-soluble BrC in Tianjin. The potential impacts of bioaerosols on water-soluble BrC can be supported by the PARAFAC-derived fluorescent results, as discussed in Sect. 3.4.
Moreover, Abs 365 and the estimated SOC showed similar variations with strong correlations in both summer (r = 0.693; p < 0.01) and winter (r = 0.881; p < 0.01; Figs. 6d and S1d), suggesting the significant impacts of secondary formation processes on BrC, even in the winter season. This is reasonable because SOA are also major contributors to BrC through photochemical reactions and/or aqueous/heterogeneous chemical processes Lin et al., 2015;Braman et al., 2020;Kasthuriarachchi et al., 2020). The correlation between Abs 365 and SOC in winter was even stronger than that between Abs 365 and EC, indicating the greater impacts of secondary formation on winter BrC compared with the primary emissions from combustion-related activities. The large contribution of secondary formation to wintertime BrC is also indicated by the strong correlations of BrC with SO 2− 4 and NO − 3 (Fig. 6g, h). To explore the relationships between BrC and SOA formed through different reaction pathways, correlations of Abs 365 with specific molecular markers of biogenic SOA tracers (e.g., C 5 alkene triols, 2-methyltetrols (MTLs), 2-methylglyceric acid (2-MGA), pinic acid, and 3-hydroxyglutaric acid (3-HGA)), as well as anthropogenic SOA tracers (e.g., 2,3-Dihydroxy-4oxopentanoic acid (DHOPA) and phthalic acids), were also examined.
The ubiquitous biogenic volatile organic compounds (BVOCs) are believed to contribute to the formation of atmospheric BrC by complex atmospheric processes (Bones et al., 2010;Updyke et al., 2012;Nguyen et al., 2013;Laskin et al., 2015). C 5 alkene triols and MTLs are the major SOA tracers due to isoprene photooxidation under low-NO x conditions, and 2-MGA is a further oxidation product of isoprene under high-NO x conditions. Pinic acid is the firstgeneration oxidation product of monoterpene, while 3-HGA is the higher-generation product (Kang et al., 2018;. Figure 6n-r demonstrate the significant correlations between Abs 365 and C 5 alkene triols (r = 0.395-0.469; p < 0.01), MTLs (r = 0.476; p < 0.01 in summer), 2-MGA (r = 0.342-0.514; p < 0.01), pinic acid (r = 0.231-0.421; p < 0.01), and 3-HGA (r = 0.388-0.415; p < 0.01). These weak-to-moderate correlation coefficients suggest that the biogenic SOA formation processes are potential sources of BrC in Tianjin, although their contributions might not be large. Since the contributions of biogenic SOA to OC are significantly elevated in summer due to the larger emissions of their precursors and strong photooxidation (Y. , biogenic SOA might be an important source of BrC in summer. DHOPA and phthalic acids are tracers for the anthropogenic SOA from toluene and naphthalene, respectively (Kleindienst et al., 2012;Fu et al., 2014). Figure 6st show that Abs 365 exhibited significantly strong relevancies with DHOPA (r = 0.472-0.638; p < 0.01) and phthalic acids (r = 0.400-0.742; p < 0.01), again confirming that anthropogenic SOA formation is also an important source for BrC in Tianjin. In addition, the much larger correlation coefficients in winter indicate the stronger influence of anthropogenic activities on secondary formation of winter BrC, in accordance with the results suggested by the stronger correlations of winter BrC with SO 2− 4 and NO − 3 . The potential sources of BrC in Tianjin with their relative contributions were further analyzed with the PMF model constrained by organic molecular markers. Figure 7 presents the profiles of the five factors, together with the temporal variations in contributions from individual factors. The first factor (F1) is mainly related to anthropogenic SOA formation processes, since it is characterized by the highest level of DHOPA, the tracer for SOA from anthropogenic aromatics. The second factor (F2), which is featured by the high abundances of glucose, trehalose, mannitol, and arabitol, is primarily derived from bioaerosol emissions. The third factor (F3), with the largest contributions of levoglucosan and its two isomers (i.e., galactosan and mannosan), is identified as the source of biomass burning, since galactosan and mannosan can also act as biomass burning tracers (Simoneit, 2002). The fourth factor (F4) shows the highest loadings of C 5 alkene triols, MTLs, 2-MGA, and pinic acid, and therefore, it can be identified as the source from biogenic SOA formation. The fifth factor (F5) had the largest abundances of OC, SO 2− 4 , NO − 3 , NH + 4 , K + , and Cl − . These components are mainly from primary emissions and subsequent aging processes of combustions of fossil fuel, such as coal and oil gas. Therefore, F5 is likely to associate with the anthropogenic emissions (i.e., fossil fuel combustion) and aging processes. The stronger effect of primary anthropogenic emissions on F5 can be supported by the significant correlation between F5 and EC concentration (r 2 = 0.50; p < 0.01). Mean relative contributions of various sources to BrC in Tianjin in different periods are plotted in Fig. 8. Obvious diurnal changes were found in source contributions of BrC. Bioaerosol emissions made a larger contribution to BrC at daytime than at nighttime, especially in summer, suggesting the influences of daytime biological activities on BrC formation. Biomass burning contributed more to BrC at night, which called for more attention to nighttime BrC formation due to biomass burning activities. In addition to the diurnal differences, remarkable seasonal changes in the sources of BrC also existed. In winter, biomass burning and anthropogenic emissions and aging were the predominant sources of BrC, with the contributions of 30.7 % and 30.0 %, respectively. The predominant contributions of biomass burning and fossil fuel combustion to winter BrC in Tianjin coincided with the source apportionment results of BrC in Xi'an in northwestern China (C. Yuan et al., 2020). Anthropogenic SOA formation and bioaerosol emission also made large contributions to BrC in winter, accounting for 21.1 % and 18.2 %, respectively. Biogenic SOA formation made a small contribution to winter BrC, which might be due to the weak emissions of BVOCs under low temperature.
However, in summer, biogenic SOA formation accounting for 23.7 % became a prominent source of BrC. Primary bioaerosol emission (38.1 %) was found to be the most important source of summertime BrC, which was led by the strong biological activities. Anthropogenic SOA formation also played an important role, although its relative contribution in summer (19.8 %) was slightly smaller than that in winter, suggesting the considerable significance of anthropogenic secondary BrC in both seasons. Compared to the significant influence in winter, anthropogenic emissions and aging processes in summer played a much minor role in BrC formation because the relative contribution dramatically de- creased to 15.3 %. Besides, biomass burning made a trivial contribution of 3.2 % to summer BrC, which contrasted sharply with the dominant contribution in winter. To sum up, the combustion-related primary emissions played a much more important role in BrC formation in winter, while secondary formation from photochemical and aqueous chemical processes contributed more to BrC in summer than in winter. Such source apportionment results again indicate that BrC in Tianjin was more affected by fresh emissions and was less aged in winter, while more aged in summer, in accordance with the fluorescent results. Since fresh biogenic SOA are generally not, or weakly, light absorbing, the larger contributions of biogenic SOA to WSOC would lower the MAE in summer (Table 1). In addition, the atmospheric aging and photobleaching processes during the formation of secondary BrC would also result in the lower summer MAE (Zhong and Jang, 2014;Liu et al., 2016).

Conclusions
This study presents the temporal variations in light absorption and fluorescent properties of water-soluble BrC in PM 2.5 over Tianjin in North China in winter and summer during 2016-2017. Sources of water-soluble BrC were comprehensively analyzed by investigating the relationships of BrC and the chemical compositions of aerosols. Results show that the light absorption properties of BrC experienced obvious seasonal variations. Abs 365 , AAE, MAE 365 , and k 365 of BrC were 6.8, 1.1, 1.8, and 1.8 times larger in win-ter than in summer, respectively, suggesting the much more abundant and stronger light absorption of water-soluble BrC in winter. However, there are no significant differences in BrC light absorption between daytime and nighttime. Watersoluble BrC contributed significantly to absorption radiative forcing, especially in the UV range, indicating their considerable influences on climate warming and ozone formation. Fluorescent indices present that BrC were associated with a slightly higher aromaticity degree and polycondensation in their chemical structures in summer and daytime, which likely resulted from photobleaching processes. In total, three humic-like components (C 1 , C 2 , and C 3 ) and two protein-like components (C 4 and C 5 ) were determined as being the major fluorescent organics by PARAFAC analysis. The humic-like components were predominant in both seasons, and their relative contributions were larger in winter than in summer. The less oxygenated humic-like components contributed more in winter and nighttime, while relative contributions of more oxygenated humic-like components obviously increased in summer and daytime, indicating that the less oxygenated fluorophores might be oxidized into more oxygenated fluorophores due to photodegradation. Combustion processes and secondary formation contributed remarkably to the humic-like and protein-like fluorescent organic aerosols.
Correlation analysis between BrC and chemical compositions of aerosols, and source apportionments by PMF analysis with the organic molecular tracers, suggested that sources contributions of BrC presented obvious seasonal and diurnal variations and fossil fuel combustion and aging processes, bioaerosol emission, and anthropogenic SOA formation were important sources of BrC in both winter and summer. Impacts of biomass burning in winter, and primary biological aerosol emission and biogenic secondary formation in summer on BrC were highlighted by the PMF results. Overall, source contributions and fluorescent properties together indicated that BrC were prominently affected by freshly emitted aerosols and less aged in winter, while they were more aged in summer. This study broadens our knowledge of the optical properties, sources, and evolution formation of BrC in the heavily polluted urban region in China, which will help us to estimate climatic effect of atmospheric aerosols and control carbonaceous aerosol pollution.
Author contributions. PF designed the study. JD, XW, SZ, and ZZ carried out the experiments and performed the data analysis. JD prepared the paper, with contributions from all co-authors.
Competing interests. At least one of the (co-)authors is a member of the editorial board of Atmospheric Chemistry and Physics. The peer-review process was guided by an independent editor, and the authors also have no other competing interests to declare.
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