A field campaign was carried out at the Dianshan Lake (DSL) Air Quality Monitoring Supersite (120.98° E, 31.09° N), Shanghai, China (Fig. S1 in the Supplement). The sampling site is ∼ 15 m above ground, and surrounded by farmland, vegetation, several villages, and Dianshan Lake. As a representative of the suburban environment, this site has been frequently selected as a reference site for the study of air pollution in the Yangtze River Delta region (Feng et al., 2023; Wu et al., 2023; Yang et al., 2022).

Table S1 summarizes the observed concentrations of VOCs. A gas chromatograph with mass spectrometry and flame ionization detection (hereinafter referred to as GC-MS/FID; TH-PKU 300B, Wuhan Tianhong Instrument Co. Ltd., China) was used to measure 56 Photochemical Assessment Monitoring Station (PAMS) compounds (including 29 alkanes, 10 alkenes, 16 aromatics, and acetylene) and 11 carbonyls (including 6 aldehydes and 5 ketones), a Kore proton transfer reaction time-of-flight mass spectrometry (KORE PTR 3C, KORE Technologies, UK) was used to measure formaldehyde and acetaldehyde, and a Vocus-2R PTR-TOF-MS (Vocus-PTR, Tofwerk AG and Aerodyne Research Inc., USA) was used to measure 57 NMHCs and 195 OVOCs without definitive identity assignments. In total, 321 VOCs (including 56 PAMS, 13 carbonyls, 57 unspecified NMHCs, and 195 unspecified OVOCs) were quantified in this campaign. In addition to VOC measurements, O₃, NO_x, temperature, and relative humidity were continuously monitored during the campaign. Details of the instruments and their operation have been described previously (Yang et al., 2022).

Additionally, ROH was measured using a comparative reactivity method (CRM) (Sinha et al., 2008; Fuchs et al., 2017) and calculated with measured inorganic and organic trace gas concentrations. In brief, pyrrole (C₄H₅N), used as a reference substance, was passed through a glass reactor and monitored by Vocus-PTR. OH radicals were then introduced to react with C₄H₅N, first in the presence of pure nitrogen gas and then in the presence of ambient air. Comparing the concentration of C₄H₅N exiting the reactor with and without the ambient air allows determination of the measured OH reactivity (Sinha et al., 2008).

The PAPM (De Gouw et al., 2005, 2018) assumes that the amount of each emitted OVOC is proportional to the amount of an inert tracer (e.g., acetylene (C₂H₂)), and that reactions with OH radicals and photolysis dominate the photochemical removal of OVOCs. In this method, ambient OVOC concentrations can be attributed to anthropogenic primary emissions (characterized by emission ratio ER_OVOC), anthropogenic secondary formation (characterized by emission ratio ER_precursor), biogenic sources (characterized by emission ratio ER_biogenic), and regional background, as expressed in Eq. (1): 1OVOC=EROVOC×C2H2×exp⁡-kOVOC∗-kC2H2OHΔta+ERprecursor×C2H2×kprecursorkOVOC∗-kprecursor×exp⁡-kprecursorOHΔta-exp⁡-kOVOC∗OHΔtaexp⁡-kC2H2OHΔta+ERbiogenic×isoprenesource+background where ER_OVOC and ER_precursor are the emission ratios of OVOC and their precursors relative to C₂H₂; kC2H2 and kprecursor are the OH rate coefficients of C₂H₂ and OVOC precursors, respectively; kOVOC∗ is the effective loss rate constant of OVOC representing the combined loss due to OH radicals and photolysis, for which the daytime photolysis of 13 carbonyls was considered in this study (Sect. S1 and Table S2); [C₂H₂] is the observed concentration of acetylene; ER_biogenic is the emission ratio of OVOCs from biogenic emissions to isoprene ([Isoprene]_source, calculated using Eq. 2), and [background] denotes the background level. OH exposure of anthropogenic VOCs ([OH]Δta) is calculated from a species ratio method using the observed ethylbenzene and m&p-xylene concentrations (Roberts et al., 1984).

Since OH radical reactions dominate VOC consumption during the daytime, only observations from 07:00 to 18:00 LT were used for the PAPM fitting, ensuring that the underlying assumption of OH-driven oxidation (Eq. 1) is satisfied. The source contributions of OVOCs were then determined by a least-squares fit, with the fitted emission ratios and background levels summarized in Tables S3 and S4.

The photochemical loss of VOCs is dominated by reactions with OH radicals during the daytime, and other removal paths, including deposition and reactions with nitrate radical (NO₃) or O₃, are regarded to be negligible. Thus, the initial concentration of NMHCs emitted from sources can be estimated by Eq. (2): 2NMHCi,jsource=NMHCi,jt×expkiOHΔtj where [NMHC_i,j]_source is the initial concentration of NMHC species i from the jth source; [NMHC_i,j]_t is the observed concentration of NMHCs species i from the jth source (including anthropogenic and biogenic sources); [OH]Δtj is the OH exposure of VOCs from the jth source, whose detailed descriptions are provided in Sects. S2 and S3; ki represents the first-order rate coefficient for the reaction of species i with OH radicals (Sect. S4 and Table S5). Unlike OVOCs, NMHCs are treated as directly emitted compounds with no secondary formation pathway. Among them, isoprene, monoterpenes (C₁₀H₁₆), and sesquiterpenes (C₁₅H₂₄) are classified as biogenic VOCs, whereas other measured NMHCs are categorized as anthropogenic VOCs.

Based on the source apportionment results (Sect. 3.1), the initial concentration of OVOCs can be estimated by Eq. (3). 3OVOCi,jsource=ERi,j×tracerjsource where ER_i,j is the emission ratios of the OVOC species i relative to the initial tracer concentration from the jth source ([tracer_j]_source, specifically [C₂H₂]_source for anthropogenic and [isoprene]_source for biogenic source).

The difference between measured ROH and calculated ROH, termed as missing ROH, is a parameter for assessing the reactivity of unmeasured or unrecognized compounds. 4MissingROH=MeasuredROH-∑ikiXi where [Xi] represents the observed concentration of inorganic or VOC species i. To explore the potential sources of missing ROH, we quantified the sources of missing ROH by a MLR method introduced by Wang et al. (2024). 5MissingROH=aC2H2+bisoprenesource+cOx+Cbackground where [O_x] is the observed concentrations of NO2+ O₃. a, b, and c are regression coefficients representing the sensitivities of missing ROH to the tracers of anthropogenic, biogenic and secondary sources, with fitted values of 0.39, 2.48 and 0.04 s⁻¹ ppb⁻¹, respectively. The intercept, C_background (2.27 s⁻¹), represents the baseline missing ROH that is independent of these three source categories.

Unmeasured VOCs, such as long-chain alkanes, diterpenes, and OVOCs with more than four oxygen atoms, mainly originate from anthropogenic sources, biogenic sources, and secondary generation, respectively. These compounds exhibit high reactivity toward OH radicals and are therefore expected to be important sources of missing ROH (Li et al., 2020; Wang et al., 2020; Wu et al., 2020). In addition to VOC species, other reactive gases such as hydrogen sulfide, HONO, and ammonia, etc., although not measured in this study, have been identified in previous studies as important contributors to total ROH (Anglada and Solé, 2017; Pai et al., 2021; Wine et al., 1981). Moreover, heterogeneous OH uptake on atmospheric aerosol surfaces represents another non-negligible sink of OH radicals (Zhang et al., 2020), which may further contribute to missing ROH. The background fraction of missing ROH exhibited no correlation with [C₂H₂], [isoprene]_source, or [O_x], hinting that it could not be attributed to the three sources represented by these tracers. We therefore attributed the background fraction of missing ROH to unmeasured inorganic reactive gases or unaccounted heterogeneous processes, and its OFP contribution was not considered in subsequent calculations. Missing ROH associated with anthropogenic, biogenic, and secondary sources was attributed to unmeasured VOCs from the corresponding source. Given that unmeasured VOCs are likely a complex mixture of diverse chemical species, we scaled the concentrations of the 191 measured species with available MIR values (Table S5) from the corresponding source to compensate for missing ROH, as shown in Eq. (6): 6unmeasuredVOCi,jt=VOCi,jt×missingROH,jROH,j where [unmeasured VOCs_i,j]_t denotes the ambient concentrations of unmeasured VOC_i originating from the jth source, [VOCs_i,j]_t represents the concentrations of measured VOCs from the jth source, missing ROH,j and ROH,j represent the OH reactivity of unmeasured and measured VOCs from the jth source, respectively.

Based on the equivalent concentrations derived from Eq. (6), the initial concentrations of unmeasured VOCs, [unmeasured VOCs_i,j]_source, were estimated following the same approach as that for measured species in Sect. 2.3. Note that unmeasured VOCs attributed to secondary formation were excluded from this calculation, as secondary OVOCs are produced during atmospheric transport rather than emitted at the source. Accordingly, the initial unmeasured anthropogenic and biogenic VOCs were determined using Eq. (7), with the same source-specific OH exposures and corresponding OH rate constants as those used for measured species. 7unmeasuredVOCi,jsource=unmeasuredVOCi,jt×exp⁡kiOHΔtj Eq. (7) follows the same formulation as Eq. (2), but is specifically applied to unmeasured VOCs using their inferred concentrations rather than directly measured values.

The MIR method was applied to calculate the OFP of individual VOC species (OFP_i) to evaluate their respective contributions to O₃ generation. 8OFPi=VOCi×MIRi where [VOC_i] is the concentration of a species i and MIR_i is the maximum incremental reactivity coefficient for an individual species i, as reported by Carter (2010). Note that MIR values are unavailable for many VOCs, particularly those detected by Vocus-PTR without structural information. To enable OFP estimation, MIR values for these species were assigned as follow: (1) If the molecular formula corresponds to a unique compound without isomers, the reported MIR value of that compound was directly assigned; (2) If the molecular formula matched multiple isomers, the minimum MIR value among multiple isomers was conservatively adopted; (3) Nevertheless, 130 OVOCs (Table S5), accounting for 7.8 % of the total observed VOC concentration, still lacked MIR values. Including them without MIR values would require additional assumptions that would introduce unquantifiable uncertainties; therefore, to ensure the robustness of the results, these species were excluded from both the OFP calculations and the estimation of unmeasured VOCs. Thus, we estimated the OFP of unmeasured VOCs with the equivalent concentrations and corresponding MIR coefficients of the 191 measured species with available MIR values. The MIR coefficients used for the OFP estimation are summarized in Table S5.

These assignment strategies and the inference of unmeasured VOCs inevitably introduce uncertainties into the OFP calculations. A detailed discussion on the uncertainties associated with VOC measurements, ki and MIR assignments, and assumptions with unmeasured species is provided in Sect. S5, together with their impacts on the OFP estimation. Additionally, it should be noted that MIR-based OFP represents a simplified reactivity metric under idealized conditions and does not explicitly account for region-specific chemical regimes. The OFP values reported in this study should therefore be interpreted as relative indicators of precursor reactivities, rather than direct representations of O₃ production under ambient conditions.

During the daytime (07:00–18:00 LT), the mean temperature and relative humidity were 28.7 °C and 75.8 %, respectively. Ambient O₃ concentrations ranged from 24.0 to 324.0 µg m⁻³ (mean ± one standard deviation: 127.1 ± 58.4 µg m⁻³), and NO_x averaged 14.0 ± 6.3 ppbv, indicating conditions favorable for photochemical oxidation of VOCs. Consistent with this chemical environment, the daytime measured total ROH averaged 39.9 ± 20.9 s⁻¹ (Yang et al., 2022), comparable to values reported at other suburban Chinese sites with substantial biogenic and photochemical influence. For example, Yang et al. (2017) reported total ROH of ∼ 30–40 s⁻¹ at the suburban Heshan site in the Pearl River Delta during summer. During our campaign, the OH exposure of anthropogenic VOCs, derived from the ethylbenzene / m&p-xylene ratio method (Roberts et al., 1984), was estimated to be 3.2 ± 3.2×1010 molecules cm⁻³ s, corresponding to a photochemical age of approximately 4.4 h, assuming a mean daytime OH concentration of ∼ 2.0×106 molecules cm⁻³. For biogenic VOCs, the OH exposure estimated using a sequential reaction model (Stroud et al., 2001) was 7.9 ± 5.1×109 molecules cm⁻³ s, equivalent to a photochemical age of 1.1 h. Overall, the air masses sampled at DSL site on average underwent 1–4 h of integrated photochemical processing prior to arrival; therefore, the observed OVOCs are expected to reflect contributions from both primary emissions and substantial secondary production.

Using the parametric method incorporating photochemical age, we quantified contributions of anthropogenic primary emissions, anthropogenic secondary formation, biogenic sources, and regional background during the daytime for 8 aldehydes, 5 ketones, and 195 unspecified OVOCs. The fitted results from Eq. (1), with the fitted parameters summarized in Tables S3 and S4, show good agreement with observed concentrations (R=0.40–0.90) and reconstruct the time series well, as illustrated for formaldehyde, acetaldehyde, and acetone in Fig. 1.

Ambient aldehydes, as shown in Fig. S2a, were predominantly of anthropogenic sources, with a large fraction of anthropogenic secondary formation (36.5 %) and anthropogenic primary emissions (33.1 %). Biogenic sources (24.7 %) also played a notable role, whereas the regional background was minor (5.6 %). Specifically, anthropogenic secondary formation was dominant for several major aldehydes, including formaldehyde (37.5 %), acetaldehyde (36.0 %), and propanal (34.6 %). In contrast, biogenic sources were dominant for methacrolein (81.8 %), pentanal (39.7 %), hexanal (67.2 %), butanal (52.1 %), and acrolein (48.7 %).

Ketones exhibited a higher regional background contribution (9.2 %) compared to aldehydes (Fig. S2b). Biogenic sources represented the dominant source of ketones (47.1 %), with particularly high contributions of methyl vinyl ketone (69.0 %), 2-pentanone (64.3 %), 2-butanone (50.7 %), and acetone (45.3 %). Anthropogenic secondary formation (24.9 %) and anthropogenic primary emissions (18.9 %) were also important contributors. Collectively, our results underscore a substantial contribution of photochemically derived carbonyls from anthropogenic VOC precursors during daytime at the DSL site.

For unspecified OVOCs measured by Vocus-PTR, as shown in Fig. S2c, anthropogenic primary emissions accounted for the largest fraction (36.9 %), followed by anthropogenic secondary formation (21.2 %), biogenic sources (34.2 %), and a low regional background level (7.7 %). Specifically, C_nH_2nO₂ (n=2–8) were predominantly attributed to primary anthropogenic sources (34.7 %–84.4 %). These compounds are likely alkanoic acids, which have been previously linked to emissions from traffic and agricultural activities (Mattila et al., 2018). Similarly, compounds such as C₆H₁₄O₂, C₉H₁₀O, C₂H₃NO₂, C₃H₇NO, C₅H₉NO, and C₆H₅NO₃ were also mainly associated with anthropogenic primary emissions (> 50 %). These species are likely solvents and amides, with potential sources including industrial processes, volatile chemical products, and wildfire, as reported by previous studies (Salvador et al., 2025; Zhang et al., 2024). OVOCs with more than or equal to three oxygen atoms (e.g., C₂H₄O₃, C₄H₄O₃, C₄H₂O₄, C₅H₆O₃, C₄H₄O₄, and C₅H₄O₄) were likely formed via multi-generation oxidation reactions of anthropogenic VOCs, with over 60 % attributed to anthropogenic secondary formation. Biogenic sources were dominant sources of C_nH_2nO (n=9–14), C₈H₈O₂, C₉H₆O₂, C₈H₆O₃, C₁₀H₁₄O₂, and C₁₀H₂₀O₂, accounting for 45.0 %–74.2 %. These species likely represent carbonyls, fatty acid derivatives, and phenylpropanoids, commonly identified as primary biogenic OVOCs (Ma et al., 2022a; Wang et al., 2024a). In addition, several compounds such as C₆H₈O, C₆H₈O₃, C₈H₁₀O₃, C₈H₆O₄, C₉H₁₄O₂, C₉H₁₀O₃, C₉H₈O₄, C₁₀H₈O₃, C₁₂H₁₈O, and C₁₃H₁₂O₂ also exhibited substantial contributions from biogenic sources, ranging from 44.8 % to 77.7 %. These OVOCs have been identified as dominant products of terpene oxidation in laboratory simulations, and frequently observed in forest environments (Calogirou et al., 1999; Li et al., 2020; Vermeuel et al., 2023).

Unlike OVOCs, 113 NMHCs, including 29 alkanes, 9 alkenes, 16 aromatics, 1 alkyne, 3 terpenes, and 55 unspecified ones, are considered directly emitted since there is no secondary formation for NMHCs. Among them, isoprene, C₁₀H₁₆, and C₁₅H₂₄ are classified as biogenic VOCs, whereas the other 110 NMHCs are categorized as anthropogenic VOCs. It should be noted, however, that terpenoids may also be emitted from anthropogenic activities, such as vehicular exhaust and the usage of volatile chemical products (Borbon et al., 2001; Gu et al., 2024; Xie et al., 2025). Moreover, certain benzenoid compounds have been reported to be emitted from biogenic sources as well (Ma et al., 2022a; Misztal et al., 2015; Wang et al., 2024a; Wohl et al., 2023). Nevertheless, the impact of these cross-sources was generally considered to be minor (Ma et al., 2022a; Seltzer et al., 2021).

In addition to the detected VOCs, numerous other VOCs are present in the ambient air but were not measured during this campaign. Those unmeasured VOCs led to a gap between the measured and calculated ROH, i.e., missing ROH. To explore the potential sources of missing ROH at the DSL site, we quantified its sources by applying an MLR method. The fitted and calculated missing ROH were in good agreement (R=0.63, Fig. S3). The estimated missing ROH is approximately 6.8 ± 4.4 s⁻¹ during the daytime. Biogenic sources accounted for the largest fraction (2.3 ± 1.7 s⁻¹, 34.3 %), followed by background (2.1 s⁻¹, 30.9 %) and secondary sources (2.1 ± 1.3 s⁻¹, 30.5 %). In contrast, anthropogenic sources played a minor role in missing ROH (0.3 ± 0.2 s⁻¹, 4.2 %). These results are consistent with previous suggestions that missing ROH was mainly from biogenic sources or photochemical production processes (Di Carlo et al., 2004; Yang et al., 2017). To quantify the OFP of unmeasured VOCs, the missing ROH attributed to anthropogenic, biogenic, and secondary sources was converted into equivalent concentrations of measured VOCs from corresponding sources using Eq. (6). The background fraction of missing ROH was not converted, as it was attributed to undetected reactive inorganic gases or unaccounted heterogeneous reactions rather than unmeasured VOCs. Our results showed that unmeasured VOCs were dominated by secondary OVOCs (4.1 ± 2.6 ppbv, 43.8 %) during daytime, followed by biogenic VOCs (3.7 ± 2.5 ppbv, 40.1 %) and anthropogenic VOCs (1.5 ± 1.0 ppbv, 16.0 %).

Based on the above calculation, as shown in Fig. 2a, the daytime average concentration of total VOCs (TVOCs, including measured and unmeasured VOC species) at the observation site was estimated to be 58.4 ± 24.2 ppbv. Among them, measured species were 49.1 ± 21.3 ppbv. Measured OVOCs were the dominant group (52.4 %), with unspecified OVOCs comprising the largest fraction (26.4 %), followed by aldehydes (17.2 %) and ketones (8.8 %). Measured NMHCs contributed 31.7 % of TVOCs, with alkanes as the major fraction (17.7 %), followed by unspecified NMHCs (4.0 %), alkenes (3.2 %), aromatics (3.2 %), terpenes (2.4 %), and alkynes (1.3 %). In addition, the daytime average concentration of unmeasured VOCs at the observation site was estimated to be equivalent to 9.3 ± 5.2 ppbv of measured VOCs, which contributed approximately 15.9 % of TVOCs.

Source apportionment reveals that anthropogenic primary sources were the largest contributors to TVOCs at the observation site (48.9 %), followed by biogenic sources (26.2 %), anthropogenic secondary formation (21.1 %), and regional background (3.8 %). This distribution reflects a substantial anthropogenic influence, consistent with nearby urban and traffic emissions at the DSL site, although contributions from biogenic sources were also evident.

After deducting secondary formation contributions and accounting for photochemical aging, the initial concentration of individual measured VOCs was estimated (Table S5). In addition, the initial concentration of unmeasured VOCs was estimated using Eq. (7) based on the equivalent observed concentrations of measured VOCs. As shown in Fig. 2b, the estimated daytime average initial concentration of TVOCs was 47.7 ± 22.6 ppbv. Among these, measured species were 41.7 ± 19.8 ppbv. In contrast to the distribution at the observation site, NMHCs (22.3 ± 18.4 ppbv, 46.6 %) constituted the largest fraction of the initial TVOCs, rather than OVOCs (19.5 ± 9.8 ppbv, 40.8 %). Based on Eq. (7), the initial concentration of unmeasured VOCs was estimated to be 6.0 ± 3.6 ppbv, accounting for 12.6 % of initial TVOCs.

Anthropogenic and biogenic source emissions contributed 71.5 % and 28.5 % of initial TVOCs, respectively. A notable feature of these emissions is the substantial presence of OVOCs in primary sources. Anthropogenic OVOCs alone contributed 24.1 % of the initial TVOCs, indicating that a considerable fraction of oxygenated compounds originated directly from anthropogenic activities. Biogenic emissions also contained a large proportion of OVOCs, representing more than half of the total biogenic VOCs. These findings are consistent with bottom-up emission inventories (Gu et al., 2021; Ou et al., 2015; Salvador et al., 2025; Yan et al., 2024), as well as direct source measurements (Li et al., 2024a; Sekimoto et al., 2023; Seltzer et al., 2021; Wang et al., 2024a), which have reported significant primary OVOC emissions from solvents, industrial activities, volatile chemical products, and plant emissions. Concentrations of primarily emitted OVOCs were comparable to those of NMHCs. However, previous studies mainly focused on NMHCs and neglected the role of primarily emitted OVOCs (Ma et al., 2022b).

Comparison between initial and observed VOCs reveals a substantial compositional change during atmospheric transport. The concentration of TVOCs at the observation site was 10.6 ppbv (22.3 %) higher than the initial TVOCs. However, NMHC concentrations were underestimated by 16.8 %. Species with the largest discrepancies were alkenes and aromatics: the average initial concentrations of alkenes and aromatics were 3.1 ± 1.7 and 2.5 ± 1.8 ppbv, respectively, significantly exceeding their respective measured concentrations of 1.8 and 1.9 ppbv at the observation site. This discrepancy can be primarily attributed to the high reactivity of these compounds and thus their rapid photochemical degradation during atmospheric transport. OVOC concentrations, if inferred from observation, were overestimated by 57.1 %. For instance, unspecified OVOCs increased from 10.2 ± 5.1 ppbv at the real emission to 15.4 ± 12.2 ppbv at the observation site, reflecting substantial secondary production during transport.

Photochemical aging also altered different sources' contributions to VOCs significantly. Anthropogenic and biogenic sources emitted 71.5 % and 28.5 % of TVOCs, respectively. However, anthropogenic primary VOCs only accounted for 48.9 % of TVOCs when transported to the observation site. Photochemically degradable VOCs were converted into OVOCs, with these secondary products accounting for 21.1 % of TVOCs at the observation site, explaining the increase of OVOCs from the real emission to ambient measurements.

To identify key O₃ precursors, we further calculated the OFP of individual VOCs using the MIR method (Table S5). As shown in Fig. 3, the total OFP (TOFP) of TVOCs at the emission site was 432.0 ± 319.2 µg m⁻³. Measured NMHCs contributed the largest fraction (52.3 %), led by aromatics (12.6 %), terpenes (12.6 %), alkenes (12.5 %), unspecified NMHCs (7.7 %), alkanes (6.6 %), and alkynes (0.2 %). These results differed remarkably from those based on the observed concentrations, i.e., the OFP of measured NMHCs was smaller by 31.7 % due to photochemical degradation. For instance, the OFP of initial alkenes was 54.1 ± 29.6 µg m⁻³, but would be underestimated by 44.7 % (30.0 ± 16.4 µg m⁻³) if photochemical losses were not considered.

OVOCs are often regarded as secondary oxidation products and overlooked as primary O₃ precursors. However, our results demonstrate that directly emitted OVOCs accounted for 33.2 % of initial TOFP, primarily from aldehydes (22.2 %) and unspecified OVOCs (9.4 %), whereas ketones contributed only 1.6 %. It should be noted that the actual contribution of OVOCs was likely larger, as many OVOCs (with a total initial concentration of 3.2 ppbv, accounting for 6.7 % of the initial TVOCs) were excluded from the OFP calculation because their MIR coefficients were unavailable. These findings show that primary OVOCs have an O₃ formation impact comparable to or exceeding that of many NMHCs. On the other hand, when estimated directly from the observed concentrations, the OFP of OVOCs, as inferred from Fig. 3, was overestimated by 42.6 % (observed OVOCs: 204.6 µg m⁻³, i.e., 42.9 % × 476.9 µg m⁻³; reconstructed primary emitted OVOCs: 143.4 µg m⁻³, i.e., 33.2 % × 432.0 µg m⁻³), which is a bias largely attributable to secondary production. This explains why, despite an underestimation of NMHCs' OFP, TOFP calculated from the observed TVOCs' concentrations, i.e., 476.9 µg m⁻³ (Fig. 3a), was still 10.4 % higher than that (432.0 µg m⁻³) derived from the reconstructed initial concentrations (Fig. 3b). These numbers highlight systematic biases introduced by photochemical aging and underscore the necessity of reconstructing initial VOC emissions for accurate OFP assessments.

The contributions of unmeasured VOCs to TOFP were also considerable. The OFP of initial unmeasured VOCs was 62.8 ± 37.6 µg m⁻³, representing 14.5 % of initial TOFP, mainly contributed by unmeasured biogenic VOCs (46.5 ± 30.2 µg m⁻³, 10.8 %), followed by unmeasured anthropogenic VOCs (16.3 ± 12.0 µg m⁻³, 3.8 %). Although their exact identities remain to be elucidated, unmeasured VOCs' substantial OFP demonstrates that they are a non-negligible fraction of the O₃ precursors. Ignoring unmeasured VOCs would underestimate VOC's contributions to O₃ pollution.

In terms of individual VOCs at the emission site, formaldehyde was the largest single contributor to TOFP (13.4 %), consistent with emission inventory findings in Beijing and Guangzhou, China (Huang et al., 2021; Wang et al., 2023). Isoprene ranked second (8.1 %), which is emitted primarily from biogenic sources with a high photochemical reactivity. Acetaldehyde was the third contributor (6.9 %), largely driven by its relatively high concentrations (2.3 ± 1.4 ppbv). Other key VOCs with high OFP included propylene, m&p-xylene, monoterpenes, ethylene, toluene, n-hexane, and o-xylene, each accounting for more than 1.5 % of TOFP (Fig. 4). The relative importance of these species differed notably from what is based on the observed concentrations (Fig. S4), particularly for propylene and n-hexane, which ranked the fourth and the tenth, respectively, based on their initial concentrations, but decreased to the seventh and the fifteenth when ranked by observed concentrations. This indicates that evaluations without considering initial concentrations could miss key O₃ precursors.

The top-ten reconstructed primary emitted VOCs collectively accounted for 55.3 % of the initial TOFP, despite representing only 31.2 % of initial TVOCs, highlighting that high OFPs did not necessarily correlate with high concentrations. For instance, C₂H₄O₂ (likely acetic acid), acetone, and ethane together comprised 12.1 % of initial TVOCs but contributed only 1.2 % to TOFP. Among the top ten contributors, eight species were primarily emitted from anthropogenic sources, reinforcing the dominant role of anthropogenic activities in O₃ formation in the suburban area of Shanghai.

Anthropogenic emissions, including both measured and unmeasured species, have the potential to form about 274.4 ± 128.6 µg m⁻³ of O₃, accounting for 63.5 % of TOFP. Initial anthropogenic NMHCs were the dominant contributors (39.7 %) to TOFP, followed by anthropogenic OVOCs (20.1 %), whereas unmeasured anthropogenic VOCs also represented a non-negligible fraction (3.8 %). Formaldehyde, propylene, and acetaldehyde were the top three contributors among anthropogenic VOCs, which cumulatively contributed 20.1 % of TOFP, even though they accounted for only 12.4 % of initial TVOC concentrations. Initial biogenic VOCs had the potential to form about 157.5 ± 111.9 µg m⁻³ of O₃ (36.5 % of TOFP), with biogenic OVOCs, terpenes, and unmeasured biogenic species contributing 13.1 %, 12.6 %, and 10.8 % to TOFP, respectively. Isoprene, monoterpenes, and formaldehyde were the dominant biogenic contributors, with contributions of 8.1 %, 4.3 %, and 4.4 %, respectively, mainly attributed to their abundant initial concentrations combined with their high MIRs.

Our results are qualitatively consistent with, yet quantitatively and conceptually distinct from, those of Zheng and Xie (2025), who compared reconstructed primary emitted versus ambient VOC concentrations at three sites in the Sichuan Basin. Both studies found that NMHCs, particularly alkenes and aromatics, were underestimated in OFP estimation when using observed rather than primary emitted concentrations, while OVOCs' OFP were overestimated. A quantitative comparison of the observed and reconstructed initial OFP estimates between the two studies is summarized in Table 1. Specifically, Zheng and Xie (2025) found that OVOCs' OFP in Chengdu decreased from ∼ 75.0 to ∼ 50.0 µg m⁻³ when emitted rather than ambient concentrations were used (∼ 50.0 % overestimation), consistent with the 42.6 % overestimation identified here; conversely, the OFP of reactive NMHCs increased, mirroring the 31.7 % underestimation for NMHCs at the DSL site. For individual species, isoprene, acetaldehyde, propylene, m&p-xylene, ethylene, toluene, and o-xylene were consistently identified as key O₃ precursors, reinforcing their priority status in O₃ control strategies. Notably, a key distinction is that our study covers a far broader range of VOC species, encompassing 321 measured VOC species (113 NMHCs and 208 OVOCs), together with ROH inferred unmeasured species, compared to the 99 species (86 NMHCs and 13 OVOCs) analyzed by Zheng and Xie (2025). This broader coverage enables us to attribute 33.2 % and 14.5 % of initial TOFP to primary emitted OVOCs and unmeasured species. The two studies are thus complementary rather than hierarchical: Zheng and Xie (2025) additionally resolved nighttime NO3/O₃-driven alkene loss, whereas our reconstruction focuses on the daytime OH-dominated window to characterize a broader range of oxygenated and unmeasured species.