Seasonal variation in nitryl chloride and its relation to gas-phase precursors during the JULIAC campaign in Germany

. Ambient measurements of nitryl chloride (ClNO 2 ) were performed at a rural site in Germany, cov-ering three periods in winter, summer, and autumn 2019, as part of the JULIAC campaign (Jülich Atmospheric Chemistry Project) that aimed to understand the photochemical processes in air masses typical of midwestern Europe. Measurements were


Introduction
Nitryl chloride (ClNO 2 ) is an important nocturnal reservoir for nitrogen oxides  because it accumulates during the night and photolyzes to nitrogen dioxide (NO 2 ) and a chlorine atom (Cl) after sunrise in the morning (Reaction R1).
At night, nitrate radicals (NO 3 ) are produced by the reaction of NO 2 with O 3 (Reaction R2), which then reacts with another NO 2 to form N 2 O 5 (Reaction R3a). N 2 O 5 decomposes thermally back to NO 2 and NO 3 (Reaction R3b). The forward and back reactions constitute a fast thermal equilibrium between NO 3 and N 2 O 5 that is established quickly at temperatures typically found in the lower troposphere . Uptake of N 2 O 5 on aqueous aerosol produces ClNO 2 when the particulate phase of the aerosol contains dissolved chloride. The yield (ϕ) of ClNO 2 is a complex function of various parameters such as temperature, aerosol water content, and chemical composition of the aerosol that influences both the uptake of N 2 O 5 into the particles (McDuffie et al., 2018a) and the subsequent aqueousphase chemistry leading to the formation of ClNO 2 (Mc-Duffie et al., 2018a). The uptake of N 2 O 5 (Reaction R4) and the reaction of NO 3 with VOCs (Reaction R5) constitute an overall loss term for the sum of NO 3 and N 2 O 5 because of the fast equilibrium between NO 3 and N 2 O 5. HNO 3 formation by Reaction (R4) is an important atmospheric sink for atmospheric nitrogen oxides in the lower atmosphere because HNO 3 photolysis is slow, so most of the produced HNO 3 does not reform NO 2 but is removed from the atmosphere by deposition . During the daytime, NO 3 is destroyed by photolysis or by reaction with nitric oxide (NO). The thermal equilibrium between NO 3 and N 2 O 5 thus leads to a rapid depletion of N 2 O 5 during the day. Therefore, significant concentrations of N 2 O 5 (the precursor of ClNO 2 ) are usually only present at night. Previous studies reporting on ClNO 2 measurements in North America (Osthoff et al., 2008;Thornton et al., 2010;Mielke et al., 2011;Wagner et al., 2012;Young et al., 2012;Mielke et al., 2013;Riedel et al., 2013;McDuffie et al., 2018b;McNamara et al., 2020), Asia Wang et al., 2016;Liu et al., 2017;Le Breton et al., 2018;Yun et al., 2018;Zhou et al., 2018;Yan et al., 2019;Jeong et al., 2019;Lou et al., 2022), and Europe (Phillips et al., 2012;Bannan et al., 2015;Priestley et al., 2018;Sommariva et al., 2018) have shown that ClNO 2 is present in various environments, even at a distance from the coast, indicating that sources of chloride other than sea spray contribute to the availability of chlorine for the formation of ClNO 2 . Observed mixing ratios of ClNO 2 in the atmosphere range from a few hundred parts per trillion by volume (pptv) to several ppbv, exhibiting significant spatial and temporal variations.
Despite the large variation in ClNO 2 concentrations and its potentially important contribution to photochemistry, systematic investigations of seasonal differences in ClNO 2 concentrations are sparse because ClNO 2 is not regularly measured at monitoring stations but rather during intensive field campaigns which typically only last a few weeks. Sommariva et al. (2018) reported ClNO 2 measurements at three different locations in the United Kingdom in all four seasons and showed a clear seasonal variation with maximum concentrations in spring and winter. Another study by Mielke et al. (2016), reporting on the seasonal behavior of ClNO 2 in Calgary, Canada, also showed maximum mixing ratios of ClNO 2 of up to 330 pptv in winter and spring.
The large variability in ClNO 2 concentrations in the atmosphere is due to the complexity of its formation mechanism (Reactions R2-R5) and the variability in its precursor concentrations. Assuming a steady state for the sum of NO 3 and N 2 O 5 concentrations, the following relationship holds: where k NO 3 represents the pseudo first-order rate constant for NO 3 loss mainly dominated by reactions with atmospheric VOCs (Reaction R5) at night with no fresh NO emissions. Considering the thermal equilibrium between NO 3 and N 2 O 5 , the [NO 3 ] can be replaced by [N 2 O 5 ]/(K eq (T )[NO 2 ]), where K eq (T ) is temperature dependent and equals to the ratio of the reaction rate constants of the thermal equilibrium, i.e., k 3a to k 3b (Reactions R3a and R3b). Equation (1) can be solved for the following: The production rate of ClNO 2 is then A production efficiency ε for ClNO 2 can be defined from this relationship as follows: It represents the formation rate of ClNO 2 from the aerosol per NO 3 produced by the reaction of NO 2 with O 3 in the gas phase. Equations (3) and (4) describe the expected influences on the ClNO 2 formation by its precursors NO 2 and O 3 , by temperature and NO 2 controlling the equilibrium between NO 3 and N 2 O 5 , and by the competing loss reactions of NO 3 and N 2 O 5 via Reactions (R5) and (R4), respectively. ϕ is an additional variable depending on the properties of the aerosol and specifically on its chloride content, as mentioned above. This study presents ClNO 2 measurements performed during the Jülich Atmospheric Chemistry Project (JULIAC) campaign in three seasons (i.e., winter, summer, and autumn 2019). The JULIAC campaign aimed to investigate the seasonal and diurnal variations in the atmospheric oxidation capacity at a rural site that is typical of midwestern Europe. To minimize the impact of the emissions from local sources, the air was drawn from 50 m aboveground, to ensure that the air is sampled from above the surface layer during the night, and flowed through the large environmental chamber, SAPHIR, at Forschungszentrum Jülich, Germany. In this work, the seasonal variation in ClNO 2 concentrations and its formation are investigated. As mentioned above, previous studies have demonstrated that ClNO 2 concentrations show significant seasonal variations (Mielke et al., 2016;Sommariva et al., 2018). However, intensive seasonal measurements in central Europe, to our knowledge, have not been performed so far. Given the ubiquitous nature of ClNO 2 and its importance in the enhancement of atmospheric oxidation processes, more detailed studies are needed to broaden our knowledge of atmospheric ClNO 2 levels, its seasonal behavior, and its distribution in environments with different chemical conditions. In addition, this work presents empirical production efficiencies of ClNO 2 determined from the nighttime measurements of ClNO 2 , NO 2 , and O 3 which are analyzed for their seasonal variations and the origin of air masses. This is a prerequisite for understanding the contribution of ClNO 2 to radical photochemistry under the chemical and meteorological conditions encountered in this campaign. Finally, a chemical box model is used here to understand the dependence of ClNO 2 formation and production efficiency on the observed nocturnal O 3 and NO 2 concentrations. The measurements and analysis presented in this paper help to illustrate the seasonal variability in ClNO 2 concentrations and shed light on the factors that control its production in different seasons.

The JULIAC campaign
The JULIAC campaign was conducted in 2019 in the atmospheric simulation chamber SAPHIR on the campus of Forschungszentrum Jülich, which is located at a rural site in Germany (50.91 • N, 6.40 • E). The SAPHIR chamber consists of a double-wall Teflon film (volume of 277 ± 3 m 3 ; Bohn et al., 2005;Rohrer et al., 2005). Its high volume to surface ratio (1 m 2 m −3 ) minimizes air-surface interactions within the chamber. The timescale of mixing is about 1 min and is ensured by two fans that are operated inside the chamber.
During this study, ambient air was drawn from 50 m height aboveground into the chamber (Fig. S1 in the Supplement). At this height, the air is expected to be decoupled from the surface layer during the night, so that the air composition is not directly impacted by sources at the ground or from the deposition of trace gases to the Earth's surface (Sect. 3.3). The inlet line (SilcoNert ® -coated stainless steel with an inner diameter of 104 mm) was mounted at a tower (JULIAC tower) next to the chamber. A fast flow rate of 660 m 3 h −1 resulted in a residence time of the air inside the inlet line of approximately 4 s. The short residence time and the inertness of the SilcoNert ® coating of the inlet line minimized loss and chemical changes in the air before entering the SAPHIR chamber. The potential loss of trace gases in the inlet line was tested for O 3 , NO, NO 2 , and CO and was found to be less than 5 %.
Instruments could either sample air directly from the inlet line or the chamber volume. In the latter case, part of the total air drawn through the inlet at the JULIAC tower flowed through the SAPHIR chamber with a flow rate of 250 m 3 h −1 that was controlled by a three-way valve right upstream of the injection point into the chamber. The remaining part was vented. The residence time of the sampled ambient air inside the SAPHIR chamber was 1.1 h and calculated from the mea-sured flow rate and the chamber volume. Sampling air from the large volume of the SAPHIR chamber has the advantage that short-term variations in trace gas concentrations flowed into the chamber due to local emissions or fast changes in air masses, for example, are smoothed.
The JULIAC campaign consisted of four intensive measurement periods in winter (14 January to 10 February 2019), spring (8 April to 5 May 2019), summer (5 August to 1 September 2019), and autumn (28 October to 24 November 2019). During these parts of the campaign, a large set of instruments sampled air from the chamber. In addition, between each intensive measurement period, a limited set of instruments for the detection of ClNO 2 , O 3 , NO, NO 2 , OH reactivity, and VOCs continued measuring directly from the inlet line at the JULIAC tower (Fig. S1).

Instrumentation
A large set of instruments was deployed during the JULIAC campaign. In this work, the focus is on measurements that are relevant for studying the chemistry of ClNO 2 .
ClNO 2 was measured by a chemical ionization mass spectrometry (CIMS) instrument from Leicester University (THS Instruments LLC, GA, USA) that was operated in the negative ion mode using iodide (I − ) as a reagent ion. ClNO 2 was detected at the mass-to-charge ratios (m/z) of 208 and 210 amu, corresponding to the two isotopes of the [I q ClNO 2 ] − ion clusters as described in Sommariva et al. (2018).
The CIMS instrument was calibrated by standard additions of ClNO 2 generated by flowing humidified air containing Cl 2 (from a cylinder containing a mixture of 5 ppmv, parts per million by volume, or ±5 % Cl 2 in N 2 ; Linde AG) over a salt bath containing a 1 : 1 mixture of NaCl and NaNO 2 (Sommariva et al., 2018). The resulting ClNO 2 concentration in the air was determined by measuring the NO 2 concentration after thermally decomposing ClNO 2 to Cl and NO 2 in a glass tube heated to a temperature of 400 • C. The NO 2 concentrations were measured using a commercial NO 2 analyzer that makes use of the cavity-attenuated phase shift method (CAPS; T500U, Teledyne API). The accuracy of the NO 2 measurements by this analyzer is ±5 %. The overall accuracy of the ClNO 2 calibration is ±17 %; the precision of the ClNO 2 measurements is 13 %, with a 2σ detection limit of 5.6 pptv at a 1 min time resolution.
The CIMS detection sensitivity depends on humidity because iodide ions form clusters with water (I q (H 2 O) − ). The water-iodine cluster is a more efficient reagent ion for producing I q (ClNO 2 ) − clusters than the I − ion (Kercher et al., 2009). The dependence of the sensitivity on humidity was characterized with calibration experiments by varying the mixing ratios of water vapor. These experiments show that the sensitivity of the instrument for the detection of ClNO 2 decreases by 19 % per 1 % water vapor mixing ratio (Fig. S2) when the signal is normalized to the I q (H 2 O) − cluster sig-nal (m/z = 145). Calibrations of the instrument were performed during each measurement period by using comparable average humidity to that of the ambient air. The variability in the sensitivity due to the changes in humidity in each 4-week-long measurement period was less than ±5 %. This is within the range of reproducibility of calibration measurements. Therefore, the sensitivity was not corrected for the humidity effect for individual data points, but an average sensitivity value was applied to all data from the entire measurement period. The uncertainty due to the humidity dependence of the sensitivity and the reproducibility of the calibration adds to the overall accuracy of ClNO 2 measurements, increasing the value to ±27 %.
Photolysis frequencies inside the SAPHIR chamber were calculated from the actinic flux measured outside the chamber and corrected for the reduction in radiation by the shading effects and the transmission of the Teflon film . Ozone was detected by a UV photometer (model O342M, Ansyco). Nitric oxide (NO) was measured by a chemiluminescence instrument (780 TR, Eco Physics) that was also used to detect NO 2 by the conversion of NO 2 to NO in a blue light photolytic converter upstream of the NO analyzer. For the period after 1 December 2019, NO 2 was measured by an instrument using the iterative cavity-enhanced differential optical absorption spectroscopy method (ICAD1005, AirYX). The NO 2 measurements from the two instruments agreed well within 5 % when both instruments measured concurrently. Water vapor and carbon monoxide (CO) concentrations were measured by a cavity ring-down instrument (G2401, Picarro). NO 3 and N 2 O 5 were measured by a custom-built cavity ring-down instrument that is similar to the one described in Wagner et al. (2011).
Particle number concentration (for particles with a diameter > 5 nm) and size distribution (for particles with a diameter between 10 and 1000 nm) were measured by a condensation particle counter (model 3787, TSI Incorporated) and a scanning mobility particle sizer (model 3080, TSI Incorporated), respectively. The aerosol surface area (S a ) was calculated based on the particle number and geometric diameter in each size bin. The chemical composition of particles was analyzed by an aerosol mass spectrometer (HR-TOF-AMS, Aerodyne Research Inc.).
The temperature and pressure of the ambient air were measured inside the chamber and also outside the chamber at different heights (2, 20, 30, 50, 80, and 120 m) by sensors mounted at a meteorological tower located approximately 200 m away from the SAPHIR chamber.

Comparability of measurements from the chamber and the inlet line
Air was sampled from 50 m above the ground from the top of the JULIAC tower at all times of the campaign (Fig. S1). However, ClNO 2 concentrations were determined in the air from either one of the two sampling points during the different periods of the campaign. During the intensive measurement periods (i.e., in February, August, and November), air was directly sampled from the SAPHIR chamber. During other times, air was sampled from the inlet system of the chamber at the JULIAC tower. In both cases, the measured concentrations are representative of the air from 50 m height. In the case of sampling from the chamber, concentrations are averaged due to the 1 h residence time of air in the chamber.
To make the data derived from both sampling points comparable, ClNO 2 concentrations measured inside the chamber (C chamber ) were converted to equivalent concentrations at the tip of the JULIAC inlet system (C 50 m ). This can be achieved from the differential equation of concentrations, taking into account dilution with the flow rate (k flow ) and loss (L chamber ) and production (P chamber ) inside the chamber, as follows: The concentration in the incoming air can be iteratively determined from the time series of measured concentrations inside the chamber if loss and production processes can be quantified. The other species used in this work (O 3 , NO x , etc.) were measured both at the tip of the JULIAC inlet and inside SAPHIR. Unless otherwise specified, the measurements presented in this work were either taken at the tip of the JULIAC inlet or corrected using Eq. (5). The production of ClNO 2 from the heterogeneous reaction of N 2 O 5 on particles is expected to be negligible on the timescale of the residence time of air in the chamber for conditions of the JULIAC campaign. Chamber wall interaction could be relevant because the surface area of the Teflon film is 10 6 µm 2 cm −3 , i.e., several orders of magnitude larger than the surface area of ambient aerosol experienced in this campaign, which were of the order of tens to hundreds of micrometers squared per cubic centimeter (µm 2 cm −3 ). To quantify potential chamber-related loss and production processes, chamber characterization experiments were conducted (Sect. 3.1). They were analyzed by using a chemical box model in which loss and production rates were adjusted to reproduce measured ClNO 2 concentrations during these experiments. Temperature, relative humidity, pressure, photolysis frequencies, and dilution rates determined from the air replenishment flow rate were constrained to measurements in the model. The conversion of N 2 O 5 to ClNO 2 via surface reactions (Reaction R6) and the loss reactions of ClNO 2 on the chamber wall (Reaction R7) were included in the model, assuming pseudo-first-order processes, as follows: In addition, the chemical loss of ClNO 2 via photolysis (Reaction R1) was considered. The results of these experiments and the model analysis are discussed in Sect. 3.1.

Chamber effects on measured ClNO 2 concentrations
Two types of experiments were performed to characterize the chamber properties with respect to the wall interaction of NO 3 , N 2 O 5 , and ClNO 2 . In these chamber characterization experiments, only a small replenishment flow of pure synthetic air compensated for leakages and extraction of air by instruments. This led to a low dilution of trace gases with a rate that is equivalent to a lifetime of 17 h and is in contrast with the 1 h lifetime during the operation of the chamber in the JULIAC campaign. Three experiments were conducted (5, 6, and 7 February 2019) to test whether ClNO 2 was exclusively lost by photolysis in the chamber or whether other processes, such as wall loss, contributed to the ClNO 2 removal. These experiments started with flowing ambient air through the SAPHIR chamber during the night, as in the operational mode of the JULIAC campaign (Sect. 2.1). The high flow was stopped before sunrise (around 06:00 UTC), and the small replenishment flow was started. The evolution of trace gas concentrations was observed until around 12:00 UTC while the air was exposed to sunlight. The N 2 O 5 concentration decreased rapidly to zero after sunrise, and thus no further ClNO 2 could be produced from the N 2 O 5 conversion, and ClNO 2 concentrations also decayed during the morning.
Measured concentrations are compared to the calculation using a chemical box model (Sect. 2.3) considering losses of ClNO 2 by dilution, photolysis, and potential wall loss. Whereas loss rates for dilution and photolysis are constrained to measurements, the wall loss rate constant is adjusted to match the observed ClNO 2 concentrations. This results in a wall loss rate constant for ClNO 2 of 2.1 × 10 −5 s −1 . This value is of the same order of magnitude as the loss rate constant of ClNO 2 due to photolysis (4.1 × 10 −5 s −1 at noon) and dilution (1.5 × 10 −5 s −1 ) for the experimental conditions of the characterization experiments. Due to the higher chamber flow rate used during the JULIAC campaign, the dilution rate is an order of magnitude higher (2.5 × 10 −4 s −1 ) than during the characterization experiments. Therefore, the wall loss rate is only 8 % of the dilution rate and thus can be neglected in the further data analysis.
An additional three experiments were performed to characterize the potential ClNO 2 formation from heterogeneous reactions of N 2 O 5 on the chamber wall. In these experiments (18 September, 18 October, and 19 November in 2019), NO 2 and O 3 were added into the dark chamber filled with pure, dry, or humidified synthetic air. These experiments lasted for about 10 h in order to observe the decay of NO 2 and O 3 concentrations and the accumulation of ClNO 2 . Figure 1 shows the measured concentrations for the experiments performed on 19 November. In this experiment, the chamber air was humidified (RH = 60 %) and 28 ppbv of NO 2 and 80 ppbv of O 3 were injected to produce NO 3 and N 2 O 5 . NO 3 mixing ratios were below the limit of detection (about a few pptv) of the cavity ring-down instrument.
N 2 O 5 measurements reached maximum mixing ratios of 0.17 ppbv shortly after the O 3 injection and decreased afterward ( Fig. 1). Also, ClNO 2 production was observed shortly after the ozone addition when N 2 O 5 was present. Because the air was particle-free, one possible explanation for the formation of ClNO 2 is the heterogeneous reaction of N 2 O 5 on the chamber wall that may contain chloride, which could have been deposited, for example, during previous experiments with ambient air.
The values of the conversion rates from N 2 O 5 to ClNO 2 (Reaction R6) that are required to match the measured ClNO 2 concentrations in the model calculations are k R6 = 4.0 × 10 −6 , 2.0 × 10 −6 , and 8.2 × 10 −6 s −1 for the experiments on 18 September, 18 October and 19 November in 2019, respectively.
During the JULIAC campaign, however, the potential contribution of ClNO 2 formation from N 2 O 5 conversion on the chamber film was negligible. Taking the typical nocturnal N 2 O 5 mixing ratio of about 50 pptv, the expected ClNO 2 production rate from N 2 O 5 conversion on the chamber wall was about 1.5 pptv h −1 , using the upper limit value of k 6 derived from the characterization experiments. This is less than 1 % of the ambient ClNO 2 mixing ratio of up to several hundred pptv in the ambient air that is flowed into the chamber. Therefore, no corrections are needed for the interpretation of ClNO 2 measurements in the chamber.
Overall, the results of the characterization experiments allow us to simplify the back-calculation of the ClNO 2 concentrations in the sampled air from measured concentrations in the chamber (Eq. 5). The chemical production rates and the deposition rates for ClNO 2 and N 2 O 5 on the chamber walls can be neglected, and only photolysis needs to be considered to be a destruction process for ClNO 2 during the daytime. For nighttime conditions, ClNO 2 concentrations in the incoming air can be determined solely from the flow rate and the measured ClNO 2 concentration inside the chamber.

Overview of measurements
In order to determine the origin of air masses sampled at the measurement site, back-trajectories were calculated using the Hybrid Single-Particle Lagrangian Integrated Trajectory model (HYSPLIT; Stein et al., 2015) for every second hour. They were calculated for a height of 50 m above the ground and started 48 h earlier before the air arrived at the measurement site. Calculations for different heights (500 and 1000 m) gave similar results to the trajectories calculated for a height of 50 m. To extract information about the relation between the source of air masses and the measurements, the cluster analysis tool of the HYSPLIT model was used, which classified the trajectories into two groups (Fig. 2).
Trajectories most often showed the prevailing longdistance transport of air masses from the southwest that traveled hundreds of kilometers from the Atlantic Ocean (approximately 1000 km away from the measurement site) within 48 h. These air masses were likely influenced by marine and continental emissions as they crossed over northern France and Belgium. They are referred to hereafter as belonging to the long-range transport group. The other group of trajectories did not show a prevalent direction but shared the common feature that these air masses circulated over the cities nearby the measurement site, e.g., Cologne, Düsseldorf, and Frankfurt (Fig. 2). These air masses are therefore influenced by regional emission sources and are referred in the following to belong to the regional transport group. Figure 3 shows the mean diurnal profiles of ClNO 2 , NO 2 , and O 3 concentrations and the photolysis frequencies of ClNO 2 in February, August, September, November, and December 2019 if the measurements are split into two groups, depending on the type of back trajectory associated with the measurement at that time. The complete time series of measurements used for the analysis in this work is shown in Figs. S3-S7.
In all cases, the diurnal profiles of ClNO 2 showed an increase in concentration after sunset, as can be expected from its chemical production during the night. Maximum concentrations were reached around midnight, and ClNO 2 concentrations remained relatively constant until sunrise when they started to decrease due to its photolysis.  The reaction chain to produce ClNO 2 at night starts with the reaction of NO 2 and O 3 . The median observed O 3 showed little diurnal variation in the cold seasons (February, November, and December; Fig. 3). At this time of the year, the O 3 level was generally higher in long-range transported air (30-40 ppbv O 3 ) compared to regionally influenced air (15-20 ppbv O 3 ), for which ozone depletion by urban NO emissions was likely more important due to fresh emissions. During summer, when photochemistry was most active (August and September), the median O 3 concentrations were consid-erably higher in regionally influenced air. Ozone mixing ratios in summer showed distinct diurnal profiles with noontime maxima of 80 ppbv in August and 40 ppbv in September and nighttime values between 20 and 30 ppbv. In contrast, long-range transported air exhibited a less pronounced diurnal variation in the O 3 concentration, and mixing ratios were often only between 20 and 40 ppbv. The high summertime ozone concentrations in regionally transported air is likely due to the fresh emissions of NO and VOCs, which are photochemically converted to O 3 .
The influence of fresh emissions from nearby sources is also visible in the measured NO 2 concentrations, which were higher in regional air masses compared to concentrations in long-range transport air masses during the entire year. For regionally transported air masses, average nocturnal NO 2 mixing ratios were around 10 ppbv in all measurement periods, except in December, when mixing ratios were lower, with values of about 5 ppbv. At night, median NO 2 concentrations in long-range transported air masses were generally lower than 5 ppbv in all seasons.
The age of the air mass could play a role in the observed levels of ClNO 2 due to the impact on NO 2 and O 3 concentrations and, hence, on ClNO 2 . As shown in Fig. 2, regionally transported air masses spend more time over urban areas picking up anthropogenic emissions (indicated by high NO 2 mixing ratios). They also have more time for the photochemical processing of pollutants compared to the longrange transported air masses. In the cold months (February, November, and December), long reaction times would lead to lower O 3 concentrations for the regional air masses due to the titration by anthropogenically emitted NO compared to conditions in August and September when photochemical ozone production is more efficient than the titration effect.
The nocturnal ClNO 2 concentrations were consistently lower in air masses from long-range transported air compared to regional transported air in nearly all seasons except, again, in December. The maximum median nighttime values were around 0.2 ppbv in long-range transported air and around 0.5 ppbv in air masses from regional transport (Fig. 3). Only in December was no significant dependence of the ClNO 2 concentration on the origin of air masses observed.
Maximum ClNO 2 mixing ratios of 1.6 ppbv (15 min average), which were observed at 03:00 UTC on 15 September in the JULIAC campaign (Fig. S5), are comparable to observations in other field campaigns. In Europe, high ClNO 2 mixing ratios have also been observed during summer in several field campaigns, in which ClNO 2 was measured, including 0.8 ppbv near Frankfurt, Germany (Phillips et al., 2012), 0.8 ppbv in London, UK (Bannan et al., 2015), and 1.1 ppbv in Weybourne, UK (180 km northeast of London; Sommariva et al., 2018).
The seasonally varying photolysis frequencies of ClNO 2 showed a diurnal noontime maxima of 0.4 × 10 −4 s −1 in winter and 2.5 × 10 −4 s −1 in summer. Sunlight lasted the longest in summer, and photolysis frequencies were sufficiently high to destroy all ClNO 2 before midday. In contrast, daytime ClNO 2 concentrations remained significantly above zero (around 30 pptv) in the cold seasons because the maximum photolysis frequencies were a least a factor of 2 lower than in summer, and the duration of the daylight was not long enough to deplete all ClNO 2 . Similar results were observed in the wintertime measurements of ClNO 2 by Sommariva et al. (2021).
Seasonal differences in ClNO 2 concentration observations in this work can be compared to the seasonal variations reported for measurements performed in Leicester, UK (Sommariva et al., 2018). In Leicester, the highest ClNO 2 mixing ratio of 0.73 ppbv was observed in February when NO 2 mixing ratios were also the highest, with values of 43 ppbv. The seasonality of ClNO 2 , NO 2 , and O 3 observed during the JU-LIAC campaign was different from the seasonality observed in Leicester. In this work, the highest ClNO 2 concentrations were experienced in summer when the air was influenced by emissions from nearby cities (regional transport), resulting in high NO 2 and O 3 concentrations. The different seasonal behavior in Jülich and Leicester suggests that the controlling factor for the production of ClNO 2 could have been different in the two locations (Sect. 3.5).

Influence of the nocturnal vertical stratification of air on ClNO 2 concentrations
The ClNO 2 measurements presented in this work were obtained in air sampled at a height of 50 m aboveground (Sect. 2). While there is a well-mixed layer due to convection during the day, the cooling of the ground results in weak convection of air after sunset, leading to stratification of the air at night. In general, layers can be identified by the vertical profile of the potential temperature. At night, a stable surface layer (typically < 20 m height) is expected to be formed in which emissions from the ground are trapped. A weakly stable nocturnal boundary layer is on top of the surface layer (NBL; typically in the height range between 20 and 200 m) and a residual layer that is fully decoupled from the ground (typical height > 200 m; Brown et al., 2007). Because the tip of the inlet of the SAPHIR-JULIAC inlet system was 50 m above the ground, it was most often located within the nocturnal boundary layer, and thus the impact of surface emissions in the sampled air is expected to be small.
This was particularly the case in the cold seasons (February, November, and December), suggesting that most of the nighttime measurements presented in this work are representative of conditions in the NBL. Similar conditions were encountered in the summer during nights with low wind speed and cloudless conditions. However, in 8 out of 30 nights from 20 August to 20 September, the sampled air at 50 m height was temporarily influenced by surface air. Indicators were, for example, observed enhancements of the NO and CO concentrations and reduced mixing ratios of ClNO 2 .
An example of such an event is shown in Fig. 4, which presents measurements from the night of 21 to 22 August 2019. After sunset (around 19:00 UTC), a stable surface layer was formed, as indicated by a positive vertical temperature gradient in the lowest 20 m (Fig. 4a). Until 22:00 UTC, the surface layer height increased and developed a strong temperature inversion at 30 m height. Above the surface layer, the temperature gradient was slightly positive up to a height of 80 m. It is expected that, for the conditions until about 22:00 UTC, the measured air at 50 m height was not influenced by surface emissions. During this time, ClNO 2 mixing ratios increased continuously to 1.5 ppbv due to chemical production. After 22:30 UTC, ClNO 2 decreased to 0.5 ppbv until 00:00 UTC. The decrease coincided with an increase in wind speed from below 2 m s −1 at 23:00 UTC to about 4 m s −1 at 00:00 UTC. This might be related to the phenomenon of nocturnal jets that can produce high wind speeds at low altitudes in a range of 50 m. The elevated wind speed and change in wind direction indicate that air mass came down the Ruhr valley from Düren, a small city 10 km away from the site. At the same time, the steep temperature gradient of the inversion at 30 m disappeared and most likely facilitated entrainment of surface air with lower ClNO 2 concentration. This assumption is supported by an enhanced NO mixing ratio of 0.2 ppbv observed shortly before midnight, indicating the presence of ground emissions (Fig. 4b).
At the same time, the NO 2 mixing ratio increased, and the O 3 mixing ratio decreased by a similar amount (10 ppbv), likely due to the chemical titration of O 3 by freshly emitted NO (Fig. 4c). The drop in ClNO 2 may have been caused by the lower ClNO 2 production in the surface layer because N 2 O 5 concentrations were low due to N 2 O 5 and NO 3 loss on surfaces and chemical loss in reactions with NO and organic compounds that have emission sources on the ground. At later times on this night, ClNO 2 mixing ratios increased again to a value of 1.3 ppbv at 01:00 UTC (Fig. 4b), when the air was again sampled from within the nocturnal boundary layer, where loss processes are expected to be smaller compared to the surface layer.
The median diurnal profiles presented in Sect. 3.2 include all measurements. The different behavior observed during the night, when air was temporarily impacted by surface interaction, only constitute a small fraction of the measurement time. To quantify the influence of surface interactions, elevated NO concentrations at the sampling point can be used. For more than 90 % of the time, measured NO mixing ratios are lower than 0.1 ppbv (Fig. S8), indicating that air masses were typically little influenced by the surface emissions. Therefore, it can be assumed that the sampling point was most often located in the nocturnal boundary layer. Median values further analyzed in this work are representative of conditions in the nocturnal boundary layer.

ClNO 2 production efficiency
The ClNO 2 production efficiency (ε) defined in Eq. (4) is affected by (1) the thermal equilibrium between NO 3 and N 2 O 5 , (2) the loss of NO 3 + N 2 O 5 by the reaction of NO 3 with VOCs and the heterogeneous uptake of N 2 O 5 on the aerosol surface, and (3) the yield of ClNO 2 from the heterogeneous reaction of N 2 O 5 . The value of the production efficiency cannot be simply calculated because the required parameters along the trajectory of the studied air mass are (a) Vertical profiles of the potential temperature derived from temperature measurements at different heights (2, 10, 20, 30, 50, 80, 100, and 120 m). (b-d) ClNO 2 , NO, NO 2 , O 3 , and CO mixing ratios sampled at 50 m height with the JULIAC-SAPHIR inlet system. CO mixing ratios were also measured at a height of 2 m. Colors of the vertical lines correspond to colors of the vertical profiles of the potential temperature. not known. Instead, a mean value of ε is estimated empirically from the observed nocturnal increase in the ClNO 2 concentration at the measurement site and the corresponding integrated NO 3 production rate. This approach assumes that there are no significant nocturnal ClNO 2 losses in the studied air.
For the calculation of the efficiency (Eq. 6) from the measured ClNO 2 concentrations, the ClNO 2 concentration at sunset ([ClNO 2 ] t 0 ) is subtracted because this fraction of ClNO 2 can be assumed to be produced during the previous night. This correction is important, especially for conditions in winter and late autumn, when tens of pptv of ClNO 2 were observed before sunset because of the long chemical lifetime of ClNO 2 under these conditions (Fig. 3). An accurate calculation of the integrated NO 3 production rate would require knowledge of the NO 2 and O 3 concentrations while the air mass is being transported, but the exact concentrations are only known at the location of the JULIAC tower. Therefore, it is necessary to make assumptions about the history of the air mass. For simplification, it is here assumed that the air mass arriving at the JULIAC site is homogeneous along the trajectory after sunset. This assumption requires that the consumption of NO 2 by a reaction with O 3 is small over the integration time and that the chemical composition of the studied air remains undisturbed by mixing with air masses containing different trace gas concentrations. The latter assumption seems reasonable when the air is sampled above the nocturnal surface layer, which was largely the case during the JULIAC campaign (Sect. 3.3). For these assumptions, the integrated NO 3 radical production P (NO 3 ) can be calculated from the measured NO 2 and O 3 concentrations at the measurement site and the reaction rate constant (k 2 ) of their reaction. The value of the reaction rate constant is taken from recommendations by the International Union of Pure and Applied Chemistry (IUPAC; Atkinson et al., 2004). Therefore, the production rate of the NO 3 radical can be substituted by the reaction rate of NO 2 and O 3 , and Eq. (6) is rewritten as follows: t 0 can be set to the time of sunset, and the time t is stepwise increased by intervals of 5 min (time resolution of the dataset) to calculate the time series of the production efficiency in 1 night. For further analysis, the first 4 h after sunset is averaged for each night because ClNO 2 increased to its maximum concentration on most of the nights of this campaign during this time. This suggests that chloride is not a limiting factor for ClNO 2 production. Mean values of the ClNO 2 production efficiency in each season can then be compared. The ClNO 2 production efficiency does not show a clear seasonal behavior, but the values are larger in the regional transported air masses than in long-range transported air masses (Fig. 5). Mean values exhibit a similar pattern if the values are taken from the entire night or a period in the second half of the night (Fig. S9).
For the air masses from regional transportation, the highest mean ClNO 2 production efficiency of 18 ± 9 % was observed in February. This is consistent with a high NO 3 production rate due to high NO 2 concentrations (Fig. 3) and the low temperatures in February which favor the formation of N 2 O 5 . Similar ClNO 2 production efficiency was observed in September, although NO 2 concentrations were low. This suggests that other factors, besides the ones included in Eq. (4), contributed to the efficient production of ClNO 2 in regional air masses in September.
The ClNO 2 production efficiencies obtained in December are similar, with values of 3 ± 3 % for both regional and longrange transportation air masses. This is consistent with observations of ClNO 2 , NO 2 , and O 3 concentrations, which were also similar regardless of the origin of air masses in December (Fig. 3). In the other seasons, however, the ClNO 2 pro- Figure 5. Mean ClNO 2 production efficiency for each measurement period for 4 h average values starting after sunset. Values are calculated for air masses originating either from regional or longrange transportation. The vertical bars denote 1σ standard deviations. duction efficiencies were 30 % to 50 % lower in air masses from long-range transportation compared to values obtained for regional air masses. This can be explained by elevated NO 2 concentrations in regional air masses, which shifts the equilibrium between NO 3 and N 2 O 5 to the side of N 2 O 5 and N 2 O 5 and therefore facilitates the production of ClNO 2 .
It should be mentioned that the production of ClNO 2 also requires the availability of particulate chloride (Reaction R4). During the JULIAC campaign, particulate chloride concentrations were measured by an aerosol mass spectrometry (AMS) instrument giving average concentrations of 0.15 ± 0.08, 0.07 ± 0.03, 0.07 ± 0.06, and 0.09 ± 0.04 µg m −3 for measurements in February, August, September, and November, respectively (measurements in December were not available; see Table S2 in the Supplement). The particulate chloride measurements by the AMS instrument are restricted to non-sea-salt aerosol because the AMS was operated to measure the nonrefractory particulate matters. As the measurement site is only 200 km away from the North Sea, sea salt was likely an important source of chloride in the JULIAC campaign. Thus, there was most likely more chlorine present than measured by the AMS, and the observed chloride concentrations must be regarded as a lower limit. Nevertheless, the high ClNO 2 production efficiency in the regional air masses suggests that particulate chloride was not a limiting factor for the formation of ClNO 2 at the measurement site (for the period of 4 h after sunset). In the following analysis, it is assumed that the availability of particulate chloride was enough to sustain Reaction R4 during this study, so ClNO 2 production was only dependent on the availability of its gas-phase precursors (see Sect. 3.5).
Previous studies have reported similar values of ClNO 2 production efficiencies. Two field studies performed in urban environments in Canada found median values of the ClNO 2 production efficiency of 1.0 % (Mielke et al., 2016) and 0.17 % (Osthoff et al., 2018). These low values were attributed to gas-phase loss reactions of NO 3 competing with the formation of ClNO 2 . In addition, the authors determined significant O 3 destruction by deposition and titration in the reaction with NO in a shallow nocturnal boundary layer, which further limited the production of ClNO 2 (Osthoff et al., 2018). In another campaign, measurements were performed on board a ship during a cruise in the Mediterranean Sea (Eger et al., 2019). The ClNO 2 production efficiency determined from these measurements was in the range between 1 % and 5 % and attributed to the efficient gas-phase loss of NO 3 and to the high temperature (usually > 25 • ) that shifted the thermal equilibrium towards NO 3 so that little N 2 O 5 was expected. In contrast, the ClNO 2 production efficiency observed in Pasadena, U.S. (Mielke et al., 2013), was much higher than in the field studies in Canada (median value of 9.5 %). These measurements were performed in the coastal boundary layer, which was characterized by high concentrations of pollutants. The authors attributed the high ClNO 2 production efficiency to the rapid N 2 O 5 reaction with Cl that was present in submicron aerosol particles from the redistribution of sea salt chloride, as proposed by Osthoff et al. (2008).
3.5 Dependence of the ClNO 2 production on the availability of NO 2 and O 3 Most of the measurements taken during the night from a height of 50 m were not affected by fresh local emissions from the ground surface, as discussed in Sect. 3.2. As a first approximation, it can be assumed that particulate chloride is not limiting the formation of ClNO 2 (Sect. 3.4). Therefore, the amount of ClNO 2 that can be formed during the night is a function of the amounts of NO 2 and O 3 available at sunset. The dependence of the ClNO 2 production on the availability of NO 2 and O 3 for ambient conditions is further investigated by box model calculations. This method was previously used by Sommariva et al. (2018), and a detailed description can be found in their work. In brief, the model is initialized with a matrix of initial NO 2 and O 3 concentrations. The chemical box model includes production and loss reactions of ClNO 2 (Reactions R1-R4; reaction rate constants are taken from the IUPAC recommendations; Atkinson et al., 2004). ClNO 2 concentrations are calculated for each initial NO 2 and O 3 concentration after 4 h. This length of the simulation is chosen because observed ClNO 2 concentrations typically reached their maximum values approximately 4 h after sunset in the JULIAC campaign.
In the model, the efficiency of the conversion of N 2 O 5 to ClNO 2 is assumed to be constant, with a value for the uptake coefficient of N 2 O 5 of 0.01 from Bertram and Thornton (2009) and a ClNO 2 yield of 0.5 (Reaction R4) from Roberts et al. (2009). The aerosol surface area (S a ) measured during JULIAC was of the order of 100 µm 2 cm −3 (Table S1) and was set to this constant value in the model. Temperature was fixed at 22 • C to represent typical summer-like conditions. Hence, the pseudo-first-order reaction rate constant for N 2 O 5 uptake is 6.0 × 10 −5 s −1 . Following Sommariva et al. (2018), a constant NO 3 loss rate is used to represent the typical loss of NO 3 radicals (k NO 3 ) in their reactions with organic compounds (Reaction R5). The assumed value of the NO 3 loss rate, k NO 3 , is adjusted so that the modeled ClNO 2 concentration agrees with the magnitude of the observations (Fig. S10), which corresponds to an NO 3 reactivity of 0.004 s −1 . It should be noted that the purpose of such a simplified model is to examine the idealized dependence of ClNO 2 on the chemical conditions and not to reproduce the measurements. Figure 6a shows the modeled ClNO 2 mixing ratios as a function of the initial NO 2 and O 3 concentrations at sunset. Given the chemical conditions of long-range transported air masses in summer (25 to 35 ppbv O 3 and 4 to 5 ppbv of NO 2 ), the model predicts ClNO 2 mixing ratios in the range of 0.1 to 0.16 ppbv. Because of the simplifications adopted in the modeling approach, calculated ClNO 2 mixing ratios tend to underestimate the measurements the measurements, which are around 0.2-0.3 ppbv (Fig. S10). For regional air masses containing higher NO 2 mixing ratios (6 to 10 ppbv of NO 2 ), the NO 3 production rates, and therefore the calculated ClNO 2 mixing ratios, are also higher (between 0.2 and 0.4 ppbv, Fig. 6a). Given the position of each measurement period in the isopleth plot, it can be concluded that all longrange transported air masses tend to be NO 2 limited while the regional transported air masses tend to be NO 2 limited in summer/autumn and O 3 limited in winter.
To further interpret the controlling factors of ClNO 2 production, the dependence of ClNO 2 production efficiency ε on NO 2 and O 3 is presented in Fig. 6c. The modeled ClNO 2 production efficiency increases with increasing mixing ratios of NO 2 but not with increasing O 3 (Fig. 6c), as expected from Eq. (4), which shows that the ClNO 2 production efficiency is a function of multiple parameters but not of the O 3 mixing ratio. In general, the model reproduces the experimentally determined ClNO 2 production efficiency (as shown in Fig. 5) within the uncertainty in the calculation (30 % to 40 %), which is mainly due to the assumptions concerning the history of air masses (Sect. 3.4). However, the relatively high ClNO 2 production efficiency found in August and September in the regional air masses (Fig. 5) is significantly underestimated by the model. The discrepancy suggests that other processes facilitate the conversion from NO 3 to ClNO 2 in the regional air masses for summer-like conditions. Though the purpose of this model calculation is not to reproduce the observations, it is critical to address the related uncertainties/limitations due to the assumptions in the simplified model. The key parameters affecting the formation of ClNO 2 concentrations are temperature, NO 3 loss, and N 2 O 5 loss. Their impact on the model results is discussed below. Figure 6b shows the dependence of modeled ClNO 2 on the temperature and NO 2 concentrations investigated by the same model approach for which the O 3 concentration is fixed to 30 ppbv (representing the typical O 3 level of long-range Figure 6. Isopleth plot of modeled (a, b) ClNO 2 mixing ratios that accumulate during the night and (c, d) the ClNO 2 production efficiency depending on (a, c) the initial O 3 and NO 2 mixing ratios and (b, d) the temperature and initial NO 2 mixing ratios. Values are taken 4 h after sunset, when maximum ClNO 2 concentrations were observed. Symbols mark calculated ClNO 2 mixing ratios for average values of NO 2 and O 3 mixing ratios measured in each period of the JULIAC campaign if the air masses originated either from longrange (L.-R.) or regional (R.) transportation. For comparison, values are also shown for measurements during the PARADE campaign in summer in Germany (Phillips et al., 2012). The dashed line (a) separates the regimes for which ClNO 2 production is more sensitive to the change in O 3 (a) and NO 2 (d).
transported air). In this case, the modeled ClNO 2 concentrations reach maximum values at temperatures of 5 • C. For these winter-like conditions, the low temperature shifts the equilibrium between NO 3 and N 2 O 5 to the side of N 2 O 5 . In contrast, the conversion of NO 2 to ClNO 2 is suppressed at high temperatures (T > 15 • ) under typical conditions in August and September. Temperature also plays an important role for the value of the ClNO 2 production efficiency due to the shift in the equilibrium between NO 3 and N 2 O 5 . The significantly higher ClNO 2 production efficiency observed in February compared to the other seasons could be largely attributed to the low temperature at that time (Fig. 6d).
Sensitivity tests demonstrate that decreasing the rate of the chemical loss of NO 3 to organic compounds (Fig. S11) only has a small impact, while the seasonal variation in chemical loss of NO 3 peaks in summer-like conditions due to the intense biogenic emission. The higher production efficiency could be attributed to faster-than-assumed conversion from N 2 O 5 to ClNO 2 , which can bring modeled and measured valued into agreement. This can be either achieved by increasing the value of the N 2 O 5 uptake coefficient (Fig. S12) or the yield of ClNO 2 in the process of the heterogeneous uptake of N 2 O 5 on aerosol (Fig. S13).
As mentioned above, the NO 3 reactivity is assumed to be 0.004 s −1 to match the observations, which is comparable to the NO 3 reactivity observed at a mountainous site in southern Germany, with a campaign-averaged value of 0.01 s −1 for nighttime conditions (Liebmann et al., 2018). As shown in the sensitivity test, a higher NO 3 reactivity leads to lower modeled ClNO 2 concentrations. Therefore, the low NO 3 reactivity in the model could be regarded as a lower limit given the similar biogenic-influenced environments.
In this model calculation, the aerosol surface area S a is held constant instead of using the value measured inside the chamber, which was likely impacted by the sampling system, but cannot be corrected for ambient measurement (Sect. 2.3). Nevertheless, the measured S a gives some confidence that the model is not using an unrealistic lower limit.
The aerosol chemical composition also plays a role in determining the production efficiency. The yield of ClNO 2 from the N 2 O 5 heterogenous reaction (ϕ(ClNO 2 )) can be expressed by assuming that the production of ClNO 2 results from the competition between Cl − and H 2 O reacting with the H 2 ONO + 2 intermediate formed from the N 2 O 5 uptake on aerosol (Bertram and Thornton, 2009;Mielke et al., 2013;McDuffie et al., 2018b).
The value of the ClNO 2 yield is different in the periods of the campaign showing maximum values of 0.6 to 0.8 in February (Fig. S14). This is consistent with the relatively high ClNO 2 production efficiency derived from the integrated production rate of NO 3 (Eq. 7). However, the calculated ClNO 2 yield decreases below 0.4 in August and September, which could be attributed to the higher aerosol liquid water content in these two periods compared to the value seen in other periods (Table S1). The calculated ClNO 2 yield is also higher for the long-range transported air masses than those for the regional one (Fig. S14). The relatively high ClNO 2 production efficiencies found in the regional air masses, which are in contrast with their relatively low calculated ϕ(ClNO 2 ), suggest that other factors play an important role in determining the ClNO 2 production, such as a larger-than-assumed uptake coefficient for N 2 O 5 and/or aerosol surface area. For comparison, the observation from another field campaign conducted in a similar rural environment in Germany is marked in the isopleth diagram (Fig. 6). The PARADE campaign took place in the Taunus Observatory of the University of Frankfurt, which is located 170 km southeast of the JULIAC measurement site (Phillips et al., 2012). The maximum observed ClNO 2 mixing ratio was 0.8 ppbv when the measurement site was influenced by air masses from the UK/North Sea. This value is lower than the results of the model calculations using the median NO 2 and O 3 observed in that campaign, which is consistent with the general underprediction for summer-like conditions for the JULIAC campaign and suggests that the conversion from NO 3 to ClNO 2 is more efficient than the model predicts in summer. The position in the isopleth diagram suggests that ClNO 2 formation was limited by the availability of NO 2 , similar to the summer period the JULIAC campaign, which is the same season as the PARADE campaign (August).

Summary and conclusions
Concentrations of ClNO 2 and other trace gases and the chemical composition of aerosols were measured during the Jülich Atmospheric Chemistry Project (JULIAC) campaign in 2019 that was performed at a rural site in Germany. Ambient air was sampled into the atmospheric simulation chamber SAPHIR from a height of 50 m, which was, most of the time, uncoupled from the surface layer during the night. Chamber characterization experiments demonstrated that no significant loss or production of ClNO 2 occurred inside the chamber for experimental conditions of the JULIAC campaign.
In all periods, ClNO 2 measurements showed a trend of increasing mixing ratios after sunset with maximum values were reached around midnight. This qualitative behavior is consistent with the chemical production of ClNO 2 and insignificant losses during the night. Photolysis was the main loss process for ClNO 2 on the following day. The maximum ClNO 2 concentration in this campaign of 1.6 ppbv was observed in September during the early hours of the morning (03:00 UTC). The analysis of the origin of air masses by calculations of back trajectories shows that mixing ratios of ClNO 2 , NO 2 , and O 3 were higher in regional air masses than in air masses that traveled a long distance.
A case study analyzing measurements at night from 21 to 22 August 2019 shows that the stratification of layers during the night can strongly impact observed trace gas concentrations, specifically when the sampling point of the inlet system was located within a height range that was characterized by poor vertical mixing of the air. During most times of the campaign, however, the sampling point was isolated from the surface layer during the night. In this case, losses of trace gases to the surface and reactions with fresh emissions on the ground, which would typically reduce ClNO 2 production, were not important.
The ClNO 2 production efficiency (i.e., the number of ClNO 2 molecules formed per produced NO 3 molecule) was higher for conditions in air masses from regional areas than from long-range transportation, mostly due to the higher NO 2 mixing ratios. The minimum average value of the production efficiency calculated for the individual measurement periods in the JULIAC campaign was 3 % and was experienced in December for all air masses independent from their origin. This low value can be attributed to the low NO 2 mixing ratios experienced in winter. For the air masses from long-range transportation, the mean ClNO 2 production efficiencies were in the range of 3 % to 6 % in the period between August and November but were as high as 12 % in February, consistent with the seasonality of the observed ClNO 2 concentrations. The highest mean ClNO 2 production efficiency was found in February, when values reached 18 ± 9 % and NO 2 concentrations were highest in the regional air masses. High ClNO 2 production efficiency was also found in September when NO 2 concentrations were low, suggesting that other factors including the available aerosol surface area (S a ), the variability in the N 2 O 5 uptake coefficient, and the yield of ClNO 2 in the heterogeneous reaction of N 2 O 5 were favoring the production of ClNO 2 .
With the help of a simple box model of nighttime chemistry for the NO 3 -N 2 O 5 -ClNO 2 system, the dependence of ClNO 2 concentration on the availability of O 3 and NO 2 was investigated. The purpose of such a simplified model is to demonstrate the general feature of ClNO 2 production versus chemical conditions but not to compare with observations. The model results suggest that ClNO 2 production was more sensitive to the availability of NO 2 than that of O 3 , especially for the air masses from long-range transportation. The seasonal variability in ClNO 2 is less pronounced compared to the seasonal changes in NO 2 and O 3 concentrations because changes in the NO 2 and O 3 concentrations partly compensated for each other. The simple model cannot predict the seasonal changes in the observed ClNO 2 mixing ratios. This indicates that processes other than the NO 3 production rate significantly impacted the ClNO 2 mixing ratios. Nevertheless, this simple model approach helps us to understand the general features of the dependence of ClNO 2 concentrations on the availability of NO 2 and O 3 in the JULIAC campaign. Data availability. The data used in this study are available from the Jülich DATA platform (https://doi.org/10.26165/JUELICH-DATA/XG6YGZ; Tan et al., 2022).
Author contributions. AH designed and organized the JULIAC campaign together with HF and FH. ZT and RS performed the measurements of ClNO 2 and analyzed the data. ZT, RS, HF, and AH wrote the paper. All co-authors contributed with data and commented on and discussed the paper and contributed to the writing of this work.
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.