Aircraft vertical profiles during summertime regional and Saharan dust scenarios over the north-western Mediterranean basin: aerosol optical and physical properties
Accurate measurements of the horizontal and vertical distribution of atmospheric aerosol particle optical properties are key for a better understanding of their impact on the climate. Here we present the results of a measurement campaign based on instrumented flights over north-eastern Spain. We measured vertical profiles of size-segregated atmospheric particulate matter (PM) mass concentrations and multi-wavelength scattering and absorption coefficients in the western Mediterranean basin (WMB). The campaign took place during typical summer conditions, characterized by the development of a vertical multi-layer structure, under both summer regional pollution episodes (REGs) and Saharan dust events (SDEs). REG patterns in the region form under high insolation and scarce precipitation in summer, favouring layering of highly aged fine-PM strata in the lower few The REG scenario prevailed during the entire measurement campaign. Additionally, African dust outbreaks and plumes from northern African wildfires influenced the study area. The vertical profiles of climate-relevant intensive optical parameters such as single-scattering albedo (SSA); the asymmetry parameter (g); scattering, absorption and SSA Ångström exponents (SAE, AAE and SSAAE); and PM mass scattering and absorption cross sections (MSC and MAC) were derived from the measurements. Moreover, we compared the aircraft measurements with those performed at two GAW–ACTRIS (Global Atmosphere Watch–Aerosol, Clouds and Trace Gases) surface measurement stations located in north-eastern Spain, namely Montseny (MSY; regional background) and Montsec d'Ares (MSA; remote site).
Airborne in situ measurements and ceilometer ground-based remote measurements identified aerosol air masses at altitudes up to more than 3.5 The vertical profiles of the optical properties markedly changed according to the prevailing atmospheric scenarios. During SDE the SAE was low along the profiles, reaching values < 1.0 in the dust layers. Correspondingly, SSAAE was negative, and AAE reached values up to 2.0–2.5, as a consequence of the UV absorption increased by the presence of the coarse dust particles. During REG, the SAE increased to > 2.0, and the asymmetry parameter g was rather low (0.5–0.6) due to the prevalence of fine PM, which was characterized by an AAE close to 1.0, suggesting a fossil fuel combustion origin. During REG, some of the layers featured larger AAE (> 1.5), relatively low SSA at 525 nm (< 0.85) and high MSC (> 9 m2 g−1) and were associated with the influence of PM from wildfires. Overall, the SSA and MSC near the ground ranged around 0.85 and 3 m2 g−1, respectively, and increased at higher altitudes, reaching values above 0.95 and up to 9 m2 g−1. The PM, MSC and MAC were on average larger during REG compared to SDE due to the larger scattering and absorption efficiency of fine PM compared with dust. The SSA and MSC had quite similar vertical profiles and often both increased with height indicating the progressive shift toward PM with a larger scattering efficiency with altitude.
This study contributes to our understanding of regional-aerosol vertical distribution and optical properties in the WMB, and the results will be useful for improving future climate projections and remote sensing or satellite retrieval algorithms.
Atmospheric aerosol particles play an important role in Earth's radiative balance directly by scattering and absorbing solar radiation and indirectly by acting as cloud condensation nuclei (Myhre et al., 2013). Globally, the aerosol particles' direct radiative effect is negative at the top of the atmosphere due to their net cooling on Earth's atmosphere system (Myhre et al., 2013). This estimation is, however, affected by a large uncertainty which reflects the large spatial and temporal variability of the optical, physical and chemical properties of optically active atmospheric aerosol particles (Myhre et al., 2013). This variability is largely due to the wide variety of aerosol sources and sinks, their intermittent nature and spatial non-uniformity together with the chemical and physical transformations that aerosol particles undergo in the atmosphere (Myhre et al., 2013). These variables affect the scattering and absorption properties of atmospheric particles and consequently their radiative properties. Thus, uncertainties remain regarding the effects that aerosol particles exert on climate from local to global scales, and a detailed characterization of their properties in the horizontal and vertical dimensions is needed (Andrews et al., 2011; Bond et al., 2013; Haywood et al., 1999; Collaud Coen et al., 2013). Accurate knowledge of their radiative forcing will improve both the climate reanalysis and forecasting models, which are needed in the current climate change context (Myhre et al., 2013). The in situ surface distribution of atmospheric particles and their physical and chemical properties is determined through an array of networks across the US and Europe and to a lesser extent in Asia and Africa (Laj et al., 2020), such as the Global Atmosphere Watch (GAW, World Meteorological Organization); the European Research Infrastructure for the observation of Aerosol, Clouds and Trace Gases (ACTRIS; http://www.actris.eu, last access: 7 January 2021); the Interagency Monitoring of Protected Visual Environments (IMPROVE; http://vista.cira.colostate.edu/Improve/, last access: 7 January 2021); the European Monitoring and Evaluation Programme (EMEP, http://www.Emep.int, last access: 7 January 2021); and the NOAA Federated Aerosol Network (NFAN; Andrews et al., 2019). These networks provide detailed optical, physical and chemical properties of atmospheric aerosol particles at the surface (Putaud et al., 2004, 2010; Andrews et al., 2011; Asmi et al., 2013; Collaud Coen et al., 2013, 2020; Cavalli et al., 2016; Zanatta et al., 2016; Pandolfi et al., 2018; Laj et al., 2020).
Given that the radiative forcing by aerosols is produced in the whole atmospheric column, the study of the vertical distribution of aerosol particles and their properties is of great importance (Sheridan et al., 2012; Samset et al., 2013). In fact, uncertainties regarding their vertical distribution and its relationship with surface emission sources are still a subject of intensive research. For example, Sanroma et al. (2010) suggested that, during cloud-free conditions, high-altitude aerosol particles are the major contributor to variations in solar radiation flux reaching the surface, at least at the high-altitude sites they studied. Moreover, the positive radiative forcing associated with strongly absorbing particles, such as black carbon (BC), is amplified when these particles are located above clouds (Zarzycki and Bond, 2010, and references therein), and the sign and magnitude of semi-direct BC effects depend on the BC location relative to the clouds and cloud type (Bond et al., 2013), with different clouds differently impacting the atmospheric heating rate of different aerosol types (Ferrero et al., 2020).
Ground-based remote sensing measurements of aerosol particles' optical and physical properties are performed by a number of projects, such as AERONET (AErosol RObotic NETwork; https://aeronet.gsfc.nasa.gov, last access: 7 January 2021), which is the international federation of ground-based sun and sky scanning radiometers and the European Aerosol Research Lidar Network (EARLINET–ACTRIS, https://www.earlinet.org, last access: 7 January 2021), providing column-integrated and vertically resolved optical properties, respectively. Satellite and sun/sky photometer measurements provide information on the aerosol properties of the entire atmospheric column, top-down and bottom-up, respectively. Polar-orbiting satellite observations provide a wide spatial coverage yet are limited in time resolution to once or twice a day. On the other hand, laser-based active instruments such as lidars (light detection and ranging) and ceilometers provide reliable information of the vertically resolved optical properties of aerosols, such as backscattering and extinction. Lidars measure at several wavelengths (e.g. Raman-elastic lidars; Ansmann et al., 1992), whereas ceilometers are usually limited to one wavelength.
The aforementioned remote sensing methods have thus limitations for directly measuring the vertically resolved distribution of specific climate-relevant optical parameters or variables such as SSA, the asymmetry parameter (g) or absorption coefficients. Although not as frequent, airborne measurements can provide the vertical profiles and horizontal variability of these parameters, as well as of other aerosol-related patterns. Instrumented flights are usually performed for specific campaigns, with a duration ranging from multiple weeks to a few years, allowing for determining aerosol properties up to heights of a few in the free troposphere. For example, Esteve et al. (2012) performed a campaign over Bondville (Illinois) aiming at comparing AERONET remote sensing measurements with measurements of aerosol properties, such as scattering, absorption and other derived variables from instrumented flights. In Asia, Clarke et al. (2002) measured aerosol particles' microphysical, optical and chemical properties over the Indian Ocean. Recently, Singh et al. (2019) measured particle size, number (N), spectral absorption and meteorology variables in different pollution layers along a Himalayan valley in Nepal by means of instrumented flights. Vertically resolved measurement campaigns have been performed with tethered balloons, for example in the Po valley (Ferrero et al., 2014); in the Arctic (Ferrero et al., 2016); and with unmanned aerial vehicles (UAVs), such as the ones over the eastern Mediterranean by Pikridas et al. (2019). Aircraft aerosol measurements over Europe were performed for example during the EUCAARI-LONGREX (European Integrated project on Aerosol Cloud Climate and Air Quality interactions Long Range Experiment) campaign as shown by Highwood et al. (2012), who presented the results of a closure study between measured vertical aerosol particles scattering and absorption and Mie theory. In North America, Sheridan et al. (2012) performed flights between 2 and 3 times per week during 3 consecutive years, measuring more than 400 vertical profiles of aerosol particles and trace gas concentrations. The vertical profiles of total and accumulation mode N concentration, BC mass concentration, lidar measurements and the estimated radiative aerosol effect during EUCAARI-LONGREX were presented by Hamburger et al. (2010), Groß et al. (2013) and Esteve et al. (2016). In the context of the ChArMEx/ADRIMED measurement campaign (the Chemistry-Aerosol Mediterranean Experiment/Aerosol Direct Radiative Impact on the regional climate in the MEDiterranean region; e.g. Mallet et al., 2016; Denjean et al., 2016) instrumented flights measuring physical and chemical properties took place. These measurement campaigns have demonstrated the usefulness of instrumented flights providing aerosol properties which cannot be measured with conventional remote sensing techniques. These vertically resolved aerosol measurements are restricted to the time span of the campaign as well as to the regional area where these take place. However, aircraft measurements might yield very relevant information for detailed radiative forcing studies and might be extremely useful for models aiming at simulating these effects over specific regions. Moreover, the results could be extrapolated to other periods when measurements are not available in the same area or to other areas with similar meteorological patterns and pollutant emissions.
Detailed studies of the vertical profiles of climate-relevant aerosol properties are especially important in climate-sensitive areas, such as the Mediterranean basin. This is one of the regions in the world characterized by high loads of both primary and secondary aerosol particles, especially in summer (Rodríguez et al., 2002; Dayan et al., 2017), from diverse emission sources. Anthropogenic emissions from road traffic, industry, agriculture and maritime shipping, among others, negatively affect the air quality in this region (Querol et al., 2009b; Amato et al., 2009; Pandolfi et al., 2014c). Moreover, the Mediterranean basin is also highly influenced by natural sources, such as mineral dust from African deserts and smoke from forest fires (Bergametti et al., 1989; Querol et al., 1998; Rodríguez et al., 2001; Lyamani et al., 2006; Mona et al., 2006; Koçak et al., 2007; Kalivitis et al., 2007; Querol et al., 2009b; Schauer et al., 2016; Ealo et al., 2016; Querol et al., 2019, among others). In addition to this, the distribution of the different types of aerosol particles in the Mediterranean basin is largely modulated by regional and large-scale circulation (Millán et al., 1997; Gangoiti et al., 2001; Kallos et al., 2007). The complex orography surrounding the WMB (western Mediterranean basin) sea and the high insolation, scarce precipitation and low winds during summertime give rise to high rates of accumulation and formation of secondary particles (Rodríguez et al., 2002). The north-east of Spain provides a frame of study that represents well the atmospheric summer conditions of the western and central Mediterranean, characterized by frequent and severe pollution episodes with high PM, UFP (ultra-fine particle) and O3 formation (Pey et al., 2013; Pandolfi et al., 2014a; Querol et al., 2017, among others). Typical atmospheric dynamics coupled to local orography results in local and regional vertical recirculation with a consequent accumulation of pollutants (Millán et al., 1997). Vertical recirculation and ageing of pollutants is favoured by weak gradient atmospheric conditions, scarce precipitation and continuous exposure to solar radiation driving photochemical reactions (Rodríguez et al., 2002; Pérez et al., 2004). This recirculation is very relevant in midsummer, when the solar radiation increases and the high-pressure periods last longer, so that the vertical recirculation reaches further inland and creates reservoir strata (loaded with pollutants) at 1–3 (Gangoiti et al., 2001; Pérez et al., 2004). In fact, due to the geography and climatic summer meteorological patterns, the formation of strong breezes from the coast through the valleys up to the Pyrenees and pre-Pyrenees range is frequent (Ripoll et al., 2014). Additionally, and especially in spring–summer, intense Saharan dust outbreaks (Querol et al., 1998, 2009b, 2019; Rodríguez et al., 2001; Escudero et al., 2007; Pey et al., 2013) and forest fires (Faustini et al., 2015) influence air quality over the WMB. The above atmospheric processes might coincide in space and time in the WMB and result in summer radiative forcing above this area being among the highest in the word (Lelieveld et al., 2002, and references therein). To the best of our knowledge, only a few in situ aircraft- or balloon-borne measurement campaigns aiming at studying the optical properties of tropospheric aerosol particles were performed in the WMB such as those performed within the ChArMEx/ADRIMED campaign (Denjean et al., 2016).
To better characterize the complex summer atmospheric scenarios of the WMB and to better understand their effect on the concentrations and optical properties of aerosols, we present here results from an aircraft measurement campaign performed in the north-western Mediterranean within the PRISMA project (aerosol optical properties and radiative forcing in the western Mediterranean as a function of chemical composition and sources). The main objective of the PRISMA project was to study the spatial and vertical distribution of the atmospheric aerosol particles with special interest in their physical and optical properties to assess the regional radiative forcing caused by the tropospheric aerosols in the WMB. To this end two measurement campaigns were performed in the summers of 2014 and 2015, combining aircraft measurements with remote and in situ surface measurements performed at the Montseny (MSY) and Montsec (MSA) stations. Herein we focus on the 2015 campaign, when vertical summer recirculation episodes, Saharan dust outbreaks and plumes from wildfires simultaneously affected air quality over the WMB. The combination of the aircraft measurements with the available surface in situ and remote measurements allowed for characterizing the summer recirculation coupled with Saharan dust outbreaks usually observed in the WMB in summer well. The results presented here provide a more exhaustive characterization of the aerosol layers than the one that can be obtained by deploying in situ surface and remote sensing techniques applied so far in the region.
In the following section (Sect. 2) we describe the methodology, with a deeper analysis of the study area, measurement stations and flight location as well as the main meteorological scenarios. In Sect. 3 we will explain the main calculations of aerosol optical properties. The main results obtained in this study are shown in Sect. 4 for the different meteorological scenarios for both surface and the vertical measurements. Finally, we discuss the obtained results in the conclusion (Sect. 5).
2.1 Area of study and meteorology
Airborne aerosol measurements were performed in an area of around 3500 km2 in the north-western Mediterranean area of Catalonia, north-eastern Spain (Fig. 1). The area is close to the Barcelona metropolitan area, where anthropogenic emissions, mostly from road traffic, industry, agriculture and maritime shipping (Barcelona is one of the major ports in the Mediterranean) negatively affect the air quality (Querol et al., 2001; Pey et al., 2013; Pérez et al., 2008; Amato et al., 2009, 2016; Reche et al., 2011, among others). Figure 1 shows the study area, the location of the Montseny (MSY; 720 ) and Montsec (MSA; 1570 ) measurement stations, and the location and ID codes (P1–P7) of the instrumented flights (Table 1).
This area is characterized by warm summers and temperate winters with irregular and rather scarce precipitation rates, especially in summer. The Azores high-pressure system plays an important role in the synoptic meteorology of the Iberian Peninsula (IP). In winter, the Azores anticyclone is located at lower latitudes, and so the IP is more influenced by low-pressure systems and the associated fronts coming from the North Atlantic. However, in summer, the anticyclonic system intensifies and moves toward higher latitudes inducing very weak pressure gradient conditions over the IP. These atmospheric stagnant conditions, coupled to local orography and sea breeze circulation, result in local and regional atmospheric dynamics that favour the accumulation and ageing of pollutants (Millán et al., 1997, 2002; Gangoiti et al., 2001; Rodríguez et al., 2002; Pérez et al., 2004, among others). The high surface temperatures give rise to the formation of the Iberian thermal low, which induces the convergence of surface winds from the coastal areas injecting polluted air masses into the middle troposphere (3.5–5 km height). During the daytime the sea breeze layer (up to 800 m high) is channelled into the coastal and pre-coastal valleys up to 90 km inland, transporting pollutants from the coastal area (Gangoiti et al., 2001). On the mountain and valley slopes, up-slope winds inject pollutants at higher levels. Sea breezes and up-slope winds over the coastal and pre-coastal mountains transport coastal pollutants inland, while a fraction of these pollutants is injected in their return flows aloft (2–3 km), forming high-pollution-loaded reservoir strata (Gangoiti et al., 2001). Pollutants are returned to the Mediterranean Sea owing to the prevalence of westerly winds above the mixing layer. Once in those upper layers, pollutants move back towards the sea, and compensatory subsidence creates stratified reservoir layers of aged pollutants. Then, the next morning the lowermost layers are drawn inland again by the sea breeze (Millán et al., 2002; Gangoiti et al., 2001).
Saharan dust outbreaks affect the Iberian Peninsula mostly in spring–summer, increasing the PM levels. The meteorological scenarios causing African dust transport over the study area are described in Rodríguez et al. (2001) and Escudero et al. (2005). Four main scenarios are differentiated: northern African high located at the surface level (NAH-S), Atlantic depression (AD), northern African depression (NAD) and northern African high located at upper levels (NAH-A). The WMB is mostly affected by the AD and NAD in spring and fall, by the NAH-A in summer, and by the NAH-S from January to March. Another potential significant source of PM affecting air quality in the WMB is wildfires, which might persist for several days and emit large amounts of primary PM and precursors of secondary aerosols (Faustini et al., 2015). In addition to the complex atmospheric patterns, the scarce precipitation and the high exposure to solar radiation drive photochemical reactions resulting in high background levels of secondary aerosols and ozone (Rodríguez et al., 2002; Pérez et al., 2004; Querol et al., 2016, 2017).
2.1.1 Detailed synoptic and mesoscale meteorological scenarios during flights
Airborne measurements of tropospheric aerosol particles physical properties were conducted during 7–8 and 14–16 July 2015 during the typical summer regional pollution episodes and aerosol layering (Gangoiti et al., 2001). HYSPLIT (HYbrid Single-Particle Lagrangian Integrated Trajectory model; Draxler and Hess, 1998) back trajectories in Fig. 2 (calculated for 7 and 16 July 2015; see more trajectories for the 8 and 14 July in Fig. S2) and the potential temperature vertical profile (Fig. S3) show that both periods were characterized by atmospheric stagnation (without major synoptic flows venting the WMB). Under these summer atmospheric scenarios sea breezes, and the vertical recirculation of air masses develop. However, during the first period an African dust outbreak affected the study area (Fig. 2), probably by high-altitude transport from northern Africa and subsequent impact on surface by convective circulations over the continent. Moreover, plumes from wildfires reached also the study area in the second period as the smoke forecast from NAAPS indicated (Navy Aerosol Analysis and Prediction System; http://www.nrlmry.navy.mil/aerosol, last access: 7 January 2021; see Fig. 2).
The geopotential height at 500 hPa and surface pressure from the ERA-INTERIM reanalysis model (https://www.ecmwf.int/en/forecasts/datasets/reanalysis-datasets/era-interim, last access: 7 January 2021) show for the first day of the measurements a high-pressure system covering central Europe (Figs. 3 and S1 in the Supplement). On 7 July (coincident with the first measurements), the Azores high-pressure system and a northern European low governed the synoptic flow. This situation persisted until 16 July, with an enhancement of the Iberian and northern African thermal lows (Fig. 3).
Thus, during the campaign, the atmospheric scenario is the typical one favouring stagnation in the WMB, which leads to the recirculations of vertical air masses driven by local and regional processes (Gangoiti et al., 2001). Furthermore, the north-eastern African high pressure at high atmospheric levels (NAH-A; Escudero et al., 2005) favoured the advection of Saharan dust at high altitudes to the area of study from noon on 4 July to the afternoon of 8 July 2015. We will refer to this first period as the SDE (Saharan dust event) period, in reference to the Saharan dust event that persisted during these days. On 14 and 16 July, smoke from wildfires over northern Africa and the IP affected the study area. During this second period there was no mineral dust on 14 July, while on 16 July a light dust outbreak took place (Fig. 2). Due to the prevalence of summer regional pollution episodes with the absence of a dominant strong Saharan dust event, we will refer to this second measurement period as an REG (regional pollution episode).
2.2 Measurements and instrumentation
2.2.1 Ground supersites and measurements
Surface measurements were performed at Montseny (MSY, regional background) and Montsec (MSA, continental background) monitoring supersites (north-eastern Spain). MSY (41∘46′46′′ N, 02∘21′29′′ E, 720 ) is located in a densely forested area, 50 km to the north–north-east of Barcelona and 25 km from the Mediterranean coast. MSA (42∘03′05′′ N, 00∘43′46′′ E, 1570 ) is located in a remote high-altitude emplacement in the southern side of the pre-Pyrenees at the Montsec d'Ares mountain range, at 140 km to the north-west of Barcelona and 140 km to the west-north-west of MSY (Fig. 1). Detailed descriptions of the measurement supersites and of the measurements performed can be found for example in Pérez et al. (2008), Pey et al. (2009) and Pandolfi et al. (2011, 2014a, 2016) for MSY and Pandolfi et al. (2014b), Ripoll et al. (2014) and Ealo et al. (2016, 2018) for MSA. These supersites are part of the Catalonian Air Quality Monitoring Network and are part of ACTRIS and GAW networks. Aerosol optical properties at the sites were measured following standard network protocols (WMO/GAW, 2016).
Similar instruments were used for in situ surface characterization of physical, chemical and optical aerosol particle properties at both MSY and MSA. Aerosol particle total scattering (σsp) and hemispheric backscattering (σbsp) coefficients were measured every 5 min at three wavelengths (450, 525 and 635 nm) with an LED-based integrating nephelometer (Aurora 3000, Ecotech Pty, Ltd, Knoxfield, Australia). Calibration of the two nephelometers was performed four times per year using CO2 as span gas, while zero adjusts were performed once per day using internally filtered particle-free air. The RH (relative humidity) threshold was set by using a processor-controlled automatic heater inside the Aurora 3000 nephelometer to ensure a sampling RH of less than 40 % (GAW, 2016). σsp coefficients were corrected for non-ideal illumination of the light source and for truncation of the sensing volumes following the procedure described in Müller et al. (2011b). Aerosol light absorption coefficients (σap) at seven different wavelengths (370, 470, 520, 590, 660, 880 and 950 nm) were obtained every 1 min at both stations by means of aethalometers (Magee Scientific AE33) with filter loading being corrected online by the dual-spot manufacturer correction (Drinovec et al., 2015). At both supersites a multi-angle absorption photometer (MAAP – Multi Angle Absorption Photometer, Model 5012, Thermo, Inc., USA; Petzold and Schönlinner, 2004) was also used for obtaining the aerosol light absorption coefficient. MAAP data in this work were reported at 637 nm by multiplying the MAAP absorption data by a factor of 1.05 as suggested by Müller et al. (2011a). At both sites the instruments were connected to a PM10 cut-off inlet. Online surface in situ optical measurements were reported to ambient temperature (T) and pressure (P) using measurements from automatic and co-located weather stations.
PM mass concentrations were obtained with an optical particle counter (OPC) (Grimm 1108.8.80) connected to an individual inlet. Particle number volume concentrations were measured every 5 min in 15 size bins from 0.3 to 20 µm and then converted to PM mass concentration by the instrument software. PM mass concentrations were corrected by comparison with standard gravimetric PM measurements (Alastuey et al., 2011). An Aerosol Chemical Speciation Monitor (ACSM, Aerodyne Research Inc.) was used to measure real-time non-refractory submicron aerosol species (organic matter, nitrate, sulfate, ammonium and chloride). Measurements with the ACSM at MSY were available from 4 to 12 July.
PM10, PM2.5 and PM1 24 h samples were daily collected on 150 mm quartz microfibre filters (Pallflex 2500 QAT-UP and Whatman QM-H) using high-volume samplers (DIGITEL DH80 and/or MCV CAV-A/MSb at 30 m3 h−1). The daily concentrations of major and trace elements and soluble ions (determined following the procedure by Querol et al., 2001), as well as those of organic (OC) and elemental (EC) carbon (by a thermal–optical carbon analyser, Sunset Laboratory Inc., following the EU project EUSAAR2 (European Supersites for Atmospheric Aerosol Research) protocol Cavalli et al., 2010), were measured during the whole campaign. The ratio between the fine, PM1, and coarse, PM10, mode is obtained as the fraction between these two concentration measurements, PM1∕10. The chemical analyses allowed for the determination of around 50 PM components, accounting for 75 %–85 % of the PM mass, the unexplained PM mass being mostly due to unaccounted moisture and non-analysed heteroatoms.
Active remote sensing measurements of attenuated backscatter (βatt) at 1064 nm were performed at MSA with a Jenoptik CHM 15k Nimbus (G. Lufft Mess- und Regeltechnik GmbH, Germany) ceilometer. The instrument operated continuously with a temporal and spatial resolution of 1 min and 15 m, respectively. The maximum height of the signal is 15.36 Calibration based on the Rayleigh calibration method was applied (Bucholtz, 1995; Wiegner et al., 2014). The overlap between the laser pulse and telescope field of views of the CHM 15k is greater than 60 % at around 500 (Martucci et al., 2010; Pandolfi et al., 2013). Further details of the ceilometer installed at MSA can be found in Titos et al. (2017). Passive remote sensing measurements were obtained at MSA by means of a CE-318 sun/sky photometer (Cimel Electronique, France) included in AERONET.
2.2.2 Airborne measurements
Flights were performed with a Piper PA 34 Seneca aircraft (Fig. 4) over north-eastern Spain (Fig. 1) from around 0.5 up to 3.5 Both the upward and downward flights had approximately the same duration (20–30 min) (Table 1), and the ascent and descent trajectories were performed in the same area when possible. The method used to perform the vertical profiles consisted of vertical ascensions and descents following helical trajectories (Font et al., 2008), thus allowing for the measurement of the aerosol particles properties around a more constrained area. The turns during the vertical helical motions were made with a radius large enough (around 900 m) to assume that the particles entered straight into the inlet. The flights were performed at a speed of around 160 km h−1 with a vertical speed of 152 m min−1, slightly larger for the downwards flights. However, some losses may arise due to the perturbation of the flow by the aircraft during the sampling, the change in the pitch angle of the aircraft due to the fuel load variation and ascending vs. descending vertical motion. For most of the cases, the up and down profiles were similar, showing therefore the representativeness of the measured profiles and a minimum interference of the aircraft emissions and turbulence. Whether to present an upward or a downward vertical profile was decided based on which of the two had better data availability and vertical resolution.
During the flights, an external volume flow controller (IONER PFC-6020) was connected to the nephelometer in order to assure a constant sampling flow (5 L min−1). Similarly to the in situ surface measurements, the scattering measurements were performed at RH < 40 % (GAW, 2016). During the SDE period the vertical profiles of scattering were collected using the Kalman filter available in the Aurora 3000 nephelometers, whereas during the REG period vertical profiles of this filter were switched off, and the raw σsp and σBsp coefficients were collected. As shown later, the Kalman filter had the effect of smoothing the measured scattering and hemispheric backscattering coefficients.
Aerosol light absorption coefficient measurements at seven different wavelengths (370 to 950 nm) were performed with the AE33 aethalometer (Magee Scientific AE33, model AE33 AVIO). The AE33 AVIO is a modified prototype, based on the AE33 aethalometer which was re-designed for aircraft measurements. The measurement and operational principle is identical to the commercial AE33 (Drinovec et al., 2015), but the AE33 AVIO model deploys a more powerful internal pump to ensure a constant flow (4 L min−1) with changing pressure. Aethalometer measurements were performed at a 1 s resolution.
Particulate matter (PM) mass concentration was obtained using an aerosol optical particle counter (OPC) (GRIMM Spectrometer, model 1129-Sky-OPC). Particle number concentration was measured in 31 size bins at 6 s and at a flow rate of 1.2 L min−1, for particles with a size diameter from 0.25 to 32 µm. The software instrument provides PM mass concentration, which is calculated assuming a constant particle density. Total particle number concentration was measured at 1 s by means of a water-base condensation particle counter (TSI EPC, model 3788) at a flow rate of 0.6 L min−1. The instrument provides size range down to 5 nm and measured concentration range up to 2.5 × 105 N cm−3.
Temperature (T) and relative humidity (RH) inlet sample air was measured at 15 s with a Rotronic HL-RC-B wireless logger. This is a passive sensor, so no flow regulator was needed to pass the air through the sensor. A Vaisala DRYCAP® dew-point transmitter, model DMT143 was used to measure dew point and water volume concentration of outdoor ambient air at 10 s via inlet 2. Ambient air was drawn out at 10 s and at a flow rate of 2 L min−1. An external pump with a flow regulator was connected to the Vaisala sensor in order to maintain a constant flow. Pressure (P) data were obtained by means of a Kestrel 4000 anemometer. All the aerosol data were converted to T and P sample air conditions.
The inlet (Fig. 4), manufactured by Aerosol d.o.o. (https://mageesci.com, last access: 7 January 2021), was designed to be close to isokinetic at a flight speed of 160 km h−1, thus minimizing the inlet losses. The inlet flow was set to 10 L min−1. It was mounted around 5 cm from the fuselage just where the cockpit changes its shape. It was placed around 1.5 m away in front of the leading edge of the wing and 2.5 m away from the propeller in the back of the wing. In order to determine aerosol sampling efficiency and particle transport losses we used the Particle Loss Calculator (PLC) software tool (von der Weiden et al., 2009). The results (not shown) indicated that the losses at the inlet were minimal for PM2.5 and that the losses inside the sampling system were large for dust particles larger than around 4–5 µm. To further confirm the PLC results, we compared the PMx measurements at the MSA station with the PMx aircraft measurements performed at the same altitude of MSA during the closest flight to MSA at a distance of 10 km. This flight (P1; 7 July 2015; Fig. 1) was performed during a Saharan dust outbreak; thus the presence of dust particles in the atmosphere was significant. Table S1 in the Supplement shows that differences were low, around 6 % for PM1 and 12 % for PM2.5 with the aircraft underestimating the measurements at MSA. However, the PM10 aircraft measurements were around 47 % lower compared to the PM10 measurements performed at MSA, thus confirming the PLC results. Therefore, the inlet losses for particles other than dust were minimal. In fact, Table S1 shows that for scattering and absorption measurements (which were performed in the PM10 fraction at MSA) the differences were < 9 % and < 16 %, respectively, because of the high scattering efficiency of fine particles compared to coarse particles (e.g. Malm and Hand, 2007) and because the absorbing fraction is mostly contained in the fine aerosol particle mode.
The optical aerosol particle characterization was performed measuring the extensive optical properties (σap, σsp and σBsp) and calculating the intensive optical properties for both in situ surface and aircraft-borne measurements. The intensive optical properties (reported below) are mass-independent properties which were determined starting from the multi-wavelength measurements of extensive properties. The intensive properties strongly depend on the physicochemical aerosol properties. Hereafter there is a brief description of the calculated intensive optical properties and the equations used to derive them:
The scattering Ångström exponent (SAE) depends on the physical properties of aerosols and mostly on the particle size. SAE values lower than 1 are associated with the presence of coarse particles, whereas SAE values > 1.5 indicate the presence of fine particles (Seinfeld and Pandis, 1998; Schuster et al., 2006). The SAE was calculated as linear fit in a log–log space using the scattering measurements at the three wavelengths.
The asymmetry parameter (g) represents the probability of radiation being scattered in a given direction. The range of values is for backward (180∘) to forward (0∘) scattering, respectively. A value of around 0.7 is employed in the climate models (Ogren et al., 2006). The g was calculated from the backscatter fractions (BFs) using the semi-empirical formula provided by Andrews et al. (2006).
The absorption Ångström exponent (AAE) depends mostly on the chemical composition of sample particles. For pure BC, typical AAE values range from 0.9 to 1.1 (Kirchstetter et al., 2004; Petzold et al., 2013). When brown carbon (BrC) or mineral dust are sampled together with BC, the AAE increases because both BrC and dust can efficiently absorb radiation in the ultraviolet and blue region of the spectrum compared to the near-infrared (IR) (Kirchstetter et al., 2004; Chen and Bond, 2010). The AAE was calculated as a linear estimation in the log–log space using the multi-wavelength absorption measurements from AE33. For the vertical profiles reported here, the AAE was calculated using the AE33 wavelengths for which the absorption measurements were positive along the profile. For most profiles, except for P3, which had all seven wavelengths available, the AAE was calculated from 370 to 590 nm.
The single-scattering albedo (SSA) reported here was calculated as the ratio between the scattering and the extinction coefficients at 525 nm. SSA indicates the potential of aerosols for cooling or warming the atmosphere.
The single-scattering albedo Ångström exponent (SSAAE) was calculated by fitting the SSA retrieved at the same Aethalometer wavelengths used to calculate the AAE. For this, the SSA was obtained by extrapolating the total scattering to the AE33 wavelengths using the calculated SAE. SSAAE is a good indicator for the presence of coarse particles (e.g. dust) when values are < 0 (Collaud Coen et al., 2004; Ealo et al., 2016).
The mass scattering cross section (MSC) is the ratio between the scattering and the PM concentration. It represents the scattering efficiency of the collected particles per unit of mass.
The mass absorption cross section (MAC) is the ratio between the light absorption and the PM concentration. It represents the absorption efficiency of the collected particles per unit of mass.
4.1 MSA and MSY in situ measurements
The time evolution of PM1, PM10 concentrations, PM1∕10 ratios, BC, PM components (as measured by ACSM at MSY), σap, σsp, SAE, AAE, g and SSA measured at MSY and MSA during the first 3 weeks of July 2015 is presented in Fig. 5 together with the concentrations of major species (, , , EC, OM (organic matter; with an OM∕OC ratio of 2.1), mineral matter (MM; calculated as the sum of typical mineral oxides) and sea salt (SS; Na + Cl)) from offline analysis of 24 h filters collected at MSY and MSA during the days of the instrumented flights. Table 2 shows the mean values of surface PM1, PM10, PM1∕10, σsp 525 nm, σap 637 nm, SAE, AAE, SSA and g measured at the MSY and MSA stations on 7, 8 and 14–16 July compared to the mean values typically measured during SDE and REG pollution episodes as reported by Pandolfi et al. (2014b) and Ealo et al. (2016).
As shown in Fig. 5 an accumulation of pollutants took place from 4 to 8 July, as evidenced by the gradual increase of concentrations of , BC, OA (organic aerosol), PM, total scattering and absorption coefficients. This accumulation was favoured by the regional stagnation and vertical recirculation of the air masses. Moreover, a Saharan dust outbreak caused a progressive increase of PM10 at both stations, as well as a simultaneous PM1∕10 ratio decrease (Fig. 5c and d). The dust event had a larger impact at MSA, where the PM10 levels increased sharply and were higher compared to MSY. As reported in Table 2 and in Fig. 5, starting from 6 July, the PM10 concentrations were higher compared to average PM10 usually measured during Saharan dust outbreaks at both stations. Then, the levels of pollutants, as well as the total scattering and absorption coefficients, decreased on 9 July due to the venting of the basin by an Atlantic north-western (ANW) advection (not shown) that cleansed the northern area of the IP (Gangoiti et al., 2006). This decrease was again sharper at MSA than at MSY due to the location of MSA at the top of a high mountain (Figs. 5c, d and S5). After this event, a new regional pollution episode occurred which favoured again the accumulation of pollutants until the end of the campaign. Furthermore, according to NAAPS modelling outputs, relatively high levels of smoke loads occurred in the air masses affecting the study area on 14–16 July 2015 (Fig. 2).
The intensive optical properties, i.e. SAE (Fig. 5g), AAE (Fig. 5h), g (525 nm; Fig. 5i) and SSA (525 nm; Fig. 5j), showed values consistent with the accumulation process and with the occurrence of the coarse Saharan dust particles, as well as the effects of the wildfires occurring in the IP. The SAE progressively decreased at both stations from values > 1.5–2.0 (indicating the predominance of fine particles) on 4 July to values < 1.0 (indicating the predominance of coarse particles) on 8 July 2015. The variability of g was less pronounced compared to the variability of the SAE, especially at MSA, likely because of the lower sensitivity of the g parameter to coarse PM compared to SAE (Pandolfi et al., 2018). The AAE was considerably > 1.0 at both sites, reaching values > 1.5. The high AAE was due to enhanced UV absorption, which typically is observed when brown carbon (BrC) and/or mineral dust particles are present in the atmosphere (Kirchstetter et al., 2004; Fialho et al., 2005; Sandradewi et al., 2008; Alastuey et al., 2011; Chen and Bond, 2010). Interestingly, the AAE measured in the whole column with the sun photometer over MSA showed even larger values, up to 2.5, until the evening of 8 July. The cleansing effect of the ANW on 9 July caused a reduction of the PM loads and consequently of the measured scattering and absorption coefficients at both sites. During this ANW flow the SAE increased again to values of 1.5–2.0, whereas both the surface and column-integrated AAE decreased due to the removal of dust by the ANW cleansing effect. As already mentioned, after the ANW advection, another regional pollution episode developed until the end of the campaign.
In the following sections, we present a detailed description and interpretation of the evolution of pollutants and aerosol optical parameters measured at MSY and MSA during the SDE and REG period. The mean values of the considered pollutants and optical parameters during airborne measurements are reported in Table 2, together with the mean values typically registered during SDE outbreaks and REG episodes.
4.1.1 Saharan dust event period, SDE
The attenuated backscatter from the ceilometer at MSA allowed for identifying the occurrence of aerosol layers up to 5 (i.e. 5.8 ) in this period (Fig. 6). The air masses featured significant dust concentrations which were probably further accumulated in the region by the regional vertical recirculation of air masses. Correspondingly, the PM10 mass concentrations measured at MSY and MSA were higher compared to the PM10 concentrations usually measured in dust outbreaks (Table 2). Mineral matter concentrations during these days (Fig. 5b) reached 21 and 15 µg m−3 at MSA and MSY, respectively. The OA occurred in very similar concentrations at both sites (∼7 µg m−3). Daily concentrations of and EC from filters were higher in the regional background (MSY) compared to the continental one (MSA) due to the larger impact of regional sources such as industries and road traffic and the emissions from maritime shipping from the Mediterranean Sea and the port of Barcelona. As expected, concentrations were rather low at both sites due to the thermal instability of nitrate in summer (Harrison and Pio, 1983; Querol et al., 2001, 2004, 2009a).
Figure 5a shows that the evolution of the concentration at the MSY station, as recorded by the ACSM, was similar to that of BC, both reaching a maximum on the evening of 7 July, with two subsequent minor peaks at midnight and on the evening of 8 July (Fig. 5). The peak just after midnight, at 00:00 UTC on 8 July, was also reflected in the OA, and concentrations. At MSA, ACSM measurements were not available; however the measured absorption showed a progressive increase on 8 July with a relative maximum being reached in the afternoon (Fig. 5d), when AAE at MSA reached values > 2.0 (Fig. 5). This sharp increase in BC was attributed to local biomass burning emissions (Fig. 2). During this first measurement period, the mean scattering and absorption coefficients at both sites (Table 2) were above the averaged values registered at the MSA and MSY stations during dust and summer regional pollution events (Pandolfi et al., 2014b). Figure 5e also shows the high AOD from the MSA sun/sky photometer during the SDE period.
Table 2 shows that during this period the intensive parameters SAE, AAE, SSA and g reached values similar to the typical coarse-PM-influenced ones recorded during dust outbreaks at both stations (Pandolfi et al., 2014b). As already pointed above, on the afternoon of 8 July a change due to local biomass burning emissions was observed in the optical aerosol properties at MSA compared to MSY. As a consequence, the SAE and AAE at MSA increased to values > 1.5 and 2.0, respectively.
4.1.2 Regional pollution episode, REG
An REG episode developed during the second aircraft measurement period leading to the accumulation of atmospheric aerosols in the area. A wildfire outbreak from northern Africa also took place (Fig. 2), as well as a light dust outbreak during 16 July (Figs. 2 and 5). The REG episode resulted in the development of aerosol layers at high altitude, as also observed with the ceilometer at MSA (Fig. 6c and d). PM10 concentrations were rather constant and quite similar at both MSA and MSY but on average lower than during the SDE period. Only on 16 July, PM10 concentrations at MSA, due to the impact of the dust outbreak at the altitude of the MSA station, were closer to an SDE scenario rather than an REG scenario (Table 2). This pattern was also reflected in the high PM1∕10 ratio measured from 10 July with the exception of the afternoon of 16 July at MSA when the PM1∕10 ratio was lower. The lower impact of the dust outbreak during these days compared to the first period was confirmed by the markedly lower MM from PM speciation analysis (Fig. 5b). Despite the higher MM at MSA, those of the remaining PM10 components and BC were similar at both sites.
The scattering (Fig. 5e) and absorption coefficients (Fig. 5f) at both sites were above the average values (Table 2) presented by Pandolfi et al. (2014a) and Ealo et al. (2016) for REG episodes, due to the strong accumulation of pollutants which took place from 10 July onward for this particular REG episode. AOD (Fig. 5e) during REG was rather low when compared to the SDE period due to the absence of dust, with the exception of 16 July, when AOD increased simultaneously with the light dust outbreak and probably the influence of wildfire pollution plumes.
The asymmetry parameter g showed similar values to those observed during the SDE period at both sites and did not change much during the dust event on 16 July because, as already observed, g is less sensitive to variations of coarse-mode aerosols. Consequently, the relatively lower SAE on this day (especially visible at MSY) suggested variations in the larger end of the accumulation mode particles and above rather than in the lower end of the mode. The lower SAE at MSY compared to MSA during REG (and especially during 16 July) was then probably due to a relative reduction of PM1 at MSY compared to the previous days, whereas PM10 kept similar values (Fig. 5) yet lower compared to the SDE period despite the light SDE event registered on 16 July (Table 2). Moreover, the higher relevance of fine PM at MSA compared to the MSY regional background could also explain the observed difference. This could be due to a combination of factors including a higher exposure of the MSA station to the fine PM from the wildfires, the lower impact of local and regional sources at MSA, and the larger segregation of particles during transport toward MSA due to its remote location. During REG, AAE decreased compared to the first period (especially at MSA), yet this was still > 1.0, indicating a mixing of regional aerosols with BrC and mineral dust. AAE of the whole column (sun/sky photometer data) was also close or slightly > 1.0. Finally, the SSA varied only slightly between REG and SDE at both sites.
4.2 In situ vertical profiles
Here we focus on the vertical profiles obtained by means of airborne measurements during the two distinct SDE and REG scenarios. Vertical profiles of optical extensive and intensive properties, as well as PM concentrations for upward and downward flights, are reported in Table 1. Our objective is to analyse the vertical-profile variation of these properties and their diurnal and spatial evolution and how these properties varied across layers in the troposphere. When possible, direct comparison with the surface data measured at the MSA station was made.
As reported above, the comparison of airborne measurements at 1.5 with in situ surface measurements at MSA for P1 reached a good agreement (Table S1), with a relative difference < 10 % for PM1 and PM2.5 concentrations and the extensive and intensive optical properties. The large underestimation of PM2.5−10, missing −47 % in the airborne measurements, is the reason for excluding the PM10 fraction from the vertical profiles. Consequently, we calculated the MSC and the MAC for PM2.5.
4.2.1 Saharan dust event, SDE
Figure 6a and b shows a clear atmospheric layering of pollutants from 0.8 to 5.0 , i.e. 1.6 to 5.8 The magenta boxes in Fig. 6a and b highlight the time window when flights were performed. Figure 7 shows the three vertical profiles during the SDE period (Table 1, namely: P1 (Fig. 7a) and P2 (Fig. 7b), which were performed close to the MSA station (Fig. 1), and P3 (Fig. 7c), which was performed over the Catalan pre-coastal mountain range (Fig. 1). We can observe from Fig. 7 that during the P1 and P3 flights the PM1 and PM2.5 concentrations were rather high in the upper atmosphere (4–12 and 7–17 µg m−3 for PM1 and PM2.5, respectively, above 2.5 ). At lower altitudes (< 1.5 ) even higher PM concentrations were measured (10–16 and 16–22 µg m−3 for PM1 and PM2.5, respectively) which were on the upper range of the typical surface concentrations reported in Ealo et al. (2016) and Pandolfi et al. (2014b) for SDE scenarios in the area. The vertical profiles of PM during P1 and P2 showed a progressive upwards reduction of PM concentrations, especially evident above 2.5 in P2 (Figs. 6 and 7). The vertical profiles of scattering and absorption coefficients showed similar patterns to the ones described for PM with an upward decrease. As already stated, the use of the Kalman filter in the nephelometer measurements of P1, P2 and P3 had a smoothing effect on the measured scattering coefficient, thus complicating a direct comparison with PM during these profiles.
The PM1∕2.5 ratio (Fig. 7) during P1 ranged from around 0.6 to 0.75 along the profile with a relative minimum between 2.5 and 3 , where the SAE reached its lowest values (< 1). Conversely, a clear increase of the PM1∕2.5 ratio above 2.5 was evident for P2, when the ratio reached 0.8. The values of both SSAAE and SAE were consistent with the PM1∕2.5 ratio found for the different layers in P1 and P2. The SAE during P1 and P2 ranged between 0.8 and 1.5, and the SSAAE kept negative values along both profiles with a pronounced minimum at the 3.0 layer during P1, highlighting a higher relative fraction of coarse particles attributed to the dust outbreak over the area of study. It should be noted that a direct comparison between the vertical profiles of PM1∕2.5 and SAE was difficult because of the Kalman filter, which smoothed the calculated intensive aerosol particles' scattering properties and made the comparison difficult, especially for g, which involves both the smoothed scattering and the hemispheric backscattering coefficients. For this reason, the g was not reported in Fig. 7. During P1 the AAE ranged between around 1.7 and 2.5 with the highest values measured above 2.5 as a consequence of the presence of UV-absorbing dust particles in the atmosphere. During P2, the AAE showed more constant values (around 2) with altitude, mirroring the less variable SAE compared to P1. Both SSA and MSC showed increasing values with altitude during P1 and P2 ranging between 0.85–0.9 and 2–4 m2 g−1, respectively, whereas the MAC (at 525 nm) kept rather constant values (around 0.2 m2 g−1) with altitude with slightly lower values above 2.0–2.5
Figure 7c shows the vertical profile P3, which was consistent with P1 and P2, even if the calculated intensive optical properties suggested a reduced effect of dust particles during P3 compared to P1 and P2. PM concentrations during P3 were similar to P2 profile, although the PM1∕2.5 ratio was higher, indicating an increased importance of the fine aerosol mode during P3 compared to P2. The scattering and absorption coefficients were similar to the values measured during P1 and P2, although the scattering was higher during P3. The intensive optical properties of P3 indicated the predominance of coarse dust particles especially around 1.7 and 2.3 , where the SAE decreased up to values close to 1 and the SSAAE was negative. In this altitude range the AAE was on average higher compared to the rest of the profile and especially around 1.8 , where it reached a value of 2.5. As already noted, the observed AAE increase at these altitudes was due to the UV absorption from dust particles. Overall, during P3 the intensive properties such as SAE, AAE and SSA showed more variability with altitude compared to P1 and P2 as also reported by the ceilometer measurements, which showed a more stratified atmosphere on 8 July (P3) compared to 7 July (P1 and P2; Fig. 6a and b).
During P1, P2 and P3, the AAE varied considerably with altitude and ranged between 1.5 and 2.5 depending on the flight and altitude. These values were higher than those measured in situ at the MSA and MSY stations, as shown in Fig. 5, and were higher compared to the typical AAE values measured during SDE at these stations (Table 2). The lower AAE measured at the MSA and MSY stations compared to the AAE in the free troposphere measured during P1, P2 and P3 was due to the increased relative importance of BC particles close to the ground and within the PBL (planetary boundary layer; estimated from the observation of the pollutant concentrations, the ceilometer profiles and the meteorological conditions: potential temperature in Fig. S3), which reduced the AAE at the two measurement stations compared to the values obtained with the flights in the free troposphere. The UV absorption properties of African dust observed during P1, P2 and P3 and the corresponding increase of AAE were driven by the presence of iron oxides, such as hematite and goethite, which efficiently absorb radiation at shorter wavelengths (e.g. Alfaro et al., 2004). The obtained PM2.5 MAC values (around 0.2–0.25 m2 g−1) observed in the dust layers during P1, P2 and P3 were consistent with the MAC values, around 0.24 m2 g−1, recently reported for dust particles by Drinovec et al. (2020).
For the P1, P2 and P3 profiles both SSA and MSC progressively increased with altitude (Fig. 7). SSA in P1, P2 and P3 was rather similar and ranged from 0.83 to 0.93 from 1.5 to 3.5 Higher SSA at higher altitudes was due to different factors including the progressive reduction of the relative importance of BC particles with altitude and the presence of more efficient scatterers at higher altitudes, together with the presence of dust, as evidenced by the higher MSC and lower MAC. The MSC during the three flights ranged from around 2 m2 g−1 at 1.5 to 3–4 m2 g−1 at 3.5 Pandolfi et al. (2014b) reported an MSC of PM2.5 at the MSA station of 3.3 ± 1.9, which was consistent with what was observed with airborne measurements at the MSA altitude (around 1.5 ). Pandolfi et al. (2014b) also showed that on average the highest MSC values at MSA were observed in summer, mostly because of aerosol ageing and the formation of efficient scatterers, such as secondary particles and OA during summer regional pollution episodes. In the area under study OA is expected to be mostly secondary organic aerosols (SOAs) (e.g. Querol et al., 2017). Recently, Obiso et al. (2017) assessed the sensitivity of simulated MSC of MM, OA and by perturbing particle microphysical properties, such as the size distribution, refractive index, mass density and shape. Perturbations were performed by changing by ± 20 % the widely used OPAC (optical properties of aerosols and clouds; Hess et al., 1998) reference values. (Obiso et al., 2017) compared the simulated MSC with the experimental MSC of PM and different PM components determined at the MSY station. High MSC, up to 4–5 m2 g−1, was simulated by Obiso et al. (2017) for OAs and , and both were more sensitive to perturbations in the refractive index than to variations in the size distribution. Lower MSC was reported by the same study for MM (0.5–2 m2 g−1), and it was found to be more sensitive to perturbations of the size distribution of dust particles compared to other particle properties. Ealo et al. (2018) calculated the MSC for different pollutant sources retrieved by applying the positive matrix factorization (PMF) model on PM10 chemically speciated data collected at the MSA station. Ealo et al. (2018) found that the MSC changed considerably depending on the sources considered, being the highest for secondary and the lowest for sources such as MM and SS (both mostly associated with coarse particles) and for anthropogenic sources, such as traffic or industry (also emitting less efficient scattering particles such as BC). Thus, the observed increase of MSC with altitude could be due to the relative increase of and OA particles, causing important changes in the refractive indexes and size distributions with altitude. These changes could be related to the ageing of the particles, which is expected to be larger for particles at higher altitudes.
4.2.2 Regional pollution episode, REG
Figure 8 shows the vertical profiles P4, P5, P6 and P7 over the MSY station and the Catalan pre-coastal mountain range (Fig. 1 and Table 1). The vertical profile of the attenuated backscatter from the ceilometer (Fig. 6) showed layering of aerosol with altitude for this period. As detailed below, the observed aerosol layers probably originated mostly from the vertical recirculation of air masses during summer regional pollution episodes (Gangoiti et al., 2001). Moreover, a PM outbreak from wildfire plumes during this period and a dust outbreak on 16 July were also detected (Fig. 2).
In the P4 profiles, the PM concentrations, scattering and absorption coefficients reached higher values below the 1.5. layer (i.e. within the PBL where most of the pollutants generated at ground were trapped) and decreased with altitude. The high PM1∕2.5 ratio ( > 0.95) for altitudes > 1.5. demonstrated the prevalence of fine particles in the troposphere compared to the PBL. Accordingly, along the profile, SAE was high (1.5–2.7), indicating the predominance of fine particles, and SSAAE was positive, indicating the absence of dust particles. Correspondingly, the asymmetry parameter g decreased with altitude above 1.5. down to 0.5, confirming the progressive shift toward smaller particles with altitude and an increased effect of particles in the lower end of the accumulation mode. Notable was the decrease of SAE (below 1.5) and SSAAE (close to 0) and the corresponding increase of g (up to 0.8), at around 3.3 , during P4, indicating the presence of coarse particles at this height. AAE kept values between 0.8 and 1.2 along the whole P4 profile, suggesting the lack of strong UV absorbers (such as BrC or mineral dust) and the prevalence of absorbing BC particles from fossil fuel combustion (e.g. Bond et al., 2004; Zotter et al., 2017). Furthermore, the MAC showed higher variability compared to P1, P2 and P3 profiles reaching values up to 0.3, suggesting a relative increasing importance of BC particles in the troposphere compared to P1, P2 and P3. As already observed during the SDE period, both SSA and PM2.5 MSC increased with altitude, especially above 2 , suggesting the presence of efficient scatterers at these altitudes. Note that, as observed during the first period of measurements, the MSC at 1.5 (2–3 m2 g−1) was consistent with the typical MSC recorded at MSA (Pandolfi et al., 2014b). At higher altitudes the MSC reached values close to 5 m2 g−1 with SSA around 0.95.
Profile P5 (Fig. 8b) was obtained 1 h after P4, and the distance between the two profiles was about 55 km (Table 1 and Fig. 1). The main differences between P4 and P5 were the consistently higher total scattering and absorption coefficients and PM concentrations at all heights during P5 compared to P4 and the presence of two layers at 2 and 3 along P5. As in P4, PM concentrations in P5 were dominated by the fine mode (a PM1∕2.5 > 0.9), as confirmed by a high SAE (> 1.75); a positive SSAAE along the profile; and rather low g values which decreased to 0.5 at 2
The absorption coefficient during P5 was dominated by BC particles from fossil fuel combustion up to 2 km a.s.l with AAE values around 1.0 or lower below 2 and with SSA and MSC reaching the lowest values around 0.7 and 1, respectively, at 2 , indicating the predominance of absorbing BC particles at this altitude. From this layer upwards, SAE remained rather constant (1.8–2-2), whereas g, SSA, AAE and MSC progressively increased with altitude. Again, the increase of g with altitude could be indicative of variations of particle size with altitude and a progressive shift toward particles in the lower end of the accumulation mode. Particles in this size range are efficient scatterers at the nephelometer wavelengths, thus explaining the larger MSC. These results together with the progressive increase of AAE and positive SSAAE suggested the presence of fine BrC particles in the free troposphere probably from wildfire smoke as also shown by modelling outputs in Fig. 2. The presence of a clear separated layer at around 2.5–3 was also shown by ceilometer measurements (Fig. 6c).
The P6 profile Fig. 8c was obtained close to P5 (4 km distance) on 16 July (2 d after P4 and P5; Table 1). Scattering and absorption coefficients and PM concentrations were higher compared to P5 as a consequence of the progressive accumulation of particles in the area due to the development of the regional pollution episode. This hypothesis was also supported by the higher aerosol load and layering in the troposphere compared to 14 July according the ceilometer measurements (Fig. 6). Both scattering coefficient and PM concentrations decreased above the PBL (estimated to be at 1.75 ), with a subsequent increase at higher altitudes where these variables kept rather constant values close to those observed within the PBL. Conversely, the absorption coefficient did not increase above the PBL, and, consequently, the SSA increased (up to 0.93–0.97) in the free troposphere compared to the SSA values obtained within the PBL. The MSC showed a similar profile to SSA reaching values around 3.5–5.0 m2 g−1, whereas the MAC decreased with altitude above the PBL. The relative abundance of fine particles during P6 was also supported by SAE values around 1.75 and low g values around 0.5–0.6 and a positive SSAAE along the whole profile. The AAE ranged between 0.8 and 1.2, indicating that the absorption was dominated by BC particles.
The profile P7 was obtained around 30 min after P6 and at a distance of around 60 km from P6 and about 5 km from P4. Scattering and absorption coefficients and PM concentrations from P7 were rather similar to P6. The scattering and absorption coefficients in the green spectrum and PM1 concentrations within the PBL (below 1.75 ) reached 50, 5 Mm−1 and 20 µg m−3, respectively. As for P6, scattering, absorption and PM decreased above the PBL and then increased again in the free troposphere, with a relative maximum at 2.0–2.5 , followed by a further increase with height, up to 3.5
Again, PM1∕2.5 (0.95), SAE (1.75–2.0), a positive SSAAE and g (0.5–0.6) indicated the prevalence of fine particles in the free troposphere above the PBL during P7. As observed during the previous flights, SSA and MSC had very similar profiles. In P7, two peaks were observed at 1.8 and 2.5 , with a marked minimum at 2.2 The similarity of SSA and MSC profiles is attributed to the relative high proportion of non-absorbing particles compared to the absorbing particles (high SSA) and the high scattering efficiency of the sampled particles. These two SSA and MSC peaks were also simultaneous with a slight increase of AAE indicating an aerosol mixture with BrC particles. These AAE–SSA–MSC parallel profiles were persistent for the whole REG period. The 1.8 peak was coincident with a reduction of scattering, absorption and PM concentrations just above the PBL and could be associated with the vertical diffusion along the day of a layer which, as shown in Fig. 6d, at 00:00 UTC on 16 July was at 2 The lower SSA, MSC and AAE at 2.2 were coincident with a relative increase of scattering, absorption and PM concentrations and indicated the presence of a layer with a larger relative proportion of BC particles. From there upwards, the subsequent observed layer can be associated with the one at 3 at midnight. If we consider also the ground MSA data (Fig. 5) and those from P6, the first of these two layers can be associated with reservoir strata (a recirculating layer according to Gangoiti et al., 2001) above the PBL, which, as day progressed and the convective dynamics intensified, was then integrated into the PBL. Conversely, the largest layer can be related to an outbreak of light mineral dust and smoke from wildfire plumes affecting the PBL (and the MSA station) later in the day. This was supported by the high albedo, with SSA > 0.9 across the whole profile and increasing with height. The AAE was close to 1.0 for the whole profile, with peaks up to 1.5 where the PM concentration was at the lowest concentrations. This could be caused by a higher relative concentration of more brownish, aged and not very fine black particles, which was related to reservoir strata, produced by the vertical recirculation of air masses, with lower SAE and higher g, SSA and MSC.
We reported on the results of an aircraft measurement campaign aiming at studying the vertical profiles of physical properties (size-segregated PM mass concentration and multi-wavelength scattering and absorption coefficients) of atmospheric particles in the western Mediterranean basin (WMB). Seven vertical profiles following helical trajectories were obtained on 7–16 July 2015 over an area of 3500 km2 in north-eastern Spain. The measurement campaign was carried out under typical summer regional pollution scenarios, with vertical recirculation of air masses that cause interlayering of polluted layers in the first few (Gangoiti et al., 2001). These aged aerosol-rich layers are driven by complex atmospheric dynamics, driven by the summer atmospheric stagnation, high insolation, low precipitation and intricate orography surrounding the WMB. We measured during two regional pollution episodes, and these already complex scenarios were also affected by two African dust outbreaks and long-range transported plumes of wildfires. The summer regional pollution episodes finished by venting the polluted air masses by synoptic western and northwestern flows, a frequent occurrence in the WMB (Gangoiti et al., 2001, 2006).
We measured vertical profiles of PM1 and PM10 concentrations and a set of climate-relevant aerosol optical parameters – single-scattering albedo (SSA), asymmetry parameter (g), scattering and absorption Ångström exponents (SAE and AAE), and PM mass scattering cross section (MSC). These intensive optical properties depend on the microphysical and chemical properties of atmospheric aerosol particles rather than on their mass and are key input parameters in climate models. Simultaneous in situ surface measurements performed at two monitoring supersites in the region (Montseny, MSY, regional background, 720 ; Montsec, MSA, remote, 1570 ) were also used to better characterize the aerosol particles sampled during the instrumented flights.
Ceilometer profiles indicated the occurrence of aerosol layers over the region up to more than 5 , and ground measurements indicated that mean PM1 and PM10 mass concentrations and the scattering and absorption coefficients were similar or even higher than the typical ones obtained in the region during summer regional pollution episodes and African dust outbreaks.
During all flights, PM concentrations, scattering and absorption were high up to around 3.5 (maximum altitude reached by the aircraft), detecting the regional layering of aerosol-rich strata at these altitudes. The first measurement period was affected by an African air mass outbreak with dust particles mixed with vertically recirculated regional aerosols, whereas during the second period, the typical summer regional pollution episode and the advected wildfire smoke plumes dominated over the area under study. The measured optical properties were distinctively affected by these two different scenarios. During the dust outbreaks, SAE was rather low along the profiles, < 1.0 in the high-dust loaded layers, where AAE increased up to 2.0–2.5, as a consequence of the high UV absorption enhanced by the presence of coarser dust particles. During the regional pollution dominated scenario, SAE reached higher values (> 2), and g asymmetry parameter was rather low (0.5–0.6), in this case due to the prevalence of fine primary and secondary particles, mostly from regional anthropogenic emissions and the favourable conditions for secondary aerosol formation (high insolation, relative stagnation and high biogenic emissions, among others). Furthermore, the vertical variation of AAE was not large, with values close to 1.0 (pointing to a high proportion of fossil fuel combustion aerosols), with the exception of few layers with increased AAE, probably associated with the influence of wildfire-related aerosols. MSC was on average higher during the regional pollution episodes compared to the dust outbreaks due to the higher scattering efficiency of fine particles with a diameter closer to the wavelength of the sampling visible light compared to coarse particles. Overall, MSC increased with altitude (2 m2 g−1 near the surface up to 4–5 m2 g−1 in the upper levels) as the presence of more efficient scatterers increases. A previous modelling study on MSC constrained with experimental measurements performed at the MSY stations suggested that the observed high MSC at higher altitudes might be due to the predominance of fine organic (mostly secondary) and inorganic (mostly sulfate in summer) aerosols. The MSC and SSA vertical profiles were rather similar during the flights with the SSA also increasing with altitude and with a vertical variability that depended on the composition of the observed layers. Typical SSA values along the profiles ranged between 0.85 (near surface) and 0.95 (higher altitudes), with a minimum of < 0.85 in polluted layers where smoke from wildfires was probably present.
The results presented here provide a unique input for climate models aiming at studying the regional radiative and climate effects of atmospheric aerosol particles in the WMB. We presented robust vertically resolved measurements of intensive aerosol particles optical properties in the WMB troposphere where the well-known particle layering driven by the regional pollution episodes accompanied by vertical recirculation takes place especially in summer. We have shown that the distribution of aerosol particles and their optical properties vary vertically along the layers formed during several days under the typical high-PM summer regional pollution regime, as well as by the strength of the advection of aerosol particles such as dust and smoke.
The data used in this study are available from the corresponding authors upon request.
The supplement related to this article is available online at: https://doi.org/10.5194/acp-21-431-2021-supplement.
AA designed the research experiment; MP, NP, ME, GT and AA performed the instrumented flights and maintained the in situ measurement stations. GM designed the inlet and helped with the instrument settings on the aircraft. ME and GT extracted the data from the instruments as well as prepared the datasets. AA, MP and XQ played a crucial role in the processes of shaping the paper structure as well as helping with the data analysis. JYD developed the data process, analysed the results, and summarized and expressed them in this article. All authors provided advice regarding the paper structure and content and contributed to the writing of the final draft of the paper.
The authors declare that they have no conflict of interest. Griša Močnik was, at the time of the aircraft campaign but not during the data analysis or paper writing, employed by the manufacturer of the Aethalometer AE33.
Marco Pandolfi is funded by a Ramón y Cajal Fellowship (grant no. RYC-2013-14036) awarded by the Spanish Ministry of Economy, Industry and Competitiveness. Gloria Titos is funded by MINECO under the Juan de la Cierva postdoctoral programme (grant nos. FJCI-2014-20819 and IJCI-2016-29838). We would also like to acknowledge Yolanda Sola for providing access to the sun/sky photometer data at the MSA station and to Aerosol d.o.o. for lending the AVIO aethalometer. The authors gratefully acknowledge the NOAA Air Resources Laboratory (ARL) for the provision of the HYSPLIT transport and dispersion model (https://www.ready.noaa.gov/HYSPLIT.php, last access: 7 January 2021) used in this publication.
This research has been supported by the Generalitat de Catalunya, Agència de Gestió d'Ajuts Universitaris i de Recerca (grant nos. AGAUR 2014 SGR33 and AGAUR 2017 SGR41); the Ministerio de Economía, Industria y Competitividad, Gobierno de España (HOUSE; grant no. CGL2016-78594-R); and the European Commission's Horizon 2020 Framework Programme (ACTRIS-2; grant no. 654109).
We acknowledge support of the publication fee by the CSIC Open Access Publication Support Initiative through its Unit of Information Resources for Research (URICI).
This paper was edited by Michael Schulz and reviewed by two anonymous referees.
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