Ultrafine particles (UFPs) are distributed highly unevenly in the lower troposphere. Although these UFPs are positively detectable and have been studied for more than a century, their three-dimensional distribution, formation, and budget in the atmosphere remain largely uncertain, despite their obvious climate relevance. This is due to their short lifetime and the fact that they are invisible to the human eye and to remote sensing techniques. From the moment of their emission or generation, their spatial distribution is a result of meteorological processes, regional-scale transport, local thermal convection, and rapid loss by interaction with clouds as cloud condensation nuclei. Here, we report about three-dimensional airborne in situ studies aimed at investigating UFP sources, distribution, and behavior on different spatial and temporal scales. We identified fossil fuel–burning power stations, refineries, and smelters as major anthropogenic UFP sources. On a regional scale, their emissions are significantly higher than urban emissions. Particle emissions from such power stations are released typically at altitudes between 200 and 300 m AGL. Detailed in situ measurements of particle concentration and related parameters, together with meteorological measurements and analyses, enable reliable source attribution even over several hundred kilometers downwind from the emitter. Comprehensive meteorological analysis is required to understand the highly variable 3D concentration patterns generated by advective transport and thermal convection. Knowledge of primary emission strength, together with size distributions and atmospheric 3D transport of UFPs derived from airborne measurements, makes it possible to estimate the aerosols’ impact on meteorology, hydrological cycles, and climate.
A decade of airborne regional-scale measurements of aerosol size distributions and meteorological parameters allows apportionment of major sources and budget estimates for ultrafine particles.
Ultrafine particles (UFPs) in the atmosphere (diameter <100 nm) have a major impact on the environment through a wide variety of processes. They provide reaction surfaces for heterogeneous chemical processes in the atmosphere or can act as cloud condensation nuclei (CCN). While fine particles (>100 nm) interact directly with shortwave radiation, UFPs do not. Yet UFPs affect short- and longwave radiation indirectly, by way of their interactions with cloud microphysics. Once UFPs reach sizes larger than 40 nm, they effectively contribute to CCN (Twomey 1977; Andreae 2009; Ma et al. 2016), which then can enhance the number of cloud droplets at the expense of cloud droplet size (Rosenfeld et al. 2008; Leaitch et al. 2010; Junkermann et al. 2009). Subsequent changes in cloud brightness and lifetime are well established (Twomey 1974; Albrecht 1989). These effects have even been proposed as a potentially exploitable physical process for geoengineering (Latham et al. 2008). Yet the concurrent reduction of cloud droplet size modes may have unwanted side effects, such as changes of the distribution and intensity of rainfall on a larger scale (Rosenfeld 2000; Teller and Levin 2006; Teller et al. 2012; Junkermann et al. 2011b; Fan et al. 2018) that, in turn, affects the hydrological cycle (Bister and Kulmala 2011; Riuttanen et al. 2016).
Techniques for the detection of UFPs, condensation particle counters (CPC), were developed more than a hundred years ago by Coulier (1875) and Aitken (1889). Since then, UFPs have been measured in polluted urban and industrial environments, as well as in remote locations. For a historic review, see Mohnen and Hidy (2010). For airborne applications, Bigg and Turvey (1978) and Ayers et al. (1979) used continuously recording counters (Pollak and Metnieks 1959) with comparatively low (∼1 min) time resolution, but size detection limits were already similar to today’s sensors, reaching well into the <10-nm range (Hogan et al. 1981).
The relative scales of number concentrations reported over more than a century have not changed much (Aitken 1894; Landsberg 1938; Went 1964, 1966). Burning of fossil fuel, vehicular traffic, and industry emissions always dominated the UFP number concentrations [see Aitken (1894) and Landsberg (1938) for early reviews; Bigg and Turvey (1978) for characteristic concentrations of remote maritime and continental areas and city plumes in Australia in the early 1970s]. In the first decades of the twentieth century, number concentrations in cities were reported to be very high (Landsberg 1938) but later decreased as a result of emission control measures, from values of >106 to about 105 cm–3 in current urban environments (Bae et al. 2010). Traffic is now considered to be the main urban source for UFPs (Paasonen et al. 2016; Rönkkö et al. 2017).
Although UFP concentrations are normally far lower in rural regions than in urban or industrial areas, number concentration magnitudes comparable to urban roadside levels have been detected even in very remote areas over the last three decades. Typically these are associated with short-duration particle burst events (Kulmala et al. 2004). During such events, which are classified in the recent literature as new particle formation (NPF), number concentrations increase rapidly by an order of magnitude within less than an hour during mid- to late morning hours. Initially, tiny particles appear in the smaller size bins of particle spectrometers [scanning mobility particle sizer (SMPS)] (∼5–20 nm). Subsequent shifts by a few nanometers per hour indicate particle growth, while number concentrations are decreasing (Kulmala and Kerminen 2008; Kulmala et al. 2013; Tröstl et al. 2016). This process, resulting in “banana”-shaped patterns in diurnal size distribution plots, is typically observed under sunny meteorological conditions (Baranizadeh et al. 2014) and more often in spring than in summer (Dal Maso et al. 2005). Nighttime events were occasionally reported with growth less significant than during the day or not occurring at all (Suni et al. 2008). Such events have not been reported in the literature before 1990 but are now observed even at remote locations, such as Arctic and Antarctic regions (Kontkanen et al. 2017; Heintzenberg et al. 2017).
Kiang et al. (1973), Kulmala et al. (2013), and Petäjä et al. (2016) suggested that atmospheric gas-to-particle conversion (GPC), the formation of H2SO4 from photochemical sulfur dioxide oxidation via hydroxide (OH) radicals, would be a key process for the production of initial aerosol clusters. These would then react with ammonia and/or amines via ternary nucleation. Subsequent particle growth could then be related to organic compounds, such as extremely low-volatility organic compounds (ELVOC), emitted from the biosphere (Ehn et al. 2014; Dall’Osto et al. 2018). A contribution of ELVOC is in agreement with the observation of UFP growth over mild to moderately polluted mid-European forested areas (Kulmala et al. 2004; Held et al. 2004). However, it is interesting to note that the frequency of observations does not follow the annual patterns of biogenic emissions. It also remains unclear where and what the source of H2SO4 would be.
When compared to anthropogenic emissions from power stations, biogenic emissions typically have far lower spatial and temporal variability of the source strength and usually exhibit a considerably more homogeneous distribution. Also, characteristic UFP burst events are not common in “clean” forested areas over Australia and the Amazon that are clearly dominated by biogenic emissions (Junkermann et al. 2009; Junkermann and Hacker 2015; Fan et al. 2018; Andreae et al. 2018). Other recent observations of pronounced horizontal (on scales of less than 50 km) and vertical UFP variability, UFP layers just at the top of the PBL, and size distributions with a clear nucleation mode at about 5–10 nm but lower number concentrations below 5 nm cannot be explained by biogenic emissions (Ma and Birmili 2015; Crippa et al. 2012; Crumeyrolle et al. 2010; Schobesberger et al. 2013; Väänänen et al. 2016; Heintzenberg et al. 2007; Kulmala et al. 2013). Anthropogenic UFPs from elevated stack emissions transported by horizontal advection and vertical convection processes do not only fit these UFP scenarios better than NPF but can also offer an explanation for their increased occurrence within the last decades.
This paper attempts to corroborate this notion based on airborne measurements of UFPs using highly flexible, well-instrumented aircraft together with meteorological observations and transport model analysis.
Connecting the short-duration UFP events with meteorological convective vertical transport and horizontal advection requires a reliable method of source apportionment and characterization of relevant transport mechanisms. Attempts at such source apportionment of UFP production in the lower troposphere have been made ever since particle instrumentation became available at the end of the nineteenth century (Aitken 1894). Aircraft-based measurements, coordinated with ground observations, were used recently in several projects: Quantification of Aerosol Nucleation in the European Boundary Layer (QUEST; Laaksonen et al. 2005, 2008), European Integrated Project on Aerosol Cloud Climate and Air Quality Interactions (EUCAARI; Kulmala et al. 2011; Schobesberger et al. 2013), and Biogenic Aerosols—Effects on Clouds and Climate (BAECC; Väänänen et al. 2016; Petäjä et al. 2016). However, even after these detailed international field studies, the sources and budgets of anthropogenic ultrafine aerosols remain highly uncertain (Dall’Osto et al. 2018).
In our studies, based on detailed airborne observations using small and slow-flying instrumented aircraft, we were able to characterize major UFP sources, their quantitative contribution to the total budget of UFPs, and how local nucleation mode particle appearance may be linked to elevated particle sources via meteorological processes. We hypothesize that particles attributable to flue-gas-cleaning efforts, established since the late 1980s, have resulted in a substantial increase in primary nucleation size mode particles and are now a major contribution to the anthropogenic budget of UFPs. This change in emissions may also be the relevant process to explain the worldwide increase of nucleation mode particles.
The present study is organized in two sections. First, we discuss the meteorology behind the three-dimensional transport within the time scales of UFP lifetime. Second, we describe selected experimental data confirming the horizontal and vertical aerosol patterns.
METEOROLOGY RELATED TO DIURNAL THREE-DIMENSIONAL UFP DISTRIBUTIONS.
Meteorological processes play a major role in the interpretation of the observed temporal and spatial patterns of UFPs. The typical emissions from elevated smoke stacks that form plumes with high UFP number concentrations offer opportunities for detailed case studies on the impact of meteorological transport phenomena on the three-dimensional distribution of UFPs. Both the lifetime of UFPs and their growth processes take place at similar time scales as regional-scale horizontal transport (i.e., between one and a few days). In contrast thereto, convective vertical transport occurs at time scales of less than 1 h and is rapid compared to aerosol aging processes (Georgii 1956; Stull 1988; Kulmala et al. 2013). Physical properties of the aerosol are thus preserved during vertical transport by thermal convection (Bigg et al. 1978) but may change during horizontal transport. Horizontal transport typically dominates during stable stratification of the lower atmosphere, at night or under daytime overcast conditions.
The emission of UFPs into the lower atmosphere from flue gas stacks (Junkermann et al. 2011a) typically takes place at heights of 200–400 m AGL, depending on stack height and excess flue gas temperatures. In daytime conditions, this release height puts the emissions well into the mid-PBL, with convective turbulence distributing the UFPs in both directions, down to the ground and up toward the cloud base. Elevated emission altitude with rapid vertical mixing (Buzorius et al. 2001; Wehner et al. 2010) typically leads to plumes reaching the ground at most by about ∼2–5 km downwind of the stack, with UFP concentrations subsequently diminished by dispersion and deposition losses. At nighttime, while wind speed usually decreases markedly in the surface layer, values of 5–10 m s–1 are still typical above the nocturnal inversion and can reach considerably higher values over large flat landscapes. Thus, during the night hours a high concentration layer of particles can form within the less turbulent residual layer (RL), containing remaining PBL air and fresh emissions injected above the nocturnal inversion layer of ∼100–150 m. Such conditions may extend over hundreds of kilometers, with little vertical mixing (Ayers et al. 1979; Junkermann et al. 2011b). Under clear or only low-cloud-cover conditions such nocturnal layering is broken up the next morning by thermal convection, and UFPs from far-distant elevated sources can reach the ground by fumigation. The highest concentrations close to the ground are thus often found about 30 min after thermal convection reaches the altitude of the UFP layer, and their location is strongly dependent on wind direction. It is not clear in what manner particles age during nighttime transport in the RL. However, as they are decoupled from fresh biogenic emissions and this layer is often drier than the PBL, growth would not always be expected and even shrinking may occur. This means that number concentrations are likely affected by coagulation and diffusion only. In either case, UFP transport to the ground depends on the strength of the thermal convection, which, in turn, depends on the energy input by solar radiation since sunrise, the strength of the inversion layer, and/or a preexisting haze or fine particle load within the surface layer that could reduce or suppress thermal convection. Convective dilution to higher altitudes, with increasing PBL height later in the day, accounts for a further decrease of particle number concentrations in the whole increasing volume of the PBL (Fig. 1). Once mixed with biogenic emissions, growth occurs as a result of agglomeration of volatile organic compounds (VOC; or ELVOC) (Ehn et al. 2014).
The observation that UFP burst events at field sites occur more frequently in spring than in summer (Dal Maso et al. 2005; Petäjä et al. 2016) is well in line with the more pronounced differences between air and surface temperatures in springtime, which offer more favorable conditions for thermal convective activity. During the summer months, the nocturnal inversion could be less pronounced because of the higher nighttime surface temperatures, but final mixing-layer depth and thus vertical dilution may be higher (Fig. 1).
EXPERIMENTAL SETUP AND OBSERVATION STRATEGY.
As the emission and modification of anthropogenically generated UFPs takes place in either the PBL or the lower free troposphere (FT) at local to regional scales, we used a highly versatile flying laboratory, with miniaturized state-of-the-art aerosol, air chemistry, and meteorology sensors (Table 1) mounted in instrumentation pods carried by aircraft capable of flying low and slow but also capable of climbing rapidly into the FT. The instruments, covering aerosols, air chemistry, and meteorology are listed in Table 2. For studies in Australia, the aerosol package was installed in the underwing pods of the Airborne Research Australia (ARA) motorized glider, which is already instrumented for (micro)meteorological measurements (Hacker and Crawford 1999; Hacker et al. 2016) (Fig. 2). Using slow-flying aircraft proved to be a well-matched approach to capturing the spatial scale of UFP events, as well as to achieve the desired spatial resolution given by the temporal resolution of the instrumentation. The comparatively slow-flying speed and simple installation in instrument pods with extremely short inlet lines (between 5 and 30 cm for the aerosol instruments) also helped to avoid sampling problems that are common in larger, faster, and often pressurized aircraft, where samples tend to be constrained to sizes >20 nm, owing to loss processes in the inlet lines (Andreae et al. 2018).
In our study, two aircraft were used, the Karlsruhe Institute of Technology (KIT) microlight (Junkermann 2001) and the ARA motorized glider (Junkermann and Hacker 2015). Typical cruising speed is 25 m s–1 for the microlight and 40 m s–1 for the motorized glider, resulting in a horizontal resolution of 1.5–2.4 km of sampling length for a complete UFP size distribution (2 min) and a 20–40-m resolution for the particle number concentration. Vertically, a 1-s resolution corresponds to less than 5-m altitude change. A real-time display of the sensor values in the cockpit allows immediate adjustment of the flight procedure. For instance, in case of a rapidly changing CPC signal, the aircraft can be held at constant altitude and approximate location until a full size distribution is completed. Overall, the instrumentation ensured a lower detection limit of below 5 nm, several size bins resolving the nucleation mode (<10 nm), and sufficient sensitivity to measure size distributions even in pristine environments.
An SMPS was used since 2006 for the measurement of the complete size distribution from 4.5 nm upward (Table 1) for the following reasons. Fresh gas-to-particle conversion particles (Mohnen and Lodge 1969; Kiang et al. 1973) grow slowly from cluster sizes (∼1 nm) into nucleation mode (>5 nm) (Kulmala et al. 2013). UFPs with a size of about 6–10 nm originating from atmospheric GPC (or NPF) should then already be a few hours old with those above 25 nm more than half a day (Kulmala et al. 2013). Direct primary emissions from anthropogenic sources, however, are emitted already in a nucleation size mode of ∼6–15 nm (Junkermann et al. 2011a; Brachert et al. 2013; Junkermann and Hacker 2015; see also Fig. 4) and contain only few particles below 5 nm. Size distributions containing both primary emissions and secondary GPC particles are characterized by a broader distribution, an aged Aitken mode, and increased numbers of particles in the lower-size bins. That way, from the shape and modes of the size distribution an approximate particle age can be derived and leads to a considerably more detailed picture than the initial twin CPC approach.
Flight patterns include initial vertical profiles extending from near the ground into the FT to define the height of the PBL, to detect UFPs in the lower FT, and to confirm that the PBL is well mixed and regional-scale (>300 km) horizontal patterns to identify and trace possible sources. Lagrangian flight patterns across plumes from several individual anthropogenic sources at different downwind distances were used to derive particle budgets and to investigate aerosol aging.
Long-distance survey flights in 2012 over Australia (distances of >3,500 km) and in 2012/14 over Germany (>2,000 km) were used to investigate the relative frequency of occurrence of anthropogenic particles, as well as any indications of potential contributions of biogenic-particle-related processes. Biogenic particles from atmospheric gas to particle conversion (nucleation) would be expected, for example, at low to midelevations of the PBL over VOC-emitting forest areas and most likely under sunny conditions (i.e., between midmorning to early afternoon hours). A search for biogenic UFPs would thus require flights between 1000 and 1500 local time and under at least partially sunny conditions (Baranizadeh et al. 2014). In contrast, anthropogenic primary emissions from continuously operating aerosol sources should be independent of the time of day. This notion was confirmed in Junkermann and Hacker (2015) for flights downwind of the 750-MW Kogan Creek power station in Queensland, Australia, over 1 h around sunset (SS) (takeoff 30 min before SS and landing 30 min after SS) and in the late morning the next day, with particle emissions of 3 × 1018 particles s–1 in both cases (Junkermann and Hacker 2015).
From an operational perspective, and to adjust and optimize flight strategy and flight patterns to the actual meteorological and environmental conditions, the real-time data display in the aircraft and visual clues observed by the scientist/pilots were essential decision-making tools. Having the freedom to fly the research aircraft mostly in noncontrolled airspace under visual flight rules (VFR) enabled rapid changes of the flight strategy in response to real-time observations. This flexibility, and the comparatively low flying altitude above ground, is usually not feasible for larger aircraft (Hamburger et al. 2012).
Results from multiple airborne campaigns flown since 1998 over various European countries as well as Australia and China (see Table 1) form the basis for the current study. The following paragraphs present key findings from these campaigns that are then combined to form a novel overall interpretation and explanation of the spatial and temporal UFP occurrence within the lower troposphere. For the campaigns C1 to C6 in Table 1, a twin CPC approach with different size cutoffs, 3 and 10 nm, was used to trace UFPs over regional-scale ranges of up to 150 km by 150 km and in the vertical from ∼10 to 3,000 m AGL. Local-scale (<5 km) UFP events were observed over individual coastal basins at the Irish west coast at Mace Head, Ireland (campaign C2), most likely attributable to biogenic sources (O’Dowd et al. 2007). High UFP concentrations over the boreal forests at Hyytiälä, Finland, in 2003 (campaign C4) and concurrent low concentrations over the embedded (ice covered) lakes in the area (O’Dowd et al. 2009) suggested a link between land surface properties, albedo, surface roughness, local biogenic emissions, and UFP spatial distribution. However, a clear source attribution was not successful with the limited instrumentation applied in these campaigns (O’Dowd et al. 2007, 2009; Laaksonen et al. 2008) (campaigns C2, C4, and C5). Anthropogenic sources of UFPs within the nucleation mode (4–10 nm) from fossil fuel burning were clearly identified for the first time as major emission in 2007 in a plume study downwind of the city of Karlsruhe, Germany. A coal-fired power station and a large refinery (REF) there dominated the city plume (Junkermann et al. 2011a; campaign C7). Similar industrial installations are located in the Italian Po Valley, a region that we investigated already in 2004 (campaign C5) without being able to identify the UFP sources. The conditions for atmospheric secondary particle formation were quite different from the boreal forest in Finland, with higher pollution levels and higher UV radiation but most likely less biogenic emissions over the agricultural land in early spring season. Also, the onset of UFP events was delayed until about noon with respect to Finland, despite the higher UV radiation levels (Hamed et al. 2007).
Using a more detailed Hybrid Single-Particle Lagrangian Integrated Trajectory model (HYSPLIT; Draxler and Rolph 2013) analysis for the case study of Laaksonen et al. (2005), the UFP events could be reassigned to a plume originating from the Mestre industrial complex in Italy about 6 h upwind under changing wind conditions.
In 2006/07 we were able to identify, for the first (and so far only) time, a local clearly non–fossil fuel source of nucleation mode particles in Western Australia (WA). Interestingly, these UFPs were found not above the forest but over the adjacent agricultural area with embedded salt lakes. These lakes were identified as the particle sources and attributable to a change in lake chemistry following deforestation decades ago (Junkermann et al. 2009; Kamilli et al. 2016) (campaigns C9 and C10). This remained the only case in about 1,200 flight hours spanning more than 15 years of our airborne research where a natural source significantly contributed to the regional budget of UFPs at a similar magnitude as anthropogenic sources. Similar to the missing nucleation mode particles in (above canopy) measurements over the Amazon (Fan et al. 2018; Andreae et al. 2018), we never found any signatures of atmospheric nucleation over the forested areas of Australia (Junkermann et al. 2009; Junkermann and Hacker 2015).
Enhanced UFP number concentrations were observed several times over the grasslands of Inner Mongolia (China) during a research project focusing on turbulent fluxes of energy and water vapor (campaign C8; Junkermann et al. 2011b). Because of legal limitations to import a radioactive source for the SMPS into China, it was only possible to use one CPC combined with sophisticated turbulence and meteorology instrumentation (Metzger et al. 2013). In one instance, while flying a 3 km by 5 km rectangular pattern at 500 m AGL, a local UFP event was observed under changing wind direction in a well-mixed boundary layer (up to 2,000 m AGL). A HYSPLIT analysis clearly related the origin of the plume to a power station at Xilinhot, China (see Fig. 3), 65 km to the north of the flight location. Over a 3-h period, the particle number concentration changed in response to this plume sweeping over the area because of a gradually backing wind direction. It increased from 1,000 cm–3 background to 40,000 cm–3 concurrently with a marked increase of surface temperature from 25° up to 45°C, well above the boundary layer temperature at 500 m of nearly constant ∼19°–20°C. The particle number concentration peaked after ∼90 min and then decreased again to background, displaying a signature very similar to UFP events observed in ground-based events elsewhere.
The most important overall finding for a better understanding of the observed patterns in UFP distributions was that, with the exception of Mace Head (O’Dowd et al. 2007) and Western Australia (Junkermann et al. 2009), all of our pronounced UFP event observations could without doubt be traced back to a limited number of large, modern, so-called clean, fossil fuel–burning sources, even in the presence of big-city plumes (Bonn et al. 2016). Most importantly, the magnitudes of these UFP events could not be explained plausibly without recognizing atmospheric advection to be the essential mechanism. It was possible to confirm this for every single case studied.
The location and technical description of most of these anthropogenic sources is well documented worldwide (http://endcoal.org/tracker). With a major nucleation mode between 5 and 15 nm and only minor particle concentrations in the lowest size bins, the size spectrum of the emitted particles matches the size distributions initially observed during ground-based UFP events well (Junkermann et al. 2011a, 2016; Junkermann and Hacker 2015).
Airborne aerosol studies in the seventies followed visible plumes for several hundreds of kilometers (Whitby et al. 1978; Pueschel and Van Valin 1978; Ayers et al. 1979; Hobbs et al. 1980). These plumes contained both fine and ultrafine particles and were thus simple to track. The invisible plumes of today, however, which lack significant number concentrations of visible fine particles but contain larger concentrations of UFPs, are more difficult to track but cover similar distances. In a similar approach to our investigations, but without using a size distribution measurement, Bigg and Turvey (1978) found enhanced particle number concentrations 160 km downwind of the city of Perth, speculatively at the time thought to be associated with urban and port emissions. In a later publication they recognized that the coal-fired Muja power station in Australia ∼180 km farther to the south may have contributed as a possible source to their measurements (Bigg et al. 2015). In the present study, the relevance of the Muja power station was confirmed for this case by HYSPLIT (not shown).
Figure 4 (top panel) shows two contrasting cases of power station emissions, observed in 2014 close to the Polish border (campaign C12), illustrating the impact of daytime versus nighttime meteorology and of clean versus polluted (hazy) PBL conditions, and the effects of horizontal transport and convective vertical mixing. The 8 Jun flight (yellow and brown bars), discussed in more detail in Junkermann et al. (2016), was flown in thermal convective conditions and moderate pollution. The 8 Jun data show two transects (south–north and north–south) under southwesterly winds and ∼1-h downwind advection time from the power stations along the Polish border, with emissions into a well-mixed turbulent boundary layer (up to 1,100 m AGL) and surface temperatures well above the threshold for thermal convection. A source strength of 1.5–2.5 × 1018 particles per second for both of the southern power stations was estimated, similar to the emission rates of the Karlsruhe power station (Junkermann et al. 2011a) or Kogan Creek, Queensland (Junkermann and Hacker 2015). On 10 Jun (gray and blue bars), under stable stratified conditions, the high PBL particle load suppressed most of the solar radiation reaching the ground, and surface temperatures accordingly stayed well below the threshold required for initiation of convection (Table 3). In the bottom panel of Fig. 4, the 10 Jun data are combined with 15-h HYSPLIT back trajectories for the planetary boundary and the early morning RL above 550 m between Dresden and Berlin, Germany. The flight altitude was changed several times to cover 1) a highly polluted hazy surface layer and 2) an approximately 400-m-deep clear RL above, separated by a strong (∼5°C) inversion at ∼500 m AGL (Fig. 4), with a further climb into the FT at the end of the flight pattern. Airmass characteristics for the PBL and the RL and FT, respectively, are summarized for both days in Table 3. In situ winds from the aircraft on 10 Jun were southeasterly but changed significantly within the few hours before the flight (see also the HYSPLIT trajectories). HYSPLIT analysis suggests that the high particle number concentrations in the upper layer are due to emissions into the evening or nocturnal RL (∼100 m AGL) from the Czech “clean” power station Melnik located 120 km upwind. The lower surface layer below 500 m AGL in Fig. 4 was, according to HYSPLIT, affected by the “dirty” power station Turow on the Polish side of the border, featuring the typical composition of unfiltered emissions with high concentrations of particulate matter with diameters of 2.5 and 10 µm or less (PM2.5 and PM10, respectively) and of black carbon (BC), as well as low ozone values (Table 3). The flight results were not conducive to derive particle budgets similar to the previous days, as the plumes were not covered by the flight to their full extent. However, they resulted in a case study of the vertical stratiform layers in the early morning lower troposphere and confirmed nighttime transport in the RL.
To illustrate the impact emissions can have on meteorological parameters, Fig. 5 shows the plume characteristics of two large UFP sources located north of Adelaide, South Australia (SA), in October 2014: the smelter (SME) at Port Pirie and the Port Augusta power station (campaign C13). At a distance of 10 km from the stacks the two plumes contained more than 180,000 and 130,000 particles per cubic centimeter, respectively. The satellite image insert (from 1997; Rosenfeld 2000) shows for the same southwesterly wind direction the cloud modification with reduced droplet sizes in stratiform clouds over distances of >1,000 km. The second insert shows SMPS data from the two UFP sources measured along a 40-km road at a distance of ∼70–100 km, after approximately 2–3-h advection time downwind.
It was possible to track these plumes over sparsely populated inland areas of Australia over 3 days and more than 1,200 km during a long-distance survey from Adelaide to Chinchilla, Queensland (Junkermann and Hacker 2015). Secondary GPC changed the size distribution within this plume during days 2 and 3. While aging shifted the initial aerosol mode to larger sizes, fresh particles from GPC in the sulfur-containing plume (Mohnen and Lodge 1969; Kiang et al. 1973) refilled the smallest-size bins but without any known sulfur emitter less than 400 km upwind. All back trajectories indicate Port Pirie and Port Augusta as the most likely sulfur sources.
Our airborne experiments resulted in a clear picture of major anthropogenic sources of primary nucleation mode particles, predominately from fossil fuel burning. We were also able to quantify these emissions, based on measurements in Europe, Australia, and China, data urgently needed for updated emission scenarios (Paasonen et al. 2016; Xausa et al. 2018).
SUMMARY AND CONCLUSIONS.
Based on airborne experiments using fully instrumented small environmental research aircraft, the impact of horizontal transport and vertical convective mixing on the UFP three-dimensional distribution was investigated in local, regional, and long-distance surveys. Size distributions, number concentrations, in situ meteorology (3D wind, temperature, and dewpoint), and HYSPLIT back trajectories allowed us to identify the most persistent UFP sources in the PBL—modern-technology fossil fuel–burning power stations (FFPS), refineries, and smelters—and even to quantify their emissions as particle number emission factors proportional to the installed power. Number concentrations in the plumes from these sources exceeded background values by up to two orders of magnitude. These continuous elevated single-point UFP emitters are perfect emission sources for detailed case studies of meteorological transport, thermal convection, and vertical mixing processes.
Synoptic transport (horizontal) and thermal convection (vertical) (Georgii 1956; Stull 1988) were identified to control the three-dimensional distribution of these primary emitted UFPs over hundreds of kilometers. Diurnal meteorological patterns affect stratification, vertical mixing, and the morning breakup of nighttime stratification. The size, number, and spatial and temporal UFP distributions observed at ground-based rural and urban field sites during all of our field campaigns are well in agreement with such a meteorology-controlled redistribution and diurnal vertical mixing of anthropogenic UFPs. The increasing number of observations of short-duration UFP events within the last decades, compared to observations before 1990, coincides with increases of the number of modern “clean” coal-fired power stations in operation worldwide. The recent changes in anthropogenic flue-gas-cleaning technology suppressing fine particles and NOx emissions lead toward a dramatic increase in nucleation mode particles (Junkermann et al. 2011b; Li et al. 2017) and affect rural clean as well as polluted environments, even including megacities (Laaksonen et al. 2005, 2008; Birmili et al. 2013; Pan et al. 2016; Kulmala 2017). Taking transport of primary UFPs from upwind fossil fuel–burning sources into account, recently postulated hypothetical elevated sources for ultrafine particles (Wehner et al. 2010; Crippa et al. 2012; Platis et al. 2015; Andreae et al. 2018) are no longer needed to understand observations. Our results also show that the long-distance origin of the air mass investigated is often less important than the contribution of pollution picked up during transport.
Not only do meteorological processes modify the aerosol distributions, but the ultrafine aerosols also affect meteorological processes, mainly through aerosol–cloud interactions. In a first step, additional CCN reduce the size of cloud droplets and increase the time necessary for raindrop formation. This has consequences for the spatial and temporal distribution of liquid cloud water, water vapor (latent heat), rainfall, and lightning (Thornton et al. 2017). Furthermore, this might also result in longer drought periods and the frequency and intensity of torrential rain (Rosenfeld et al. 2011; Fan et al. 2018). As the underlying physical processes are highly nonlinear and subject to several feedback loops between ultrafine and fine particles, cloud droplets and their size distributions, water vapor, radiation, and aerosol removal processes through rainout and deposition, a detailed investigation of the secondary cloud processes requires sophisticated modeling efforts that include updated emission scenarios for fossil fuel power station emissions (Paasonen et al. 2016; Xausa et al. 2018). Model calculations for Western Australia (Heinzeller et al. 2016) confirmed that the impact of realistic UFP emissions in terms of size and order of magnitude from single anthropogenic sources is well in agreement with the observed changes in regional-scale rainfall.
Further targeted numerical simulations that include detailed aerosol and cloud microphysics are required to better understand these complex processes combined with further airborne and ground-based measurements. Experimental quantification of the contribution of fossil fuel–burning emitters to the regional budget of UFPs and CCN could be shown to be possible using suitably equipped small environmental research aircraft with miniaturized instrumentation. Airborne measurements as presented here provide the required input data concerning source strength (emission factors) and size distributions to improve current and future emission scenarios for such simulations.
The flight campaign in Inner Mongolia was funded by the German Research Foundation, research group FOR 536 MAGIM, “Matter fluxes in grasslands of Inner Mongolia as influenced by stocking rate,” and the National Natural Science Foundation of China, Grant 41021004. Survey flights in Australia were supported by the German Federal Ministry for Education and Research, Grant AUS 10/031, and the European Commission supported the QUEST project (EVK2-CT2001-00127). The ARA Research Aircraft was donated by the late Ms. Joyce Schulz of Glen Osmond. ARA is supported by the Hackett Foundation in Adelaide.
© 2018 American Meteorological Society.