Analysis of pollutants exchange between the Po Valley and the surrounding European region

Finardi, S.; Silibello, Camillo; D’Allura, A.; Radice, Paola

doi:10.1016/j.uclim.2014.02.002

Cited by 34 publications

(29 citation statements)

References 41 publications

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“…In case of NMVOC emission reduction, our numbers (up to −2 %) are only half of the relative ozone reduction achieved in their study (up to −4 %). The small ozone decreases due to NO x reduction in terms of AOT40s and exceedances further from cities in our simulations are probably caused by less NO x available in urban plumes when it mixes with biogenic NMVOC emissions over downwind areas (Im et al, 2011a, b;Finardi et al, 2014).…”

Section: The Urban Emissions Impact On Air Qualitymentioning

confidence: 76%

“…On regional scales, many studies focused on European urban centers, especially those in the Mediterranean region (e.g. Im et al, 2011a, b;Escudero et al, 2014;Finardi et al, 2014), but also covering London and the Ruhr area (Hodnebrog et al, 2011), or Paris (Skyllakou et al, 2014Markakis et al, 2015). The importance of multi-model modeling approach for investigating the megacities impact on air quality and climate was analyzed in detail by Baklanov et al (2010) in the framework of the European FP7 project MEGAPOLI.…”

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confidence: 99%

“…(2) Previously, model based estimates of urban emission impact over Europe considered relatively short time periods (1-2 months) often separately for winter and summer seasons (e.g. Im et al, 2011a;Im and Kanakidou, 2012;Finardi et al, 2014). These periods are however short to eliminate the potential influence of specific meteorological conditions during those time periods.…”

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confidence: 99%

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On the long-term impact of emissions from central European cities on regional air quality

2016

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Abstract. For the purpose of qualifying and quantifying the impact of urban emission from Central European cities on the present-day regional air quality, the regional climate model RegCM4.2 was coupled with the chemistry transport model CAMx, including two-way interactions. A series of simulations was carried out for the 2001-2010 period either with all urban emissions included (base case) or without considering urban emissions. Further, the sensitivity of ozone production to urban emissions was examined by performing reduction experiments with −20 % emission perturbation of NO x and/or non-methane volatile organic compounds (NMVOC).The modeling system's air quality related outputs were evaluated using AirBase, and EMEP surface measurements showed reasonable reproduction of the monthly variation for ozone (O 3 ), but the annual cycle of nitrogen dioxide (NO 2 ) and sulfur dioxide (SO 2 ) is more biased. In terms of hourly correlations, values achieved for ozone and NO 2 are 0.5-0.8 and 0.4-0.6, but SO 2 is poorly or not correlated at all with measurements (r around 0.2-0.5). The modeled fine particulates (PM 2.5 ) are usually underestimated, especially in winter, mainly due to underestimation of nitrates and carbonaceous aerosols.European air quality measures were chosen as metrics describing the cities emission impact on regional air pollution. Due to urban emissions, significant ozone titration occurs over cities while over rural areas remote from cities, ozone production is modeled, mainly in terms of number of exceedances and accumulated exceedances over the threshold of 40 ppbv. Urban NO x , SO 2 and PM 2.5 emissions also significantly contribute to concentrations in the cities themselves (up to 50-70 % for NO x and SO 2 , and up to 60 % for PM 2.5 ), but the contribution is large over rural areas as well (10-20 %). Although air pollution over cities is largely determined by the local urban emissions, considerable (often a few tens of %) fraction of the concentration is attributable to other sources from rural areas and minor cities. For the case of Prague (Czech Republic capital), it is further shown that the inter-urban interference between large cities does not play an important role which means that the impact on a chosen city of emissions from all other large cities is very small. At last, it is shown that to achieve significant ozone reduction over cities in central Europe, the emission control strategies have to focus on the reduction of NMVOC, as reducing NO x (due to suppressed titration) often leads to increased O 3 . The influence over rural areas is however always in favor of improved air quality, i.e. both NO x and/or NMVOC reduction ends up in decreased ozone pollution, mainly in terms of exceedances.

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Section: The Urban Emissions Impact On Air Qualitymentioning

confidence: 76%

mentioning

confidence: 99%

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confidence: 99%

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On the long-term impact of emissions from central European cities on regional air quality

2016

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“…On regional scales, many studies focused on European urban centres (e.g. Hodnebrog et al, 2011;Im and Kanakidou, 2012;Finardi et al, 2014;Skyllakou et al, 2014;Markakis et al, 2015;Markaris et al, 2016), on megacities in eastern Asia (Guttikunda et al, 2003;Tie et al, 2013) and Mexico city (Li et al, 2011).…”

Section: Introductionmentioning

confidence: 99%

The regional impact of urban emissions on climate over central Europe: present and future emission perspectives

et al. 2016

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Abstract. The regional climate model RegCM4.2 was coupled to the chemistry transport model CAMx, including twoway interactions, to evaluate the regional impact of urban emission from central European cities on climate for presentday (2001)(2002)(2003)(2004)(2005)(2006)(2007)(2008)(2009)(2010) and future (2046)(2047)(2048)(2049)(2050)(2051)(2052)(2053)(2054)(2055) periods, and for the future one only emission changes are considered. Short-lived non-CO 2 emissions are considered and, for the future impact, only the emission changes are accounted for (the climate is kept "fixed"). The urban impact on climate is calculated with the annihilation approach in which two experiments are performed: one with all emissions included and one without urban emissions. The radiative impacts of non-CO 2 primary and secondary formed pollutants are considered, namely ozone (O 3 ), sulfates (PSO 4 ), nitrates (PNO 3 ), primary organic aerosol and primary elementary carbon (POA and PEC).The validation of the modelling system is limited to key climate parameters, near-surface temperature and precipitation. It shows that the model, in general, underestimates temperature and overestimates precipitation. We attribute this behaviour to an excess of cloudiness/water vapour present in the model atmosphere as a consequence of overpredicted evaporation from the surface.The impact on climate is characterised by statistically significant cooling of up to −0.02 and −0.04 K in winter (DJF) and summer (JJA), mainly over cities. We found that the main contributors to the cooling are the direct and indirect effects of the aerosols, while the ozone titration, calculated especially for DJF, plays rather a minor role. In accordance with the vertical extent of the urban-emission-induced aerosol perturbation, cooling dominates the first few model layers up to about 150 m in DJF and 1000 m in JJA. We found a clear diurnal cycle of the radiative impacts with maximum cooling just after noon (JJA) or later in afternoon (DJF). Furthermore, statistically significant decreases of surface radiation are modelled in accordance with the temperature decrease. The impact on the boundary layer height is small but statistically significant and decreases by 1 and 6 m in DJF and JJA respectively. We did not find any statistically significant impact on precipitation and wind speed. Regarding future emissions, the impacts are, in general, smaller as a consequence of smaller emissions, resulting in smaller urban-induced chemical perturbations.In overall, the study suggest that the non-CO 2 emissions play rather a minor role in modulating regional climate over central Europe. Much more important is the direct climate impact of urban surfaces via the urban canopy meteorological effects as we showed earlier.

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“…The Paris Area is one of the hot spots for air pollution in Western Europe, along with the Po Valley [ Highwood et al ., ; Finardi et al ., ; Beekmann et al ., ], the London megapolis [ McMeeking et al ., ], and the BeNeLux/Rhine‐Ruhr area [ Gladtke , ]. Several experimental campaigns and theoretical studies have been performed to study the air quality in the Paris Area, under the framework of various international projects: in summer 1998–2000 during the “Air Pollution Over the Paris Region” (ESQUIF) [e.g., Vautard et al ., ; Chazette et al ., ; Tombette et al ., ], in summer 2007 during the “Lidar pour la Surveillance de l'AIR” campaign [ Raut and Chazette , ], and more recently in summer and winter 2009 with the “megacities: emissions, urban, regional and global atmospheric pollution and climate effects, and integrated tools for assessment and mitigation program” [e.g., Royer et al ., ; Freutel et al ., ; Pikridas et al ., ].…”

Section: Introductionmentioning

confidence: 99%

Springtime major pollution events by aerosol over Paris Area: From a case study to a multiannual analysis

Chazette

Royer

2017

JGR Atmospheres

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A study of the intense spring pollution events occurring between 2007 and 2016 on the Paris Area is presented using ground‐based and spaceborne measurements. Emphasis is placed on 2011 where data included ground‐based lidar measurements. This last period corresponds with the highest regional pollution levels of the past decade. The information threshold (daily average of (mass concentration of particles with aerodynamic diameter less than 10 μm) PM10 > 50 μg m−3) was exceeded 16 times, while the alert threshold (daily average of PM10 > 80 μg m−3) was exceeded twice. The information (alert) threshold exists to protect the most fragile people (the entire population). Ground‐based and spaceborne measurements demonstrate the benefit of their synergy as each is representative of specific space and time scales. The operational products of the spaceborne instruments Cloud‐Aerosol LIdar with Orthogonal Polarization (CALIOP) and the Moderate Resolution Imaging Spectroradiometer are used. For 2011, CALIOP vertical profiles are inversed to assess the backscatter to extinction ratio, which is then successfully compared with similar results derived from the CALIOP operational products, a ground‐based lidar and Sun photometers. The aerosols are identified to be polluted continental and polluted dust aerosols following the criteria used for the inversion of the CALIOP profiles. Aerosol typing is consistent between the ground‐based and spaceborne lidars, demonstrating the importance of CALIOP for other years where the ground‐based lidar was not in operation. The main pollution sources responsible for the spring aerosol pollution, occurring during anticyclonic meteorological conditions, are identified as coming from Western Europe: Benelux, Rhine‐Ruhr area, and the Lorraine area.

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Analysis of pollutants exchange between the Po Valley and the surrounding European region

Cited by 34 publications

References 41 publications

On the long-term impact of emissions from central European cities on regional air quality

On the long-term impact of emissions from central European cities on regional air quality

The regional impact of urban emissions on climate over central Europe: present and future emission perspectives

Springtime major pollution events by aerosol over Paris Area: From a case study to a multiannual analysis

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