Ricardo AEA (United Kingdom)

An evaluation has been made of a number of contrasting atmospheric chemical transport models, of varying complexity, applied to estimate sulphur and nitrogen deposition in the UK. The models were evaluated by comparison with annually averaged measurements of gas, aerosol and precipitation concentrations from the national monitoring networks. The models were evaluated in relation to performance criteria. They were generally able to satisfy a criterion of ‘fitness for purpose’ that at least 50% of modelled concentrations should be within a factor of two of measured values. The second criterion, that the magnitude of the normalised mean bias should be less than 20%, was not always satisfied. Considering known uncertainties in measurement techniques, this criterion may be too strict. Overall, simpler models were able to give a good representation of measured gas concentrations whilst the use of dynamic meteorology, and complex photo-chemical reactions resulted in a generally better representation of measured aerosol and precipitation concentrations by more complex models.The models were compared graphically by plotting maps and cross-country transects of wet and dry deposition as well as calculating budgets of total wet and dry deposition to the UK for sulphur, oxidised nitrogen and reduced nitrogen. The total deposition to the UK varied by ±22–36% amongst the different models depending on the deposition component. At a local scale estimates of both dry and wet deposition for individual 5 km × 5 km model grid squares were found to vary between the different models by up to a factor of 4.

Abstract. The impact of 27 volatile organic compounds (VOCs) on the regional O3 increment was investigated using measurements made at the UK EMEP supersites Harwell (1999–2001 and 2010–2012) and Auchencorth (2012). Ozone at these sites is representative of rural O3 in south-east England and northern UK, respectively. The monthly-diurnal regional O3 increment was defined as the difference between the regional and hemispheric background O3 concentrations, respectively, derived from oxidant vs. NOx correlation plots, and cluster analysis of back trajectories arriving at Mace Head, Ireland. At Harwell, which had substantially greater regional O3 increments than Auchencorth, variation in the regional O3 increment mirrored afternoon depletion of anthropogenic VOCs due to photochemistry (after accounting for diurnal changes in boundary layer mixing depth, and weighting VOC concentrations according to their photochemical ozone creation potential). A positive regional O3 increment occurred consistently during the summer, during which time afternoon photochemical depletion was calculated for the majority of measured VOCs, and to the greatest extent for ethene and m+p-xylene. This indicates that, of the measured VOCs, ethene and m+p-xylene emissions reduction would be most effective in reducing the regional O3 increment but that reductions in a larger number of VOCs would be required for further improvement. The VOC diurnal photochemical depletion was linked to anthropogenic sources of the VOC emissions through the integration of gridded anthropogenic VOC emission estimates over 96 h air-mass back trajectories. This demonstrated that one factor limiting the effectiveness of VOC gridded emissions for use in measurement and modelling studies is the highly aggregated nature of the 11 SNAP (Selected Nomenclature for Air Pollution) source sectors in which they are reported, as monthly variation in speciated VOC trajectory emissions did not reflect monthly changes in individual VOC diurnal photochemical depletion. Additionally, the major VOC emission source sectors during elevated regional O3 increment at Harwell were more narrowly defined through disaggregation of the SNAP emissions to 91 NFR (Nomenclature for Reporting) codes (i.e. sectors 3D2 (domestic solvent use), 3D3 (other product use) and 2D2 (food and drink)). However, spatial variation in the contribution of NFR sectors to parent SNAP emissions could only be accounted for at the country level. Hence, the future reporting of gridded VOC emissions in source sectors more highly disaggregated than currently (e.g. to NFR codes) would facilitate a more precise identification of those VOC sources most important for mitigation of the impact of VOCs on O3 formation. In summary, this work presents a clear methodology for achieving a coherent VOC, regional-O3-impact chemical climate using measurement data and explores the effect of limited emission and measurement species on the understanding of the regional VOC contribution to O3 concentrations.

Cohort evidence linking long-term exposure to outdoor particulate air pollution and mortality has come largely from the United States. There is relatively little evidence from nationally representative cohorts in other countries. To investigate the relationship between long-term exposure to a range of pollutants and causes of death in a national English cohort. A total of 835,607 patients aged 40-89 years registered with 205 general practices were followed from 2003-2007. Annual average concentrations in 2002 for particulate matter with a median aerodynamic diameter less than 10 (PM(10)) and less than 2.5 μm (PM(2.5)), nitrogen dioxide (NO(2)), ozone, and sulfur dioxide (SO(2)) at 1 km(2) resolution, estimated from emission-based models, were linked to residential postcode. Deaths (n = 83,103) were ascertained from linkage to death certificates, and hazard ratios (HRs) for all- and cause-specific mortality for pollutants were estimated for interquartile pollutant changes from Cox models adjusting for age, sex, smoking, body mass index, and area-level socioeconomic status markers. Residential concentrations of all pollutants except ozone were positively associated with all-cause mortality (HR, 1.02, 1.03, and 1.04 for PM(2.5), NO(2), and SO(2), respectively). Associations for PM(2.5), NO(2), and SO(2) were larger for respiratory deaths (HR, 1.09 each) and lung cancer (HR, 1.02, 1.06, and 1.05) but nearer unity for cardiovascular deaths (1.00, 1.00, and 1.04). These results strengthen the evidence linking long-term ambient air pollution exposure to increased all-cause mortality. However, the stronger associations with respiratory mortality are not consistent with most US studies in which associations with cardiovascular causes of death tend to predominate.

Purpose This study of seven foods assessed whether there are modes or locations of production that require significantly fewer inputs, and hence cause less pollution, than others. For example, would increasing imports of field-grown tomatoes from the Mediterranean reduce greenhouse gas (GHG) emissions by reducing the need for production in heated greenhouses in the UK, taking account of the additional transport emissions? Is meat production in the UK less polluting than the import of red meat from the southern hemisphere?

Ionizing radiation is an extremely important tool for their wide applications in industry and medicine, but it can pose a hazard to human health. For this reason, special precautions must be observed when using and working around ionizing radiation. Safe application of radioactive materials and radiation producing equipments (or irradiation facilities) poses problems that are different from those in most other settings. This attributed to the wide variety of procedures using radiation. Meeting the challenge of supervising the radiation safety program at the irradiation facilities require considerable training and experiences. For most situations, the types and maximum quantities of radioactive materials possessed, the manner in which they may be used, and the individuals authorized to use radioactive materials are stipulated in the form of a "specific" license from the appropriate regulatory authority.

ABSTRACT Contributions of the emissions from a U.K. regulated fossil-fuel power station to regional air pollution and deposition are estimated using four air quality modeling systems for the year 2003. The modeling systems vary in complexity and emphasis in the way they treat atmospheric and chemical processes, and include the Community Multiscale Air Quality (CMAQ) modeling system in its versions 4.6 and 4.7, a nested modeling system that combines long- and short-range impacts (referred to as TRACK-ADMS [Trajectory Model with Atmospheric Chemical Kinetics–Atmospheric Dispersion Modelling System]), and the Fine Resolution Atmospheric Multi-pollutant Exchange (FRAME) model. An evaluation of the baseline calculations against U.K. monitoring network data is performed. The CMAQ modeling system version 4.6 data set is selected as the reference data set for the model footprint comparison. The annual mean air concentration and total deposition footprints are summarized for each modeling system. The footprints of the power station emissions can account for a significant fraction of the local impacts for some species (e.g., more than 50% for SO2 air concentration and non-sea-salt sulfur deposition close to the source) for 2003. The spatial correlation and the coefficient of variation of the root mean square error (CVRMSE) are calculated between each model footprint and that calculated by the CMAQ modeling system version 4.6. The correlation coefficient quantifies model agreement in terms of spatial patterns, and the CVRMSE measures the magnitude of the difference between model footprints. Possible reasons for the differences between model results are discussed. Finally, implications and recommendations for the regulatory assessment of the impact of major industrial sources using regional air quality modeling systems are discussed in the light of results from this case study. IMPLICATIONS Modeling tools are required to assess the contribution of industrial sources to ambient levels of air pollution, acid deposition, and eutrophication. This study evaluates the performance characteristics of regional air quality modeling systems in predicting contributions of the emissions from a U.K. regulated fossil-fuel power station to regional air pollution and deposition. It contrasts acid deposition modeling approaches used in the United Kingdom and demonstrates the sensitivity of the modeling systems to large emission changes. This work suggests considering an ensemble average of model calculations to provide an estimate of the uncertainty associated with an industrial source footprint.

Abstract The article contains sections titled: 1. X‐Ray Photoelectron Spectroscopy (XPS) 1.1. Principles 1.2. Instrumentation 1.2.1. Vacuum Requirements 1.2.2. X‐Ray Sources 1.2.3. Synchrotron Radiation 1.2.4. Electron Energy Analyzers 1.2.5. Spatial Resolution 1.3. Spectral Information and Chemical Shifts 1.4. Quantification, Depth Profiling, and Imaging 1.4.1. Quantification 1.4.2. Depth Profiling 1.4.3. Imaging 1.5. The Auger Parameter 1.6. Applications 1.6.1. Catalysis 1.6.2. Polymers 1.6.3. Corrosion and Passivation 1.6.4. Adhesion 1.6.5. Superconductors 1.6.6. Interfaces 2. Ultraviolet Photoelectron Spectroscopy (UPS) 3. Auger Electron Spectroscopy (AES) 3.1. Principles 3.2. Instrumentation 3.2.1. Vacuum Requirements 3.2.2. Electron Sources 3.2.3. Electron Energy Analyzers 3.3. Spectral Information 3.4. Quantification and Depth Profiling 3.4.1. Quantification 3.4.2. Depth Profiling 3.5. Applications 3.5.1. Grain Boundary Segregation 3.5.2. Semiconductor Technology 3.5.3. Thin Films and Interfaces 3.5.4. Surface Segregation 4. Scanning Auger Microscopy (SAM) 5. Other Electron‐Detecting Techniques 5.1. Auger Electron Appearance Potential Spectroscopy (AEAPS) 5.2. Electron Energy Loss Methods 5.2.1. Electron Energy Loss Spectroscopy (EELS) and Core‐Electron Energy Loss Spectroscopy (CEELS) 5.2.2. High‐Resolution Electron Energy Loss Spectroscopy (HREELS) 5.3. Diffraction Methods 5.3.1. Low‐Energy Electron Diffraction (LEED) 5.3.2. Reflection High‐Energy Electron Diffraction (RHEED) 5.4. Ion‐Excitation Method 5.4.1. Ion (Excited) Auger Electron Spectroscopy (IAES) 5.4.2. Ion‐Neutralization Spectroscopy (INS) 5.4.3. Metastable Quenching Spectroscopy (MQS) 5.5. Inelastic Electron Tunneling Spectroscopy (IETS)

Abstract The article contains sections titled:1.Secondary Ion Mass Spectrometry1.1.Static Secondary Ion Mass Spectrometry (SSIMS)1.1.1.Principles1.1.2.Instrumentation1.1.2.1.Ion Sources1.1.2.2.Mass Analyzers1.1.3.Quantification1.1.4.Spectral Information1.1.5.Applications1.1.5.1.Oxide Films1.1.5.2.Interfaces1.1.5.3.Polymers1.1.5.4.Biosensors1.1.5.5.Surface Reactions1.1.5.6.Imaging1.1.5.7.Ultrashallow Depth Profiling1.2.Dynamic SIMS1.2.1.Principles1.2.2.Instrumentation1.2.2.1.Ion Sources1.2.2.2.Mass Analyzers1.2.2.3.Detectors1.2.3.Spectral Information1.2.4.Quantification1.2.5.Mass Spectra1.2.6.Depth Profiles1.2.7.Imaging1.2.8.Applications1.2.8.1.Implantation Profiles1.2.8.2.Layer Analysis1.2.8.3.3D Bulk Element Distribution2.Secondary Neutral Mass Spectrometry (SNMS)2.1.General Principles2.2.Electron‐Beam and HF‐Plasma SNMS2.2.1.Principles2.2.2.Instrumentation2.2.3.Spectral Information2.2.4.Quantification2.2.5.Element Depth Profiling2.2.6.Applications2.3.Laser‐SNMS2.3.1.Principles2.3.1.1.Nonresonant Laser‐SNMS2.3.1.2.Resonant Laser‐SNMS2.3.1.3.Experimental Setup2.3.1.4.Ionization Schemes2.3.2.Instrumentation2.3.3.Spectral Information2.3.4.Quantification2.3.5.Applications2.3.5.1.Nonresonant Laser‐SNMS2.3.5.2.Resonant Laser‐SNMS3.Ion‐Scattering Techniques3.1.Rutherford Backscattering Spectroscopy (RBS)3.1.1.Principles3.1.2.Instrumentation3.1.3.Spectral Information3.1.4.Quantification3.1.5.Applications3.2.Low‐Energy Ion Scattering (LEIS)3.2.1.Principles3.2.2.Instrumentation3.2.3.Information3.2.4.Quantification3.2.5.Applications4.Other Ion‐Detecting Techniques4.1.Desorption Methods4.1.1.Electron‐Stimulated Desorption (ESD) and Electron‐Stimulated Desorption Ion Angular Distribution (ESDIAD)4.1.2.Thermal Desorption Spectroscopy (TDS)4.2.Glow Discharge Mass Spectroscopy (GDMS)4.3.Fast Atom Bombardment Mass Spectroscopy (FABMS)4.4.Atom Probe Microscopy4.4.1.Atom Probe Field‐Ion Microscopy (APFIM)4.4.2.Position‐Sensitive Atom Probe (POSAP)