Iodine speciation in atmospheric aerosols in the marine boundary layer

Iodine chemistry plays an important role in the tropospheric ozone depletion and the new particle formation in the Marine Boundary Layer (MBL). The sources, reaction pathways, and the sinks of iodine are investigated using lab experiments and field observations. The aims of this work are, firstly, to develop analytical methods for iodine measurements of marine aerosol samples especially for iodine speciation in the soluble iodine; secondly, to apply the analytical methods in field collected aerosol samples, and to estimate the characteristics of aerosol iodine in the MBL. Inductively Coupled Plasma – Mass Spectrometry (ICP-MS) was the technique used for iodine measurements. Offline methods using water extraction and Tetra-methyl-ammonium-hydroxide (TMAH) extraction were applied to measure total soluble iodine (TSI) and total insoluble iodine (TII) in the marine aerosol samples. External standard calibration and isotope dilution analysis (IDA) were both conducted for iodine quantification and the limits of detection (LODs) were both 0.1 μg L-1 for TSI and TII measurements. Online couplings of Ion Chromatography (IC)-ICP-MS and Gel electrophoresis (GE)-ICP-MS were both developed for soluble iodine speciation. Anion exchange columns were adopted for IC-ICP-MS systems. Iodide, iodate, and unknown signal(s) were observed in these methods. Iodide and iodate were separated successfully and the LODs were 0.1 and 0.5 μg L-1, respectively. Unknown signals were soluble organic iodine species (SOI) and quantified by the calibration curve of iodide, but not clearly identified and quantified yet. These analytical methods were all applied to the iodine measurements of marine aerosol samples from the worldwide filed campaigns. The TSI and TII concentrations (medians) in PM2.5 were found to be 240.87 pmol m-3 and 105.37 pmol m-3 at Mace Head, west coast of Ireland, as well as 119.10 pmol m-3 and 97.88 pmol m-3 in the cruise campaign over the North Atlantic Ocean, during June – July 2006. Inorganic iodine, namely iodide and iodate, was the minor iodine fraction in both campaigns, accounting for 7.3% (median) and 5.8% (median) in PM2.5 iodine at Mace Head and over the North Atlantic Ocean, respectively. Iodide concentrations were higher than iodate in most of the samples. In the contrast, more than 90% of TSI was SOI and the SOI concentration was correlated significantly with the iodide concentration. The correlation coefficients (R2) were both higher than 0.5 at Mace Head and in the first leg of the cruise. Size fractionated aerosol samples collected by 5 stage Berner impactor cascade sampler showed similar proportions of inorganic and organic iodine. Significant correlations were obtained in the particle size ranges of 0.25 – 0.71 μm and 0.71 – 2.0 μm between SOI and iodide, and better correlations were found in sunny days. TSI and iodide existed mainly in fine particle size range (< 2.0 μm) and iodate resided in coarse range (2.0 – 10 μm). Aerosol iodine was suggested to be related to the primary iodine release in the tidal zone. Natural meteorological conditions such as solar radiation, raining etc were observed to have influence on the aerosol iodine. During the ship campaign over the North Atlantic Ocean (January – February 2007), the TSI concentrations (medians) ranged 35.14 – 60.63 pmol m-3 among the 5 stages. Likewise, SOI was found to be the most abundant iodine fraction in TSI with a median of 98.6%. Significant correlation also presented between SOI and iodide in the size range of 2.0 – 5.9 μm. Higher iodate concentration was again found in the higher particle size range, similar to that at Mace Head. Airmass transport from the biogenic bloom region and the Antarctic ice front sector was observed to play an important role in aerosol iodine enhancement. The TSI concentrations observed along the 30,000 km long cruise round trip from East Asia to Antarctica during November 2005 – March 2006 were much lower than in the other campaigns, with a median of 6.51 pmol m-3. Approximately 70% of the TSI was SOI on average. The abundances of inorganic iodine including iodine and iodide were less than 30% of TSI. The median value of iodide was 1.49 pmol m-3, which was more than four fold higher than that of iodate (median, 0.28 pmol m-3). Spatial variation indicated highest aerosol iodine appearing in the tropical area. Iodine level was considerably lower in coastal Antarctica with the TSI median of 3.22 pmol m-3. However, airmass transport from the ice front sector was correlated with the enhance TSI level, suggesting the unrevealed source of iodine in the polar region. In addition, significant correlation between SOI and iodide was also shown in this campaign. A global distribution in aerosol was shown in the field campaigns in this work. SOI was verified globally ubiquitous due to the presence in the different sampling locations and its high proportion in TSI in the marine aerosols. The correlations between SOI and iodide were obtained not only in different locations but also in different seasons, implying the possible mechanism of iodide production through SOI decomposition. Nevertheless, future studies are needed for improving the current understanding of iodine chemistry in the MBL (e.g. SOI identification and quantification as well as the update modeling involving organic matters).

On the inheritance and mechanism of baculovirus resistance of the codling moth, Cydia pomonella (L.)

Das Cydia pomonella Granulovirus (CpGV, Baculoviridae) wird seit Ende der 1980er Jahre als hoch-selektives und effizientes biologisches Bekämpfungsmittel zur Kontrolle des Apfelwicklers im Obstanbau eingesetzt. Seit 2004 wurden in Europa verschiedene Apfelwicklerpopulationen beobachtet die resistent gegenüber dem hauptsächlich angewendeten Isolat CpGV-M aufweisen. Die vorliegende Arbeit befasst sich mit der Untersuchung der Vererbung und des Mechanismus der CpGV Resistenz. Einzelpaarkreuzungen zwischen einem empfindlichen Laborstamm (CpS) und einem homogen resistenten Stamm (CpRR1) zeigten, dass die Resistenz durch ein einziges dominantes Gen, das auf dem Z-Chromosom lokalisiert ist, vererbt wird. Massernkreuzungen zwischen CpS und einer heterogen resistenten Feldpopulation (CpR) deuteten zunächst auf einen unvollständig dominanten autosomalen Erbgang hin. Einzelpaarkreuzungen zwischen CpS und CpR bewiesen jedoch, dass die Resistenz in CpR ebenfalls monogen dominant und geschlechtsgebunden auf dem Z-Chromosom vererbt wird. Diese Arbeit diskutiert zudem die Vor- und Nachteile von Einzelpaarkreuzungen gegenüber Massernkreuzungen bei der Untersuchung von Vererbungsmechanismen. Die Wirksamkeit eines neuen CpGV Isolates aus dem Iran (CpGV-I12) gegenüber CpRR1 Larven, wurde in Bioassays getestet. Die Ergebnisse zeigen, dass CpGV-I12 die Resistenz in allen Larvenstadien von CpRR1 brechen kann und fast so gut wirkt wie CpGV-M gegenüber CpS Larven. Daher ist CpGV-I12 für die Kontrolle des Apfelwicklers in Anlagen wo die Resistenz aufgetreten ist geeignet. Um den der CpGV Resistenz zugrunde liegenden Mechanismus zu untersuchen, wurden vier verschiedene Experimente durchgeführt: 1) die peritrophische Membran degradiert indem ein optischer Aufheller dem virus-enthaltenden Futtermedium beigefügt wurde. Das Entfernen dieser mechanischen Schutzbarriere, die den Mitteldarm auskleidet, führte allerdings nicht zu einer Reduzierung der Resistenz in CpR Larven. Demnach ist die peritrophische Membran nicht am Resistenzmechanismus beteiligt. 2) Die Injektion von Budded Virus in das Hämocoel führte nicht zur Brechung der Resistenz. Folglich die die Resistenz nicht auf den Mitteldarm beschränkt, sondern auch in der Sekundärinfektion wirksam. 3) Die Replikation von CpGV in verschiedenen Geweben (Mitteldarm, Hämolymphe und Fettkörper) von CpS und CpRR1 wurde mittels quantitativer PCR verfolgt. In CpS Larven konnte in allen drei Gewebetypen sowohl nach oraler als auch nach intra-hämocoelarer Infektion eine Zunahme der CpGV Genome in Abhängigkeit der Zeit festgestellt werden. Dagegen konnte in den Geweben aus CpRR1 nach oraler sowie intra-hämocoelarer Infektion keine Virusreplikation detektiert werden. Dies deutet darauf hin, dass die CpGV Resistenz in allen Zelltypen präsent ist. 4) Um zu untersuchen ob ein humoraler Faktor in der Hämolymphe ursächlich an der Resistenz beteiligt ist, wurde Hämolymphe aus CpRR1 Larven in CpS Larven injiziert und diese anschließend oral mit CpGV infiziert. Es konnte jedoch keine Immunreaktion beobachtet und kein Faktor in der Hämolymphe identifiziert werden, der Resistenz induzieren könnte. Auf Grundlage dieser Ergebnisse kann festgestellt werden, dass in resistenten Apfelwicklerlarven die virale Replikation in allen Zelltypen verhindert wird, was auf eine Virus-Zell Inkompatibilität hinweist. Da in CpRR1 keine DNA Replikation beobachtet wurde, wird die CpGV Resistenz wahrscheinlich durch eine frühe Unterbindung der Virusreplikation verursacht.Das früh exprimierte Gen pe38 codiert für ein Protein, das wahrscheinlich für die Resistenzbrechung durch CpGV-I12 verantwortlich ist. Interaktionen zwischen dem Protein PE38 und Proteinen in CpRR1 wurden mit Hilfe des Yeast Two-Hybrid (Y2H) Systems untersucht. Die detektierten Interaktionen sind noch nicht durch andere Methoden bestätigt, jedoch wurden zwei mögliche Gene auf dem Z-Chromosom und eines auf Chromosom 15 gefunden, wie möglicherweise an der CpGV Resistenz beteiligt sind.

Exchange of nitrogen dioxide (NO 2) between plants and the atmosphere under laboratory and field conditions

Nitrogen is an essential nutrient. It is for human, animal and plants a constituent element of proteins and nucleic acids. Although the majority of the Earth’s atmosphere consists of elemental nitrogen (N2, 78 %) only a few microorganisms can use it directly. To be useful for higher plants and animals elemental nitrogen must be converted to a reactive oxidized form. This conversion happens within the nitrogen cycle by free-living microorganisms, symbiotic living Rhizobium bacteria or by lightning. Humans are able to synthesize reactive nitrogen through the Haber-Bosch process since the beginning of the 20th century. As a result food security of the world population could be improved noticeably. On the other side the increased nitrogen input results in acidification and eutrophication of ecosystems and in loss of biodiversity. Negative health effects arose for humans such as fine particulate matter and summer smog. Furthermore, reactive nitrogen plays a decisive role at atmospheric chemistry and global cycles of pollutants and nutritive substances.rnNitrogen monoxide (NO) and nitrogen dioxide (NO2) belong to the reactive trace gases and are grouped under the generic term NOx. They are important components of atmospheric oxidative processes and influence the lifetime of various less reactive greenhouse gases. NO and NO2 are generated amongst others at combustion process by oxidation of atmospheric nitrogen as well as by biological processes within soil. In atmosphere NO is converted very quickly into NO2. NO2 is than oxidized to nitrate (NO3-) and to nitric acid (HNO3), which bounds to aerosol particles. The bounded nitrate is finally washed out from atmosphere by dry and wet deposition. Catalytic reactions of NOx are an important part of atmospheric chemistry forming or decomposing tropospheric ozone (O3). In atmosphere NO, NO2 and O3 are in photosta¬tionary equilibrium, therefore it is referred as NO-NO2-O3 triad. At regions with elevated NO concentrations reactions with air pollutions can form NO2, altering equilibrium of ozone formation.rnThe essential nutrient nitrogen is taken up by plants mainly by dissolved NO3- entering the roots. Atmospheric nitrogen is oxidized to NO3- within soil via bacteria by nitrogen fixation or ammonium formation and nitrification. Additionally atmospheric NO2 uptake occurs directly by stomata. Inside the apoplast NO2 is disproportionated to nitrate and nitrite (NO2-), which can enter the plant metabolic processes. The enzymes nitrate and nitrite reductase convert nitrate and nitrite to ammonium (NH4+). NO2 gas exchange is controlled by pressure gradients inside the leaves, the stomatal aperture and leaf resistances. Plant stomatal regulation is affected by climate factors like light intensity, temperature and water vapor pressure deficit. rnThis thesis wants to contribute to the comprehension of the effects of vegetation in the atmospheric NO2 cycle and to discuss the NO2 compensation point concentration (mcomp,NO2). Therefore, NO2 exchange between the atmosphere and spruce (Picea abies) on leaf level was detected by a dynamic plant chamber system under labo¬ratory and field conditions. Measurements took place during the EGER project (June-July 2008). Additionally NO2 data collected during the ECHO project (July 2003) on oak (Quercus robur) were analyzed. The used measuring system allowed simultaneously determina¬tion of NO, NO2, O3, CO2 and H2O exchange rates. Calculations of NO, NO2 and O3 fluxes based on generally small differences (∆mi) measured between inlet and outlet of the chamber. Consequently a high accuracy and specificity of the analyzer is necessary. To achieve these requirements a highly specific NO/NO2 analyzer was used and the whole measurement system was optimized to an enduring measurement precision.rnData analysis resulted in a significant mcomp,NO2 only if statistical significance of ∆mi was detected. Consequently, significance of ∆mi was used as a data quality criterion. Photo-chemical reactions of the NO-NO2-O3 triad in the dynamic plant chamber’s volume must be considered for the determination of NO, NO2, O3 exchange rates, other¬wise deposition velocity (vdep,NO2) and mcomp,NO2 will be overestimated. No significant mcomp,NO2 for spruce could be determined under laboratory conditions, but under field conditions mcomp,NO2 could be identified between 0.17 and 0.65 ppb and vdep,NO2 between 0.07 and 0.42 mm s-1. Analyzing field data of oak, no NO2 compensation point concentration could be determined, vdep,NO2 ranged between 0.6 and 2.71 mm s-1. There is increasing indication that forests are mainly a sink for NO2 and potential NO2 emissions are low. Only when assuming high NO soil emissions, more NO2 can be formed by reaction with O3 than plants are able to take up. Under these circumstance forests can be a source for NO2.