La micro-algue verte Chlamydomonas reinhardtii est considérée comme un modèle dans l’étude du stress métallique chez les organismes photosynthétiques. Les mécanismes de tolérance au stress induit par le cadmium ne sont pas encore clairement établis. Afin de déterminer ces mécanismes, la localisation subcellulaire et la spéciation chimique in situ du cadmium ont été déterminées chez trois souches de C. reinhardtii exposées au cadmium en condition mixotrophe (CO2 + Acétate) : (i) une souche de type sauvage (wt), (ii) la souche cell-wall less (cw15) qui est déficiente en paroi cellulaire, (iii) la souche pcs1 qui surexprime la phytochélatine synthase (PCS), enzyme ordinairement cytosolique, directement dans son chloroplaste. Pour ce faire, la toxicité du cadmium a été déterminée en mesurant la croissance ainsi que la teneur en chlorophylle et en amidon des micro-algues. Puis, la localisation du cadmium au niveau subcellulaire a été réalisée par trois techniques complémentaires (fractionnement subcellulaire, µXRF, TEM/X-EDS). La spéciation chimique in situ du cadmium a été effectuée par µXAS et XAS. Enfin, l’imagerie élémentaire et isotopique par nanoSIMS a permis de compléter les distributions élémentaires dans la cellule et de déterminer l’impact du cadmium sur les mécanismes d’assimilation du carbone. (i) Les résultats de ce travail montrent que la souche wt est la plus sensible au cadmium des trois avec une diminution de la croissance et de la teneur en chlorophylle. Lorsqu’elle ne présente pas ces signes de toxicité, le cadmium est séquestré dans l’ensemble de la cellule par des ligands thiolés et de façon mineure par les granules de polyphosphates. Suite à l’exposition à de fortes concentrations en cadmium, le cadmium intracellulaire est lié majoritairement à des ligands carboxylés probablement induits par le stress oxydatif. De plus, la présence du cadmium dans le pyrénoïde bloque l’assimilation du carbone inorganique (CO2), au profit de l’assimilation du carbone organique (acétate), qui est stocké sous forme d’amidon. (ii) La surexpression de la PCS de la souche pcs1 provoque une production d’amidon importante autour du pyrénoïde et protège la chlorophylle du stress lié au cadmium. Bien que la synthèse de phytochélatines soit potentiellement élevée, la moitié du cadmium intracellulaire est séquestrée par les granules de polyphosphates et l’amidon. (iii) La souche cw15 est la plus tolérante des trois souches et n’accumule pas la totalité du cadmium disponible, contrairement aux cellules possédant une paroi cellulaire. Similairement au wt, le cadmium intracellulaire est séquestré majoritairement par des ligands thiolés et de façon mineure par les granules de polyphosphates. L’observation de granules de polyphosphates excrétées par les micro-algues permet l’hypothèse de l’excrétion du cadmium vacuolaire induisant un flux constant de cadmium à travers la cellule. En conclusion, la séquestration du cadmium via des ligands soufre, potentiellement par des polypeptides thiolés, est le mécanisme de tolérance majoritaire mis en place par C. reinhardtii. Néanmoins, la séquestration du cadmium par les granules de polyphosphates semble apporter une plus grande tolérance vis-à-vis du stress lié au cadmium. / The green micro-alga Chlamydomonas reinhardtii is commonly used as a model for the study of the metallic stress in photosynthetic organisms. Tolerance mechanisms against stress induced by cadmium are not well understood. In order to determine these mechanisms, subcellular location and in situ speciation have been determined in three C. reinhardtii strains exposed to cadmium in mixotrophic conditions (CO2 + Acetate) : (i) a wild type strain (wt), (ii) a cell-wall less strain (cw15) which is deficient in cell-wall, (iii) the pcs1 strain which overexpresses the cytosolic enzyme phytochetlatin synthase (PCS) directly in the chloroplast. Cadmium toxicity has been determined by the monitoring of growth and chlorophyll, starch content in micro-algae. Then, cadmium location at subcellular level has been performed using three complementary techniques (subcellular fractionation, µXRF and TEM/X-EDS). In situ cadmium speciation has been studied by µXAS and XAS. Finally, elemental and isotopic imaging by nanoSIMS has allowed to complete elemental distribution in the cells and to determine the impact of cadmium on the assimilation of carbon. (i) The results of this work show that the wt strain is the most sensitive strain to cadmium stress among the three studied strains with a growth and chlorophyll content decrease. When wt cells do not show signs of toxicity, cadmium is mainly sequestered in the whole cell by thiolated ligands and in polyphosphate granules. After an exposure to high concentration of cadmium, intracellular cadmium is mainly bound to carboxylated ligands, probably induced by oxidative stress. Moreover, cadmium located in the pyrenoid blocks inorganic carbon (CO2) assimilation and increases organic carbon (acetate) assimilation which is stored as starch. (ii) The overexpresssion of PCS in the pcs1 strain induces a strong production of starch around the pyrenoid and proctects the chlorophyll against cadmium stress. Although the synthesis of phytocheltins was potentially strong, half of the intracellular cadmium is sequestered in polyphosphate granules and in starch. (iii) Unlike cell-walled cells, the cw15 strain is the most tolerant strain and does not accumulate the totality of available cadmium. Similarly to wt strain, intracellular cadmium is mainly sequestered by thiolated ligands and in polyphosphate granules. The observation of polyphosphate granules excreted by the micro-algae allows the hypothesis of the excretion of vacuolar cadmium, inducing a constant flux of cadmium through the cells. In conclusion, cadmium sequestration by sulfur ligands, potentially by thiolated polypeptides, is the main tolerance mechanism implemented by C. renhardtii. However, cadmium sequestration in polyphosphate granules seems to allow a better tolerance against cadmium stress.

Diss. (sammanfattning) Linköping : Linköpings universitet, 2008. / Härtill 4 uppsatser. Includes bibliographical references.

Diss. (sammanfattning) Linköping : Linköpings universitet, 2008. / Härtill 4 uppsatser.

L'électrocoagulation (EC) est une méthode électrochimique non spécifique couramment utilisée pour le traitement de l'eau et des eaux usées. Dans ce travail, l’EC est d'abord étudiée comme une technique classique de traitement des eaux usées dédiée à l'élimination des protéines de lactosérum de l'eau pour laquelle les mécanismes d'élimination sont expliqués et un modèle est développé. Ensuite, l'utilisation de l’EC est étendue à la séparation et à la purification d’acides gras volatils issus de la fermentation acidogénique. Dans cette deuxième étude, les effets des paramètres opératoires sur l'efficacité et le coût de l’EC sont discutés. En outre, l’EC est utilisée pour la récolte de deux espèces de microalgues de leur milieu de culture. En ce qui concerne la récolte de Chlamydomonas reinhardtii, la méthodologie de la surface de réponse est utilisée et deux modèles permettant de prédire respectivement l'efficacité de la récupération et le coût opératoire sont développés. La récolte d’une autre espèce de microalgues, Chlorella vulgaris, est étudiée en utilisant l’EC respectivement en mode discontinu et continu. En mode discontinu, les effets des principaux paramètres de fonctionnement sur l'efficacité du processus sont expliqués et les mécanismes de récupération sont discutés. Dans l'étude en mode continu, la méthodologie de la surface de réponse est utilisée et un modèle permettant de prédire l’efficacité de récupération des microalgues est développé. Enfin, la comparaison des performances de l'EC en mode continu avec et sans échange de polarité aux performances de l'EC en mode discontinu est effectuée. / Electrocoagulation (EC) is a non-specific electrochemical method usually used for water and wastewater treatment. In this work, EC is firstly investigated as a conventional wastewater treatment technique for the removal of whey proteins from water, where the mechanisms of removal are explained and a model on whey proteins elimination is developed. Then, EC use is extended for the separation and purification of volatile fatty acids issued from acidogenic fermentation. In this second study, the effects of operating parameters on EC efficiency and cost are discussed. Moreover, EC is used for the harvesting of two microalgae species from their culture medium. In the study that concerns recovering Chlamydomonas reinhardtii, response surface methodology (RSM) is employed and two models for predicting recovery efficiency and operating cost are developed. The harvesting of the other microalgae species Chlorella vulgaris is studied using EC in the batch and continuous modes. In the batch mode, the effects of the main operating parameters on the process effectiveness are explained along with discussing the mechanisms of recovery. In the continuous mode study, response surface methodology (RSM) is applied and a model for predicting microalgae recovery is developed. Finally, comparison of EC performance in continuous mode with and without polarity exchange (PE) to EC performance in batch mode is carried out.

Les nanoparticules (NPs) d'Ag sont très utilisées dans le secteur de la santé, dans l'industrie alimentaire et dans les produits de consommation pour leurs propriétés antimicrobiennes. Le grand rapport surface sur volume des NPs d'Ag permet une augmentation importante du relargage d'Ag comparé au matériau massif et donc une toxicité accrue vis à vis des micro-organismes sensibles à cet élément. Ce travail de thèse présente une évaluation des propriétés antimicrobiennes de petites NPs d'Ag (<20 nm) enrobées dans des matrices de silice sur la photosynthèse d'algues vertes. Deux techniques d'élaboration par voie physique ont été utilisées pour fabriquer ces nanocomposites: (i) l'implantation ionique à basse énergie et (ii) la pulvérisation d'Ag couplée avec la polymérisation plasma. Les propriétés structurales et optiques de ces nanostructures ont été étudiées par microscopie électronique à transmission, réflectivité et ellipsométrie. Cette dernière technique, couplée à un modèle basé sur l'approximation quasi-statique de type Maxwell-Garnett, a permis la détection de petites variations dans la taille et la densité des NPs d'Ag. Le relargage d'argent de ces NPs d'Ag enrobées dans des diélectriques a été mesuré par spectrométrie de masse après immersion dans de l'eau tamponnée. La toxicité à court terme de l'Ag sur la photosynthèse d'algues vertes, Chlamydomonas reinhardtii, a été évaluée par fluorométrie. L'enrobage des nanoparticules dans un diélectrique réduit leur interaction avec l'environnement, et les protège d'une oxydation rapide. La libération d'Ag bio-disponible (impactant sur la photosynthèse des algues) est contrôlée par la profondeur à laquelle se trouvent les NPs d'Ag dans la matrice hôte de silice. Cette étude permet d'envisager le design de revêtements à effet biocide contrôlé. En couplant les propriétés antimicrobiennes de ces NPs d'Ag enrobées à leur qualité d'antenne plasmonique, ces nanocomposites peuvent être utilisés pour détecter et prévenir les premières étapes de la formation de biofilms sur des surfaces. Ainsi, une dernière partie de ce travail est dédiée à l'étude de la stabilité et de l'adsorption de protéines fluorescentes Discosoma rouges recombinantes (DsRed) sur ces surfaces diélectriques avec la perspective du développement de dispositifs SERS. / Silver nanoparticles (AgNPs) because of their strong biocide activity are widely used in health-care sector, food industry and various consumer products. Their huge surface-volume ratio enhances the silver release compared to the bulk material, leading to an increased toxicity for microorganisms sensitive to this element. This work presents an assessment of the biocide properties on algal photosynthesis of small (<20 nm) AgNPs embedded in silica layers. Two physical approaches were used to elaborate these nanocomposites: (i) low energy ion beam synthesis and (ii) combined silver sputtering and plasma polymerization. These techniques allow elaboration of a single layer of AgNPs embedded in silica films at defined nanometer distances (from 0 to 7 nm) beneath the free surface. The structural and optical properties of the nanocomposites were studied by transmission electron microscopy, reflectance spectroscopy and ellipsometry. This last technique, coupled to modelling based on the quasi-static approximation of the classical Maxwell-Garnett formalism, allowed detection of small variations over the size and density of the embedded AgNPs. The silver release from the nanostructures after immersion in buffered water was measured by inductively coupled plasma mass spectrometry. The short-term toxicity of Ag to the photosynthesis of green algae, Chlamydomonas reinhardtii, was assessed by fluorometry. Embedding AgNPs reduces their interactions with the buffered water, protecting the AgNPs from fast oxidation. The release of bio-available silver (impacting on the algal photosynthesis) is controlled by the depth at which AgNPs are located for the given host silica matrix. This provides a procedure to tailor the biocide effect of nanocomposites containing AgNPs. By coupling the controlled antimicrobial properties of the embedded AgNPs and their quality as plasmonic antenna, these coatings can be used to detect and prevent the first stages of biofilm formation. Hence, the last part of this work is dedicated to a study of the structural stability and adsorption properties of Discosoma recombinant red (DsRed) fluorescent proteins deposited on these dielectric surfaces with perspectives of development of SERS devices.

L’explosion de la nanotechnologie a permis l’intégration d’une multitude de nanoparticules dans des produits de consommation. Les nanoparticules d’argent (nAg) sont les plus utilisées à ces fins, selon les derniers recensements disponibles. La plupart des études toxicologiques, à ce jour, ont fait état de l’implication très évidente de l’ion Ag+ dans la toxicité aigüe des nAg; cependant, quelques études ont mis en évidence des effets toxicologiques dus aux nAg. Il y a un certain consensus à propos d’un risque de contamination des eaux douces via leur rejet par les effluents des réseaux d’aqueducs. Puisque les concentrations en Ag+ sont généralement très faibles dans les eaux douces (de l’ordre du pg L-1), de par la formation de complexes non-labiles avec des thiols (organiques et inorganiques) et des sulfures, la toxicité inhérente aux nAg pourrait ne pas être négligeable- comparativement aux tests en laboratoires. Cette étude s’intéressait donc aux mécanismes de bioaccumulation d’argent par l’algue verte C. reinhardtii suite à l’exposition à des nAg de 5 nm (enrobage d’acide polyacrylique). La bioaccumulation d’argent pour l’exposition à Ag+ servait de point de comparaison; également, les abondances de l’ARNm de l’isocitrate lyase 1 (ICL1) et de l’ARNm de Copper Transporter 2 (CTR2) étaient mesurées comme témoins biologiques de la bioaccumulation de Ag+. Les expériences ont été menées en présence d’un tampon organique (NaHEPES, 2 x 10-2 M; Ca2+, 5x 10-5 M) à pH de 7,00. Pour des expositions à temps fixe de 2 heures, la bioaccumulation d’argent pour nAg était supérieure à ce qui était prédit par sa concentration initiale en Ag+; cependant, il n’y avait pas de différence d’abondance des ARNm de ICL1 et de CTR2 entre nAg et Ag+. D’un autre côté, pour une exposition à temps variables, la bioaccumulation d’argent pour nAg était supérieure à ce qui était prédit par sa concentration initiale en Ag+ et une augmentation de l’abondance de l’ARNm de ICL1 était notée pour nAg. Cependant, il n’y avait aucune différence significative au niveau de l’abondance de l’ARNm de CTR2 entre nAg et une solution équivalente en Ag+. L’ajout d’un fort ligand organique (L-Cystéine; log K= 11,5) à une solution de nAg en diminuait radicalement la bioaccumulation d’argent par rapport à nAg-sans ajout de ligand. Par contre, l’abondance des ARNm de ICL1 et de CTR2 étaient stimulées significativement par rapport à une solution contrôle non-exposée à nAg, ni à Ag+. Les résultats suggéraient fortement que les nAg généraient des ions Ag+ au contact de C. reinhardtii. / The recent developments in nanotechnology have given rise to a new and increasing economical market where nanoparticles are at the forefront. Recent inventories of the nanoparticles-containing products have shown that silver nanoparticle- containing products are the most frequently used consumer nanomaterial. Due to the fear of a large scale contamination-and even pollution- of the aquatic environment from silver nanoparticles (nAg), studies have been conducted to assess their toxicities, which, in many cases, have been found to be mediated by the concomitant presence of Ag+. Notably, few studies have found evidence of toxicity due to the nAg, per se. Since numerous non-labile complexes are formed with Ag+ in freshwaters- especially with thiols and sulfides-, nAg toxicity might be more relevant in comparison to laboratory tests where the Ag+ tends to dominate toxicity studies. Therefore, this study investigated the mechanisms underlying silver bioaccumulation by the green alga, C. reinhardtii upon exposure to solutions of nAg (nominal size of 5 nm; poly-acrylate coating). Silver bioaccumulation upon exposures to the free ion alone served for comparison. In parallel, the abundance of two mRNAs- ICL1 and CTR2- were used to better understand the mechanisms underlying the bioaccumulation of Ag+ (and potentially nAg). The experiments were conducted in pH buffered solutions (NaHEPES, 2 x 10-2 M; Ca2+, 5x 10-5 M) at pH 7.00. For 2-hour exposures, the silver bioaccumulation for solutions of nAg exceeded what was expected from their Ag+ content only; however, no differences were noticed in the abundance of the expression of ICL1 and CTR2. For variable time exposures, the silver bioaccumulation for solutions of nAg exceeded what was expected from their Ag+ content only. Moreover, the expression of ICL1 was significantly higher for nAg than what was expected based upon an exposure to Ag+ only. When exposed to nAg, expression levels of CTR2 could be predicted from levels based solely on the Ag+ concentrations. The addition of a large excess of L-Cysteine, which is a very strong silver ligand (log K =11.5), to a nAg solution largely decreased silver bioaccumulation, however, bioaccumulation remained significant and the expression of both ICL1 and CTR2 were significantly higher than that of the control solutions (without Ag+). The results strongly suggest that nAg generated Ag+ ions when in contact with C. reinhardtii and that the nAg released to freshwaters might exert its toxicity through organism-contact-dependant release of Ag+.

When conspecific individuals are crossed, the ensuing hybridization creates a spectrum of phenotypes in the resulting offspring. Many of hybrid traits will be additive, similar to the parental phenotypes. In some cases however, transgressive phenotypes are formed, outside the range of that of the parental phenotypes. Transgressive phenotypes can either be restricted to the F1 generation or be heritable throughout the hybrid lineage. While the mechanism behind heritable transgressive phenotyped is yet to be determined, transgressive gene expression is thought to be the root cause of their formation. Epigenetics modifications, heritable variation separate to the DNA code, can alter gene expression, persist through generations, and vary between individuals and over time. This makes them ideal candidates to be involved in the formation of transgressive phenotypes. RNA silencing is an epigenetic mechanism of gene regulation relying on 20Q24nt single stranded small RNAs (sRNAs). Small RNAs, due to their ability to set up persistent epigenetic marks at a locus, have the potential to create heritable transgressive gene expression. For example, when genetic variation from one parental genome presents novel targets to the sRNAs of the other parental genome, new epigenetic marks such as DNA methylation or secondary sRNAs can be created at target sites. In order to understand the potential of small RNAs to influence hybrid phenotype, I designed crossing experiments with Chlamydomonas reinhardtii, choosing this unicellular alga due to the genetic tools available and the haploid nature of its vegetative cells. The specific aim of the experiment was to identify transgressively expressed sRNA populations. Crossing two geographically distinct strains of C. reinhardtii, and sequencing both the genomes and sRNAomes of parents and recombinants, I was able catalogue both genetic and epigenetic variation in the parental strains providing unique insight into the inheritance of small RNAs in this alga. In this thesis, I first compare the genomes of the parental strains, identifying polymorphisms and assessing genetic variation in RNA silencing pathway components. I then describe the sRNA profiles of the parental strains, identifying differentially expressed sRNA loci. I then describe my approach to identifying transgressively expressed sRNA loci in the hybrids. While many sRNA loci in the recombinants exhibit additive sRNA expression, I found multiple transgressively expressed sRNA loci. Using the available bioinformatics tools, I identified potential miRNAs and phased secondary sRNAs within the list of transgressively expressed loci. Target analysis of one of the transgressively expressed miRNAs linked it with the transgressive expression of certain phased loci, suggesting a potential for sRNAs to be able to set up heritable epigenetic marks in recombinant C. reinhardtii cells.

Chlamydomonas reinhardtii can utilize CO2 for autotrophic growth (HSM plus 5% CO2) or acetate for mixotrophic growth (TAP). This study was to elucidate the differential regulation of methionine sulfoxide reductase (MSR) gene expression between HSM plus 5% CO2 and TAP cultured cells, and also to determine the difference of gene expression in response to high light (1,000 £gE m-2 s-1). The role of photosynthetic electron transport (PET) in the regulation of MSR gene expression was also examined by the use of PET inhibitors. High light inhibited PSII activity (Fv/Fm and Fv'/Fm') of HSM plus 5% CO2 and TAP cultured cells., while the responses of CrMSR gene expression in mixotrophically grown cells were different from autotrophically grown cells, High light increased the expression of CrMSRA1, CrMSRA2, CrMSRA3, CrMSRA5, CrMSRB1.2, and CrMSRB2.1, but inhibited the expression of CrMSRA4 and CrMSRB2.2 in autotrophically grown cells. The expression of CrMSRA3, CrMSRA5, and CrMSRB2.1 in mixotrophically grown cells was increased by high light but that of CrMSRA1, CrMSRA4, and CrMSRB2.2 was inhbited. The number of MSR isoform that was up-regulated by high light was greater in autotrophically grown cell than that in mixotrophically grown cells. Using the PET inhibitors (3-(3,4-dichlorophenyl)-1,1- dimethylurea (DCMU) and 2,5-dibromo-3-methyl-6-isopropyl-p-benzoquinone (DBMIB)), most of the CrMSRA expression was regulated by reduced QA for autotrophically grown cells while reduced PQ was the main site for mixotrophically grown cells by high light. The expression of CrMSRB in autotrophically grown cells was mainy modulated by QA (-) or Cytb6f (-), while that was not affected by PET, except a role of Cytb6f (-) on the high light-induced CrMSRB2.2 expression. We fouind that CrMSRB gene expression in autotrophically grown cells was highly affected by PET but not for micotrophically grtown cells. The present result that H2O2 did not accumulate in autotrophically and mixotrophically grown cells suggests that H2O2 may be not involved in the regulation of high light regulation of CrMSR gene expression. The present study shows that the mRNA expression of CrMSR isoforms in Chlamydomonas was diffrerentially regulated between autotrophically and mixttrophically grown cells. The relationship between the utilization of different C source and CrMSR gene expression will be discussed.

L’explosion de la nanotechnologie a permis l’intégration d’une multitude de nanoparticules dans des produits de consommation. Les nanoparticules d’argent (nAg) sont les plus utilisées à ces fins, selon les derniers recensements disponibles. La plupart des études toxicologiques, à ce jour, ont fait état de l’implication très évidente de l’ion Ag+ dans la toxicité aigüe des nAg; cependant, quelques études ont mis en évidence des effets toxicologiques dus aux nAg. Il y a un certain consensus à propos d’un risque de contamination des eaux douces via leur rejet par les effluents des réseaux d’aqueducs. Puisque les concentrations en Ag+ sont généralement très faibles dans les eaux douces (de l’ordre du pg L-1), de par la formation de complexes non-labiles avec des thiols (organiques et inorganiques) et des sulfures, la toxicité inhérente aux nAg pourrait ne pas être négligeable- comparativement aux tests en laboratoires. Cette étude s’intéressait donc aux mécanismes de bioaccumulation d’argent par l’algue verte C. reinhardtii suite à l’exposition à des nAg de 5 nm (enrobage d’acide polyacrylique). La bioaccumulation d’argent pour l’exposition à Ag+ servait de point de comparaison; également, les abondances de l’ARNm de l’isocitrate lyase 1 (ICL1) et de l’ARNm de Copper Transporter 2 (CTR2) étaient mesurées comme témoins biologiques de la bioaccumulation de Ag+. Les expériences ont été menées en présence d’un tampon organique (NaHEPES, 2 x 10-2 M; Ca2+, 5x 10-5 M) à pH de 7,00. Pour des expositions à temps fixe de 2 heures, la bioaccumulation d’argent pour nAg était supérieure à ce qui était prédit par sa concentration initiale en Ag+; cependant, il n’y avait pas de différence d’abondance des ARNm de ICL1 et de CTR2 entre nAg et Ag+. D’un autre côté, pour une exposition à temps variables, la bioaccumulation d’argent pour nAg était supérieure à ce qui était prédit par sa concentration initiale en Ag+ et une augmentation de l’abondance de l’ARNm de ICL1 était notée pour nAg. Cependant, il n’y avait aucune différence significative au niveau de l’abondance de l’ARNm de CTR2 entre nAg et une solution équivalente en Ag+. L’ajout d’un fort ligand organique (L-Cystéine; log K= 11,5) à une solution de nAg en diminuait radicalement la bioaccumulation d’argent par rapport à nAg-sans ajout de ligand. Par contre, l’abondance des ARNm de ICL1 et de CTR2 étaient stimulées significativement par rapport à une solution contrôle non-exposée à nAg, ni à Ag+. Les résultats suggéraient fortement que les nAg généraient des ions Ag+ au contact de C. reinhardtii. / The recent developments in nanotechnology have given rise to a new and increasing economical market where nanoparticles are at the forefront. Recent inventories of the nanoparticles-containing products have shown that silver nanoparticle- containing products are the most frequently used consumer nanomaterial. Due to the fear of a large scale contamination-and even pollution- of the aquatic environment from silver nanoparticles (nAg), studies have been conducted to assess their toxicities, which, in many cases, have been found to be mediated by the concomitant presence of Ag+. Notably, few studies have found evidence of toxicity due to the nAg, per se. Since numerous non-labile complexes are formed with Ag+ in freshwaters- especially with thiols and sulfides-, nAg toxicity might be more relevant in comparison to laboratory tests where the Ag+ tends to dominate toxicity studies. Therefore, this study investigated the mechanisms underlying silver bioaccumulation by the green alga, C. reinhardtii upon exposure to solutions of nAg (nominal size of 5 nm; poly-acrylate coating). Silver bioaccumulation upon exposures to the free ion alone served for comparison. In parallel, the abundance of two mRNAs- ICL1 and CTR2- were used to better understand the mechanisms underlying the bioaccumulation of Ag+ (and potentially nAg). The experiments were conducted in pH buffered solutions (NaHEPES, 2 x 10-2 M; Ca2+, 5x 10-5 M) at pH 7.00. For 2-hour exposures, the silver bioaccumulation for solutions of nAg exceeded what was expected from their Ag+ content only; however, no differences were noticed in the abundance of the expression of ICL1 and CTR2. For variable time exposures, the silver bioaccumulation for solutions of nAg exceeded what was expected from their Ag+ content only. Moreover, the expression of ICL1 was significantly higher for nAg than what was expected based upon an exposure to Ag+ only. When exposed to nAg, expression levels of CTR2 could be predicted from levels based solely on the Ag+ concentrations. The addition of a large excess of L-Cysteine, which is a very strong silver ligand (log K =11.5), to a nAg solution largely decreased silver bioaccumulation, however, bioaccumulation remained significant and the expression of both ICL1 and CTR2 were significantly higher than that of the control solutions (without Ag+). The results strongly suggest that nAg generated Ag+ ions when in contact with C. reinhardtii and that the nAg released to freshwaters might exert its toxicity through organism-contact-dependant release of Ag+.

The first type of dynein identified, axonemel dynein (Gibbons and Rowe, 1965), slides adjacent microtubules within the axoneme, generating the force necessary for ciliary and flagellar beating. The outer dynein arm is an important component of the flagellar axoneme, providing up to 60% of the force for flagellar motility. In the absence of the outer arm, cells swim with a slow-jerky motion at about 1/3rd the speed of wild-type cells, and the flagellar beat frequency is markedly reduced. Sixteen genes (ODA1-ODA16) have been identified that are required for outer arm assembly in Chlamydomonas reinhardtii. In addition, PF13, PF22, and FLA14 are required for outer dynein arm assembly, but their phenotypes are pleiotropic, suggesting that they affect additional flagellar components. Of the uncloned genes, ODA5, ODA8, and ODA10 are of particular interest because they do not encode subunits of the outer arm or the outer dynein arm-docking complex (ODA-DC). Mutant alleles of these genes are unable to complement in temporary dikaryons, suggesting that the gene products interact with each other (Kamiya, 1988). Since the genes encoding all of the known components of the outer dynein arm and the ODA-DC have been characterized, it is of great interest to identify the gene products of these additional, uncloned ODA alleles. The first chapter provides an introduction to the Chlamydomonasflagellum, the dyneins in general, the outer dynein arm in particular, and mutations that impinge on the assembly and regulation of this important axonemal structure. The second chapter addresses the identification and isolation of genomic DNA containing the ODA5 gene. Utilizing a NIT1-tagged oda5-insertional mutant, I identified sequences flanking the site of the inserted NIT1 gene. These sequences were used to isolate wild-type genomic clones spanning the ODA5 gene. When transformed into the oda5 mutant, the wild-type clones rescued the mutant phenotype. These results demonstrated the successful isolation of the ODA5 gene. The third chapter describes the identification of the ODA5 gene and its corresponding cDNA. The rescuing genomic fragments were sequenced. Gene modeling was used to predict intron-exon splice sites. Primers to predicted exons were designed and used to obtain the ODA5 cDNA. The gene structure of Oda5 was analyzed and its predicted amino acid sequence deduced. Secondary structure predictions indicate that Oda5p is likely to contain a series of coiled-coil domains, followed by a poly-glycine sequence and a short, highly charged region. Northern analysis demonstrated that ODA5 gene expression is upregulated by deflagellation, a hallmark of many flagellar mRNAs. Data in CHAPTER IV further characterize the Oda5 protein and its association with the axoneme. Oda5p localizes to the flagellum, consistent with the enhancement in mRNA levels in response to deflagellation. Within the flagellum, Oda5p is an axonemal component that is released from the axoneme upon high salt extraction, as are the ODA-DC and the outer dynein arm. However, Oda5p does not associate with this super-complex in the high salt extract as determined by sucrose gradient sedimentation. Oda5p assembles onto the axoneme independently of the outer dynein arm and the ODA-DC,demonstrating it does not require these complexes for localization. Furthermore, Oda5p assembles onto the axoneme in the oda8, but not the oda10 mutant, demonstrating a role for the Oda10 protein in localization of Oda5p. These data provide the first biochemical evidence for an interaction between Oda5p and Oda10p. CHAPTER V reveals the discovery of a previously unrecognized phenotype exhibited in both oda5 and oda10 mutant strains: a defect in the assembly of a previously unknown flagellar adenylate kinase (AK). The protein levels of this flagellar AK are reduced in oda5 mutant axonemes, as determined by quantitative mass spectrometry. Direct enzymatic assays confirmed a reduction in AK activity in both oda5 and oda10 mutant axonemes, providing a second line of biochemical evidence supporting a complex containing Oda5p and OdalOp. The sequence of the flagellar AK gene and its cDNA were determined. CHAPTER VI details our efforts to identify the ODA10 gene. Genomic clones were isolated, which contain sequences at, or near, the ODA10 locus. Analysis of the genomic clones yielded no insights into the identity of the ODA10 gene. The inability of these clones to rescue the Oda10-motility phenotype indicates that these clones most likely do not contain an intact ODA10 gene. And lastly, CHAPTER VII discusses future experimentation that can be done based on the data provided by the current study.