Visitor guide, United States Botanic Garden.

"4/08."

Contribuição para a valorização, geoconservação e gestão da jazida fossilífera de Cacela (Parque Natural da Ria Formosa, Algarve, Portugal)

Dissertação de mest. em Gestão e Conservação da Natureza, Faculdade de Ciências do Mar e do Ambiente, Univ. do Algarve, 2004

The Mind of primitive man : a course of lectures delivered before the Lowell Institute, Boston, Mass., and the National University of Mexico, 1910-1911 /

Partly reprinted from various sources.

Proceedings of the Massachusetts national Democratic convention : and of the mass meeting for the ratification of the nominations of Breckinridge & lane, held at the Tremont Temple, Boston, Sept. 12, 1860.

Mode of access: Internet.

Bioremediation of PAHs - Limitations and soultions

Introduction 1.1 Occurrence of polycyclic aromatic hydrocarbons (PAH) in the environment Worldwide industrial and agricultural developments have released a large number of natural and synthetic hazardous compounds into the environment due to careless waste disposal, illegal waste dumping and accidental spills. As a result, there are numerous sites in the world that require cleanup of soils and groundwater. Polycyclic aromatic hydrocarbons (PAHs) are one of the major groups of these contaminants (Da Silva et al., 2003). PAHs constitute a diverse class of organic compounds consisting of two or more aromatic rings with various structural configurations (Prabhu and Phale, 2003). Being a derivative of benzene, PAHs are thermodynamically stable. In addition, these chemicals tend to adhere to particle surfaces, such as soils, because of their low water solubility and strong hydrophobicity, and this results in greater persistence under natural conditions. This persistence coupled with their potential carcinogenicity makes PAHs problematic environmental contaminants (Cerniglia, 1992; Sutherland, 1992). PAHs are widely found in high concentrations at many industrial sites, particularly those associated with petroleum, gas production and wood preserving industries (Wilson and Jones, 1993). 1.2 Remediation technologies Conventional techniques used for the remediation of soil polluted with organic contaminants include excavation of the contaminated soil and disposal to a landfill or capping - containment - of the contaminated areas of a site. These methods have some drawbacks. The first method simply moves the contamination elsewhere and may create significant risks in the excavation, handling and transport of hazardous material. Additionally, it is very difficult and increasingly expensive to find new landfill sites for the final disposal of the material. The cap and containment method is only an interim solution since the contamination remains on site, requiring monitoring and maintenance of the isolation barriers long into the future, with all the associated costs and potential liability. A better approach than these traditional methods is to completely destroy the pollutants, if possible, or transform them into harmless substances. Some technologies that have been used are high-temperature incineration and various types of chemical decomposition (for example, base-catalyzed dechlorination, UV oxidation). However, these methods have significant disadvantages, principally their technological complexity, high cost , and the lack of public acceptance. Bioremediation, on the contrast, is a promising option for the complete removal and destruction of contaminants. 1.3 Bioremediation of PAH contaminated soil & groundwater Bioremediation is the use of living organisms, primarily microorganisms, to degrade or detoxify hazardous wastes into harmless substances such as carbon dioxide, water and cell biomass Most PAHs are biodegradable unter natural conditions (Da Silva et al., 2003; Meysami and Baheri, 2003) and bioremediation for cleanup of PAH wastes has been extensively studied at both laboratory and commercial levels- It has been implemented at a number of contaminated sites, including the cleanup of the Exxon Valdez oil spill in Prince William Sound, Alaska in 1989, the Mega Borg spill off the Texas coast in 1990 and the Burgan Oil Field, Kuwait in 1994 (Purwaningsih, 2002). Different strategies for PAH bioremediation, such as in situ , ex situ or on site bioremediation were developed in recent years. In situ bioremediation is a technique that is applied to soil and groundwater at the site without removing the contaminated soil or groundwater, based on the provision of optimum conditions for microbiological contaminant breakdown.. Ex situ bioremediation of PAHs, on the other hand, is a technique applied to soil and groundwater which has been removed from the site via excavation (soil) or pumping (water). Hazardous contaminants are converted in controlled bioreactors into harmless compounds in an efficient manner. 1.4 Bioavailability of PAH in the subsurface Frequently, PAH contamination in the environment is occurs as contaminants that are sorbed onto soilparticles rather than in phase (NAPL, non aqueous phase liquids). It is known that the biodegradation rate of most PAHs sorbed onto soil is far lower than rates measured in solution cultures of microorganisms with pure solid pollutants (Alexander and Scow, 1989; Hamaker, 1972). It is generally believed that only that fraction of PAHs dissolved in the solution can be metabolized by microorganisms in soil. The amount of contaminant that can be readily taken up and degraded by microorganisms is defined as bioavailability (Bosma et al., 1997; Maier, 2000). Two phenomena have been suggested to cause the low bioavailability of PAHs in soil (Danielsson, 2000). The first one is strong adsorption of the contaminants to the soil constituents which then leads to very slow release rates of contaminants to the aqueous phase. Sorption is often well correlated with soil organic matter content (Means, 1980) and significantly reduces biodegradation (Manilal and Alexander, 1991). The second phenomenon is slow mass transfer of pollutants, such as pore diffusion in the soil aggregates or diffusion in the organic matter in the soil. The complex set of these physical, chemical and biological processes is schematically illustrated in Figure 1. As shown in Figure 1, biodegradation processes are taking place in the soil solution while diffusion processes occur in the narrow pores in and between soil aggregates (Danielsson, 2000). Seemingly contradictory studies can be found in the literature that indicate the rate and final extent of metabolism may be either lower or higher for sorbed PAHs by soil than those for pure PAHs (Van Loosdrecht et al., 1990). These contrasting results demonstrate that the bioavailability of organic contaminants sorbed onto soil is far from being well understood. Besides bioavailability, there are several other factors influencing the rate and extent of biodegradation of PAHs in soil including microbial population characteristics, physical and chemical properties of PAHs and environmental factors (temperature, moisture, pH, degree of contamination). Figure 1: Schematic diagram showing possible rate-limiting processes during bioremediation of hydrophobic organic contaminants in a contaminated soil-water system (not to scale) (Danielsson, 2000). 1.5 Increasing the bioavailability of PAH in soil Attempts to improve the biodegradation of PAHs in soil by increasing their bioavailability include the use of surfactants , solvents or solubility enhancers.. However, introduction of synthetic surfactant may result in the addition of one more pollutant. (Wang and Brusseau, 1993).A study conducted by Mulder et al. showed that the introduction of hydropropyl-ß-cyclodextrin (HPCD), a well-known PAH solubility enhancer, significantly increased the solubilization of PAHs although it did not improve the biodegradation rate of PAHs (Mulder et al., 1998), indicating that further research is required in order to develop a feasible and efficient remediation method. Enhancing the extent of PAHs mass transfer from the soil phase to the liquid might prove an efficient and environmentally low-risk alternative way of addressing the problem of slow PAH biodegradation in soil.

Ecological investigations in the wadden area off Borkum, East Frisian Islands, Germany

Die Bodentiergemeinschaft des Wattenmeeres ist von Frühjahr bis Herbst eines jeden Jahres durch extrem hohe Dichten von Jungtieren charakterisiert. Die Kenntnisse über die Ansiedlung von fplanktischen Larven im Wattenmeer, sowie die Dynamik postlarvaler Stadien sind aufgrund der üblicherweise verwendeten, großen Siebmaschenweiten gering. Gerade aber diesen Altersstadien kommt möglicherweise eine besondere Stellung im Energiefluß des Wattenmeeres zu. An 5 Stationen (von NWL bis HWL, B1-B5) im Rückseitenwatt der ostfriesischen Insel Borkum wurden 1986 Ansiedlung, räumliche Verteilung, Wachstum, Mortalität und Produktion der Altersklasse 0 von Macoma balthica, Mya arenaria und Cerastoderma edule untersucht. Um die Ansiedlung der planktotrophen Larven dieser Arten zu beschreiben, wurden ihre Dichten in Plankton und Bodenproben miteinander verglichen. Die Untersuchungen zur Dynamik der benthischen Stadien wurden mit zwei in der Probenfläche und der Siebmaschenweite unterschiedlichen Probenserien durchgeführt. Die Drift postlarvaler Stadien wurde durch bodennahe Planktonfänge innerhalb des Eulitorals nachgewiesen. Parallel zu den Untersuchungen an der Endofauna wurden das Vorkommen und die Größe epibenthischer Räuber im Untersuchungsgebiet erfaßt. Die Hauptansiedlung von M. balthica- und M. arenaria-Larven erfolgte nahezu gleichzeitig Ende Mai/Anfang Juni. Die meisten Larven beider Arten gingen an der prielnächsten (tiefsten) Station (B1) zum Bodenleben über, gefolgt von der nächst höher gelegenen Station B2. Während frühe Bodenstadien von M. arenaria nicht im oberen Bereich des Watts (B3,B4) gefunden wurden, ist eine geringfügige Erstansiedlung von M. balthica in diesem Gebiet nicht auszuschließen. Ein die Ansiedlung limitierender Einfluß der relativ dichten Mya arenaria-Siedlung an den Stationen B1 und B2 sowie der Alttiere von M. balthica konnte nicht festgestellt werden. Die Ähnlichkeit des Ansiedlungsprozesses bei beiden Arten, die sich im Zahlenverhältnis Larvenangebot zu Anzahl der ersten Bodenstadien widerspiegelt, kann ein Hinweis auf eine überwiegend passive Ansiedlung der Larven am Boden sein. Der Ort der Hauptansiedlung von C. edule wurde durch den Transekt nicht erfaßt. Die Station B2 war zwar durch ein Herzmuschelfeld charakterisiert, dieses war aber nach zwei Eiswintern nahezu vollständig eliminiert. Der Abundanz der planktischen Larven zufolge war der Hauptansiedlungszeitraum ebenfalls Ende Mai/Anfang Juni. Zu dieser Zeit wurden nur vereinzelt frühe Bodenstadien an den Stationen B1 und B2 gefunden, keine an den Stationen B3 und B4. Während die frühen postlarvalen Stadien von M. arenaria überwiegend am Ort der Ansiedlung blieben, verbreiteten sich die von M. balthica bis in den oberen Bereich des Untersuchungsgebietes (B3-B5). Analog zu der Besiedlung dieser Gebiete durch postlarvale M. balthica wurde die im Verlauf des Untersuchungsjahres stattfindende Kolonisierung der Station B1 durch C. edule ebenfalls postlarvalem Transport zugeschrieben. Demzufolge spielt bei beiden Muschelarten postlarvaler Transport eine wichtige Rolle bei der Besiedlung von Habitaten. Planktonfänge innerhalb der bodennahen Wasserschicht bestätigten, daß im Untersuchungsgebiet M. balthica die am stärksten verdriftende Muschelart war, gefolgt von C. edule. Mortalität, Wachstum, mittlere Biomasse, Produktion und P/B-Verhältnis wurden für M. balthica an den Stationen B1, B3 und B4 sowie für M. arenaria an der Station B1 bestimmt. Wachstum und damit auch Produktion beider Arten erwiesen sich hier - wie an den höher gelegen Stationen (nur M. balthica) - als durch größenselektiven Feinddruck beeinflußt. Der Effekt postlarvalen Transports auf Wachstum wird diskutiert. Übergreifend über die auf Artebene diskutierten Ergebnisse wird die Bedeutung der Dispersion postlarvaler Stadien und die Wirkung epibenthischen Feinddrucks im Wattenmeer erörtert. Der Vergleich postlarvalen Transportes mit der Dispersion planktischer Larvenstadien, der Dispersion von Meiofauna und der Mobilität adulter Stadien der Makrofauna verdeutlicht, daß es sich hierbei um eine Strategie handeln kann, innerhalb eines unvorhersagbaren Biotops freiwerdende Ressourcen zu nutzen und dadurch Konkurrenz zu vermeiden. Es wird die Hypothese aufgestellt, daß Initialansiedlung und Immigration einerseits sowie Feinddruck und Emigration andererseits einen Regelkreis darstellen, der in verschiedenen Teilbereichen des Watts mit unterschiedlicher Geschwindigkeit abläuft.

On the fine structure of oxygen distribution in surface water layers in the area between Iceland and Faroe Islands

During the international "Overflow-Expedition'' 1973 on R.V. "Meteor" oxygen concentrations in surface layers were measured in order to determine the oxygen gradients within the first two meters and to add some informations to the mechanisms of oxygen exchange at the air-sea interface. These investigations may be interesting also with regard to longterm- observations of the oxygen distribution in the Atlantic, especially the problem of the A.O.U. (apparent oxygen utilization) determination. To measure oxygen gradients a special sampler was built which is able to take water samples each 20 cm of the first 2 meters. These data were supplemented by further samples down to 150 m, taken by conventional water samplers, from which samples were also taken to measure N2/O2-relations. By comparing these relations with theoretical relations in air-saturated water the influence of biological production and consumption on the oxygen contents in water could be estimated. A simple glass apparatus was built to extract gas from the water samples, and hereafter the N2/O2-relations were determined by mass spectrometry. Most distributions of the oxygen anomaly show a negative oxygen balance which varies largely, probably due to strong mixing processes in the Iceland-Faroe ridge area. The distribution of surface oxygen saturation values are of two different types. The values of the stations 260, 262 and 270 stem from mixed water and show homogeneous supersaturations, as can be found instantly when whitecaps appear. The values of 9 other stations are from water, sampled during calm periods which has been mixed and supersaturated before. They show a decreasing oxygen saturation towards the sea surface and often undersaturation in the upper decimeters up to 98 % and even 91 %. So at the air-sea interface even less initial oxygen saturation than 100 % can be found after supersaturation during heavy weather periods.