Projected length annealing of etched Sm-152 ion tracks in apatite

Conselho Nacional de Desenvolvimento Científico e Tecnológico (CNPq)

Melle H. Beard Photograph Album - Accession 276 - M119 (152)

The Melle H. Beard Photograph Album collection consists of a photograph album of with images of Winthrop buildings, campus scenes, and pictures of Mrs. Beard and her friends while students at Winthrop College from 1917-1919. Melle Hanahan Beard from Charlotte, NC was a 1919 graduate of Winthrop Normal and Industrial College with an AB degree in Education.

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.

Dose escalation and pharmacokinetic study of AEZS-108 (AN-152), an LHRH agonist linked to doxorubicin, in women with LHRH receptor-positive tumors

Receptors for luteinizing hormone-releasing hormone (LHRH) can be utilized for targeted chemotherapy of cytotoxic LHRH analogs. The compound AEZS-108 (previously AN-152) consists of [D-Lys?]LHRH linked to doxorubicin. The objectives of this first study in humans with AESZ-108 were to determine the maximum tolerated dose and to characterize the dose-limiting toxicity, pharmacokinetics, preliminary efficacy, and hormonal effects.

A urokinase receptor promoter element (-152/-135) bound with an AP-2-alpha-related protein and SP1 is required for the induction of gene expression by PMA and SRC

The urokinase-type plasminogen activator receptor (u-PAR) promotes extracellular matrix degradation, invasion and metastasis. A first objective of this dissertation was to identify cis-elements and trans-acting factors activating u-PAR gene expression through a previously footprinted (–148/–124) promoter region. Mobility shifting experiments on nuclear extracts of a high u-PAR-expressing colon cancer cell line (RKO) indicated Sp1, Sp3 and a factor similar to, but distinct from, AP-2α bound to an oligonucleotide spanning –152/–135. Mutations preventing the binding of the AP-2α-related factor reduced u-PAR promoter activity. In RKO, the expression of a dominant negative AP-2 (AP-2αB) diminished u-PAR promoter activity, protein and u-PAR mediated laminin degradation. Conversely, u-PAR promoter activity in low u-PAR-expressing GEO cells was increased by AP-2αA expression. PMA treatment, which induces u-PAR expression, caused an increased amount of the AP-2α-related factor-containing complex in GEO, and mutations preventing AP-2α-like and Sp1/Sp3 binding reduced the u-PAR promoter stimulation by PMA. In resected colon cancers, u-PAR protein amounts were related to the amount of the AP-2α-related factor-containing complex. In conclusion, constitutive and PMA- inducible u-PAR gene expression and -proteolysis are mediated partly through transactivation via a promoter sequence (–152/435) bound with an AP-2α-related factor and Sp1/Sp3. ^ A second interest of this dissertation was to determine if a constitutively active Src regulates the transcription of the u-PAR gene, since c-src expression increases invasion in colon cancer. Increased u-PAR protein and laminin degradation paralleling elevated Src activity was evident in SW480 colon cancer cells stably expressing a constitutively active Src (Y- c-src527F). Nuclear run-on experiments indicated that this was due largely to transcriptional activation. While transient transfection of SW480 cells with Y-c-src527F induced a u-PAR-CAT-reporter, mutations preventing Sp1-binding to promoter region –152/435 abolished this induction. Mobility shift assays revealed increased Sp1 binding to region –152/135 with nuclear extracts of Src-transfected SW480 cells. Finally, the amounts of endogenous u-PAR in resected colon cancers significantly correlated with Src-activity. These data suggest that u-PAR gene expression and proteolysis are regulated by Src, this requiring the promoter region (–152/–135) bound with Sp1, thus, demonstrating for the first time that transcription factor Sp1 is a downstream effector of Src. ^

Ms. hebr. oct. 152 - Rashi ʻal ha-Torah

Vorbesitzer: Abraham Merzbacher

Ms. Barth. 152 - Medizinische Sammelhandschrift

Vorbesitzer: Bartholomaeusstift Frankfurt am Main