Search

Arylsulphatase, β-1,3 glucanase, phosphatase and urease responded differently to γ-irradiation (5-50 Mrad) in air-dried and moist soils. In all instances phosphatase was the most stable. The variability between enzymes may be due to inherent biochemical and stuctural characteristics or to their location within the soil microenvironment. [ABSTRACT FROM AUTHOR]

Bioremediation was investigated as a method of treating a mixture ofForties Crude Oil and Heavy Fuel Oil stranded on Bullwell Bay, Milford Haven, UK after the grounding of the Sea Empress in 1996. A randomised block design in triplicate was used to test the efficacy of two bioremediation treatments: a weekly application of mineral nutrients dissolved in seawater and a single application of a slow-release fertilizer. Each treatment supplied an equivalent amount of nitrogen and phosphorus. Concentrations of residual hydrocarbons normalised to thebiomarker 17a(H),21p(H)-hopane showed that after two months the oil was significantly (p<0.001) more biodegraded in the treated plots than in the controls. On average, the oil in the nutrient amended plots was 37% more degraded than that found in the controls. There was no evidence that the bioremediation treatments increased the toxicity of the oiled sediment. The results confirm that bioremediation can be used to treat a mixture of crude and heavy fuel oil on a pebble beach. In particular, the data suggest that the application of a slowreleasefertilizer alone may be a cost-effective method of treating low-energy, contaminated shorelines after a spill incident. [ABSTRACT FROM AUTHOR]

Introduction: Treatments for Adult ADHD include stimulants, two non-stimulant medications, as well as cognitive-behavioral therapy (CBT). These pharmacological agents are often associated with side effects, contributing to poor treatment adherence. Patients with ADHD have regularly stated that cannabis has helped improve their ADHD symptoms; however, scientific literature describing the effects of cannabis on symptoms of ADHD is scarce., Methods: We systematically searched MEDLINE, EMBASE, EMCARE, PsycINFO, Web of Science, Cochrane Library, and Clinicaltrials.gov. The searches included all publications in English up to June 27, 2022. We included both experimental and observational studies that assessed the effect of cannabis on ADHD symptomatology and neuropsychiatric outcomes. To synthesize our current understanding of the potential effects of cannabis use on ADHD symptoms and pathophysiology, and the effects of ADHD on cannabis use, data was extracted from each study regarding the characteristics of its population, methods used to assess both cannabis consumption and ADHD symptoms, and key findings., Results: Our scoping review included a total of 39 studies. Only one study employed a randomized and placebo-controlled design to directly measure the effect of cannabis on ADHD, and no significant effect was observed for the study's primary outcome, the QbTest (Est = -0.17, 95% CI -0.40 to 0.07, p = 0.16). Most of the literature consists of cross-sectional studies that evaluate the association between ADHD severity and cannabis use. 15 studies addressed the neuropsychiatric effects of cannabis on ADHD by employing either a battery of neuropsychiatric tests or neuroimaging. The concentration and amount of THC and CBD used were not well measured in most of the studies. Although some studies indicated that cannabis improved ADHD symptoms, most studies indicated it worsened or had no effect on ADHD symptoms., Conclusions: Given the current evidence, cannabis is not recommended for people with ADHD. Limitations of the literature include the absence of objective measurements for cannabis exposure and ADHD symptoms, heterogenous definitions, oversampling, and small sample sizes., (Copyright © 2022. Published by Elsevier Ltd.)

Exposure to pollution exerts strong selective pressure on microbial communities, which may affect their potential to adapt to current or future environmental challenges. In this microcosm study, we used DNA fingerprinting based on 16S rRNA genes to document the impact of high concentrations of benzene on two bacterial communities from a benzene-contaminated aquifer situated below a petrochemical plant (SIReN, UK). The two groundwaters harboured distinct aerobic benzene-degrading communities able to metabolize benzene to below detection levels (1 microg L(-1)). A benzene concentration of 100 mg L(-1) caused a major shift from Betaproteobacteria to Actinobacteria, in particular Arthrobacter spp. A similar shift from Betaproteobacteria to Arthrobacter spp. and Rhodococcus erythropolis was observed in minimal medium (MM) inoculated with a third groundwater. These Gram-positive-dominated communities were able to grow on benzene at concentrations up to 600 mg L(-1) in groundwater and up to 1000 mg L(-1) in MM, concentrations that cause significant solvent stress to cellular systems. Therefore, Gram-positive bacteria were better competitors than Gram-negative organisms under experimental conditions of high benzene loads, which suggests that solvent-tolerant Gram-positive bacteria can play a role in the natural attenuation of benzene or the remediation of contaminated sites.

In this study we analysed the relationship between bacterial community structures and geochemistry of groundwater in a sandstone aquifer (SIReN site) impacted mainly by BTEX hydrocarbons (benzene, toluene, ethylbenzene and xylenes), of which benzene is most abundant. The long-term presence of benzene reduced bacterial diversity: in groundwaters contaminated with more than 1.8 x 10(4) microg l(-1) of benzene, bacterial diversity was half of that in clean groundwaters. Terminal restriction fragment length polymorphism (T-RFLP) analysis of 16S rDNA revealed that the community structures were very similar in uncontaminated groundwaters, whereas communities subjected to long-term benzene contamination were different, not only from uncontaminated groundwater communities, but also from each other. Canonical correspondence analysis of the community profiles and the geochemical data showed that this divergence in community structure was not primarily caused by the direct toxic or stressful effects of benzene, but by the environmental changes brought about by benzene metabolism, in particular a decrease in redox potential.

The release of 14CO2 from 9-[14C]phenanthrene, 4,5,9,10-[14C]pyrene and 7-[14C]benzo[a]pyrene, added to Brent/Fortes crude oil and mixed into a pristine sand soil (0.40% organic C) and a pristine organic soil (22.9% organic C), was determined. After 244 days at 25 degrees C, 11.1 +/- 3.5% (sand) and 17.1 +/- 0.30% (organic) phenanthrene-14C and 9.77 +/- 2.8% (sand) and 5.86 +/- 1.4% (organic) benzo[a]pyrene-14C was released. After 210 days, 3.65 +/- 0.5% (sand) and 4.43 +/- 0.33% (organic) pyrene-14C was released. Inoculation of these two soils with DC1 and PD2 (bacteria capable of accelerating the phenanthrene and pyrene mineralisation in soil in the absence of crude oil) either at day 0 or after release as 14CO2 by indigenous degraders had ceased, failed to increase or initiate further mineralisation. Thus, aged PAH residues were non-bioavailable to these metabolically competent degrading microorganisms. At the end of the first period of incubation (210 days or 244 days), the total aromatic hydrocarbons recovered using Soxhlet extraction was 0.18% (sand) and 42.8% (organic) compared with approximately 100% from bio-inhibited soils. This confirmed that the indigenous microbiological activity not only caused a limited amount of PAH mineralisation but also reduced the extractability of residues, possibly due to the generation of metabolites which were chemisorbed and bound (and non extractable) in 'aged' soils.

Inoculation of soil with bacteria (a Gram-negative rod [PD2] and a 4-membered consortium [DC1]) accelerated mineralisation of phenanthrene and pyrene (but not naphthalene) added individually to a pristine sand and a pristine organic soil. The half-life of naphthalene was 3.5 days in both soils whether inoculated or non-inoculated. However, the half-life of phenanthrene decreased from 86 days in non-inoculated sand soil and 80 days in the non-inoculated organic soil to 3.6 days in the sand and 3.1 days in organic soil when inoculated with PD2, and to 6.6 days in the sand and 8.7 days in the organic soil when inoculated with DC1. Phenanthrene mineralisation ceased after 23 days in DC1-inoculated soil and was 71.3 +/- 3.6% (sand) and 63.3 +/- 2.8% (organic). This compared with 96.8 +/- 3.8% (sand) 102.8 +/- 2.5% (organic) after 8 days in PD2-inoculated soil. Inoculation with DC1 (but not PD2) also accelerated mineralisation of pyrene, where the half-life decreased from 155 days to 18 days in the sand soil, and from 216 days to 33 days in organic soil.