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How can I buy cocaine online in Ruda Slaska

Official websites use. Share sensitive information only on official, secure websites. The images or other third party material in this article are included in the article's Creative Commons licence, unless indicated otherwise in a credit line to the material. If material is not included in the article's Creative Commons licence and your intended use is not permitted by statutory regulation or exceeds the permitted use, you will need to obtain permission directly from the copyright holder. Sulfonamides circulating in the environment lead to disturbances in food chains and local ecosystems, but most importantly contribute to development of resistance genes, which generate problems with multidrug-resistant bacterial infections treatment. In urban areas, sources of sulfonamide distribution in soils have received comparatively less attention in contrast to rural regions, where animal-derived manure, used as a natural fertilizer, is considered the main source. The aim of this study was to determine eight sulfonamides sulfadiazine, sulfamerazine, sulfamethazine, sulfamethizole, sulfamethoxazole, sulfapyridine, sulfathiazole, and sulfisoxazole in environmental soil samples collected from urbanized regions in Silesian Voivodeship with increased animal activity. These soils were grouped according to the organic carbon content. It was necessary to develop versatile and efficient extraction and determination method to analyze selected sulfonamides in various soil types. The obtained results show the high impact of organic matter on analytes adsorption in soil, which influences recovery. All eight sulfa drugs were determined in environmental samples in the concentration range 1. The transformation products of the analytes were also identified, and 29 transformation products were detected in 24 out of 27 extracts from soil samples. Sulfonamides SAs are a group of compounds with a broad spectrum of activity against bacteria and protozoa of the genera Toxoplasma and Plasmodium. SAs are analogs of para-aminobenzoic acid SA core , the activity of which depends on the type of amine attached to the SA core Yousef et al. The widespread and long-term use of SAs in medicine has greatly affected the environment by contaminating surface waters, groundwater, and soil Sacher et al. The adsorption of SAs on soil particles increases with the aromaticity and electronegativity of the substituent attached to the SA core Thiele-Bruhn et al. In a study carried out on 13 types of soil, it was found that the sorption of SAs strongly depends on soil properties, such as the content of organic carbon OC Leal et al. Soil pH may also influence on the sorption of selected SAs. For example, the sulfamethazine SFM sorption coefficient depends on the soil pH, but it is not the dominant factor Lertpaitoonpan et al. Primary sources of SAs in soil environment are manure or slurry Pan et al. The type of soil, the type of fertilizers used, and the presence of plants significantly influence the dispersion and accumulation of SAs in the soil environment Leal et al. The occurrence of SAs in soils might also be influenced by wastewater discharges, although it has not been definitively proven Yi et al. Once introduced into the soil, SAs are transformed into transformation products TPs. SAs are mainly biodegradable due to the action of heterotrophic microorganisms, e. Within the literature, the most described degradation reactions of SAs in the environment are acetylation, hydroxylation, nitration, nitrosation, glucosidation and glucuronidation. However, it is possible for multiple transformation reactions to occur simultaneously, including those originating from human metabolism Majewsky et al. The pathways of SAs transformation under environmental conditions are not fully understood, and most of the papers dealing with the topic focus on the degradation of SMX Barbieri et al. The residues of SAs and their TPs are potentially harmful to humans. Based on the toxicity tests of SAs, it was found that their residues in aquatic environment showed an additive toxic effect for the tiny vascular plants, as e. Additionally, SAs presence in the environment not only contributes to antibiotic-resistant pathogens development, but also to the spread of resistance genes Ayukekbong et al. Hoff et al. Due to the complexity of the soil matrix and its variable composition, it is necessary to use multi-stage procedures to extract and clean samples before analysis Hoff et al. Despite the many developed and validated soil preparation procedures, they are characterized by low reproducibility. Our previous report found that most of the literature on procedures for extracting pharmaceuticals from the soil does not provide information on soil type and characteristics Stando et al. It can be assumed that the soil composition in particular, OC content influences the recovery of the analytes. Understanding the relationship between soil matrix composition and analyte recovery is extremely important for accurate monitoring studies of soils with various compositions. Proper sample preparation is crucial, especially when determining trace amounts of compounds like SAs. This study aimed to develop a procedure for isolating and determining SAs in soils with different compositions. In the first step, soils with various OC content, pH, and elemental composition were used to develop the extraction procedure. The procedure has been validated, and the recovery has been determined at four levels of OC content. The developed procedure was applied to environmental samples of soil collected in the Silesian Voivodeship. In monitoring studies, 27 soil samples were collected from areas where increased animal activity was observed. An additional aim of the study was to identify the TPs of SAs in soil. For each SAs, the solubility in different solvents was examined, and the solvent for each SA was selected experimentally based on its observed solubility. Stock solutions were prepared with concentrations of 1 mg mL All the working stock solutions mixtures of selected SAs were obtained by diluting standard solutions with methanol. Twenty-seven environmental surface soil samples 0—20 cm were collected from cities in the Silesian Voivodeship, Poland, located in the temperate climate zone. From each sampling site, 1 kg of soil was collected from enclosed dog paddocks, recreational areas near the lakes, and agricultural fields. No information is available on fertilization of farmlands. Then samples were homogenized and placed in plastic containers. The entire method development was conducted on soil with medium OC content blank sample without SAs spiked with SAs standard stock solution to achieve the concentration of ng g SLE parameters, such as extraction solvents, shaking time, and the use of ultrasound, were tested to improve SAs recovery. The volume of the SLE solvent was constant at 10 mL for 1 g of soil. The order of the performed steps was as follows — sonication 10 min , followed by shaking 30 or 60 min , and finally centrifugation 10 min. In procedures 2—7, extractions were repeated with new portions of solvent. Shaking was conducted with a Vibramax orbital shaker with nine flask clamps Heidolph Instruments, Schwabach, Germany with rpm selected as an optimum speed. A Hermle Z K centrifuge with a rotor for 12 tubes Hermle Labortechnik, Wehingen, Germany was used for isolating solid particles from the extracts. Solutions collected from each extraction were combined and diluted to mL with water. Then the soil-solvent suspension was shaken for 60 min at rpm and centrifuged for 10 min at rpm. This step was repeated with another 10 mL portion of the extraction solvent. Before the sample was passed through, the sorbent was conditioned with solvents in an appropriate order. The sample was loaded to the sorbent, which was then dried for 30 min, and the analytes were eluted with 12 mL 0. The mobile phase consisted of A 0. Elution was performed using the following gradient system: 0. The detector was equipped with an electrospray ionization ESI source, which was operated in positive ion mode for all the SAs. For qualitative and quantitative analysis, multiple reaction monitoring MRM mode was used. Due to rich soil matrices and their significant impact on analytes determination, the OC content and pH of every soil used in this study was examined. The content of elements such as Al, Ca, Mg, Na, and K was also assessed because of scientific reports suggesting the possible effect of these ions on the adsorption of SAs in soils Xu et al. Each soil sample was prepared in three replicates, each of which was measured three times. The percentage carbon content quantification was based on a calibration curve, and standard deviations were also calculated. The pH value was measured according to the ISO standard using soil-water suspensions. For each sample, the soil measurement was performed three times. Al, Ca, Mg, Na, and K were chosen due to their essential functions in the sorption of chemicals in soil. The content of the selected elements was assessed using inductively coupled plasma atomic emission spectroscopy ICP-AES. Initially, samples were prepared by microwave mineralization in aqua regia solution. Prior to analysis, the samples were diluted with distilled water. Samples were prepared in three replicates, each of which was measured three times. A calibration curve was used for calibration, and the results were calculated as an average value obtained for all analytical lines of the selected element. The soil samples were enriched with SAs prior to extraction, resulting in a final yield of ng g -1 for each sample three repetitions for each soil. Initial concentrations of selected SAs in the soils before spiking were measured to determine the precise amount of standard solution required for the enrichment to obtain final concentration ng g Parameters such as accuracy, precision, linearity, limit of detection LOD , limit of quantification LOQ , matrix effect ME , and recovery were determined. The soil matrix extract medium amount of OC and neutral pH prepared according to the procedure described in Method validation Results and discussion section was used to determine the validation parameters. Due to the presence of trace amounts of the determined SAs in the selected soil, a standard addition method was performed concerning blank sample. Calibration curves were constructed over the concentration range 1— ng L -1 by adding the appropriate volume of working standard solutions to extracts from soil with a medium OC content and neutral pH soil sample SWIV. These measurements were also used for linearity and coefficient of determination R 2 calculations for all analytes. The LOD values were obtained from equation 1 :. For ME evaluation, samples were prepared by adding SAs standards mixture to both 0. The ME was calculated from equation 2. R was calculated from equation 3. The chromatographic separation conditions and ion source parameters were the same as for the targeted analysis. In the first step, a screening analysis was performed using the pseudo-multiple reaction monitoring p-MRM mode. Non-targeted analysis was performed using a retrospective approach to mass spectral analysis. The TPs identified in this way were compared with information from databases or the literature if possible. Complex matrices specific to soil samples may cause difficulties in the quantitative assessment of selected pharmaceuticals using electrospray ionization due to the matrix effect Taylor ; Rossmann et al. It is crucial to apply solutions that will compensate for the impact of co-eluted compounds. Our previous study showed that SAs were more stable in McIlvaine buffer than in citrate buffer Stando et al. The effectiveness of dual extraction was also examined. Procedures with an increased shaking time and without sonication SLE3 , with the addition of an ion exchanger sodium fluoride — SLE4 Hou et al. None of the abovementioned modifications had a relevant influence on recovery increase all below The addition of the chelating agent EDTA impacted positively on extraction effectiveness by showing an ability to bind metal ions, e. SAs have varied pK a values, but generally, they have a cationic form at a pH below 3 and an anionic form above 4. While developing an extraction procedure for liquid samples, it was proven that a pH in the range 3. Nevertheless, the obtained recoveries were significantly lower lower than A possible explanation is too strong adsorption of analytes to the MAX sorbent, which can interact with the cationic form of SAs. Initial conditioning solvents for selected SAs were 6 mL methanol, 6 mL 0. The first option was to dry to dryness under a stream of nitrogen and dissolve the residues in 1 mL of methanol. This additional wash did not improve extraction efficacy. The best results were obtained after dispensing with the concept of complete drying. SAs can adsorb onto glass walls in small amounts Shikuku et al. This effect can be caused by the strength of the acids employed. Acetic acid is weaker and decreases pH to a lesser extent than formic acid, to a value that may have a favorable impact on the elution process of the selected SAs. While the two-stage extraction procedure could be seen as a potential drawback, its strength lies in its adaptability to various soil types. To obtain an effective and universal procedure for soils with distinct characteristics, the influence of OC content on SAs recovery was determined. Detailed information on the 27 collected soil samples and their characteristics are presented in Table S5. The OC content was assessed for 27 environmental soil samples. These were divided into three groups, giving 6 soils with very low, 4 with low, and 17 with medium OC content based on European Soil Bureau guidance. Following our previous research, it was assumed that the increase in organic matter content was responsible for the lower recoveries for the same extraction procedure Stando et al. It was clear that recoveries significantly rose for arenaceous quartz where the matrix was deprived of organic matter, which probably caused stronger SAs adsorption in model soil Li et al. Considering the obtained results, the following number of soils were assigned to each group: 3 acidic, 6 slightly acidic, 7 neutral, and 11 basic. This gave a large diversity of samples in terms of this parameter. Another important consideration was that as the pH of the soil rose, the cation exchange capacity increased as well. This phenomenon is caused by an increase in the negative charge of organic and mineral substances because of the deprotonation of functional groups Shuey To confirm the statistical influence of organic carbon content on recovery, Spearman's rank correlation coefficients were calculated. The results were as follows, sequentially: A strong negative correlation between recovery and OC was shown for each of the SAs, which confirms that as the OC content increases, the SAs recovery decreases. Soil sample extracts with a medium OC content were used for validation, and nine independent repetitions were performed each time. The calibration curves for SAs were linear from 1. The R 2 was in the range of 0. Accuracy and precision were determined based on the analysis of QC samples at three concentration levels: 10 ng g -1 low , ng g -1 medium , and ng g -1 high. No interference peaks were observed at the retention times of the selected SAs in blank soil extract samples. To develop an extraction method suitable for environmental monitoring studies, the validation was extended to the determination of recoveries for soils with various OC contents. Extracts of samples of these soils very low to medium OC content were analyzed with the addition of appropriate amounts of SAs. The adopted range of OC content in the medium criterion was too wide to assess the impact of OC on recovery objectively. The obtained recoveries differed depending on the OC content in the soil. A decrease in SAs recoveries is related to an increase in the OC content of the soil. The SAs recoveries for soils with very low, low, medium-low, and medium-high OC content changed by According to the literature, SAs sorption in soil increases with OC content, which may result in low recovery of analytes Leal et al. Another factor reducing the SAs recovery is the coextraction of matrix compounds with analytes in SLE. In our previous study, we showed that the presence of soil matrix components significantly reduces the recovery of pharmaceuticals at the SPE stage Stando et al. Therefore, we recalculated the concentrations of quantified SAs based on the aforementioned four recovery ranges established for various OC contents. According to the literature, the SAs content in various soil types is in the 0. The established procedure is sufficiently sensitive to determine SAs residues in the environment. Determining recoveries at four levels of OC made it possible to obtain accurate results for soil samples with various compositions and confirmed the Shelver et al. Despite the availability of many procedures for extracting SAs from the soil, their comparison with the newly developed procedure is difficult due to the lack of or incomplete information on the soil composition. To our best knowledge, this is the only study that links the effects of OC at various levels to SAs recovery obtained after extraction from soil samples. Monitoring of SAs in soils was carried out in six cities in the Silesian Voivodeship — the most urbanized and industrialized area in Poland. Twenty-seven sampling points that met the criterion of increased activity of animals were selected. The areas with 'increased animal activity' can be understood broadly and will refer to the various areas, depending on urban, suburban, and agricultural areas. The determined concentrations of SAs in soil samples are listed in Table 2. The main route of SAs introduction to the soil is livestock manure, which is used as a natural fertilizer Zhao et al. However, not only agricultural area is exposed to the accumulation of SAs. The same compounds are used in the treatment of farm animals calves, castles, swine, horses and in the treatment of domestic animals mainly cats and dogs Hsu In urban areas, places with increased activity of animals, and thus the most exposed to SAs accumulation are parks, dog and horse paddocks, separate playgrounds for pets, green regions in the vicinity of residential estates together with tourist centers, due to the many domestic animals present. Concentrations of selected SAs in soil samples collected from areas with increased animal activity. Each of the selected eight SAs was determined in soils collected from dog paddocks. The SMX maximum concentration among samples from dog paddocks was There were no significant differences in the concentrations of SAs collected from the paddocks in Katowice and Sosnowiec. In both cities, there was one dog paddock where all eight SAs were determined in the soil, in concentrations ranging from 2. Poland contains an estimated 6—8 million dogs and It can be concluded that the factors influencing the increased accumulation of SAs in dog runs are the small usable area of the paddocks — m 2 , the large population of dogs in cities, and the widespread use of drug therapy in domestic animals. The low amount of SAs detected in soils from horse paddocks compared to dog paddocks is related to the specificity of the population of these animals. Specific breeders own horse paddocks, so the population of horses in a given area is significantly limited, and sick individuals are isolated from healthy ones. Dog runs are public places where the rotation of dogs during the day is high, and the only limitation is their space. Agricultural fields are not directly exposed to animal activity, and the source of SAs contamination is animal manure used as fertilizer. As a part of the research, three fields in suburban areas PM, PP, and KBP where animal manure was used in the last two years were selected. The method of fertilizing the field by the owners and the type of manure used is unknown. The tendency to accumulate SAs in the soil after fertilization with manure has been the subject of many studies Ho et al. The concentration of SAs in greenhouse soils and soils from open fields after fertilization with manure were respectively in the following ranges: 0. In addition, the concentration range in which SAs were detected in soil samples from the agricultural fields was lower than for soil samples taken from dog paddocks. These results show that SAs are continuously introduced into the water and soil system in the Paprocany center. SAs are easily leached from the soil, which allows them to migrate into the environment Albero et al. We suspect that the presence of SAs in soil extracts may be related to the high activity of visiting domestic animals or the migration of pollutants in the environment associated with runoff from agricultural fields. The lowest levels of SAs compared to dog paddocks and agricultural fields were found in the green areas. In JK1, no SAs were detected. Literature data on the occurrence of SAs in soils in urban areas are limited. In the report of Xinzhu Yi et al. SAs were detected at a higher concentration in groundwater 0. All eight selected SAs were detected in soil samples collected in urban and suburban areas. The highest concentrations of SAs were found in dog runs, which confirms that increased activity of domestic animals in the areas designated for them results in the accumulation of SAs in the soil. A total of 29 TPs of SAs were detected in 24 out of 27 extracts from soil samples. In Table 3 , the structures of the SAs TPs are presented, along with the mass of the molecular ion and fragment ions, while in Table S6 the distribution and frequency of the detected SAs TPs in soil samples are shown. Ten TPs of p-aminobenzoic acid were detected, resulting from the degradation of any of the SAs present in the soil. The degradation of p-aminobenzoic acid leads to simple benzene derivatives BZ. BZ TPs were found in soil extracts, but it is impossible to establish their source. Zheng et al. SFR differs from SFM by one methyl group attached to the pyrimidine ring, so their degradation may result in the formation of the same TPs. All three hydroxylated TPs were detected in the Fenton water purification process Deng et al. There is no information in the literature on the presence of hydroxylated SFR TPs in the soil-water environment. Hydroxylation is a reaction characteristic of the first phase of drug metabolism Huynh and Reinhold , and we suppose that these compounds can also be formed under environmental conditions. A universal, effective, reproducible method of extracting eight SAs from soil samples with different physicochemical properties was developed as part of this research. The recovery of selected SAs depended to a varying extent on the content of sodium and potassium in the soil, but no effect of pH was observed. It was noted that with an increase in the OC, K, or Na content, SAs bound more strongly to soil particles, making them difficult to extract. To confirm the universality of the method, the SAs recovery was determined at four levels of OC content. The soil samples were collected from the areas of six cities in the highly urbanized agglomeration in Silesian Voivodeship. The sampling sites were selected using the following criteria: increased soil contact with the livestock agricultural fields or domestic animals parks, paddocks, or tourist resorts. Each of the eight SAs was detected in the soil samples. The highest concentrations of SA were found in soils from dog paddocks 1. It is worth noting that the content of SAs in the soils from the dog runs was higher than in the agricultural soils. This observation suggests that the increased number and activity of dogs in their designated areas might be a contributing factor to the higher presence of SAs in the soil. The screening revealed 29 SAs TPs resulting from the transformation of 4-aminobenzoic acid or an aromatic amine that was part of the structure of an SA. This suggests that the formation of TPs in soil depends on the concentration of SAs in the soil and on the frequency of their introduction into the environment. To the best of our knowledge, this is one of the few studies dealing with TPs in the community Hoff et al. According to our knowledge, this is the first paper to consider the effect of soil OC content on SAs recovery. The impact of OC on recovery is crucial in comparing SAs residues in different soil types. The obtained results suggest that SAs are constantly being transferred to the environment, including in highly urbanized areas. It has been found that excrement from veterinary-treated domestic animals may also be a source of soil contamination with SAs. The findings reported here fill a research gap on the spread of pharmaceuticals in urban areas which can also be a potential reservoir for the emergence of drug-resistant bacterial strains. The authors would like to thank Ms. Anna Byczek-Wyrostek for technical help with the lyophilization of samples. All authors contributed to the study. The authors have read and approved the final draft of the manuscript. The authors received no financial support for the research, authorship, and publication of this article. Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations. This section collects any data citations, data availability statements, or supplementary materials included in this article. As a library, NLM provides access to scientific literature. Environ Sci Pollut Res Int. Krzywoustego 6 Str, Gliwice, Poland. Find articles by Klaudia Stando. Find articles by Joanna Wilk. Krzywoustego 8 Str, Gliwice, Poland. Find articles by Ewa Felis. Find articles by Sylwia Bajkacz. Received May 4; Accepted Sep 25; Issue date Open in a new tab. ESM 1 Similar articles. Add to Collections. Create a new collection. 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How can I buy cocaine online in Ruda Slaska