The Swedish EPA (Naturv&#229;rdsverket) (agreement 2208-13-001) and Centre for Chemical Pesticides (CKB) are gratefully acknowledged for funding this project. We thank M&#228;rit Peterson, Henrik Jernstedt, Emma Gurnell and Elin Paulsson at the OMK-lab, SLU, for skillful assistance with analytical support and supply of pesticide standards.

1. Passive Sampler Planung und Vorbereitung <ol><li> Silikon - Gummiplatten <ol><li> Schneiden Sie die Silikongummiplatten (600 mm x 600 mm, 0,5 mm dick) in Streifen von 2,5 mm x 600 mm und 2,5 mm x 314 mm ein Edelstahl-Cutter und verbinden sie ein Edelstahl-Blindniete mit (3,2 mm x 10 mm ) mit einer Nietmaschine insgesamt sampler Streifengröße von 2,5 mm x 914 mm (Oberfläche = 457 cm 2, Sorbensmasse = 15,6 g, Volumen = 22,9 cm 3) zu erhalten. </li></ol></li><li> Legen Sie die Silikonkautschuke in einer Extraktionskammer einer Soxhletapparat. 50 ml EA in der Extraktionskammer und 250 ml EA und drei Siedesteine ​​in einem 500-ml-Rundkolben, Flasche. <ol><li> Verbinden Sie die Extraktionskammer mit der Flasche Kolben und einem Kondensator. Reinigen Sie die Siliconkautschuke durch Soxhlet-Extraktion für 96 Stunden bei etwa 80 ° C, und trocknen Sie sie danach unter leichtem Stickstoffgas. </li></ol></li><li> Bringen Sie die Silikonkautschuk striPE auf eine Edelstahl spider Probenhalter durch die Silikongummistreifen Umwickeln um die Stäbe auf dem Halter (Abbildung 1). Befestigen jedes Ende des Silikongummistreifen an einer Stange auf dem Halter unter Verwendung von Kabelbindern. </li></ol><img alt="Abbildung 1" src="/files/ftp_upload/54053/54053fig1.jpg" /> Abbildung 1. Schematische aus Silikonkautschuk. Passive Sampler Schema für Silikonkautschuk , welche die Befestigung des Silikonkautschuk - Streifen auf eine Edelstahl Spinne Probenhalter A) von oben und B) der Seitenansicht. <a href="https://www.jove.com/files/ftp_upload/54053/54053fig1large.jpg" target="_blank">Bitte klicken Sie hier</a> , um <a href="https://www.jove.com/files/ftp_upload/54053/54053fig1large.jpg" target="_blank">eine größere Version zu sehen diese Figur.</a> <ol start="2"><li> POCIS-A und POCIS-B <ol><li> Für POCIS-A Platzieren 220 mg HLB bulk Sorptionsmittel (Oberfläche = 1,78 x 10 6 cm 2) zwischen zwei 9,0 cm mal 9,0 cm square Polyethersulfon (PES) Membranen (Abbildung 2). </li><li> Für POCIS-B Platzieren 220 mg eines Sorptionsmittel - Mischung (dh hydroxyliertes Polystyrol-Divinylbenzol - Harz (80%) und ein kohlenstoffhaltiges Adsorptionsmittel auf einem Styrol - Divinylbenzol - Copolymer dispergiert ist (20%)) (Oberfläche = 2,82 x 10 6 cm 2) zwischen zwei PES - Membranen (Abbildung 2). </li><li> Komprimiert das Sorbens und zwei PES zwischen zwei Edelstahlringe manuell (Innen - Ø = 5,4 cm) und befestigen Sie ihn auf einem Edelstahl - Probenhalter (Abbildung 2). </li></ol></li></ol><img alt="Figur 2" src="/files/ftp_upload/54053/54053fig2.jpg" /> Abbildung 2. Schematische Darstellung der zur passiven Probenplatten. Passive Sampler Schema für POCIS A, POCIS B, SDB-RPS Scheibe und 18 C - Platte zeigt A) den Zusammenbau des Passivsammlers Edelstahlringe mit Polyethersulfon (PES) membranes, und die Empfangsphase und B) die Montage auf einem Edelstahl - Probenhalter. <a href="https://www.jove.com/files/ftp_upload/54053/54053fig2large.jpg" target="_blank">Bitte klicken Sie hier</a> , um <a href="https://www.jove.com/files/ftp_upload/54053/54053fig2large.jpg" target="_blank">eine größere Version dieser Figur zu sehen.</a> <ol start="3"><li> SDB-RPS Platte und C 18 Scheibe <ol><li> Legen Sie die SDB-RPS (Oberfläche = 35 cm 2, Sorbens Masse = 0,34 g, Volumen = 1,7 cm 3) und C 18 Scheiben (Oberfläche = 35 cm 2, Sorbens Masse = 0,58 g, Volumen = 1,7 cm 3) zwischen zwei PES - Membranen (Abbildung 2). Komprimieren Sie die Scheiben und zwei PES zwischen zwei Edelstahlringe manuell (Innen - Ø = 5,4 cm) und befestigen Sie ihn auf einem Edelstahl - Probenhalter (Abbildung 2). </li></ol></li></ol> 2. Labor Uptake Experimente HINWEIS: Die Aufnahme Laborexperimente wurden durchgeführt, um quantitativ die Aufnahme k charakterisiereninetics für 124 einzelne Pestizide für fünf verschiedene passive Sampler Geräte unter kontrollierten Bedingungen. <ol><li> Führen Sie die Aufnahme Studie in rechteckigen Glasbehältern (jeweils ~ 95 L): Tank 1) Silikonkautschuk (n = 16), Tank 2) POCIS-A (n = 16), POCIS-B (n = 16) und Tank 3 ) SDB-RPS Platte (n = 16), 18 Platte C (n = 16). Füllen Sie natürliche Wasser in die drei Tanks. </li><li> Führen alle Versuche bei einer konstanten Wassertemperatur (~ 20 ° C) und unter turbulenten Wasserbedingungen (~ 10 cm sec -1) unter Verwendung von zwei Elektropumpen an der Wand auf jeder Seite angebracht. Führen Sie die Experimente im Dunkeln die Wirkung der photochemischen Abbau zu minimieren. </li><li> Spike jedes Glasbehälter mit einem Pestizid Standardmischung , die 124 Pestizide eine Glasspritze (c ≈ 400 ng L -1 für einzelne Pestizide im Wassertank). Nehmen Sie die Passivsammler manuell aus den Tanks, in Zeitintervallen von 5, 11, 20, und 26 days, die Abtastraten der Pestizide zu bestimmen. </li><li> Überwachen Sie die Konzentrationen der Pestizide in jedem Tank durch das Sammeln von 100 ml Wasserproben am Tag 0, 5, 11, 20 und 26. Die Analyse der Wasserproben durchgeführt wird, wie an anderer Stelle 21 beschrieben. <ol><li> Für die Qualitätskontrolle aussetzen Leerproben auf Raumluft für 1 Stunde am Tag 0 und dann speichern und sie als reale Proben zu behandeln. Speichern Sie alle Extrakte sowie die 100 ml Wasserproben aus den Tanks bei -18 ° C bis zur weiteren Analyse gesammelt. </li></ol></li></ol> 3. Probenextraktion <ol><li> Silikon-Gummi <ol><li> Vor der Extraktion, Trocknen des Silikongummistreifen unter einem Strom von hochreinem Stickstoffgas. </li><li> Für die Gaschromatographie-Massenspektrometrie (GC-MS) Analyse, Durchführung der Fest-Flüssig - Extraktion Soxhlet - Extraktion 22 verwendet wird . <ol><li> Legen Sie das Silikongummi in den Soxhlet-Extraktor. In 250 ml PE / ACE (50/50, v / v) und 3 boiling Steine ​​in die runde Flasche Kolben. </li><li> Spike der Silikonkautschuk mit 100 ul einer IS - Mischung (c = 5 ng ml -1) unter Verwendung einer Glasspritze. 50 ml PE / ACE (50/50, v / v) in den Soxhlet-Extraktor. Schalten Sie die Heizung und führen Sie die Soxhlet-Extraktion für 19 h und dann schalten Sie die Heizung ab. </li><li> Konzentrieren der Extrakte durch Rotationsverdampfung, gefolgt von leichten Stickstoffblasen bis zu 1 ml. Tauschen Sie das Lösungsmittel CH / ACE (90/10, v / v) durch Zugabe von dreimal 1 ml CH / ACE (90/10, v / v) während der Stickstoffblasen bis zu 1 ml. </li></ol></li><li> Für Flüssigchromatographie-Tandem - Massenspektrometrie (LC-MS / MS - Analyse), führen die Extraktion Soxhlet - Extraktion 22 verwendet wird . <ol><li> Legen Sie das Silikongummi in den Soxhlet-Extraktor. In 250 ml Methanol und 3 Siedesteinen in die runde Flasche Kolben und 50 ml Methanol in den Soxhlet-Extraktor. Spike der Silikonkautschuk mit 100 ul einer IS - Mischung (c = 5 ng ml -1) unter Verwendung eines Glas SYRinge. </li><li> Schalten Sie die Heizung und führen Sie die Soxhlet-Extraktion für 19 h und dann schalten Sie die Heizung ab. Konzentrieren der Extrakte durch Rotationsverdampfung, gefolgt von leichten Stickstoffblasen bis zu 1 ml. Tauschen Sie das Lösungsmittel zu ACN durch Zugabe von 1 ml ACN während der Stickstoffblasen bis zu 1 ml. </li></ol></li></ol></li><li> POCIS-A und POCIS-B <ol><li> Öffnen Sie die POCIS Sampler sorgfältig und übertragen das Sorbens mit Reinstwasser einen Trichter in eine vorgereinigte leer Polypropylen Festphasenextraktion (SPE) Patrone (6 ml), die zwei Polyethylen (PE) Fritten. Trocknen Sie das Sorbens durch Vakuum Wasser zu entfernen. Das Gewicht des leeren und verpackt SPE-Kartusche, das Gewicht des Sorptionsmittel zu steuern. Bitte beachten Sie, dass verschiedene Patronen verwendet werden, für die GC-MS und LC-MS / MS-Analyse. </li><li> Vor der Elution, Spike das Sorbens mit 100 ul einer IS - Gemisch (c = 5 ng ml -1) mit einer Glasspritze. Eluieren POCIS-A und POCIS-B Sorptionsmittel 5 unter Verwendung vonml EA für GC-MS - 22. <ol><li> Konzentrieren der Extrakte auf 1 ml durch leichten Stickstoffblasen nach unten. Tauschen Sie das Lösungsmittel CH / ACE (90/10, v / v) durch Zugabe von dreimal 1 ml CH / ACE (90/10, v / v) während der Stickstoffblasen bis zu 1 ml. </li></ol></li><li> Elute POCIS-A und B-POCIS Kartuschen unter Verwendung von 1,5 ml MeOH , gefolgt von 8 ml DCM / MeOH (80/20, v / v) für die LC-MS / MS - Analyse 22. Konzentrieren der Extrakte auf 1 ml durch leichten Stickstoffblasen nach unten. Tauschen Sie das Lösungsmittel zu ACN durch Zugabe von 1 ml ACN während der Stickstoffblasen bis zu 1 ml. </li></ol></li><li> SDB-RPS und C 18 Scheibe <ol><li> Übertragen Sie einzelne Platten von SDB-RPS und C 18 Scheibe in ein Becherglas und trocknen Sie sie unter Stickstoffgas. Spike der Platten mit 100 ul einer IS - Mischung (c = 5 ng ml -1) unter Verwendung einer Glasspritze und beschallen sie zweimal in einem Becherglas bei Raumtemperatur, zuerst mit 5 ml EE für 10 min und dann mit 3 ml von 10 min EA. </li><li> Transfer boten Extrakte in ein Glasrohr, konzentrieren sie auf 2 ml durch leichten Stickstoff Schlag nach unten, und teilen sie in zwei Fraktionen von 1 ml (für GC-MS und LC-MS / MS-Analyse, beziehungsweise). </li><li> Konzentrieren der Extrakte auf 0,5 ml durch leichten Stickstoffblasen nach unten und tauschen das Lösungsmittel CH / ACE (90/10, v / v) für die GC-MS - Analyse 22. Konzentrieren der Extrakte auf 0,5 ml durch leichten Stickstoffblasen nach unten und tauschen das Lösungsmittel zu ACN für LC-MS / MS - Analyse 22. </li></ol></li></ol> 4. Wasserproben <ol><li> Spike 20 ml Wasserprobe mit 100 ul einer IS - Mischung (c = 5 ng ml -1) mit einer Glasspritze, 3 ml DCM, Wirbel für 3 min, und dekantieren in einem Phasentrenner für die GC-MS - Analyse 22. <ol><li> Nachdem die beiden Phasen werden getrennt, die DCM-Phase in ein Glasrohr Perkolat. Die Extraktion mit 3 ml DCM, und spülen Sie das Röhrchen mit 2 ml DCM. Schließlich konzentrieren, die Extrakte auf 0,5 ml durch leichten Stickstoff blow-down und Excge das Lösungsmittel CH / ACE (90/10, v / v). </li></ol></li><li> Analysieren die Wasserproben unter Verwendung großvolumiger Injektion, ähnlich dem Verfahren , beschrieben an anderer Stelle durch LC-MS / MS 21. </li></ol> 5. instrumentelle Analytik <ol><li> GC-MS-Analyse <ol><li> Führen der instrumentellen Analysen der CH / ACE Extrakte GC-MS - Systeme in Elektronenionisation (EI) und negative chemische Ionisierung (NCI) Modus, bzw. 22. </li><li> Für die GC-MS-Methode EI Verwendung injizieren Aliquots von 1 &amp; mgr; l mit splitless Injektionsverfahren auf einer HP-5 MS UI-Säule (30 m, 0,25 mm Innendurchmesser, 0,25 &amp; mgr; m-Film). </li><li> Für die GC-MS-Methode unter Verwendung von CI, injizieren Teilmengen von 3 ul auf einer HP-5 MS UI-Säule (30 m, 0,25 mm Innendurchmesser, 0,25 &amp; mgr; m-Film). </li></ol></li><li> HPLC-MS / MS-Analyse <ol><li> Führen Sie die instrumentellen Analysen der ACN-Extrakte mittels HPLC-MS / MS-Schnittstelle mit einem Elektrospray-Ionisations-Quelle in negativer ((-) ESI) und positiv-Ionen-mOde ((+) ESI) 22. </li><li> Für (+) ESI, verdünnen 100 ul der ACN extrahiert mit 900 &amp; mgr; l Reinstwasser auf pH 5 FA mit. </li><li> Für (-) ESI, verdünne 100 ul des ACN extrahiert mit 900 &amp; mgr; l Lösung von 1% FA in Reinstwasser. </li><li> Für (+) ESI Verwenden eines binären Gradienten , bestehend aus 2-Propanol / Methanol / 10 mM Ammoniumformiat (6/2/92, v / v / v) und MeOH bei einer Fließgeschwindigkeit von 0,3 ml min -1. </li><li> Für (-) ESI für eine binäre Gradient aus ACN / Reinstwasser 0,1% HAc und ACN + 0,1% HAc bei einer Fließgeschwindigkeit von 0,3 ml min -1. </li><li> Injizieren alle Proben eine großvolumige Injektion von 500 &amp; mgr; l unter Verwendung von mit zwei Online - SPE - Säulen (jeweils 20 x 2 mm id und 20-25 &amp; mgr; m Teilchengrße) und einer analytischen Säule (C 18, 100 x 3 mm, 3,5 &amp; mgr; m) 21. </li></ol></li></ol> 6. Theorie auf Passive Sampling HINWEIS: Die Aufnahme Profil der Chemikalie auf die Passivsammler medium (PSM) ist in drei Abschnitte unterteilt: Linear, krummlinigen und Gleichgewicht (Abbildung 3). <img alt="Figur 3" src="/files/ftp_upload/54053/54053fig3.jpg" /> Abbildung 3. Passive Probenaufnahmekurve. A) und C) Aufnahmekurve für die akkumulierte Menge an Acetamiprid und Dimethoat, jeweils in den Passivsammler (N t) in ng absolute und B) und D) Wassertank Konzentration von Acetamiprid und Dimethoat jeweils in ng L - 1. <a href="https://www.jove.com/files/ftp_upload/54053/54053fig3large.jpg" target="_blank">Bitte hier klicken</a> , um <a href="https://www.jove.com/files/ftp_upload/54053/54053fig3large.jpg" target="_blank">eine größere Version dieser Figur zu sehen.</a> <ol><li> Berechnen Sie den äquivalenten Wasservolumen (V eq L) für einen Passivsammler durch die akkumulierte Menge an Zielverbindungen in der Passivsammler nach t Tagen nach der Exposition Dividieren (N &#39;t </sup&gt;, ng) durch die Konzentration in der Wasserphase greifen und die Zeit integriert aktive Probenahme mit (c w, ng L -1). <img alt="Gleichung 1" src="/files/ftp_upload/54053/54053eq1.jpg" /> (1) </li><li> Leiten Sie die Abtastrate (R S, L Tag -1) von der linearen Aufnahmephase der Aufnahmeprofil, durch die Steigung von V eq gegen Stationierung Zeit. </li><li> Berechnen Sie die K PW (L kg -1) für einzelne Pestizide mit Gl. 2. <img alt="Gleichung 2" src="/files/ftp_upload/54053/54053eq2.jpg" /> (2) wobei m p das Sorbens Masse pro Sampler ist (ng). </li><li> In der linearen Aufnahmephase, die Berechnung der TWA - Konzentration des Analyten in Wasser durch das Passivsammler abgeleitet (c TWA, ng L -1) unter Verwendung von Gl. 3. <img alt="Gleichung 3" src="/files/ftp_upload/54053/54053eq3.jpg" /> (3) wobei R S die sampling Rate (L Tag -1) und t ist die Bereitstellungszeit (Tage). </li><li> In der gekrümmten Phase berechnen c TWA Gl. 4. <img alt="Gleichung 4" src="/files/ftp_upload/54053/54053eq4.jpg" /> (4) </li><li> In der Gleichgewichtsphase, berechnen c TWA Gl. 5. <img alt="Gleichung 5" src="/files/ftp_upload/54053/54053eq5.jpg" /> (5) </li></ol> 7. Statistische Datenanalyse <ol><li> Testen nicht-normalen Verteilung der Daten einen Shapiro-Wilk - Test 23 verwendet wird . Verwenden Sie nicht-parametrischer Spearman-Rangkorrelation für K PW und R S vs physikalisch - chemischen Eigenschaften der getesteten Pestizide (Spearman-rho im Bereich von -1 bis 1) 24. </li></ol>

<ol>
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C. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Environmental+monitoring+of+hydrophobic+organic+contaminants:+The+case+of+mussels+versus+semipermeable+membrane+devices.">Environmental monitoring of hydrophobic organic contaminants: The case of mussels versus semipermeable membrane devices.</a> Environ. Sci. Technol. 40 (12), 3893-3900 (2006).</li><li>Harman, C., Allan, I. J., Vermeirssen, E. L. M. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Calibration+and+use+of+the+polar+organic+chemical+integrative+sampler-a+critical+review.">Calibration and use of the polar organic chemical integrative sampler-a critical review.</a> Environ. Toxicol. Chem. 31 (12), 2724-2738 (2012).</li><li>Jonker, M. T. O., Der Heijden, S. A. V. a. n., Kotte, M., Smedes, F. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Quantifying+the+effects+of+temperature+and+salinity+on+partitioning+of+hydrophobic+organic+chemicals+to+silicone+rubber+passive+samplers.">Quantifying the effects of temperature and salinity on partitioning of hydrophobic organic chemicals to silicone rubber passive samplers.</a> Environ. Sci. Technol. 49 (11), 6791-6799 (2015).</li><li>Jansson, C., Kreuger, J. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Multiresidue+analysis+of+95+pesticides+at+low+nanogram/liter+levels+in+surface+waters+using+online+preconcentration+and+high+performance+liquid+chromatography/tandem+mass+spectrometry.">Multiresidue analysis of 95 pesticides at low nanogram/liter levels in surface waters using online preconcentration and high performance liquid chromatography/tandem mass spectrometry.</a> J. AOAC Int. 93 (6), 1732-1747 (2010).</li><li>Ahrens, L., Daneshvar, A., Lau, A. E., Kreuger, J. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Characterization+of+five+passive+sampling+devices+for+monitoring+of+pesticides+in+water.">Characterization of five passive sampling devices for monitoring of pesticides in water.</a> J. Chromatogr. A. 1405, 1-11 (2015).</li><li>Royston, P. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Approximating+the+Shapiro-Wilk+W-test+for+non-normality.">Approximating the Shapiro-Wilk W-test for non-normality.</a> Stat. Comput. 2 (3), 117-119 (1992).</li><li>Gauthier, T. D. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Detecting+trends+using+Spearman's+rank+correlation+coefficient.">Detecting trends using Spearman's rank correlation coefficient.</a> Environ. Forensics. 2 (4), 359-362 (2001).</li><li>Morin, N., Mi&#232;ge, C., Coquery, M., Randon, J. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Chemical+calibration,+performance,+validation+and+applications+of+the+polar+organic+chemical+integrative+sampler+(POCIS)+in+aquatic+environments.">Chemical calibration, performance, validation and applications of the polar organic chemical integrative sampler (POCIS) in aquatic environments.</a> TrAC - Trend. Anal. Chem. 36, 144-175 (2012).</li><li>. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Water+Quality+-+Sampling+-+Part+23:+Guidance+on+Passive+Sampling+in+Surface+Waters.">Water Quality - Sampling - Part 23: Guidance on Passive Sampling in Surface Waters.</a> ISO 5667-23:2011. , (2011).</li><li>Morin, N., Camilleri, J., Cren-Oliv&#233;, C., Coquery, M., Mi&#232;ge, C. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Determination+of+uptake+kinetics+and+sampling+rates+for+56+organic+micropollutants+using+"pharmaceutical"+POCIS.">Determination of uptake kinetics and sampling rates for 56 organic micropollutants using "pharmaceutical" POCIS.</a> Talanta. 109, 61-73 (2013).</li></ol>

The authors have nothing to disclose.

Für die Qualitätskontrolle als Standardverfahren, Labor Rohlingen, Nachweisgrenzen (LOD), Einziehungen und die Wiederholbarkeit wurden 23 untersucht. Einige Pestizide wurden in den Leerproben bei niedrigen Konzentrationen nachgewiesen. LOD wurden als der Wert des tiefsten Punktes der Eichkurve eingestellt, die die Kriterien eines Signal-Rausch-Verhältnis von 3. Die durchschnittlichen LOD absolute auf Spalte für Silikonkautschuk injiziert wurden 8,0 pg trifft, 1,7 pg absolut für POCIS-A, 1,6 pg absolut f?...

Pestizide werden kontinuierlich in die Gewässer eingeleitet und kann ein Risiko für Wasserorganismen 1 darstellen. Die Überwachung von Pestiziden in der wässrigen Umgebung wird in der Regel greifen Probenahme unter Verwendung von , jedoch geht diese Sampling - Technik nicht in vollem Umfang für die zeitlichen Veränderungen berücksichtigen aufgrund von Schwankungen der Strömung oder episodisch Eingänge in Konzentrationen (zB Niederschlag, Mischwassereinleitungen, Abwasser Lagune release) 2 , 3. So müssen Überwachungsverfahren für eine bessere Abschätzung von Umweltrisiken mit Pestiziden verbessert werden. Passive Abtastung ermöglicht eine kontinuierliche Überwachung über einen längeren Zeitraum mit minimaler Infrastruktur und niedrige Schadstoffkonzentrationen 4,5. Passivsammler wurden im Grundwasser 6, Frischwasser 7-10, Abwasser 11 und Meeresgewässer 12 ein wertvolles Werkzeug für die Überwachung erwiesen. Neben Überwachungszwecke <sup&gt; 13,14, Passivsammler sind auch für Nicht-Zielanalyse 15, Toxikologie - Tests 16,17, und als Alternative 18 bis Sediment und Biomonitoring verwendet. Passivsammler sammeln Chemikalien kontinuierlich von Wasser und bieten zeitgewichteter Durchschnitt (TWA) Konzentrationen 14. Die Aufnahme der Verunreinigung hängt von der Abtastrate (R S) und Passivsammler-Wasser - Verteilungskoeffizienten (K PW), die auf der Passivsammlers Design abhängig, Sampler Material, physikalisch - chemischen Eigenschaften der Verunreinigung und den Umgebungsbedingungen (zB Wasser Turbulenz, Temperatur) 13,14,19,20. Die detaillierte Video soll zeigen, wie zu kalibrieren und Passivsammler für Pestizide in Wasser gelten. Die spezifischen Ziele enthalten i) Vorbereitung, Extraktion und instrumentelle Analytik für 124 einzelne Pestizide unter Verwendung von fünf verschiedenen Arten von passiven sampl auszuführenERS, einschließlich Silikongummi, polares organisch - chemisches integrative sampler (POCIS) -A, POCIS-B, SDB-RPS und C 18 Disk, ii) zu beurteilen , R S und K PW für die Pestizide in einer Laborstudie Aufnahme und iii) zu zeigen, wie die entsprechende Passivsammler der Zielverbindung von Interesse auszuwählen und wie TWA-Konzentrationen für den jeweiligen Passivsammlers zu berechnen. Referenzstandards und passive Sampler Geräte Zielverbindungen enthalten 124 Erbe und derzeit verwendeten Pestizide einschließlich Herbizide, Insektizide und Fungizide (Tabelle 1). Interne Standardmischung (IS - Gemisch) enthalten fenoprop (2,4,5-TP), Clothianidin-D 3, ethion und Terbuthylazin-D 5. Andere Chemikalien enthalten Methanol (MeOH), Acetonitril (ACN), Aceton (ACE), Dichlormethan (DCM), Cyclohexan (CH), Ethylacetat (EA), Petroleum ether (PE), 2-Propanol, 25% ige Ammoniaklösung, Essigsäure (HAc) und Ameisensäure (FA). Fünf verschiedene passive Probenahme - Geräte wurden charakterisiert, einschließlich Silikonkautschuk, POCIS-A und POCIS-B, SDB-RPS und C 18 Scheibe 1,21. Tabelle 1. Passive Sampler Abtastrate (R &#39;S, L Tag -1), Sampler-Wasser - Verteilungskoeffizienten (K&#39; PW, L kg -1) und Gleichungen (Gl.) Für die Berechnung der Konzentrationen in Feldproben verwendet für einzelne Pestizide ein. (Nachdruck aus Journal of Chromatography A, 1405, Lutz Ahrens, Atlasi Daneshvar, Anna E. Lau, Jenny Kreuger, Charakterisierung von fünf passive Probenahmegeräte zur Überwachung von Pestiziden in Wasser, 1-11, Copyright (2015), mit Genehmigung von Elsevier 22.) <a href="https://www.jove.com/files/ftp_upload/54053/Table_1.xlsx" target="_blank">Bitte hier klicken</a> , um <a href="https://www.jove.com/files/ftp_upload/54053/Table_1.xlsx" target="_blank">diese Datei herunterzuladen.</a>

<table border="0" cellpadding="0" cellspacing="0" width="1047">
	<tbody>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">Methanol</td>
			<td style="width:164px;">Merck Millipore</td>
			<td style="width:163px;">1.06035.2500</td>
			<td style="width:228px;"></td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;">Acetonitrile</td>
			<td>Merck Millipore</td>
			<td>1.00029.2500&#160;</td>
			<td></td>
		</tr>
		<tr height="21">
			<td height="21" style="height:22px;width:492px;">Acetone</td>
			<td>Merck Millipore</td>
			<td style="width:163px;">1.00012.2500</td>
			<td></td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;">2-propanol</td>
			<td>Merck Millipore</td>
			<td>1.00272.2500</td>
			<td></td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;">Dichloromethane</td>
			<td>Merck Millipore</td>
			<td>1.06054.2500</td>
			<td></td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;">Ammoniak</td>
			<td>Merck Millipore</td>
			<td>1.05428.1000</td>
			<td>Purity 25%</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;">Formic acid</td>
			<td style="width:164px;">Sigma-Aldrich</td>
			<td>94318-50ML-F</td>
			<td>Purity ~98%</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:22px;">Ethyl acetate&#160;</td>
			<td style="width:164px;">Sigma-Aldrich</td>
			<td>31063-2.5L</td>
			<td>for pesticide residue analysis</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:22px;">Petroleum ether&#160;</td>
			<td style="width:164px;">Sigma-Aldrich</td>
			<td>34491-4X2.5L</td>
			<td>for pesticide residue analysis</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;">Acetic acid&#160;</td>
			<td style="width:164px;">Sigma-Aldrich</td>
			<td>320099-500ML</td>
			<td>Purity &#8805;99.7%</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;">Cyclohexane&#160;</td>
			<td style="width:164px;">Fisher Chemicals</td>
			<td>C/8933/17</td>
			<td>for residue analysis</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;">Empty polypropylene SPE Tube with PE frits, 20 &#956;m porosity, volume 6&#160;mL</td>
			<td style="width:164px;">Supelco</td>
			<td>57026</td>
			<td></td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">Empore SPE Disks, C18, diam. 47&#160;mm</td>
			<td>Supelco</td>
			<td style="width:163px;">66883-U</td>
			<td>Passive sampler</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">Empore SPE Disks, SDB-RPS (Reversed-Phase Sulfonate), diam. 47&#160;mm</td>
			<td>Supelco</td>
			<td style="width:163px;">66886-U&#160;</td>
			<td>Passive sampler</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">POCIS-A&#160;</td>
			<td>EST</td>
			<td style="width:163px;">POCIS-HLB</td>
			<td>Passive sampler</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">POCIS-B</td>
			<td>EST</td>
			<td style="width:163px;">POCIS-Pesticide&#160;</td>
			<td>Passive sampler</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">Polyethersulfone (PES) membranes</td>
			<td>EST</td>
			<td style="width:163px;">PES</td>
			<td></td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">Silicone rubber sheet</td>
			<td style="width:164px;">Altec</td>
			<td style="width:163px;">03-65-4516</td>
			<td>Passive sampler</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">Agilent 5975C</td>
			<td style="width:164px;">Agilent Technologies</td>
			<td style="width:163px;">5975C</td>
			<td>GC-MS</td>
		</tr>
		<tr height="23">
			<td height="23" style="height:23px;width:492px;">HP-5MS UI</td>
			<td style="width:164px;">J&#38;W Scientific</td>
			<td style="width:163px;">HP-5MS</td>
			<td>Analytical column for GC-MS</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">Agilent 6460</td>
			<td style="width:164px;">Agilent Technologies</td>
			<td style="width:163px;">6460</td>
			<td>HPLC-MS/MS</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">Strata C18&#8211;E, 20 x 2 mm id and 20&#8211;25 &#956;m particle size</td>
			<td style="width:164px;">Phenomenex</td>
			<td style="width:163px;">Strata C18&#8211;E</td>
			<td style="width:228px;">Online SPE column for LC-MS/MS</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">Strata X, 20 x 2 mm id and 20&#8211;25 &#956;m particle size</td>
			<td style="width:164px;">Phenomenex</td>
			<td style="width:163px;">Strata X</td>
			<td style="width:228px;">Online SPE column for LC-MS/MS</td>
		</tr>
		<tr height="42">
			<td height="42" style="height:42px;width:492px;">Zorbax Eclipse Plus C18</td>
			<td style="width:164px;">Agilent Technologies</td>
			<td style="width:163px;">Zorbax Eclipse Plus C18</td>
			<td>Analytical column for LC-MS/MS</td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">Isolute phase separator, 25 mL</td>
			<td style="width:164px;">Biotage</td>
			<td style="width:163px;">120-1907-E</td>
			<td></td>
		</tr>
		<tr height="21">
			<td height="21" style="height:21px;width:492px;">Stainless steel blind rivet, 3.2x10 mm</td>
			<td style="width:164px;">Ejot &#38; Avdel</td>
			<td style="width:163px;">951222</td>
			<td></td>
		</tr>
	</tbody>
</table>

characterization and application of passive samplers for monitoring of pesticides in water

Fünf verschiedene Wasserpassivsammler wurden unter Laborbedingungen kalibriert für die Messung von 124 Legacy- und aktuell verwendete Pestizide. Diese Studie liefert ein Protokoll für die passive Probenvorbereitung, Kalibrierung, Extraktionsverfahren und Instrumentalanalysen. Abtastraten (R S) und Passivsammler-Wasser - Verteilungskoeffizienten (K PW) wurden für Silikonkautschuk berechnet, polaren organischen chemischen integrative Sampler POCIS-A, POCIS-B, SDB-RPS und 18 C - Laufwerks. Die Aufnahme der ausgewählten Verbindungen auf ihre physikalisch - chemischen Eigenschaften abhängig, das heißt, Silikonkautschuk zeigte eine bessere Aufnahme für mehrere hydrophobe Verbindungen, während POCIS-A (Octanol-Wasser - Verteilungskoeffizient (K OW)&gt; 5,3 log), POCIS-B und SDB- RPS Scheibe waren besser geeignet für die hydrophilen Verbindungen (log K OW &lt;0,70).

Fünf verschiedene passive Probentechniken wurden für die Aufnahme von 124 Vermächtnis verglichen und aktuell verwendete Pestizide einschließlich Silikonkautschuk (Abbildung 1), und POCIS A, POCIS B, SDB-RPS und C 18 Scheibe (Abbildung 2). Die Leistung des Extraktionsverfahrens und die instrumentelle Analytik wurde optimiert. Die Ergebnisse der Experimente zur Aufnahme Labor verwendet werden , um die &quot;S und log ...

Watch this Scientific Journal Video about Characterization and Application of Passive Samplers for Monitoring of Pesticides in Water at JoVE.com

Characterization and Application of Passive Samplers for Monitoring of Pesticides in Water

A protocol about the characterization and application of five different passive sampling devices is presented.

Charakterisierung und Anwendung von Passivsammler für die Überwachung von Pestiziden in Wasser

Five different water passive samplers were calibrated under laboratory conditions for measurement of 124 legacy and current used pesticides. This study ...

characterization-application-passive-samplers-for-monitoring

Research

JoVE Journal

Environment

9.4K Aufrufe.  Swedish University of Agricultural Sciences. A protocol about the characterization and application of five different passive sampling devices is presented.

Serie: Characterization and Application of Passive Samplers for Monitoring of Pesticides in Water

Waste Water Derived Electroactive Microbial Biofilms: Growth, Maintenance, and Basic Characterization

The growth of anodic electroactive microbial biofilms from waste water inocula in a fed-batch reactor is demonstrated using a three-electrode setup controlled by a potentiostat. Thereby the use of potentiostats allows an exact adjustment of the electrode potential and ensures reproducible microbial culturing conditions. During growth the current production is monitored using chronoamperometry (CA). Based on these data the maximum current density (jmax) and the coulombic efficiency (CE) are discussed as measures for characterization of the bioelectrocatalytic performance. Cyclic voltammetry (CV), a nondestructive, i.e. noninvasive, method, is used to study the extracellular electron transfer (EET) of electroactive bacteria. CV measurements are performed on anodic biofilm electrodes in the presence of the microbial substrate, i.e. turnover conditions, and in the absence of the substrate, i.e. nonturnover conditions, using different scan rates. Subsequently, data analysis is exemplified and fundamental thermodynamic parameters of the microbial EET are derived and explained: peak potential (Ep), peak current density (jp), formal potential (Ef) and peak separation (&#916;Ep). Additionally the limits of the method and the state-of the art data analysis are addressed. Thereby this video-article shall provide a guide for the basic experimental steps and the fundamental data analysis.

Chronoamperometric growth of anodic electroactive microbial biofilms in a fed-batch reactor using a three-electrode setup, controlled by a potentiostat, is demonstrated. The extracellular electron transfer is characterized using cyclic voltammetry in the presence of the electron donor and in the absence of the electron donor. Fundamental data analysis is demonstrated.

The growth of anodic electroactive microbial biofilms from waste water inocula in a fed-batch reactor is demonstrated using a three-electrode setup ...

Forschung

Umwelt

EPA Method 1615. Measurement of Enterovirus and Norovirus Occurrence in Water by Culture and RT-qPCR. I. Collection of Virus Samples

EPA Method 1615 was developed with a goal of providing a standard method for measuring enteroviruses and noroviruses in environmental and drinking waters. The standardized sampling component of the method concentrates viruses that may be present in water by passage of a minimum specified volume of water through an electropositive cartridge filter. The minimum specified volumes for surface and finished/ground water are 300 L and 1,500 L, respectively. A major method limitation is the tendency for the filters to clog before meeting the sample volume requirement. Studies using two different, but equivalent, cartridge filter options showed that filter clogging was a problem with 10% of the samples with one of the filter types compared to 6% with the other filter type. Clogging tends to increase with turbidity, but cannot be predicted based on turbidity measurements only. From a cost standpoint one of the filter options is preferable over the other, but the water quality and experience with the water system to be sampled should be taken into consideration in making filter selections.

EPA Method 1615 uses an electropositive filter to concentrate enteroviruses and noroviruses in environmental and drinking waters. This manuscript describes the procedure for collecting samples for Method 1615 analyses.

EPA-Methode 1615 Messung der Enterovirus und Norovirus Vorkommen in Wasser von Kultur und RT-qPCR. I. Sammlung von Virenproben

EPA Method 1615 was developed with a goal of providing a standard method for measuring enteroviruses and noroviruses in environmental and drinking waters. ...

EPA Method 1615. Measurement of Enterovirus and Norovirus Occurrence in Water by Culture and RT-qPCR. Part III. Virus Detection by RT-qPCR

EPA Method 1615 measures enteroviruses and noroviruses present in environmental and drinking waters. This method was developed with the goal of having a standardized method for use in multiple analytical laboratories during monitoring period 3 of the Unregulated Contaminant Monitoring Rule. Herein we present the protocol for extraction of viral ribonucleic acid (RNA) from water sample concentrates and for quantitatively measuring enterovirus and norovirus concentrations using reverse transcription-quantitative PCR (RT-qPCR). Virus concentrations for the molecular assay are calculated in terms of genomic copies of viral RNA per liter based upon a standard curve. The method uses a number of quality controls to increase data quality and to reduce interlaboratory and intralaboratory variation. The method has been evaluated by examining virus recovery from ground and reagent grade waters seeded with poliovirus type 3 and murine norovirus as a surrogate for human noroviruses. Mean poliovirus recoveries were 20% in groundwaters and 44% in reagent grade water. Mean murine norovirus recoveries with the RT-qPCR assay were 30% in groundwaters and 4% in reagent grade water.

Here we present a procedure to quantify enterovirus and norovirus in environmental and drinking waters using reverse transcription-quantitative PCR. Mean virus recovery from groundwater with this standardized procedure from EPA Method 1615 was 20% for poliovirus and 30% for murine norovirus.

EPA-Methode 1615 Messung der Enterovirus und Norovirus Vorkommen in Wasser, Kultur und RT-qPCR. Teil III. Virenerkennung durch RT-qPCR

EPA Method 1615 measures enteroviruses and noroviruses present in environmental and drinking waters. This method was developed with the goal of having a ...

Calibrated Passive Sampling - Multi-plot Field Measurements of NH3 Emissions with a Combination of Dynamic Tube Method and Passive Samplers

Agricultural ammonia (NH3) emissions (90% of total EU emissions) are responsible for about 45% airborne eutrophication, 31% soil acidification and 12% fine dust formation within the EU15. But NH3 emissions also mean a considerable loss of nutrients. Many studies on NH3 emission from organic and mineral fertilizer application have been performed in recent decades. Nevertheless, research related to NH3 emissions after application fertilizers is still limited in particular with respect to relationships to emissions, fertilizer type, site conditions and crop growth. Due to the variable response of crops to treatments, effects can only be validated in experimental designs including field replication for statistical testing. The dominating ammonia loss methods yielding quantitative emissions require large field areas, expensive equipment or current supply, which restricts their application in replicated field trials. This protocol describes a new methodology for the measurement of NH3 emissions on many plots linking a simple semi-quantitative measuring method used in all plots, with a quantitative method by simultaneous measurements using both methods on selected plots. As a semi-quantitative measurement method passive samplers are used. The second method is a dynamic chamber method (Dynamic Tube Method) to obtain a transfer quotient, which converts the semi-quantitative losses of the passive sampler to quantitative losses (kg nitrogen ha-1). The principle underlying this approach is that passive samplers placed in a homogeneous experimental field have the same NH3 absorption behavior under identical environmental conditions. Therefore, a transfer co-efficient obtained from single passive samplers can be used to scale the values of all passive samplers used in the same field trial. The method proved valid under a wide range of experimental conditions and is recommended to be used under conditions with bare soil or small canopies (&#60;0.3 m). Results obtained from experiments with taller plants should be treated more carefully.

Calibrated Passive Sampling - Multi-plot Field Measurements of NH3 Emissions with a Combination of Dynamic Tube Method and Passive Samplers

Ammonia emissions are a major threat to the environment by eutrophication, soil acidification and fine particle formation and stem mainly from agricultural sources. This method allows ammonia loss measurements in replicated field trials enabling statistical analysis of emissions and of relationships between crop development and emissions.

Kalibrierte Passive Sampling - Multi-Plot Feldmessungen von NH<sub&gt; 3</sub&gt; Emissionen mit einer Kombination von Dynamic Tube-Methode und Passive Samplers

Agricultural ammonia (NH3) emissions (90% of total EU emissions) are responsible for about 45% airborne eutrophication, 31% soil acidification and 12% ...

Extraction of Organochlorine Pesticides from Plastic Pellets and Plastic Type Analysis

Plastic resin pellets, categorized as microplastics (&#8804;5 mm in diameter), are small granules that can be unintentionally released to the environment during manufacturing and transport. Because of their environmental persistence, they are widely distributed in the oceans and on beaches all over the world. They can act as a vector of potentially toxic organic compounds (e.g., polychlorinated biphenyls) and might consequently negatively affect marine organisms. Their possible impacts along the food chain are not yet well understood. In order to assess the hazards associated with the occurrence of plastic pellets in the marine environment, it is necessary to develop methodologies that allow for rapid determination of associated organic contaminant levels. The present protocol describes the different steps required for sampling resin pellets, analyzing adsorbed organochlorine pesticides (OCPs) and identifying the plastic type. The focus is on the extraction of OCPs from plastic pellets by means of a pressurized fluid extractor (PFE) and on the polymer chemical analysis applying Fourier Transform-InfraRed (FT-IR) spectroscopy. The developed methodology focuses on 11 OCPs and related compounds, including dichlorodiphenyltrichloroethane (DDT) and its two main metabolites, lindane and two production isomers, as well as the two biologically active isomers of technical endosulfan. This protocol constitutes a simple and rapid alternative to existing methodology for evaluating the concentration of organic contaminants adsorbed on plastic pieces.

Microplastics act as vector of potentially toxic organic contaminants with unpredictable effects. This protocol describes an alternative methodology for assessing the levels of organochlorine pesticides adsorbed on plastic pellets and identifying the polymer chemical structure. The focus is on pressurized fluid extraction and attenuated total reflectance Fourier transform infrared spectroscopy.

Extraktion von Organochlor-Pestiziden aus Kunststoff-Pellets und Kunststoff-Typ-Analyse

Plastic resin pellets, categorized as microplastics (&#8804;5 mm in diameter), are small granules that can be unintentionally released to the environment ...

Continuous Instream Monitoring of Nutrients and Sediment in Agricultural Watersheds

Pollutant concentrations and loads in watersheds vary considerably with time and space. Accurate and timely information on the magnitude of pollutants in water resources is a prerequisite for understanding the drivers of the pollutant loads and for making informed water resource management decisions. The commonly used &#34;grab sampling&#34; method provides the concentrations of pollutants at the time of sampling (i.e., a snapshot concentration) and may under- or overpredict the pollutant concentrations and loads. Continuous monitoring of nutrients and sediment has recently received more attention due to advances in computing, sensing technology, and storage devices. This protocol demonstrates the use of sensors, sondes, and instrumentation to continuously monitor in situ nitrate, ammonium, turbidity, pH, conductivity, temperature, and dissolved oxygen (DO) and to calculate the loads from two streams (ditches) in two agricultural watersheds. With the proper calibration, maintenance, and operation of sensors and sondes, good water quality data can be obtained by overcoming challenging conditions such as fouling and debris buildup. The method can also be used in watersheds of various sizes and characterized by agricultural, forested, and/or urban land.

With the advancement of technology and the rise in end-user expectations, the need and use of higher temporal resolution data for pollutant load estimation has increased. This protocol describes a method for continuous in situ water quality monitoring to obtain higher temporal resolution data for informed water resource management decisions.

Kontinuierliche Instream Überwachung von Nährstoffen und Sediment in landwirtschaftlichen Wasserscheiden

Pollutant concentrations and loads in watersheds vary considerably with time and space. Accurate and timely information on the magnitude of pollutants in ...

Continuous Hydrologic and Water Quality Monitoring of Vernal Ponds

Vernal ponds, also referred to as vernal pools, provide critical ecosystem services and habitat for a variety of threatened and endangered species. However, they are vulnerable parts of the landscapes that are often poorly understood and understudied. Land use and management practices, as well as climate change are thought to be a contribution to the global amphibian decline. However, more research is needed to understand the extent of these impacts. Here, we present methodology for characterizing a vernal pond's morphology and detail a monitoring station that can be used to collect water quantity and quality data over the duration of a vernal pond's hydroperiod. We provide methodology for how to conduct field surveys to characterize the morphology and develop stage-storage curves for a vernal pond. Additionally, we provide methodology for monitoring the water level, temperature, pH, oxidation-reduction potential, dissolved oxygen, and electrical conductivity of water in a vernal pond, as well as monitoring rainfall data. This information can be used to better quantify the ecosystem services that vernal ponds provide and the impacts of anthropogenic activities on their ability to provide these services.

Understanding the ecosystem services and processes provided by vernal ponds and the impacts of anthropogenic activities on their ability to provide these services requires intensive hydrologic monitoring. This sampling protocol using in-situ monitoring equipment was developed to understand the impact of anthropogenic activities on water levels and quality.

Kontinuierliche hydrologischen und Qualitätsüberwachung von Vernal Teichen

Vernal ponds, also referred to as vernal pools, provide critical ecosystem services and habitat for a variety of threatened and endangered species. ...

Improving Infrared Spectroscopy Characterization of Soil Organic Matter with Spectral Subtractions

Soil organic matter (SOM) underlies numerous soil processes and functions. Fourier transform infrared (FTIR) spectroscopy detects infrared-active organic bonds that constitute the organic component of soils. However, the relatively low organic matter content of soils (commonly &#60; 5% by mass) and absorbance overlap of mineral and organic functional groups in the mid-infrared (MIR) region (4,000-400 cm-1) engenders substantial interference by dominant mineral absorbances, challenging or even preventing interpretation of spectra for SOM characterization. Spectral subtractions, a post-hoc mathematical treatment of spectra, can reduce mineral interference and enhance resolution of spectral regions corresponding to organic functional groups by mathematically removing mineral absorbances. This requires a mineral-enriched reference spectrum, which can be empirically obtained for a given soil sample by removing SOM. The mineral-enriched reference spectrum is subtracted from the original (untreated) spectrum of the soil sample to produce a spectrum representing SOM absorbances. Common SOM removal methods include high-temperature combustion (&#39;ashing&#39;) and chemical oxidation. Selection of the SOM removal method carries two considerations: (1) the amount of SOM removed, and (2) absorbance artifacts in the mineral reference spectrum and thus the resulting subtraction spectrum. These potential issues can, and should, be identified and quantified in order to avoid fallacious or biased interpretations of spectra for organic functional group composition of SOM. Following SOM removal, the resulting mineral-enriched sample is used to collect a mineral reference spectrum. Several strategies exist to perform subtractions depending on the experimental goals and sample characteristics, most notably the determination of the subtraction factor. The resulting subtraction spectrum requires careful interpretation based on the aforementioned methodology. For many soil and other environmental samples containing substantial mineral components, subtractions have strong potential to improve FTIR spectroscopic characterization of organic matter composition.

SOM underlies many soil functions and processes, but its characterization by FTIR spectroscopy is often challenged by mineral interferences. The described method can increase the utility of SOM analysis by FTIR spectroscopy by subtracting mineral interferences in soil spectra using empirically obtained mineral reference spectra.

Verbesserung der Infrarot-Spektroskopie Charakterisierung der organischen Bodensubstanz mit spektralen Subtraktionen

Soil organic matter (SOM) underlies numerous soil processes and functions. Fourier transform infrared (FTIR) spectroscopy detects infrared-active organic ...

The Plant Infection Test: Spray and Wound-Mediated Inoculation with the Plant Pathogen Magnaporthe Grisea

Plants possess a powerful system to defend themselves against potential threats by pathogenic fungi. For agriculturally important plants, however, current measures to combat such pathogens have proved too conservative and, thus, not sufficiently effective, and they can potentially pose environmental risks. Therefore, it is extremely necessary to identify host-resistance factors to assist in controlling plant diseases naturally through the identification of resistant germplasm, the isolation and characterization of resistance genes, and the molecular breeding of resistant cultivars. In this regard, there is need to establish an accurate, rapid, and large-scale inoculation method to breed and develop plant resistance genes. The rice blast fungal pathogen Magnaporthe grisea causes severe disease symptoms and yield losses. Recently, M. grisea has emerged as a model organism for studying the mechanisms of plant-fungal pathogen interactions. Hence, we report the development of a plant virulence test method that is specific for M. grisea. This method provides for both spray inoculation with a conidial suspension and wounding inoculation with mycelium cubes or droplets of conidial suspension. The key step of the wounding inoculation method for detached rice leaves is to make wounds on plant leaves, which avoids any interference caused by host penetration resistance. This spray/wounding protocol contributes to the rapid, accurate, and large-scale screening of the pathotypes of M. grisea isolates. This integrated and systematic plant infection method will serve as an excellent starting point for gaining a broad perspective of issues in plant pathology.

The Plant Infection Test: Spray and Wound-Mediated Inoculation with the Plant Pathogen Magnaporthe Grisea

Here, we present a protocol to test plant virulence with the plant pathogen Magnaporthe grisea. This report will contribute to the large-scale screening of the pathotypes of fungi isolates and serve as an excellent starting point for understanding the resistant mechanisms of plants during molecular breeding.

Die Pflanze-Infektion-Test: Spray und Wunde-vermittelten Inokulation mit Pflanzen Pathogen Magnaporthe Grisea

Plants possess a powerful system to defend themselves against potential threats by pathogenic fungi. For agriculturally important plants, however, current ...

Visualizing Efficacy of Pesticides Against Disease Vector Mosquitoes in the Field

Efficacy of public health pesticides targeting nuisance and disease-vector insects such as mosquitoes, sand flies, and filth-breeding flies is not uniform across ecological zones. To best protect public and veterinary health from these insects, the environmental limitations of pesticides need to be investigated to inform effective use of the most appropriate pesticide formulations and techniques. We have developed a research program to evaluate combinations of pesticides, pesticide application equipment, and application techniques in hot-arid desert, hot-humid tropical, warm and cool temperate, and urban locations to derive pesticide use guidelines specific to target insect and environment. To these ends we designed a system of protocols to support efficient, cost-effective, portable, and standardized evaluation of a diverse range of pesticides and equipment across multiple environments. At the core of these protocols is the use of an array of small cages with colony-reared sentinel mosquitoes (adults and immatures) and sand flies (adults), strategically arranged in natural habitats and exposed to pesticide spray. Spatial and temporal patterns of pesticide efficacy are derived from percent mortality in sentinel cages, then mapped and visualized in a geographic information system. Maps of sentinel mortality data may be statistically compared to evaluate relative efficacy of a pesticide across multiple environments, or to study multiple pesticides in a single environment. Protocols may be modified to accommodate a variety of scenarios, including, for example, the vertical orientation of sentinels in canopy habitats or simultaneous testing of ground and aerial application methods.

The efficacy of public health pesticides targeting nuisance and disease-vector insects is not uniform across different ecological zones. Here we present a system of techniques using captive vector insects as sentinels for pesticide efficacy to derive electronic maps supporting the standard evaluation of pesticides across multiple environments.

Wirksamkeit von Pestiziden gegen Krankheit Vektor Mücken im Bereich Visualisierung

Efficacy of public health pesticides targeting nuisance and disease-vector insects such as mosquitoes, sand flies, and filth-breeding flies is not uniform ...