Pyrethroid Insecticides [1st ed.] 9783030556952, 9783030556969

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The Handbook of Environmental Chemistry 92 Series Editors: Damià Barceló · Andrey G. Kostianoy

Ethel Eljarrat  Editor

Pyrethroid Insecticides

The Handbook of Environmental Chemistry Volume 92 Founding Editor: Otto Hutzinger Series Editors: Dami
a Barcelo´ • Andrey G. Kostianoy

Editorial Board Members: Jacob de Boer, Philippe Garrigues, Ji-Dong Gu, Kevin C. Jones, Thomas P. Knepper, Abdelazim M. Negm, Alice Newton, Duc Long Nghiem, Sergi Garcia-Segura

In over three decades, The Handbook of Environmental Chemistry has established itself as the premier reference source, providing sound and solid knowledge about environmental topics from a chemical perspective. Written by leading experts with practical experience in the field, the series continues to be essential reading for environmental scientists as well as for environmental managers and decisionmakers in industry, government, agencies and public-interest groups. Two distinguished Series Editors, internationally renowned volume editors as well as a prestigious Editorial Board safeguard publication of volumes according to high scientific standards. Presenting a wide spectrum of viewpoints and approaches in topical volumes, the scope of the series covers topics such as • • • • • • • •

local and global changes of natural environment and climate anthropogenic impact on the environment water, air and soil pollution remediation and waste characterization environmental contaminants biogeochemistry and geoecology chemical reactions and processes chemical and biological transformations as well as physical transport of chemicals in the environment • environmental modeling A particular focus of the series lies on methodological advances in environmental analytical chemistry. The Handbook of Envir onmental Chemistry is available both in print and online via http://link.springer.com/bookseries/698. Articles are published online as soon as they have been reviewed and approved for publication. Meeting the needs of the scientific community, publication of volumes in subseries has been discontinued to achieve a broader scope for the series as a whole.

Pyrethroid Insecticides

Volume Editor: Ethel Eljarrat

With contributions by ` . Aznar-Alemany
R. Barra
S. M. Brander
J. Dachs
O A. Dallegrave
F. R. de Aquino Neto
E. Eljarrat
M. L. Feo
B. Jara
A. Klimowska
K. M. Major
S. Malard
O. Malm
L. Me´janelle
C. E. T. Parente
T. M. Pizzolato
W. Rodzaj
A.-M. Saillenfait
F. Tucca
C. P. Weisel
B. Wielgomas

Editor Ethel Eljarrat Institute of Environmental Assessment and Water Research (IDAEA-CSIC) Barcelona, Spain

ISSN 1867-979X ISSN 1616-864X (electronic) The Handbook of Environmental Chemistry ISBN 978-3-030-55695-2 ISBN 978-3-030-55696-9 (eBook) https://doi.org/10.1007/978-3-030-55696-9 © Springer Nature Switzerland AG 2020 This work is subject to copyright. All rights are reserved by the Publisher, whether the whole or part of the material is concerned, specifically the rights of translation, reprinting, reuse of illustrations, recitation, broadcasting, reproduction on microfilms or in any other physical way, and transmission or information storage and retrieval, electronic adaptation, computer software, or by similar or dissimilar methodology now known or hereafter developed. The use of general descriptive names, registered names, trademarks, service marks, etc. in this publication does not imply, even in the absence of a specific statement, that such names are exempt from the relevant protective laws and regulations and therefore free for general use. The publisher, the authors, and the editors are safe to assume that the advice and information in this book are believed to be true and accurate at the date of publication. Neither the publisher nor the authors or the editors give a warranty, expressed or implied, with respect to the material contained herein or for any errors or omissions that may have been made. The publisher remains neutral with regard to jurisdictional claims in published maps and institutional affiliations. This Springer imprint is published by the registered company Springer Nature Switzerland AG. The registered company address is: Gewerbestrasse 11, 6330 Cham, Switzerland

Series Editors Prof. Dr. Dami
a Barcelo´

Prof. Dr. Andrey G. Kostianoy

Department of Environmental Chemistry IDAEA-CSIC C/Jordi Girona 18–26 08034 Barcelona, Spain and Catalan Institute for Water Research (ICRA) H20 Building Scientific and Technological Park of the University of Girona Emili Grahit, 101 17003 Girona, Spain [email protected]

Shirshov Institute of Oceanology Russian Academy of Sciences 36, Nakhimovsky Pr. 117997 Moscow, Russia and S.Yu. Witte Moscow University Moscow, Russia [email protected]

Editorial Board Members Prof. Dr. Jacob de Boer VU University Amsterdam, Amsterdam, The Netherlands

Prof. Dr. Philippe Garrigues Universite´ de Bordeaux, Talence Cedex, France

Prof. Dr. Ji-Dong Gu Guangdong Technion-Israel Institute of Technology, Shantou, Guangdong, China

Prof. Dr. Kevin C. Jones Lancaster University, Lancaster, UK

Prof. Dr. Thomas P. Knepper Hochschule Fresenius, Idstein, Hessen, Germany

Prof. Dr. Abdelazim M. Negm Zagazig University, Zagazig, Egypt

Prof. Dr. Alice Newton University of Algarve, Faro, Portugal

Prof. Dr. Duc Long Nghiem University of Technology Sydney, Broadway, NSW, Australia

Prof. Dr. Sergi Garcia-Segura Arizona State University, Tempe, AZ, USA

Series Preface

With remarkable vision, Prof. Otto Hutzinger initiated The Handbook of Environmental Chemistry in 1980 and became the founding Editor-in-Chief. At that time, environmental chemistry was an emerging field, aiming at a complete description of the Earth’s environment, encompassing the physical, chemical, biological, and geological transformations of chemical substances occurring on a local as well as a global scale. Environmental chemistry was intended to provide an account of the impact of man’s activities on the natural environment by describing observed changes. While a considerable amount of knowledge has been accumulated over the last four decades, as reflected in the more than 150 volumes of The Handbook of Environmental Chemistry, there are still many scientific and policy challenges ahead due to the complexity and interdisciplinary nature of the field. The series will therefore continue to provide compilations of current knowledge. Contributions are written by leading experts with practical experience in their fields. The Handbook of Environmental Chemistry grows with the increases in our scientific understanding, and provides a valuable source not only for scientists but also for environmental managers and decision-makers. Today, the series covers a broad range of environmental topics from a chemical perspective, including methodological advances in environmental analytical chemistry. In recent years, there has been a growing tendency to include subject matter of societal relevance in the broad view of environmental chemistry. Topics include life cycle analysis, environmental management, sustainable development, and socio-economic, legal and even political problems, among others. While these topics are of great importance for the development and acceptance of The Handbook of Environmental Chemistry, the publisher and Editors-in-Chief have decided to keep the handbook essentially a source of information on “hard sciences” with a particular emphasis on chemistry, but also covering biology, geology, hydrology and engineering as applied to environmental sciences. The volumes of the series are written at an advanced level, addressing the needs of both researchers and graduate students, as well as of people outside the field of vii

viii

Series Preface

“pure” chemistry, including those in industry, business, government, research establishments, and public interest groups. It would be very satisfying to see these volumes used as a basis for graduate courses in environmental chemistry. With its high standards of scientific quality and clarity, The Handbook of Environmental Chemistry provides a solid basis from which scientists can share their knowledge on the different aspects of environmental problems, presenting a wide spectrum of viewpoints and approaches. The Handbook of Environmental Chemistry is available both in print and online via www.springerlink.com/content/110354/. Articles are published online as soon as they have been approved for publication. Authors, Volume Editors and Editors-in-Chief are rewarded by the broad acceptance of The Handbook of Environmental Chemistry by the scientific community, from whom suggestions for new topics to the Editors-in-Chief are always very welcome. Dami
a Barcelo´ Andrey G. Kostianoy Series Editors

Preface

The book on “Pyrethroid Insecticides” is based on the scientific developments and results achieved along several years of research. Pyrethroid insecticides, introduced in the late 1970s, actually represent 25% of global sales of insecticides. In the last decades, they have increasingly replaced organochlorine pesticides due to their relatively lower mammalian toxicity, selective insecticide activity and lower environmental persistence. They are considered to be “safe” because they are converted to non-toxic metabolites by oxidative metabolism in fish and by hydrolysis in mammals. However, recent studies demonstrated their environmental ubiquity, their bioaccumulation and their toxicity in different aquatic and terrestrial organisms and even in humans. This book aims to review and compile the main developments and knowledge acquired over many years of study from a multidisciplinary way, including analytical chemistry, environmental, biological and toxicological developments. The book is structured in 12 different chapters, covering the state of the art of analysis, fate and behaviour and toxicity of pyrethroid insecticides. Experts in the field provide an overview of their physico-chemical properties and uses, the advanced chemical analytical methods, the occurrence in environment and biota, the isomeric and enantiomeric behaviour, the toxicological effects and the human exposure. Finally, the last chapter concerns the main conclusions and future trends, being the starting point to be taken in mind for the future studies in the field of pyrethroid insecticides. We hope the book will be of interest to a broad audience of scientific researchers as well as for authorities and producers. Finally, I would like to thank all the contributing authors of this book for their time and effort in preparing this comprehensive compilation of research papers. Barcelona, Spain January 2020

Ethel Eljarrat

ix

Contents

Introduction to Pyrethroid Insecticides: Chemical Structures, Properties, Mode of Action and Use . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . ` . Aznar-Alemany and E. Eljarrat O

1

Analytical Methods for Determining Pyrethroid Insecticides in Environmental and Food Matrices . . . . . . . . . . . . . . . . . . . . . . . . . . . . . Maria Luisa Feo

17

Analytical Methods for Determination Urinary Metabolites of Synthetic Pyrethroids . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . Bartosz Wielgomas, Anna Klimowska, and Wojciech Rodzaj

47

Fate of Pyrethroids in Freshwater and Marine Environments . . . . . . . . Laurence Me´janelle, Bibiana Jara, and Jordi Dachs

81

The Ecological and Evolutionary Implications of Pyrethroid Exposure: A New Perspective on Aquatic Ecotoxicity . . . . . . . . . . . . . . . . . . . . . . . 109 Kaley M. Major and Susanne M. Brander Stereoselectivity and Environmental Behaviour of Pyrethroids . . . . . . . 149 Cla´udio Ernesto Taveira Parente, Olaf Malm, and Francisco Radler de Aquino Neto Environmental Risks of Synthetic Pyrethroids Used by the Salmon Industry in Chile . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 177 Felipe Tucca and Ricardo Barra Bioavailability and Bioaccumulation of Pyrethroid Insecticides in Wildlife and Humans . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 205 ` . Aznar-Alemany and E. Eljarrat O Indoor and Outdoor Pyrethroid Air Concentrations . . . . . . . . . . . . . . . 227 Clifford P. Weisel

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Contents

Risk Assessment of Human Exposure to Pyrethroids Through Food . . . 245 T^ania Mara Pizzolato and Alexsandro Dallegrave Human Risk Associated with Long-Term Exposure to Pyrethroid Insecticides . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 259 Anne-Marie Saillenfait and Ste´phane Malard Conclusions and Future Trends . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 305 E. Eljarrat

Introduction to Pyrethroid Insecticides: Chemical Structures, Properties, Mode of Action and Use Ò. Aznar-Alemany and E. Eljarrat

Contents 1 History and Impact . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 2 The Compounds . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 4 3 Properties . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 4 4 Metabolisation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 8 5 Toxicity . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 6 Legislation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 11 References . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 13

Abstract During the 1920s, pyrethrin was studied because of its potential as a precursor for synthetic organic pesticides. The first pyrethroid pesticide, allethrin, was identified in 1949. It is a type I pyrethroid because of a carboxylic ester of cyclopropane. Type II was created with the addition of a cyano group in α position. Some phenylacetic 3-phenoxybenzyl esters missing the cyclopropane but with the cyano group are also considered type II. In the 1970s, pyrethroids transitioned from mere household products to pest control agents in agriculture. Later, pyrethroids have replaced organophosphate pesticides in most of their applications the same way the latter had replaced organochlorinated pesticides before. Works on the optimisation of pyrethroids has granted them better photostability without compromising their biodegradability, as well as selective toxicity, metabolic routes of degradation and more effectivity, translating into the use of smaller amounts. Most pyrethroids present different isomers, each with different biological activity and, therefore, different toxicity. Pyrethroids account for a quarter of the pesticides used nowadays. Pyrethroids’ relative molecular mass is clearly above 300 g mol
1; they are highly hydrophobic, photosensitive and get easily hydrolysed, with degradation times below 60 days. They are not persistent and mammals can metabolise them.

Ò. Aznar-Alemany (*) and E. Eljarrat Department of Environmental Chemistry, IDAEA-CSIC, Barcelona, Spain e-mail: [email protected] Ethel Eljarrat (ed.), Pyrethroid Insecticides, Hdb Env Chem (2020) 92: 1–16, DOI 10.1007/698_2019_435, © Springer Nature Switzerland AG 2020, Published online: 22 February 2020

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Ò. Aznar-Alemany and E. Eljarrat

However, pyrethroids have been proven to bioaccumulate in marine mammals and humans. Studies in mammals reported carcinogenic, neurotoxic and immunosuppressive properties and potential for reproductive toxicity mainly. Acceptable daily intake values and no observed adverse effect level values have been established at 0.02–0.07 mg (kg body weight)
1 day
1 and 1–7 mg (kg body weight)
1 day
1. Keywords Chemical structures, Metabolisation, Pest control, Pesticides, Physicochemical properties, Pyrethroids, Toxicity

Abbreviations ADI BAF BCF DDT DT50 EFSA EPA IC50 Kow LOD LOEC Mr MRL NOAEL NOEC POP

Acceptable daily intake Bioaccumulation factor Bioconcentration factor Dichlorodiphenyltrichloroethane Degradation time for 50% of the substance European Food Safety Authority Environmental Protection Agency Half-maximal inhibitory concentration Octanol-water partition coefficient Limit of detection Lowest observed effect concentration Relative molecular mass Maximum residue level No observed adverse effect level No observed effect concentration Persistent organic pollutant

1 History and Impact During the 1920s, pyrethrin was studied because of its potential as a precursor for synthetic organic pesticides. Pyrethrin was extracted from pyrethrum, a plant of the family of chrysanthemums [1]. Research on synthetic organic pesticides increased in the 1930s, and in 1939, dichlorodiphenyltrichloroethane (DDT) was synthesised. It proved to be effective for many plagues. DDT was so effective that other organochlorinated compounds were studied with the aim of obtaining cheap and persistent pesticides. At first, pesticides were not considered to affect health or the environment. However, in 1962 Rachel Carson published Silent Spring, where she warned about the effects of pesticides on the environment with the image of dead birds in her garden.

Introduction to Pyrethroid Insecticides: Chemical Structures, Properties, Mode. . .

3

This field observation prompted several research studies about environmental and mesocosm models focused on the assessment of pyrethroids and other pesticides [1]. As a consequence, some regulation agencies came into existence. In 1970, the Environmental Protection Agency (EPA) was founded. From that moment on, the use of organochlorinated compounds was restricted or banned as they were considered toxic and contaminant [2, 3]. Nevertheless, they are still allowed to fight malaria [4–6]. In the 1940s, it was discovered that many organophosphate compounds had unique properties for the protection of plants – and that the most volatile and toxic could be used as chemical weapons. However, not until the 1960s did organophosphate compounds become popular. At the end of the same decade, there was an increasing interest in carbamate pesticides. Organophosphates and carbamates had simple structures, and it was easy to synthesise analogous derivatives. They also showed some advantages over organochlorinated pesticides [1]. They were selectively toxic with different effects depending on the species; they affected insects more than mammals [7]; the effects on mammals occurred mostly after intense exposition rather than accumulation; they were more biodegradable, therefore, less persistent, and they allowed the creation of compounds that stay inside the plants for a few weeks and protect them. On the other hand, regulations and bans on the use of organophosphates and carbamates emerged as a consequence of new data on their actual toxicity [8]. Toxicology studies are a key element of the development of new pesticides nowadays. In the 1970s, pyrethroids stopped being mere household products to become pest control agents in agriculture. Moreover, in the last couple of decades, pyrethroids have replaced organophosphate pesticides in most of their applications the same way the latter had replaced organochlorinated pesticides before [9, 10]. Pyrethroids were very effective. Works on the optimisation of these derivatives from pyrethrin had been going on for decades, and several improvements were achieved [1]. Their photostability was improved without compromising their biodegradability. They achieved a selective toxicity and metabolic routes of degradation – that were different for cis and trans isomers. They were produced as fumigants as well as soil pesticides. And they were made more powerful so that smaller amounts would need to be used and environmental contamination would be reduced. The development of pyrethroids included some aspects that helped reduce the impact of pesticides on the environment: higher effectiveness implying smaller amounts of product needed, selective toxicity, concern on the occurrence of pesticides in the environment and replacement of persistent compounds with degradable compounds [1].

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Ò. Aznar-Alemany and E. Eljarrat

Fig. 1 Pyrethroid types according to their general structure

2 The Compounds The first pyrethroid pesticide, allethrin, was identified in 1949 [11]. It is a type I pyrethroid because of the carboxylic ester of cyclopropane. Type II was created with the addition of a cyano group in α position, which increased the pesticide effect of pyrethroids (Figs. 1, 2 and 3). Additionally, pesticide activity was detected in some phenylacetic 3-phenoxybenzyl esters that missed the cyclopropane but had the cyano group [11]. These esters were still considered type II pyrethroids and originated compounds such as fenvalerate. Due to the cyclopropane and the cyano group, most pyrethroids present different isomers, each with different biological activity and, therefore, different toxicity. Type I pyrethroids have two chirality centres, hence two diastereoisomers or enantiomeric pairs. Type II pyrethroids present three chirality centres, hence four diastereoisomers. The bonds that are responsible for the existence of enantiomeric pairs are represented with winding lines in Figs. 2 and 3. These diastereoisomers present different properties [12]. More detailed information of pyrethroid stereoselectivity is presented in Chapter “Stereoselectivity and Environmental Behaviour of Pyrethroids”. Pyrethroids account for a quarter of the pesticides used nowadays [1, 13]. They were believed to be the ideal pesticides because they are not persistent and were thought to be metabolised and not bioaccumulate [14, 15]. Thus they replaced the previously banned pesticides. Total organic pesticide production in the United States increased from about 15 tons per year in 1945 to over 630 tons per year in 1976 [16]. In 2006 over 433 tons of pesticides were used worldwide, 400 tons in 2007 [17]. Pyrethroids account for about 25% of the pesticide use. Pyrethroids have applications as pesticides in households, in commercial products and in medicine against scabies and lice (Table 1). In tropical countries, mosquito nets are impregnated with solutions of deltamethrin, cyhalothrin or cypermethrin to control malaria [11].

3 Properties Pyrethroids present somewhat similar physicochemical properties among them (Table 2). Their relative molecular mass (Mr) is clearly above 300 g mol
1. They are highly hydrophobic, with logarithm of the octanol-water partition coefficient

Introduction to Pyrethroid Insecticides: Chemical Structures, Properties, Mode. . .

5

O O

O

CH2

H3C

O CH3

CH3

Cl

O

F

CH3

CH3

F F

CH3

allethrin O

H3C

O CH3

O

O

N

CH3

O

S

N

O

CH3

CH

imiprothrin

O

H3C

H3C

O

O Cl

CH3

CH3

CH3

O

CH O Cl

O CH3

CH3

CH3

O Cl

H3C

O

CH3

prallethrin

resmethrin

O

O

O Cl

H3C H3C

CH3

phenothrin

O H3C

O CH3

O

tetramethrin

F F

O

N Cl

H3C

O

O

permethrin

CH3

O

CH3

kadethrin

O Cl

CH3

bifenthrin

O

CH3

CH3

H3C

CH3

F F

transfluthrin

Fig. 2 Type I pyrethroids

(Kow) between 4 and 7, and show low very low solubility in water of a few μg L
1. Pyrethroids are photosensitive and get easily hydrolysed; therefore their degradation time for 50% of the substance (DT50) – indicating persistence – is very low, below 60 days [21]. Organic contaminants include a wide variety of families. Some of them have been considered persistent organic pollutants (POPs). The Stockholm Convention on Persistent Organic Pollutants defined four factors that make a compound dangerous and that qualify it as a POP [22]. These are the requirements a compound needs to meet to be included in the list of the Stockholm Convention:

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Ò. Aznar-Alemany and E. Eljarrat N

N O

O Cl

O

O Cl

Cl F

H3C

CH3

F

F

F

CH3

CH3

cyfluthrin

cyhalothrin

N

N

O Cl

O O

O Cl

H3C

O

O

Br Br

CH3

O

O CH3

H3C

cypermethrin

deltamethrin Cl

N

Cl

O

O

O H3C

N

Cl

O

O

O CH3

H3C

CH3

fenvalerate

F

flumethrin

N Br

O NH

O

O

F F

N Br

Br

O

Br H3C

O

O

CH3 H3C

F

CH3

fluvalinate

tralomethrin

Fig. 3 Type II pyrethroids Table 1 Pyrethroid applications [18–20] Insects Ants, bedbugs, beetles, caterpillars, cockroaches, flies, greenflies, lice, lobsters, locusts, mites, mosquitoes, moths, termites, wasps, whiteflies

Crops Alfalfa, apple, bean, beetroot, cereal, citrus, coffee, cotton, fig, grape, green bean, lettuce, melon, olive, onion, pea, peach, peanut, pear, potato, rice, seeds, soy, sugarcane, sunflower, tea, tobacco, tomato, walnut, watermelon, wheat

Others Forests, gardens, grass, greenhouses, households, industries, ornaments, pets, public health, shampoo, shops, warehouses, wood

Introduction to Pyrethroid Insecticides: Chemical Structures, Properties, Mode. . .

7

Table 2 Properties of pyrethroids [21] Pyrethroid Allethrin Bifenthrin Imiprothrin Kadethrin Permethrin Phenothrin Prallethrin Resmethrin Tetramethrin Transfluthrin Cyfluthrin Cyhalothrin Cypermethrin Deltamethrin Fenvalerate Flumethrin Fluvalinate Tralomethrin

Type I I I I I I I I I I II II II II II II II II

Molecular formula C19H26O3 C23H22O2ClF3 C17H22N2O4 C23H24O4S C21H20O3Cl2 C23H26O3 C19H24O3 C22H26O3 C19H25NO4 C15H12Cl2F4O2 C22H18NO3Cl2F C23H19NO3ClF3 C22H19NO3Cl2 C22H19NO3Br2 C25H22NO3Cl C28H22Cl2FNO3 C26H22N2O3ClF3 C22H19NO3Br4

Mr (g mol
1) 302.4 422.9 318.4 396.5 391.3 350.5 300.4 338.5 331.4 371.2 434.3 449.9 416.3 505.2 419.9 510.4 502.9 665.0

log Kow 4.96 6.6 2.43 6.29 6.1 6.01 4.49 5.43 4.6 5.46 6 6.9 5.3 4.6 5.01 – 3.85 5

Water solubility at 20 C (μg L
1) 0.1 1 93,500 14 200 9.7 8,030 10 1,830 57 6.6 4 9 0.2 1 – 2 80

DT50 (days) – 26 – – 13 – – 30 3 7 33 57 60 13 40 – 7 3

1. To be persistent in the environment. POPs have half-lives greater than 2 months in water or greater than 6 months in soil and sediment. 2. To bioaccumulate. POPs have bioconcentration factors (BCFs) or bioaccumulation factors (BAFs) in aquatic species greater than 5,000 or, when unknown, their log Kow is greater than 5. 3. To have potential for long-range transport. POPs are detected far from the emission source; data show they have been transported via air (half-live in air over 2 days), water or migratory species. 4. To have adverse effects. POPs are proved to have adverse effects on human health or on the environment. The original list of the Stockholm Convention included 12 POPs that were banned or restricted. Eight of them were organochlorinated pesticides: aldrin, endrin, dieldrin, chlordane, DDT, heptachlor, mirex and toxaphene. These pesticides were considered safe when they first entered the market, but data proved them to cause long-term adverse effects on human health and on the environment. New compounds have been added to the list throughout the years. Some other compounds, like pyrethroids, cannot be classified as POPs, but cause concern in the scientific community due to their properties, sometimes close to those of POPs. Pyrethroids have logarithms of Kow on the limit of POPs and affect organisms by design. However, they are not persistent and thus cannot be transported long distances and mammals can metabolise them [14, 23]. Conversely they have been proved to bioaccumulate in marine mammals and humans [24, 25].

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More detailed information of bioaccumulation of pyrethroids in wildlife and humans is presented in Chapter “Bioavailability and Bioaccumulation of Pyrethroid Insecticides in Wildlife and Humans”. The Water Framework Directive (Directive 2000/60/EC) named a group of pesticides that could be toxic, persistent and bioaccumulate. Among them, cypermethrin was listed. Due to their production volume and extensive application, pesticides such as pyrethroids are always present in the environment despite not being persistent and are therefore considered pseudo-persistent organic contaminants [26].

4 Metabolisation The capacity of mammals of metabolising pyrethroids has been regarded as one of the best qualities of these pesticides. The metabolisation route differs with the organism. However, the routes are equivalent for many mammals, and the mechanism in humans will serve as an example. The liver is the main organ responsible for disintoxication in humans, although other organs and tissues possess the required enzymes to treat xenobiotics. This disintoxication usually proceeds in two steps [27]. The first step consists in increasing the polarity of the xenobiotic molecular through processes like hydroxylation, deamination or the N-oxidation. In the second step, the metabolite – which is more polar than the original molecule – is combined with endogen products of the cell, such as methyl or acetyl groups, monosaccharides or amino acids. This increases the metabolite solubility making it easier for it to be excreted in urine. This is the reason why exposition of humans to pyrethroids is studied through the analysis of their metabolites in urine [28]. The first step of the metabolisation of pyrethroids in humans can occur through two pathways. One is the breakdown of the ester to produce carboxylic acid and the corresponding alcohol by the action of carboxylesterases [29]. Then, alcohol can be oxidised to a benzoic acid (Fig. 4). The carboxylesterases required for this metabolisation are found in the plasma of mammals at higher concentrations than in fish or birds [30]. This could be a factor in explaining the lower toxicity of pyrethroids in mammals. On the other hand, carboxylesterases present isoenzymes that can be found in different proportions in each individual depending on factors such as species, age or gender [30]. Each isoenzyme can have a different activity on different isomers of pyrethroids, thus making the capacity of metabolising these compounds change not only among species, but also among individuals of different age and gender [31]. The second pathway for the first step of the metabolisation of pyrethroids in humans is hydroxylation by monooxygenases. The process usually undergoes transformation via both pathways producing secondary products such as 4-hydroxy-3phenoxybenzoyl and 4-hydroxy-3-phenoxylbenzaldehyde for permethrin. These compounds can be stronger endocrine disruptors than their non-hydroxylated analogues [32].

Introduction to Pyrethroid Insecticides: Chemical Structures, Properties, Mode. . . Fig. 4 Metabolisation of permethrin

9

O Cl

O

O Cl

H3C

CH3

permethrin carboxylesterase O Cl

OH Cl

H3C

+

O

HO

CH3

alcohol

carboxylic acid

O HO

O

benzoic acid

However, it is important to note that despite the fact that mammals can metabolise pyrethroids, studies have shown that they can also bioaccumulate these pesticides [25, 33].

5 Toxicity Exposition of organisms to pyrethroids causes concern due to the toxicity of the pesticides [34]. Recent studies in mammals reported carcinogenic, neurotoxic and immunosuppressive properties and potential for reproductive toxicity [12, 35, 36]. Type I pyrethroids cause tremors and reflex hyperexcitability, while type II cause hyperexcitability, salivation, seizures and choreoathetosis [37]. The main action of pyrethroids is on the sodium channels and chloride channels, which drive the ions through the cell membrane [1, 11, 13]. Pyrethroids lower the threshold of the action potential of nerve cells and muscle cells and cause repeated stimulation [7, 38]. At high concentrations, the entrance of sodium can prevent the generation of the action potential, block conduction and cause paralysis. Small amounts are sufficient to affect the sensitivity of nerve cells. Type II pyrethroids also decrease the flux of chloride through the chloride channels. Additionally, relatively high concentrations of type II pyrethroids can affect the receptors of γ-aminobutyric acid and cause cataleptic attacks, which have been documented in humans [11, 37].

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Pyrethroids are about 2,250 times more toxic for insects than mammals. Insects have more sensitive sodium channels, smaller bodies and low body temperatures. Moreover, the absorption through the skin in mammals is weak, and they can metabolise them into non-toxic compounds fast [11]. Human exposition to pyrethroids has been documented studying their metabolites in urine of German children and teenagers [28], in hair and blood of pregnant women and meconium of babies [39], in plasma of pregnant women from rural areas of South Africa [40] and in human milk [25, 33]. A few studies focused on marine organisms including different tissues of Brazilian dolphins [24, 41], Mediterranean dolphins [42] and wild and edible fish from Spanish rivers [43]. Seafood production has experimented a 3.2% yearly growth since 1961 [44]. Aquaculture is responsible for half of the seafood production worldwide, and the world annual fish consumption per capita is about 20 kg. While concern about the application of pyrethroids in fish farms against fish parasites exists, pyrethroid ingestion has been reported to be below the accepted daily intake (ADI) [45]. More detailed information of effect of salmon industry in the marine environment is presented in Chapter “Environmental Risks of Synthetic Pyrethroids Used by the Salmon Industry in Chile”. Most of the professional exposure is due to skin absorption. The main effect of dermal exposition is paresthesia, probably caused by the hyperactivity of cutaneous nerves, especially on the face. Paresthesia increases with stimuli such as heat, sunlight, sweat or contact with water [11]. Paresthesia disappears in 12–24 h and no special treatment is required. However, topical administration of vitamin E can reduce its symptoms. Ingestion of pyrethroids causes sore throat, nausea, vomit and abdominal pain in a few minutes. Mouth ulcers, increased secretion or dysphagia may occur [11]. Inhalation is less important, but it increases when pyrethroids are used in closed spaces. Systemic effects appear 4–48 h after exposition. The effects usually include dizziness, headache and tiredness. Less frequent effects are palpitations, chest oppression and blurry sight. Regarding long-term exposition to pyrethroids at low concentrations, a study in humans concluded that chronic toxicity of pyrethroids does not cause any specific symptoms. What could be detected were combinations and correlations of symptoms caused by the accumulative effect of pyrethroids in nerve tissue such as brain dysfunction, polyneuropathy, immunosuppression or motor problems due to multiple sclerosis or Parkinson disease [46, 47]. It was also suggested that chronic toxicity of pyrethroids affect fertility. This hypothesis was proved in rats being administered small doses of permethrin for a maximum time period of 2 months [48]. On the other hand, these results have been criticised [49] because of the experimental design [50], because pyrethroids were not believed to cause irreversible effects according to studies on sodium channels [51] or because it was thought that mammals did not bioaccumulate them [52]. Other studies researched the chronic toxicity of cis-bifenthrin in Daphnia magna and its cytotoxicity in ovarian cells of Chinese hamster (Cricetulus griseus) and in human cervical carcinoma cells [53]. The lowest observed effect concentration

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11

(LOEC) and the no observed effect concentration (NOEC) for daphnia were 0.02 and 0.01 μg L
1, respectively. The chronic value was 0.014 μg L
1. Half-maximal inhibitory concentration (IC50) for hamster ovarian cells and human carcinoma cells were 3.2  10
5 and 4.0  10
5 mol L
1, respectively. These data proved the chronic toxicity of cis-bifenthrin in both invertebrates and mammals. Male Wistar rats were administered for a year a mixture of pyrethroids equivalent to a 5th or a 25th of what is in cereals and vegetables consumed by an average Indian adult [54]. Altered oxidant and antioxidant status; severe anatomical damage in the caput, cauda, kidney, liver, lung, prostate and testis; and increased serum glutamatepyruvate transaminase, serum glutamic oxaloacetic transaminase and alkaline phosphatase activity were clear for all the groups. Decreased levels of 3β- and 17β-hydroxy steroid dehydrogenase activity, litter size and impaired acrosome reaction were detected in all the groups. Exposure to very low levels of pyrethroids for longer periods may cause damage to important tissues and male reproductive physiology [54]. Cypermethrin has been reported to cause adverse effects on the immune system, fertility, the liver metabolism and cardiovascular and enzyme activity in vertebrates, and a recent study suggests that it reduces the ovarian reserve in mice via apoptosis in granulosa cells by mitochondrial-related pathways [55]. An important toxicological parameter for pyrethroids is their enantiomeric composition as different isomers can present different toxicities [56–58].

6 Legislation No pesticide can be used in the European Union unless it has been proved to be effective against pests and to be safe for the human health and the environment. The European Union regulates the sustainable use of pesticides in order to regulate their risks and impacts on human health and the environment [59]. Directive 2009/128/EC includes key points about national action plans, education for professional consumers and pesticide distributors, public information and awareness, aerosol regulation, minimisation of use or ban of pesticides, revision of equipment and integral management of pests with limitation of chemical products. Pesticides leave residues in the treated products. The maximum residue level (MRL) is the highest concentration of a pesticide allowed by the regulation. The European Commission establishes MRLs at concentrations that are safe for the consumers and as low as possible. The MRLs are available at the European Union Pesticides database [60] (Tables 3 and 4). MRLs have been set for about 1,100 compounds in over 300 fresh products and for the same products after processing in order to take into account dilution or concentration effects. When MRLs for a pesticide are not stated, the accepted default value is 0.01 μg g
1, which usually corresponds to the limit of detection (LOD) [59]. The European Food Safety Authority (EFSA) assesses the safety for every consumer group – adults, kids, vegetarians, etc. – based on the pesticides’ toxicity

12 Table 3 Maximum residue levels for pyrethroids in different products [60]

Ò. Aznar-Alemany and E. Eljarrat Product 1. Fruits and nuts 2. Vegetables 3. Pulses 4. Oilseeds and oilfruits 5. Cereals 6. Tea, coffee, infusions, cocoa and carobs 7. Hops 8. Spices 9. Sugar plants 10. Products of terrestrial animals Tissue (a) Swine Fat Liver (b) Bovine Fat Liver (c) Sheep Fat Liver (d) Goat Fat Liver (e) Equine Fat Liver (f) Poultry (g) Others Fat Liver Milk Bird eggs Honey Amphibians and reptiles Terrestrial invertebrate animals Wild terrestrial vertebrate animals

Limits (μg g
1) 0.01–0.5 0.01–2 0.01–1 0.01–1 0.02–2 0.01–5 0.1–30 0.01–1 0.01–0.5 0.01–3 0.02–3 0.01–3 0.05–3 0.01–0.5 0.01–3 0.05–3 0.01–0.2 0.01–3 0.05–3 0.01–0.5 0.01–3 0.05–3 0.01–0.5 0.01–3 0.05–3 0.01–0.5 0.01–0.2 0.01–3 0.01–3 0.01–0.5 0.02–0.2 0.01–0.1 0.01–0.05 0.01–0.05 0.01–0.05 0.01–0.05

and the maximum typical concentrations of pesticides in food from the different diets around Europe. Additionally, acceptable daily intake (ADI) values and no observed adverse effect level (NOAEL) values have been established. ADI values for pyrethroids are between 0.02 and 0.07 mg kg
1 day
1 (mg of pyrethroid per kg of consumer’s body weight per day), and NOAEL values are set between 1 and 7 mg kg
1 day
1 [36] (Table 4).

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13

Table 4 IDA and NOAEL values for pyrethroids [36] Pyrethroid Bifenthrin Cyfluthrin Cyhalothrin Cypermethrin Deltamethrin Etofenprox Permethrin D-Fenothrin

IDA (mg kg
1 day
1) 0.02 0.02 0.002 0.05 0.01 0.03 0.05 0.07

NOAEL (mg kg
1 day
1) 1.5 2 1.5 1 3.1 5 7

Current relevant regulation for pyrethroids is: • Regulation 283/2013/EU – Commission Regulation (EU) No 283/2013 of 1 March 2013 setting out the data requirements for active substances, in accordance with Regulation (EC) No 1107/2009 of the European Parliament and of the Council concerning the placing of plant protection products on the market. • Regulation 284/2013/EU – Commission Regulation (EU) No 284/2013 of 1 March 2013 setting out the data requirements for plant protection products, in accordance with Regulation (EC) No 1107/2009 of the European Parliament and of the Council concerning the placing of plant protection products on the market. • Regulation 1107/2009/EC – Regulation (EC) No 1107/2009 of the European Parliament and of the Council of 21 October 2009 concerning the placing of plant protection products on the market and repealing Council Directives 79/117/EEC (ban on some active substances) and 91/414/EEC (commerce of phytosanitary products). • Directive 2009/128/EC – Directive 2009/128/EC of the European Parliament and of the Council of 21 October 2009 establishing a framework for community action to achieve the sustainable use of pesticides.

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Analytical Methods for Determining Pyrethroid Insecticides in Environmental and Food Matrices Maria Luisa Feo

Contents 1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 Sample Preparation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2.1 Extraction from Water Sample . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2.2 Extraction from Soil and Sediment Samples . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2.3 Extraction from Air Samples . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2.4 Extraction from Biological Samples . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2.5 Extraction from Food Samples . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 3 Instrumental Analysis . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 3.1 GC Methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 3.2 LC Methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 4 Enantioselective Separation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 Quantitative Methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 Conclusion . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . References . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .

18 24 24 31 33 33 34 36 36 37 38 39 39 41

Abstract In this chapter, an overview of different aspects of current analytical methodologies such as sample preparation, extraction, purification, and instrumental analysis for pyrethroids is discussed. Recent development in sample preparation and extraction is presented. Regarding instrumental analysis, gas chromatography (GC) coupled to electron capture detection or mass spectrometry (MS) including tandem MS is generally preferred for analysis of pyrethroids. Although liquid chromatography has been used as a possible solution to reduce isomerization of pyrethroids that can occur at higher temperature, the advantages and disadvantages of different instrumental techniques are discussed here.

M. L. Feo (*) Istituto per lo studio degli impatti Antropici e Sostenibilità in Ambiente Marino-Consiglio Nazionale della Ricerca, Torretta Granitola, Sicily, Italy e-mail: [email protected] Ethel Eljarrat (ed.), Pyrethroid Insecticides, Hdb Env Chem (2020) 92: 17–46, DOI 10.1007/698_2019_428, © Springer Nature Switzerland AG 2020, Published online: 18 June 2020

17

18

M. L. Feo

Keywords Enantiomeric separation, Environmental analysis, Food analysis, Gas chromatography, Mass spectrometry, Pyrethroids

1 Introduction Pyrethroid insecticides were developed to replace organophosphorus pesticides, which were largely used in the past three decades and were demonstrated to have potentially toxic effects on humans [1]. Pyrethroids are the synthetic analogues of pyrethrins which were developed as pesticides from the extracts of dried and powdered flower heads of Chrysanthemum cinerariaefolium. Because of the rapidly decomposition of pyrethrins in the presence of light, pyrethroids were developed to increase stability to light and residence time in the environment, maintaining the effective insecticidal activity of the pyrethrins [2]. Pyrethroids are persistent compounds with high hydrophobicity (log Kow 5.7–7.6) [3, 4] and very low water solubility (a few lg/L), so they preferentially adsorbed to solid particles [5]. They can persist in the environment for few months before being degraded [6, 7] and can be bioaccumulated in aquatic organisms [8, 9] and humans [10, 11]. Aquatic organisms such as invertebrates and fish are extremely sensitive to the neurotoxic effect of these insecticides. In fish (e.g., bluegill and lake trout), LC50 values were estimated to be less than 1 g/L [12]. Regarding their effects on humans, reversible symptoms of poisoning and suppressive effects on the immune system have been reported [13]. Moreover, pyrethroids have been included in a list of suspected endocrinedisrupting chemicals [14]. The development of analytical methods for the analysis of pyrethroid insecticides is very important, considering their large usage for domestic and agricultural pest control applications and their presence in the environment and in food and their capacity to be bioaccumulated by organisms. Table 1 shows a list of pyrethroids usually determined in environmental, biological, and food samples. In addition to conventional extraction methods (e.g., liquid-liquid extraction or solidphase extraction for liquid samples and sonication or pressurized liquid extraction for solid samples), new methods simple and rapid with reduced reagent use have been recently developed for the extraction of pyrethroids from environmental, biological, and food samples. Examples of these are the liquid-liquid microextraction based on solidification of floating organic droplet used for liquid samples or QuEChERS (stands for quick, easy, cheap, effective, rugged, and safe) method applied to solid samples. Following extraction and purification, the detection and quantification of pyrethroids can be performed by gas chromatography (GC) combined with electron capture detection (ECD) or mass spectrometry (MS), as well as by liquid chromatography (LC). This chapter describes the various aspects of sample preparation, extraction, purification, and instrumental analysis of synthetic pyrethroids in different environmental and food matrices mainly focusing on the development made in the last 15 years.

541.4

C26H21F6NO5

C19H26O3

C23H22ClF3O2

C22H18Cl2FNO3

Allethrin (ALLE) (bioallethrin)

Bifenthrin (BIFE)

Cyfluthrin (CYFL) (β-isomer)

453.3

422.9

302.4

MW

Formula

Pyrethroid (acronym) Pyrethroid esters Acrinathrin (ACRI)

Table 1 List of pyrethroids usually determined in environmental, biological and food samples Molecular structure

(continued)

Analytical Methods for Determining Pyrethroid Insecticides in Environmental and. . . 19

Formula C23H19ClF3NO3

C22H19Cl2NO3

C24H25NO3

C22H19Br2NO3

Pyrethroid (acronym) Cyhalothrin (CYHA) (γ- and λ-isomers)

Cypermethrin (CYPE) (α-, β-, θ- and ζ-isomers)

Cyphenothrin (CYPH)

Deltamethrin (DELT)

Table 1 (continued)

505.2

375.5

416.3

MW 449.9

Molecular structure

20 M. L. Feo

C22H23NO3

C25H22C1NO3

C26H23F2NO4

C26H22ClF3N2O3

C18H22N2O3

C21H20Cl2O3

Fenpropathrin (FENP)

Fenvalerate (FENV) (esfenvalerate)(ESFE)

Flucythrinate (FLUC)

Fluvalinate (FLUV) (τ-isomer)

Imiprothrin (IMIP)

Permethrin (PERM) (biopermethrin and transpermethrin)

391.3

318.4

502.9

451.4

419.9

349.4

(continued)

Analytical Methods for Determining Pyrethroid Insecticides in Environmental and. . . 21

Formula C23H26O3

C19H24O3

C22H26O3

C17H14ClF7O2

C19H25NO4

Pyrethroid (acronym) Phenothrin (PHEN)

Prallethrin (PRAL)

Resmethrin (RESM) (bioresmethrin and cismethrin)

Tefluthrin (TEFL)

Tetramethrin (TETR)

Table 1 (continued)

331.4

418.7

338.4

300.4

MW 350.5

Molecular structure

22 M. L. Feo

C22H19Br4NO3

C15H12Cl2F4O2

C24H23BrF2O3

Tralomethrin (TRAL) (δ-isomer)

Transfluthrin (TRAN)

Pyrethroid ethers Halfenprox (HALF) 477.3

371.2

665.0

Analytical Methods for Determining Pyrethroid Insecticides in Environmental and. . . 23

24

M. L. Feo

2 Sample Preparation Table 2 synthesizes the recent analytical techniques in terms of extraction, purification, and instrumental analysis showing recoveries and method limit of detection (MLOD) for determination of pyrethroids in environmental and food matrices.

2.1

Extraction from Water Sample

Pyrethroid concentrations in water are generally low, as they are preferentially sorbed to soil or sediment, due to their hydrophobic character. Thus, analytical methods for determination of pyrethroids in water should include extraction and pre-concentration to reach the required limits of detection. Liquid-liquid extraction (LLE) is the most common extraction technique for water samples. Its main drawbacks are the high solvent consumption and the long analysis time. For this reason, alternative extraction methods in which solvent consumption and time of analysis are reduced were introduced. Among these are solid-phase extraction (SPE), solidphase microextraction (SPME), and stir bar sorptive extraction (SBSE). Moreover, recently, liquid-liquid microextraction (LLME) and LLME based on solidification of floating organic droplet (LLME-SFO) have been developed. LLE of pyrethroids from water uses nonpolar solvents such as dichloromethane [15] and hexane [16]. After extraction, the sample is dried and redissolved in a small volume of organic solvent ready to be injected into GC for analysis. Pyrethroid recoveries by LLE were in the range 75–115% for unfiltered river samples with method limit of detection (MLOD) of 1–3 ng/L [15] and 94–105% for aqueous solution [16]. Dispersive liquid-liquid microextraction (DLLME) assisted by ultrasound was developed by Yan et al. as a method for the pre-concentration and determination of six pyrethroids in river water samples [17]. Tetrachloromethane was used as waterimmiscible extractant, and acetone was used as water-miscible dispersive solvent. Ultrasonic treatment was performed to make the analytes fully extracted into the fine droplets. The phase separation was performed by a rapid centrifugation. Recoveries were ranging between 86 and 109%. MLODs were 0.1–0.30 μg/L [17]. A novel LLME based on solidification of floating organic droplet (LLME-SFO) has been recently developed by Khalili-Zanjani et al. which was based on the extraction of the analytes by microliter volume of the extraction solvent (floated on the surface of the aqueous sample) from the aqueous sample matrix [53]. In this method, small volume of an organic solvent with a melting point near room temperature (in the range of 10–30 C, such as undecanol and 1-dedecanol) is floated on the surface of aqueous solution. Transferring the sample in an ice bath, the organic solvent microdrop is solidified and ready to be transferred into a conical vial where it melts immediately at room temperature and thus is ready to be injected into a GC for analysis. The advantages of the method are simplicity of operation, small amount of solvent

SPME

Tap water, groundwater, river water, runoff, and wastewater Water SPME

SPME

Sediment pore water

FENP, CYHA, PERM, CYPE FENV, DELT

SPME

Groundwater

FENP, CYHA, DELT, FENV, PERM, FLUV, BIFE BIFE, FENP, CYHA, PERM, CYFL, CYPE, ESFENV, DELT TRANSFU ALLETR, TETRA, CYHA, CYPHE, PERM, CYFL, CYPE, DELT

SPE

SPE

LLE Ultrasound LLME LLME-SFO

Sample preparation LLE

Groundwater and marine water

Tap water, well water, and river water Water

Aqueous samples River water

Matrix River water

FENP, CYHA, DELT, FENV, PERM, FLUV, BIFE

CYPE, FENV, DELT

Analytes BIFE, CYHA, PERM, CYFL, CYPE, ESFENV CYHA, DELT, CYPE, FENV TETR, ALLE, CYPE, PRAL, TRAN, IMIP FENP, CYHA, PERM, CYFL, CYPE, FENV, PERM

GC-ECD

GC-μECD

GC-ECD

LC-PIF-FD

LC-ESI-MS

GC-μECD

GC-ECD

GC-ECD HPLC-UV-Vis

Instrumental analysis GC-ECD 1

1

1

1

1

0.12–0.43 ng mL

0.05–2.18 ng L

1–7 ng L

1

5.0  10 4 to 1.5  10 2 ng L 1 0.3–0.7 ng L 1 for groundwater sample 0.7–1.5 ng L 1 for marine water samples 3–9 ng L 1

2.0–50 ng L

Not reported 0.1–0.3 μg L

MLODs 1–3 ng L

Table 2 Recent analytical techniques used for pyrethroid determinations in environmental and food matrices

83–112

81–125

(continued)

[24]

[23]

[22]

[21]

92–109 56–119

[20]

[19]

[18]

[16] [17]

Ref. [15]

80–115

70–103

79–114

94–105 86–109

Recovery (%) 75–115

Analytical Methods for Determining Pyrethroid Insecticides in Environmental and. . . 25

CYFL, CYPE, DELT, FENVA, PERM, PHEN, TETR, BIFE, λ-CYHA, ESFE, FEN, τ-FLUV, RESM, and TRAL FENV, DELT, CYPE, CYFL, PHEN, BIFE Solid samples BIFE, CYHA, PERM, CYFL, CYPE, ESFENV CYPE, DELT, FENV

Analytes BIFE, FENP, CYHA, PERM, CYFL, CYPE, FLUV, FENV, DELT RESM, BIFE, FENP, CYHA, PERM, CYPE, FENV, DELT CYFL, DELT, CYPE, FLUCY, ACRINA, FENV, FLUV, CYHA, TEFLU, PERM, HALFE CYHA, CYPE, FENV, FLUC, FLUV, PERM, TEFL CYHA, DELT, FENV, FULV, BIFE

Table 2 (continued)

SBSE Dual-SBSE

SBSE TILDLME

Water

River water and brewed green tea

Water

Tap water, groundwater, river reservoir water River water

MI-SPE

PFE, GPC Sonication, Florisil

Aquaculture seawater

Sediments

Sediment

UAEE

Sample preparation MA-HSSPME

Matrix Water and groundwater

GC-μECD

GC-ECD

GC-ECD

GC-NCI-MS

LC-UV

TD-GC-MS

TD-LTM-GC-MS

GC-MS

Instrumental analysis GC-ECD

1

1

1

1

1

3.0  10 5– 1.5  10 3 ng g

0.5–4 ng g

16.6–37.0 ng/L

0.03–35.8 ng L

280–600 ng L

>10 ng L

3–100 ng L

0.02–1.4 ng L

MLODs 0.2–2.6 ng/L

1

1

71–103

83.8–108

86–96

63–100

76.7–135.6

82–113

17–33

40–80

Recovery (%) 88–115

[19]

[15]

[30]

[29]

[28]

[27]

[26]

[4]

Ref. [25]

26 M. L. Feo

CYFL, CYPE, DELT, FENV, PERM, TETR, BIFE, CYHA, ESFE, FENP, FLUV, RESM ALLE, PRAL, RESM, TETR, BIFE, FENP, PHEN, PERM, CYHA, CYFL, CYPE, FLUC, FENV, DELT TETR, CYFLU, FLUC, DELT, BIFE, PERM, CYPE, FLUV CYFL, CYPE, FENV ALLE, CYFL, CYHA, CYPE, CYPH, DELT, FENV, FLUC, PERM, TEFL, TETR, TRAN BIFE, FENP, CYHA, CYFLU, CYPE, FENV BIFE, FENP, CYHA, ACRI, PERM, CYFL, CYPE, FLUCI, FENV, DELT TRAN, ALLE, TETR, CYHA, CYPH, PERM, CYFL, CYPE, DELT ALLE, CYFL, CYHA, CYPE, DELT, FENP, IMIP, PERM, PHEN, PRAL, RESM, TETR CYPH, ALLE, TRAN, CYFL, TETR, PERM, PHEN, CYHA, CYPE BIFE, CYHA, PERM, CYFL, CYPE, ESFENV Soxhlet, Florisil

MAE Florisil

SFE, C18 HS-SPME

PSA, C18 Chromosorb 106 and Tenax TA MASE, Florisil

Sediment

Soil

Soil Soil

Soil

Urban air

Sonification, SPE HS-SPME

PFE, GPC

House dust

Indoor air

Biological tissue

Indoor dust

Sonication Florisil

Marine sediment

GC-ECD

GC-ECD

GC-MS

GC-μECD

GC-MS-MS

GC-MS-MS

1

1

1

1–3 ng g

1

0.083–4.6 ng/m3

1–60 ng g

1–7 ng g

0.5–27 ng g (LOQ)

0.3–5 μg/kg

74.3–98.7

77–111

51–101

84–101

[15]

[39]

[38]

[37]

[36]

[35]

[33] [34]

[32]

[31]

[6]

(continued)

67–117 for Chromosorb 106 and 65–115 for Tenax TA

88–96

70–97 81–122

1

500 mL) required. For this reason, miniaturized methods (SPME and SBSE) which are simple, solventless techniques were introduced [54, 55]. Parrilla Vazquez et al. developed a procedure for SPME analysis of pyrethroids in unfiltered groundwater, using polydimethylsiloxane/divinylbenzene (PDMS/ DVB 60 μm) as the most appropriate fiber coating [21]. The sample solution was buffered to pH 3 using a phosphate buffer, and the solution was kept at 65  2 C for 30 min. Recoveries were 92–109% with MLODs of 3–9 ng/L [21]. Bondarenko found analyzing sediment pore water recoveries of 56–119% with similar MLODs (30 μm PDMS fiber; 20 min stirring at 600 rpm) [22]. Casas et al. studied the influences (e.g., temperature, fiber coating, salting out effect, and sampling mode) on the efficiency of pyrethroid extraction from unfiltered water samples [23]. The best conditions were found to be using PDMS fibers, direct sampling (D-SPME), at 50 C with an exposure time of only 20 min and without adding salt. The recoveries were 81–125% with MLODs of 0.05–2.18 ng/L [23]. A novel solid-phase microextraction (SPME) fiber coated with multiwalled carbon nanotubes/polypyrrole (MWCNTs/Ppy) was prepared with an electrochemical method and used for the extraction of pyrethroids in natural water samples. The results showed that the MWCNTs/Ppy-coated fiber was more effective and superior to commercial PDMS and PDMS/DVD fibers in extracting pyrethroids in natural water samples. Recoveries were of 83–112%, and MLODs were within the

Analytical Methods for Determining Pyrethroid Insecticides in Environmental and. . .

31

range 0.12–0.43 ng/mL [24]. A one-step microwave-assisted headspace solid-phase microextraction (MA-HS-SPME) has been applied to be a pretreatment step in the analysis of aqueous pyrethroid residuals by GC analysis [25]. Microwave heating was applied to accelerate the vaporization of pyrethroids into the headspace and then being absorbed directly on a SPME fiber under the controlled conditions. Extraction of pyrethroids from aqueous (at pH 4) was achieved with the use of a 100 m PDMS fiber, microwave irradiation of 157 W, and sampling at 30 C for 10 min. Recoveries were between 88.5 and 115.5%, and MLODs were 0.2–2.6 ng/L [25]. The method was applied to groundwater samples [25]. Van Hoeck et al. developed an SBSE method for the enrichment of pyrethroids from unfiltered water samples [4]. The method consists of adding the stir bar in the water sample (10 mL) together with methanol to minimize wall adsorption. The SBSE method is followed to thermal desorption (TD) in classical GC split/splitless inlet equipped with a flip top inlet sealing system. The extraction was performed at room temperature, with stirring at 900 rpm. Recoveries were of 40–80% and MLODs of 0.02–1.4 ng/L [4]. Sequential SBSE followed by thermal desorption (TD)-low thermal mass (LTM) gas chromatography mass spectrometer (GC-MS) was developed by Ochai et al. [26, 27]. The usage of dual SBE was to provide more uniform enrichment over the entire polarity/ volatility range for organic pollutants at ultra-trace levels in water. In a first experiment, two stir bars were added to the unfiltered water, the extraction was performed at room temperature, and then, pyrethroids were desorbed from the two stir bars directly in the glass desorption liner. Recoveries were low (17–33%) and MLODs were 3–100 ng/L [26]. In a second experiment, the authors first added one stir bar to the sample without modifier and then a second stir bar to the same sample after adding 30% NaCl. The first extraction with unmodified sample was mainly to target for solutes with high Kow (log Kow > 4.0); and the second extraction with modified sample solution (containing 30% NaCl) was targeted at solutes with low and medium Kow (log Kow < 4.0). After the extraction, the two bars were placed in a single glass desorption liner and were simultaneously desorbed. Recoveries were 82–113% with low MLODs (>10 ng/L) [27]. Molecularly imprinted solid-phase extraction (MI-SPE) based on selective molecularly imprinted polymers (MIPs) has been used for the isolation and cleanup of pyrethroid insecticides in aquaculture seawater [30]. Recoveries were 86–96% and MLODs were 16.6–37.0 ng/L [30].

2.2

Extraction from Soil and Sediment Samples

The interaction between pyrethroids and soil/sediment matrix is much stronger than it is in water due to the hydrophobic character of pyrethroids [5] and to the consequently formation of bound residues in soil/sediment [56]. Thus, more exhaustive extraction procedures are required to liberate pyrethroids from the solid matrix. Conventional methods as Soxhlet extraction have been used for pyrethroid extraction from sediments although the method is time-consuming and requires a large amount of solvents. Dichloromethane was used as solvent and by Florisil for the

32

M. L. Feo

cleanup. Recoveries were of 90–135% and MLODs of 0.2–1.5 ng/g [31]. Sonication has been also used for the extraction of pyrethroids from sediment samples. Xue et al. used methanol/acetonitrile (50/50 volume/volume) as extraction solvent and performed the cleanup of the extracts on a Florisil column using dichloromethane/ hexane (20/80 v/v) as eluent [19]. They found recoveries of 71–103% and MLODs of 3.0  10 5–1.5  10 3 ng/g [19]. However, Feo et al. used hexane/ dichloromethane (2:1) as extraction solvent in a sonicator for 15 min at room temperature and performed the cleanup with Florisil cartridge (2 g/15 mL). Ethyl acetate was used as eluent. Recoveries were of 51–105% and MLODs were of 2.6–62.4 pg/g [6]. In the last years, new extraction techniques have been developed for solid samples (such as supercritical fluid extraction, solid-phase microextraction, microwave-assisted extraction, pressurized fluid extraction) with the intent to reduce the volume of the organic solvent used for the extraction and the time of the analysis. Pressurized fluid extraction (PFE), which consists of using organic solvents, pumped into an extraction cell containing the sample and brought to an elevated temperature and pressure [57], has been used for extraction of pyrethroids from sediments [15]. PFE was followed by cleanup with gel permeation (GP) (size exclusion), and dichloromethane was used as eluent. Recoveries were 84–108% with 0.5–4 ng/g MLODs [15]. Supercritical fluid extraction consists of using supercritical fluids (normally water or carbon dioxide), as extraction agents. Supercritical fluids exhibit a liquid-like density, while their viscosity and diffusivity remain between gas-like and liquid-like values. Thus, supercritical fluids have lower viscosity and higher diffusivity compared to organic solvents. The applicability of supercritical fluid extraction (SFE) for multi-residue analysis was studied for soil samples. The best efficiency was achieved at 400 bar using methanol as modifier at 60 C. Cleanup was carried out using C18 cartridge and dichloromethane/hexane (50:50 v/v) as eluent. Recoveries were 70–97% with MLODs overnight at RT

Derivatization

PFBBr – strong lachrymator

Notice

[5]

Ref.

60 B. Wielgomas et al.

CDCA (0.0088; 0.029); DF, 52.6– 69.4% cis-DCCA (0.0072; 0.024); DF, 95.6– 95.9% trans-DCCA (0.0096; 0.032); DF, 94.7– 100% DBCA (0.0060; 0.020); DF, 5.3– 12.2% 3PBA (0.013; 0.043); DF, 91.8–94.7% 4F3PBA (0.0053; 0.018); DF, 32.5– 55.1% cis-DCCA (0.007; nd); DF, 99% trans-DCCA (0.01; nd); DF, 99% DBCA (0.006; nd); DF, 77% 3PBA (0.01; nd); DF, 100% 4F3PBA (0.008; nd); DF, 71%

V: 5 mL H: enzymatic E: LLE C: No I: GC-MS (quadrupole, negative mode, SIM)

V: 5 mL H: enzymatic E: LLE I: GC-MS (quadrupole, SIM, negative mode)

LLE: • Extraction: 9 mL n-hexane • Evaporation to dryness

• Washing: 5 mL hexane and 2 mL hexane-toluene (70:30) • Elution: 8 mL hexane-toluene (60:40) • Evaporation – gentle stream of nitrogen • Reconstitution: 0.5 mL hexane LLE: • Extraction: 2  5 mL DCM • Evaporation

• External quality control: (G-EQUAS) • Population: pregnant women residing in ten Englishspeaking Caribbean countries (n ¼ 295)

• 30 μL HFIP, 20 μL DIIC, 2 mL of iso-octane/hexane (2:98) • Evaporation • Reconstitution: hexane

[22]

[25]

(continued)

• External Quality Control: G-EQUAS • Population: rural population of the Montérégie area, Quebec (adults n ¼ 114, children, n ¼ 49), Canada

• 250 μL ACN, 30 μL HFIP, 20 μL DIIC, 10 min, RT • Wash and extraction: 1 mL 1 M NaHCO3 + 250 μL hexane

Analytical Methods for Determination Urinary Metabolites of Synthetic. . . 61

cis-DCCA (nd; 0.01); DF, 100% trans-DCCA (nd; 0.01); DF, 100% cis-DBCA (nd; 0.01); DF, 80% 4F3PBA (nd; 0.01); DF, 5%

Analytes (LOD ng/mL; LOQ ng/mL); DF DBCA (0.833; 2.5); DF, nd 3PBA (0.008; 0.025); DF, 30–35% 4F3PBA (0.017; 0.05); DF, 20–25% cis-DCCA (0.1; nd); DF, 95.3% trans-DCCA (0.1; nd); DF, 98.3% 3PBA (0.1; nd); DF, 98.8%

Table 2 (continued)

V: 5 mL H: acidic (1 mL HCl; 1 h, 90 C) E: LLE C: LLE I: GC-MS/MS (quadrupole, EI)

V: 5 mL H: acidic (1 mL HCl; 1 h, 90 C) E: LLE C: LLE I: GC-MS (quadrupole, SIM)

Sample volume (V), hydrolysis (H), extraction (E), cleanup (C), instrument (I) V: 10 mL H: acidic E: LLE I: GC-MS/MS (triple quadrupole)

Ref. [26]

[23]

[9]

Notice • Population: 20 adults and 20 children without occupational exposure (China) • Modification of Kühn et al. [3] • Population: pregnant women in an agricultural area of the Province of Jiangsu (n ¼ 1,149), China

• External quality control: G-EQUAS • Population: general with no known exposure to synthetic pyrethroids (n ¼ 38), Germany

Derivatization • 0.5 mL toluene + 20 μL MTBSTFA (75 C, 45 min)

• 3 mL 10% H2SO4 in MeOH (75 C, 1 h)

MTBSTFA (10 μL) • 80 C, 1 h

Extraction and cleanup details LLE • Extraction: 20 mL isopropanol-hexane (5:95) • Evaporation to dryness

LLE: • Extraction: 2  4 mL hexane • Evaporation (gentle stream of nitrogen) • Derivatization: 3 mL 10% H2SO4 in MeOH (75 C, 1 h) Cleanup LLE: • Re-extraction: 3 mL hexane +3 mL saturated NaCl solution • Evaporation (gentle stream of nitrogen) • Reconstitution: 100 μL of toluene LLE: • Extraction: 2  5 mL hexane • Cleanup: 2 mL 0.1 N NaOH • Re-extraction: +0.1 mL conc. HCl + 1.8 mL hexane • Evaporation under nitrogen to 50 μL

62 B. Wielgomas et al.

3PBA (nd; 0.01); DF, 100% ClF3CA (nd; 0.01); DF, 90% CPBA (nd; 0.01); DF, 40% MPA (nd; 0,01); DF, 5% cis-DCCA (0.05 μg L1); DF, 52% trans-DCCA (0.05 μg L1); DF, 72% DBCA (0.05 μg L1); DF, 13% 3PBA (0.05 μg L1); DF, 70% 4F3PBA (0.05 μg L1); DF, 4% cis-DCCA (0.006; 0.020); DF, nd trans-DCCA (0.005; 0.017); DF, nd DBCA (0.019; 0.062); DF, nd 3PBA (0.003; 0.010); DF, nd CPBA (0.002; 0.007); DF, nd [7]

• High usage of organic solvents: about 35 mL • Population: six occupationally exposed, two non-exposed occupationally, Spain • 10 μL HFIP, 15 μL DIIC – 3 min, RT • Wash: 1 mL 5% K2CO3

SPE: • Conditioning: 7.5 mL MeOH, 5 mL water • Sample • 6 mL water • Drying • Elution: 10 mL acetone • Evaporation Cleanup: • Residue dissolution in 2 mL

V: 3 mL H: acidic (0.5 mL H2SO4; 1 h, 90 C) E: SPE (C18 Sep-Pak, 500 mg, waters) C: LLE I: GC-MS/MS (ion trap)

(continued)

[11]

• External quality control: yes • Population: group without known exposure to pyrethroids (n ¼ 26 females, 20 males) Germany

10 μL MTBSTFA • 70 C, 45 min

LLE • Extraction: 2  5 mL hexane • Organic phase + 2 mL 0.1 N NaOH • Aqueous phase + 0.1 mL conc. HCl + 2 mL hexane • Drying organic phase (vacuum centrifuge) • Dissolution: 50 μL toluene

V: 10 mL H: acidic (1 mL HCl; 1 h, 90 C) E: LLE C: LLE I: GC-MS (quadrupole, EI, SIM)

Analytical Methods for Determination Urinary Metabolites of Synthetic. . . 63

cis-DCCA (0.5; nd); DF, 100% trans-DCCA (0.5; nd); DF, 100% DBCA (0.3; nd); DF, nd 3PBA (0.5; nd); DF, 100% 4F3PBA (0.5; nd); DF, nd ClF3CA (LLOQ 0.06); DF, nd cis-DCCA (LLOQ 0.08); DF, nd trans-DCCA (LLOQ 0.08); DF, nd DBCA (LLOQ 0.06); DF, nd 3PBA (LLOQ 0.06); DF, nd

Analytes (LOD ng/mL; LOQ ng/mL); DF

Table 2 (continued)

V: 0.4 mL H: Enzymatic E: MEPS (C18, SGE) I: LVI-GC-MS (ion trap, μSIS)

V: 10 mL H: acidic (2 mL H2SO4; 1 h, 90 C) E: SPE (C18, 500 mg, Bakerbond) I: GC-MS (quadrupole, SIM)

Sample volume (V), hydrolysis (H), extraction (E), cleanup (C), instrument (I) Extraction and cleanup details

SPE (MEPS): • Conditioning: 4  50 μL MeOH, 3  20 μL 2% HCOOH • Sample: 5  100 μL • Washing: 3  50 μL 30% MeOH • Drying under vacuum • Elution: 2  40 μL 1%HFIP and 2%DIIC in hexane

of saturated NaCl + 2  5 mL n-hexane • Evaporation to dryness (gentle stream of nitrogen) • Reconstitution: 1 mL hexane SPE: • Conditioning: 3 mL EtAc, 3 mL n-hexane, 6 mL MeOH, 9 mL H2O • Sample • Washing: 6 mL water • Drying Elution: 3 mL MeOH

• 1% HFIP, 2% DIIC in hexane

• 1 mL of 98% H2SO4, 1 h, 75 C

Derivatization

• External quality control: G-EQUAS

• External quality control: yes • Population: occupational exposure (n ¼ 8), Germany

Notice

[17]

[6]

Ref.

64 B. Wielgomas et al.

cis-DCCA (nd; 0.1); DF, 8% trans-DCCA (nd; 0.1); DF, 7% DBCA (nd; 0.1); DF, 11% 3PBA (nd; 0.1); DF, 80% HOCH2-FB-Al (0.01; 0.1); DF, 82% MTFBL (0.05; 0.31); DF, 54% MMTFBL (0.05; 0.31); DF, 56% FB-Al (0.02, 0.31); DF, 84% cis-DCCA (0.03; 0.10); DF, 88% trans-DCCA (0.02; 0.10); DF, 100% 3PBA (0.01; 0.05); DF, 100% trans-CDCA (0.06, 0.31); DF, 68% CH3-FB-Ac (0.01; 0.31); DF, 38% MTFBL (0.01; 0.04); DF, nd MMTFBL (0.02; 0.07); DF, nd TMCA (0.04; 0.12); DF, 0%

V: 25 mL H: enzymatic E: LLE C: No I: GC-MS (EI, SIM)

V: 2.5 mL H: acidic (0.6 mL, 6 mol/L HCl; 2 h, 106 C) E: LLE (24-well plate; Extrahera) C: No I: GC-MS/MS (triple quadrupole, EI)

V: 3 mL H: acidic (0.6 mL HCl; 90 min, 95 C) E: LLE C: LLE I: GC-MS (ion trap, SIS)

LLE • Extraction: 2  2 mL toluene • Dehydration: 1 g Na2SO4 • +1 mL toluene (washing Na2SO4)

LLE • Extraction: 2  4 mL hexane • Re-extraction to 0.5 mL 0.1 M NaOH • Re-extraction (0.1 mL HCl + 2 mL hexane) • Evaporation – under stream of nitrogen LLE • Extraction: 3 mL and 2.5 mL MTBE • Organic phase divided into two parts • Evaporation under vacuum (4 C in ice block) [8]

• Population: 3-year-old children (n ¼ 50), Japan

• Population: six subjects without occupational exposure, Japan

Part I: 100 μL acetone + 50 μL BSTFA: TMCS (99:1) 30 min, room temperature • Wash with 1 mL NaHCO3 (1 mol/L) + 100 μL iso-octane Part II: 100 μL of ACN + 15 μL HFIP + 10 μL DIC 30 min, room temperature • Wash with 0.5 mL NaHCO3 (1 mol/L) + 100 μL iso-octane

• Alcoholic group (MTFBL, MMTFBL): 50 μL TMSI (30 min, 70 C) • Carboxylic acid: 30 μL MTBSTFA (30 min, 70 C)

(continued)

[20]

[24]

• External quality control: ClinCal Urine Calibrator

• 10 μL HFIP, 15 μL DIC, 250 μL hexane – 10 min, RT • Wash: 1 mL 5% K2CO3

Analytical Methods for Determination Urinary Metabolites of Synthetic. . . 65

TFBA (0.06; 0.20); DF, nd ClF3CA (0.03; 0.09); DF, nd MPCA (0.04; 0.14); DF, nd DCCA (0.08; 0.26); DF, nd CXCA (0.12; 0.41); DF, nd FPBA (0.07; 0.24); DF, 0% 3PBA (0.09; 0.30); DF, nd MPA (0.10; 0.33); DF, nd cis-DCCA (12, nd); DF, nd trans-DCCA (9, nd); DF, nd DBCA (7, nd); DF, nd 3PBA (1.8, nd); DF, nd 4F3PBA (17, nd); DF, nd

Analytes (LOD ng/mL; LOQ ng/mL); DF

Table 2 (continued)

V: 1 mL H: acidic (0.1 mL HCl; 10 min, 70 C) E: HF-LPME C: No I: GC-ECD

Sample volume (V), hydrolysis (H), extraction (E), cleanup (C), instrument (I)

HF-LPME: • Extraction to Accurel Q3/2 polypropylene hollow-fiber membrane (600-μm ID, 800-μm OD, pore size 0.2 μm) impregnated with 8 μL 1-octanol)

• Concentration to 1 mL – under stream of nitrogen

Extraction and cleanup details

• 1 μL HFIP, 2 μL DIC – derivatization in the syringe barrel

Derivatization

• In-syringe derivatization

Notice

[28]

Ref.

66 B. Wielgomas et al.

DCCA (mixture of isomers) (0.02; nd); DF, 100% DBCA (0.04; nd); DF, 50% 3PBA (0.06; nd); DF, 100% 4F3PBA (0.02; nd); DF, 100% MPA (0.04; nd); DF, 0% CPBA (0.04; nd); DF,70% ClF3CA (0.08, nd); DF, 80%

V: 2.5 mL H: enzymatic E: automatic SPE (C18 Agilent SampliQ, 200 mg) C: No I: GC-MS (quadrupole, EI, SIM) SPE: • Conditioning: 6 mL MeOH, 3 mL ACN, 3 mL 2% HCOOH • Sample • Washing: 1.5 mL 20% MeOH 2% HCOOH in water • Drying • Elution: 3.5 mL ACN • Concentration to 200 μL (TurboVap Evaporator) • Derivatization • LLE: 200 μL isooctane

• 20 μL DIC, 30 μL HFIP (vortexing 10 min) • Wash: 1 mL 1 M NaHCO3

• SPE (C18) – RapidTrace auto-SPE WorkStation; • Population: ten children living in Boston, MA (USA) [33]

Analytical Methods for Determination Urinary Metabolites of Synthetic. . . 67

cis-DCCA (0.4; nd); DF, 14.5% trans-DCCA (0.4; nd); DF, 16.4% DBCA (0.4; nd); DF, nd 3PBA (0.03; nd); DF, 52.7% 4F3PBA (0.03; nd); DF, 5.5%

Analytes (LOD ng/mL; LOQ ng/mL); DF cis-DCCA (0.5; nd); DF, 36% trans-DCCA (0.5; nd); DF, 50% DBCA (0.2; nd); DF, 3.2% 3PBA (0.1; nd); DF, 64% 4F3PBA (0.3; nd); DF, 8.6% 3PBA (15; 50); DF, nd 4OH3PBA (15; 50); DF, nd

V: 1 mL H: enzymatic E: automated SPE (OASIS HLB 96-well 30 mg, Waters) I: HPLC-MS/MS (quadrupole, negative mode)

V: 1 mL H: acidic (0.2 mL HCl; 90 min, 95 C) E: HF-LPME I: HPLC-DAD

Sample volume (V), hydrolysis (H), extraction (E), cleanup (C), instrument (I) V: 5 mL H: enzymatic E: SPE (waters Oasis HLB 6 cc) I: HPLC-MS/MS (triple quadrupole, negative mode) Extraction and cleanup details SPE: • Conditioning: 4 mL MeOH, 4 mL water • Sample • Washing: 2 mL 5% MeOH • Elution: 2 mL MeOH • Evaporation (TurboVap) • Reconstitution: 50 μL ACN • Evaporation • Reconstitution: 7 μL ACN HF-LPME • +100 mg NaCl • Extraction (solvent dihexyl ether) 120 min • Desorption: 0.1 mL 0.1 M NaOH 120 min SPE: • Conditioning: 0.5 mL acetone, 0.5 mL 1% acetic acid • Sample • Washing: 25% MeOH in 1% acetic acid • Drying (TurboVap under stream of nitrogen) • Elution: 2  325 μL acetone • Evaporation • Reconstitution: 10 μL internal standard (3-chloro-2-phenoxybenzoic acid) and 110 μL 25% MeOH in water • 96-well plate SPE • External quality control: G-EQUAS • Population: diverse group of male and female adult volunteers with no documented occupational exposure to the target pesticides or their precursors (n ¼ 55), USA

• Hollow-fiber microextraction

Notice • Population: half the cohort was suspected to have residential exposure (n ¼ 217), USA

Table 3 Liquid chromatography methods for determination of synthetic pyrethroid metabolites in human urine

[16]

[12]

Ref. [29]

68 B. Wielgomas et al.

cis-DBCA (0.1; nd); DF, nd cis-DCCA (0.2; nd); DF, nd trans-DCCA (0.4; nd); DF, nd 4F3PBA (0.2; nd);

cis-DCCA (0.015; 0.020); DF, 97% trans-DCCA (0.015; 0.030); DF, 100% DBCA (0.015; 0.025); DF, 97% 3PBA (0.015; 0.025); DF, 100% 4F3PBA (0.015; 0.025); DF, 10% 4F3PBA (0.019; nd); DF, 54% 3PBA (0.018; nd); DF, 82% SPE: • Conditioning: 1 mL MeOH/acetone (25:75); 1 mL 1% CH3COOH in water • Sample • Washing: 0.5 mL 1% CH3COOH in water • Cartridge drying (20 min under vacuum) • Elution: 1.5 mL MeOH/acetone (25:75) • Evaporation – gentle stream of nitrogen • Reconstitution in 120 μL MeOH: H2O (25:75) SPE: • Conditioning: 1 mL MeOH, 1 mL 1% CH3COOH in water • Sample • Washing: 5% MeOH in 1% acetic acid solution • Cartridge drying (30 s – vacuum)

V: 1 mL H: enzymatic E: SPE (Oasis HLB 3 cc, waters) C: No I: UPLC-MS/MS (triple quadrupole, ESI-)

V: 2 mL H: enzymatic E: SPE (Oasis HLB 3 cc, waters) C: No I: HPLC-TIS-MS/MS (triple quadrupole, negative mode)

LLE: • Extraction: 2  6 mL hexane • Re-extraction to 3 mL 0.1 M NaOH • Re-extraction to 0.2 mL conc. HCl + 6 mL hexane • Evaporation – gentle stream of nitrogen • Reconstitution in 80 μL 0.1% formic acid in water/methanol mixture (70/30, v/v)

V: 5 mL H: Enzymatic E: LLE C: LLE I: LC-MS/MS (triple quadrupole; negative mode)

(continued)

[30]

[21]

• External quality control: G-EQUAS • Population: human urine samples from two adult Spanish populations in Catalonia and Galicia (n ¼ 125), Spain

• Population: 115 samples

[14]

• Extraction similar to Schettgen et al. [11] • Population: 39 adults – 23 women and 16 men – aged between 24 and 62 years old Limousin Region, France

Analytical Methods for Determination Urinary Metabolites of Synthetic. . . 69

V: 10 mL H: acidic (HCl, conditions not specified) E: LLE C: LLE I: HPLC-UV

V: 1 mL H: acidic (6 M HCl; 2 h, 100 C) E: SPE (OASIS HLB 150 mg/ 6 cc, waters) C: No I: HPLC-MS/MS

LLE: • 10 mL of urine, 0.1 mL HCl, 2 mL chloroform • Organic phase, 0.1 mL 4 M NaOH, 1 mL water • 0.5 mL aqueous phase, 0.5 mL HPLC mobile phase (ACN:1% H2SO4; 1:1) SPE: • Conditioning: MeOH, water • Sample • Washing: 5% MeOH • Drying • Elution: MeOH • Evaporation • Reconstitution in 100 μL ACN

V: 5 mL H: enzymatic E: SPE (Sep-Pak C18 cartridges; waters) C: No I: UHPLC- MS Q-TOF (ESI-)

cis-DCCA (14 fmol injected; nd); DF, nd trans-DCCA (18 fmol injected; nd); DF, nd 3PBA (31 fmol injected; nd); DF, nd LODs range: 0.1– 0.3 ng/mL MPA (2.5 ng/mL); DF, nd 3PBA (2.5 ng/ mL); DF, nd

3PBA (0.02; nd); DF, 97.8%

• Elution: 1.5 mL MeOH + 2 mL ACN • Evaporation to dryness • Reconstitution in 50 μL ACN (reconstitution) SPE: • Conditioning: 4 mL MeOH, 8 mL water • Sample • Washing: 8 mL water • Elution: 8 mL MeOH • Evaporation – gentle stream of nitrogen • Reconstitution in 1 mL MeOH

TIS – turbo ion spray atmospheric pressure ionization

DF, nd 3PBA (0.1; nd); DF, nd

Extraction and cleanup details

Sample volume (V), hydrolysis (H), extraction (E), cleanup (C), instrument (I)

Analytes (LOD ng/mL; LOQ ng/mL); DF

Table 3 (continued)

[32, 35, 36]

[27]

[31]

• Large sample volume • Not applicable for the measurement of environmental exposure levels

• Based on Baker et al. [29] • Population: pregnant women in the first trimester of gestation (n ¼ 231), Japan

Ref.

None

Notice

70 B. Wielgomas et al.

cis-DCCA (nd; 10); DF, nd trans-DCCA (nd; 10); DF, nd 3PBA (nd; 5); DF, nd 4F3PBA (nd; 5); DF, nd cis-DCCA (nd; 3.2); DF, nd trans-DCCA (nd; 3.2); DF, nd DBCA (nd, 10); DF, nd 3PBA (nd; 10); DF, 10% 4F3PBA (nd; 2); DF, nd cis-DCCA (nd; 0.4); DF, 10% trans-DCCA (nd; 0.4); DF, 26% DBCA (nd, 0.8); DF, 23% 3PBA (nd; 0.8); DF, 23% 4F3PBA (nd; 0.2); DF, 0% Online SPE: • Raw urine filtration through a 0.2 μm nylon filter • 0.5 mL of sample was injected onto the online extraction procedure

QuEChERS: • 10 mL of acetonitrile • Pouch of QuEChERS EN extraction salt packet • Evaporation to dryness under a stream of nitrogen • Dissolution • Analysis

Generic method to Olsson et al. [30]

V: 0.5 mL H: none reported E: online TurboFlow™ C: no I: UHPLC-Orbitrap-MS

V: 5 mL H: enzymatic E: QuEChERS EN C: no I: UHPLC-Orbitrap-MS

V: 5 mL H: enzymatic E: SPE, (Strata-X, 500 mg/3 mL, Phenomenex) C: no I: LC–MS/MS

[37]

[19]

[34]

• Population: women and men living near the agricultural areas of Almeria (n ¼ 37), Spain

• Population: children from Valencia Region (n ¼ 20), Spain

• Population: children from Valencia Region (n ¼ 125), Spain

Analytical Methods for Determination Urinary Metabolites of Synthetic. . . 71

3PBA

3PBA

3PBA

3PBAlcGluc

Indirect competitive ELISA

Direct competitive fluorescence enzyme immunoassay

Indirect competitive ELISA

cis-/ transDCCAglycine 3PBA

Analytes

Indirect competitive ELISA

Luminescent paramagnetic particlebased immunoassay

Format Immunoassays Indirect competitive ELISA

0.05

0.05

10

0.5

0.5

0.5

Sample volume (mL)

Dilution

Dilution with buffer (20fold)

Mixed-mode SPE (C8 + SAX), elution with 1% acetic acid in 70:30 Hex/EtAc Mixed-mode SPE (C8 + SAX), elution with 1% acetic acid in 70:30 Hex/EtAc LLE (DCM)

SPE (C18), elution with EtAc

Sample preparation

Primary: pAb (rabbit) Secondary: GAR-HRP

Primary: pAb (rabbit) Secondary: GAR-HRP Anti-analyte: Nb-AP fusion protein

Primary: pAb (rabbit) Secondary: GAR-HRP Primary: pAb (rabbit) Secondary: GAR-HRP (on a paramagnetic particle) Primary: pAb (rabbit) Secondary: GAR-HRP

Antibodies

3PBAlcGluc-BSA

3PBA-BSA

3PBA-BSA

3PBA-BSA

Acridinium ester-labeled 3PBA-BSA

cis-hapten 5b-BSA

Competitive hapten

3-phenoxybenzaldehyde 22.6%, 3PBAlc