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MASKANA.Vol. 9, Ed. 2, 35-40, 20= 18

https://doi.org/1= 0.18537/mskn.09.02.05

Š Author(s) 2018. This work is distributed under the Creative Commons Attribution 4.0 License.<= /span>

 

Art= ículo de Investigación

 

Niveles de c= admio en atún fresco y enlatado para consumo humano en Ecuador<= /b>

Evelyn Flores, Wilson Pozo , Beatriz Pernía , Williams Sánchez

= Facultad de Ciencias Naturales, Universidad de Guayaquil, Av. Raúl Gómez Lince s/n y Av. Juan Tanca Marengo, Guayaquil, Ecuador, C.P. 090= 150.

Autor para correspondencia: wilson.pozog@ug.edu.ec

Fecha de recepción: 2 de noviembre de 2018 - Fecha de aceptación: 6 de diciembre de 2018

 

RESUMEN

Actualmente, la bioacumulación de cadmio (Cd) en peces está aumentando y es un motivo de preocupación debido a su toxicidad. Por esto, el objetivo de esta investiga= ción fue determinar la concentración de cadmio en 36 muestras de atún fresco y enlatado, provenientes de los mercados Caraguay, Puerto Pesquero Santa Rosa (PPSR) y atún enlatado de consumo nacional y de exportación. Para cuantific= ar la concentración de cadmio, las muestras de atún recolectadas fueron analiz= adas mediante el método de espectrofotometría de absorción atómica. Los niveles = de concentración de cadmio de las muestras analizadas fueron comparados con la norma nacional NTE INEN 183 y 184, y con el Reglamento de la Unión Europea = No 488/2014, cuyo límite máximo permitido es de 0.10 ppm Cd. En atún enlatado de consumo nacional se encontraron concentraciones de 0.441ą0.046 ppm Cd y en atún de exportación 0.297ą0.109 ppm Cd; sin embargo, las diferencias no fueron estadísticamente significativas (p>0.05). De igual forma, las concentraciones en atún fresco de la especie Katsuwonus pelamis fue de 0.385ą0.174 ppm Cd, y de Thunnus albacares 0.295ą0.187 ppm = Cd en el mercado de Caraguay. Por el contrario, las concentraciones de Cd en atún proveniente del PPSR fueron mucho menores: 0.079ą0.061 ppm Cd y 0.030ą0.050 para Katsuwonus pelamis y Thunnus albacares, respectivamente= . No hubo diferencias significativas entre el atún enlatado y fresco (p>0.05)= . El 66% de las muestras analizadas superaron los límites permisibles de Cd de las normas nacionales e internacionales, por lo que se recomienda mantener una vigilancia sanitaria permanente del atún en el Ecuador.

Palabras claves: Atún, Cadmio, Katsuwonus, Thunnus, e= spectrofotometría de absorción atómica.

 

ABSTRACT<= /o:p>

Currently, cadmium bioaccumulation in fish is increasing and is a concern due to toxicity. This research is intended to define the Cadmium concentration in 36 samples of fresh tuna and canning, respectively from the Caraguay Market in the city of Guayaquil, the fishing port Santa Rosa (PPSR), and canned tuna for national consumption and export. The cadmium concentration in the tissue of the collected tuna samples was analyzed by atomic absorption spectrophotometry. Levels of cadmium concentration in the analyzed samples were compared to the national regulat= ion norm NTE INEN 183 and 184, and the European Union regulation norm No 488/20= 14. According to those norms the maximum permissible cadmium content in foodstu= ff might not exceed 0.10 ppm Cd. In canned tuna for national consumption we fo= und concentrations of 0.441ą0.046 ppm Cd and in the canned tuna for export the cadmium level varied around 0.297ą0.109 ppm; differences were however not statistically significant (p>0.05). Similarly, the Cd concentrations in fresh tuna of the species Katsuwonus pelamis was 0.385ą0.174 ppm and of the species Thunnus albacares 0.295ą0.187 ppm in the market of Caraguay. In contrast, Cd concentrations in tuna from the PPSR were much lower: 0.079 ą 0.061 ppm Cd and 0.030 ą 0.050 for Katsuwonus pelamis and Thunnus albacares, respectively. 66% of the analyzed samples exceeded the permissible limits of Cd according national and international standards. It is recommen= ded to maintain a permanent health surveillance of tuna in Ecuador.<= /span>

Keywords: Tuna, Cadmiu= m, Katsuwonus, Thunnus, atomic absorption spectrophotometry.

 

1.&n= bsp;          = INTRODUCCIÓN

Una vez terminada la segunda guerra mundial se originó un aumento en el consumo de atún, debido a que este recurso es accesible y rico en proteínas y minerales. La alta dema= nda hizo que la industria del atún se tecnifique, tanto en el arte de la pesca = como en su procesamiento, de tal manera que en la actualidad su captura, para el consumo mundial, es en miles de toneladas al ańo. Sin embargo, los indiscutibles beneficios derivados del consumo de atún pueden ser opacados = por la presencia en su carne de metales tóxicos, como cadmio (Cd), plomo (Pb) y mercurio (Hg), a menudo en niveles superiores a las normas de seguridad establecidas por la legislación de los distintos países (Storelli, <= span lang=3DES-EC style=3D'font-size:9.0pt;font-family:"Times New Roman",serif; mso-bidi-font-weight:bold'>Barone, Cuttone, Giungato, & Garofalo= , 2010).

Dentro de los metales pesados el Cd es un me= tal altamente tóxico y no esencial, obtenido como subproducto del tratamiento metalúrgico del zinc y del plomo que, junto con otras actividades industria= les tales como el uso de fertilizantes, galvanizantes, pigmentos y baterías de níquel-cadmio, constituyen importantes fuentes de contaminación ambiental (Pernía, De Sousa, Reyes, & Castrillo, 2008). Generalmente, se encuentra en el ambiente en bajas concentraciones, pero la actividad humana= ha aumentado considerablemente esos niveles. El cadmio puede desplazarse a gran distancia desde la fuente de emisión por transferencia atmosférica y se acu= mula fácilmente en muchos organismos, especialmente en peces, moluscos y crustác= eos (OMS, 2010). El Cd se halla presente en el medio acuático como consecuencia= de fenómenos naturales, como el vulcanismo marino, o de fenómenos geológicos y geotérmicos, pero también se derivan de la contaminación causada por la metalurgia y explotación minera intensivas, la evacuación de residuos y la incineración, así como la lluvia ácida provocada por la contaminación industrial (FAO, 1989).

La considerable acumulación de Cd podría inc= idir en disfunción renal, dańos en el esqueleto y deficiencia reproductiva (Cope, Leidy, & Hodgson, 2004). Se ha descrito= que el Cd afecta los rińones, pulmones, esqueleto, testículos y sistema nervioso central de los animales y humanos, generando hipocalcemia, diabetes, osteoporosis y cáncer (Burger, 2008; Clemens, Aarts, Thomine, & Verbruggen, 2013)<= !--[if supportFields]>= . Los peces tienen la capacidad de almacenar en su organismo una concentración ma= yor de metales que la presente en el medio, por lo que son indicadores importan= tes de la contaminación, pero también esto implica que su consumo se puede convertir en un problema de salud para las poblaciones que se alimentan de = este recurso (Suhaimi, Wong, Lee, & Low= = , 2005; Moncayo, Trejos, Maridueńa & Castro, 2010).

Las especies de atún son organismos pelágicos de alto rendimiento, con altas ta= sas de metabolismo y consumo de alimentos, lo que los expone a elementos traza (Kojadinovic, Potier, Le Corre, Cosson, & Bustamante, 2007). Por consiguiente, se pueden generar efectos adversos para la salud humana si este pez se consume con demasiada frecuencia o en grandes cantida= des. En este contexto, también se debe considerar el atún enlatado puesto que, e= ntre los productos pesqueros en conserva, son sin duda los más importantes y frecuentemente consumidos (Storelli et al., 2010)<= /span>= . El atún en conserva es, de hecho, muy consumido a nivel mundial y asequible pa= ra la mayoría de las familias trabajadoras. Existen evidencias de contaminación por Hg y Cd en atún del Golfo Pérsico (Ganjavi, Ezzatpanah, Givianrad, & Shams, 2010), Gran= ada, Espańa (Olmedo, Hernández, Barbier, Ayouni, & Gil, 2013) y del Océano Atlántico e Índico (Chen et al., 2018). En Ecuador se ha registrado contaminación por Cd en atún de Manta, e= n la provincia de Manabí (Araujo et al., 2016).

La evaluación del contenido de metales pesados en peces es primordial por sus efectos sobre la salud humana. Según Senior, Cornejo-Rodríguez, Tobar, Ramírez-Muńoz, & Márquez (2016),= la información sobre el contenido de metales en peces de elevado consumo en el Ecuador es insuficiente y seńalan que esta información es importante para la toma de decisiones para la protección de los consumidores y la inocuidad alimentaria. Es por ello que el objetivo del presente trabajo fue detectar = la presencia de Cd en muestras de atún enlatado y fresco, de consumo nacional = y de exportación, para compararlo con los límites máximos permisibles según las normas ecuatorianas NTE INEN 183 y 184 y las del Reglamento de la Unión Eur= opea (UE) No 488/2014. El estudio examinó los niveles de Cd del atún fresco y enlatado para consumo humano en Guayaquil y en el Puerto Pesquero Santa Rosa (PPSR) y su área de influencia. Los presentes resultados sirven para concientizar a la ciudadanía sobre el cuidado del ambiente y de los aliment= os que se consumen en los hogares ecuatorianos.

 

2.&n= bsp;          METODOLOGÍA

 

2.1.        Área de estudio<= /b>

Las muestras de atún fresco se colectaron en el PPSR en la provincia de Santa Elena, Ecuador (2°12'39.95"S y 80°56'53.98"O), principal puerto q= ue abastece de productos marinos a los habitantes de Guayaquil, y en el Mercado Municipal “Caraguay” en la ciudad de Guayaquil, Ecuador (2°13'35.44"S y 79°53'14.18"O). Por otro lado, el atún enlatado se obtuvo de manera aleatoria de diferentes marcas nacionales y de exportación, en diferentes supermercados de la ciudad de Guayaquil. Las especies de atún fresco que se recolectaron fueron Thunnus albacar= es (Bonnaterre, 1788) y Katsuwonus pel= amis (Linnaeus, 1758).

 

= 2.2.      =   Muestreo=

Se recolectaron 12 muestras de músculo de atún fresco en el PPSR en la provinc= ia de Santa Elena y 12 en el Mercado Municipal “Caraguay” en la ciudad de Guayaquil, así mismo se tomaron 6 muestras de atún enlatado de diferentes marcas en varios supermercados de distintos sectores de la ciudad de Guayaq= uil y 6 de atún enlatado para exportación.

 

= 2.3.      =   Análisis= de laboratorio

Una vez recolectadas las muestras se procedió a su traslado al laboratorio en fundas herméticas a 4şC. Una vez en el laboratorio, las muestras del tejido muscular fueron pesadas en una balanza Sartorius (modelo BL210S). Posteriormente, un gramo de atún fue digerido utilizando HNO3 (Merck) al 60% y calentadas a 60şC en una planch= a de calentamiento, filtradas con papel Whatman Nş40 y enrazadas a 50 mL en un b= alón aforado. Las muestras fueron analizadas en un Espectrofotómetro de absorción atómica de llama Perkin Elmer (modelo AAnalyst 100), usando la metodología interna del laboratorio del IIRN basad= a en metodología descrita en Standard Methods (2005). Para generar las curvas de calibración se utilizaron estándares comerciales de Cd (AccuStandar). Las muestras se leyeron a 228.8 nm para el = Cd, con un límite de detección de 0.002 ppm. Todas las mediciones se realizaron= por triplicado (n=3D3).

 

= 2.4.      =   Análisis estadísticos

Se determinó la normalidad de = los datos utilizando una prueba de Anderson-Darling y homocedasticidad mediante= un test de Levene. Para comparar las medias de las concentraciones de Cd en at= ún nacional vs de exportación, y de atún enlatado vs fresco, se aplicó un ANOV= A de una vía, tomando p<0.05 como valor significativo y un test a posteriori = de Tukey. Para determinar la existencia de relaciones entre las variables peso= y talla con las concentraciones de Cd en los atunes, se realizó un análisis de correlación de Pearson. Las pruebas estadísticas se realizaron utilizando e= l programa MINITAB versión 17.0.

 

3.&n= bsp;          RESULTADOS Y DISCUSIÓN<= /p>

De las 36 muestras de atún estudiadas el 66% superó los límites máximos permisibles según las normas NTE INEN 183, 184 y el Reglamento de la Unión Europea (UE) 488/2014, cuyo límite máximo permitido es de 0.10 ppm Cd. Los resultados indican que el contenido de cadmio en atún supera el límite máxi= mo permisible de 2 a 5 veces, considerando el rango de concentraciones de 0.2 a 0.5 ppm Cd. Comparativamente, no existen diferencias estadísticamente significativas entre la concentración de Cd en tejidos de atún enlatado de consumo nacional y de exportación (F=3D2.64; p=3D0.077). De igual forma, no existen diferencias entre la concentración d= e este metal pesado en atún enlatado o fresco (Fig. 1 y Tabla 1). Por otro lado, existe una leve tendencia hacia una mayor acumulación de Cd en atún de cons= umo nacional (0.441ą0.046 ppm Cd) en comparación con el atún de exportación (0.297ą0.109 ppm Cd); sin embargo, las diferencias no fueron estadísticamen= te significativas (p>0.05). Por otro lado, las concentraciones en atún fres= co de la especie Katsuwonus pelamis (0.385ą0.174 ppm Cd) parecieran ser mayores a las de la especie Thunnus albacares (0.295ą0.187 ppm= Cd) pero tampoco existen diferencias significativas (p>0.05).

Figura 1. Comparación entre las concentraciones de Cd (ppm) en tejido de atún en las muestras obtenidas de enlatado y pescado fresco. Letras iguales seńalan q= ue no hay diferencias estadísticamente significativas entre las medias, según ANOVA de 1-vía (p<0.05) y test de Tukey.

 

Tabla 1.<= /span>

Cd (ppm)

Muestras enlatadas

Mercado nacional=

Exportación

Media

0.441

0.297

DS

0.046

0.109

Mín.

0.399

0.142

Máx.

0.491

0.458

 

En cuanto al sitio de expendio= en el cual fueron obtenidas las muestras de atún fresco, sí existen diferencia= s en la concentraciones de Cd, sin importar la especie (F=3D13.57; p=3D0.000), s= iendo= el Mercado de Caraguay el que presenta los mayores valores de Cd para ambas es= pecies (Fig. 2 y Tabla 2)= . Según los resultados obtenidos, la concentración de Cd no depende de la especie, = sino del lugar donde fueron capturados. Los atunes de la especie Thunnus albacares del PPSR presentaron un valor promedio 0.030ą0.050 ppm Cd, si= n embargo, se detectaron valores mínimos de 0.000 ppm Cd y máximos de 0.140 ppm Cd.

 

Figura 2. Comparación entre las concentraciones de Cd (ppm) en tejido de atún Thunnus albacares (Thunnus) y Katsuwonus pelamis (Katsuwonus) obtenido de los mercados Santa Rosa y Caraguay. Letras igual= es seńalan que no hay diferencias estadísticamente significativas entre las medias, según ANOVA de 1-vía (p<0.05) y test de Tukey.

 

Así mismo, en las muestras de = la especie Katsuwonus pelamis se o= bservó un promedio de 0.079ą0.061 ppm Cd, con una alta desviación estándar debido a que el Cd no fue detectable en 2 muestras con valores mínimos de 0.000 ppm = Cd y máximo de 0.148 ppm Cd. Por otro lado, las muestras de las especies expendi= das en el mercado Caraguay presentaron valores mucho mayores. Los atunes de la especie Thunnus albacares tenían niveles de Cd de 0.295ą0.187 ppm Cd, con un valor mínimo de 0.058 y máximo = de 0.517 ppm Cd (Tabla 2). Por otro lado, la especie Katsuwonus pelamis registró un valor promedio de 0.385ą0.174 ppm Cd, con un valor mínimos de 0.2677 y máximo de 0.592 ppm Cd.

Las diferencias existentes en = las concentraciones de Cd en el atún procedente del PPSR y del mercado Caraguay podría ser la procedencia de los peces. Al PPSR solo llegan los atunes capturados en las zonas aledańas al puerto mientras que el mercado Caraguay recibe las especies capturadas en la zona norte de la provincia de Guayas, = de General Villamil y los puertos de la zona sur de la provincia de Manabí. Es conocido que la provincia de Guayas presenta contaminación por Cd en sus rí= os, los cuales desembocan en el Golfo de Guayaquil, además de la contribución de contaminación del Estero Salado, proveniente de descargas industriales y domésticas (Pernía et al., 2018= ; Mero et al., 2019).

Los resultados del presente trabajo fueron mayores a los hallados en un estudio realizado por el Instituto Nacional de Pesca durante el período enero 2006 y julio 2009, quienes registraron en atún concentraciones de 0.10 a 0.26 ppm = Cd (Moncayo et al., 2010). Este incremento en la concentración del metal pesado podría indicar que existe un mayor índice de contaminación en el sistema marino.

 

Tabla 2. Contenidos de Cd, talla y peso de atún fresco (Thunnus albacares y Katsuwonus pelamis) expendidos e= n los mercados Caraguay y Santa Rosa (PPRS).

 

Mercado Caraguay

Thunnus albacares

Katsuwonus pelamis

Talla (cm)=

Peso (lbs)=

Cd (ppm)

 

Talla (cm)=

Peso (lbs)=

Cd (ppm)

Media

70.200

20.460

0.295

 

54.714

5.400

0.385

DS

31.068

24.264

0.187

 

6.467

1.168

0.174

Mín.

38.000

2.800

0.058

 

44.500

4.000

0.117

Máx.

120.000

63.000

0.517

 

62.000

7.000

0.592

 

Mercado Santa Rosa

Thunnus albacares

Katsuwonus pelamis

Talla (cm)=

Peso (lbs)=

Cd (ppm)

 

Talla (cm)=

Peso (lbs)=

Cd (ppm)

Media

116.811

69.56

0.030

 

56.250

5.500

0.079

DS

46.90

41.12

0.050

 

7.089

0.891

0.061

Mín.

34.50

2.50

0.000

 

50.000

4.500

0.000

Máx.

146.00

100.00

0.140

 

65.000

6.300

0.148

 

Los presentes resultados muestran valores de Cd inferiores a los mencionados en otras zonas de Ecuador como Manta, donde Araujo & Cedeńo-Macías (2016) detectaron 2.4 ppm en te= jido muscular. Similarmente, los resultados fueron inferiores a los registrados = en otras zonas tales como Golfo Pérsico 0.062 ppm Cd (Ganjavi et al., 2010), Egipto 0.043 ppm Cd (Hussein & Khaled, 2014), Océano Atlántico 0.15 ppm, Océano Índigo 0.22 ppm (Chen et al., 2018) y Libia 0.32 ppm Cd (Voegborlo & El-Methnani, 1999). Adem= ás, el análisis de correlacion lin= eal y de Pearson mostró que no existe correlación entre la concentración de Cd = y la talla (R2=3D0.137; r=3D0.370; p=3D0.263) o peso (R2= =3D0.107; r=3D0.328 p=3D0.326) de los peces (Figs. 3 y 4). Contrario a estos resultad= os= , en la literatura se discute sobre la biomagnificación de los metales pesados y se asume que a mayor tamańo de un depredador mayor será su contenido de metales pesados. En el presente trabajo no se observó correlación entre el tamańo d= el animal y la concentración de Cd. Los ejemplares de menor tamańo de las espe= cies Katsuwonus pelamis y Thunnus albacares, por ser individ= uos pequeńos y al encontrarse desarrollando su ciclo de vida a pocos metros, o kilómetros, de la orilla del mar –que es la zona de pesca artesanal, tiende= n a acumular mayor cantidad de cadmio en el tejido muscular. Esto podría debers= e a la contaminación existente en las ciudades cercanas y que llega desde los r= íos con descargas y sedimentos; por otra parte, mediante los vientos, la atmósf= era que trasporta las cenizas volcánicas emanadas en la cordillera andina, las mismas caen en los océanos, contaminando el sistema marino.

En los individuos de mayor peso y talla, de la especie Thunnus albacares, no se logró detectar niveles de cadmio visib= les a través de la lectura del espectrofotómetro de absorción atómica. Creemos = que esto debe al efecto de dilución de la contaminación en los océanos, los individuos de mayor tamańo prefieren mantenerse en aguas profundas a difere= ncia de las especies de menor tamańo que están más cerca de la orilla. Así mismo= , es necesario mencionar que estas especies, por ser de sangre fría, realizan un proceso de detoxificación por un mecanismo celular que involucra un sistema= de transporte de membrana el cual internaliza al metal pesado, presente en el entorno celular, con gasto de energía. Este consumo energético se genera a través del sistema H+-ATPasa. Una vez que el metal pesado es incorporado al citoplasma, éste es secuestrado por la presencia de proteínas ricas en grup= os sulfhidrilos, llamadas metalotioneínas, o también puede ser compartimentali= zado para posteriormente ser expulsado por la orina.

 

Figura 3. Análisis de correlación lineal entre la concentración de Cd en el atún del mercado de Caraguay (Thunnus alba= cares y Kwatsuvonus pelamis) y la t= alla del pez. R2 representa la correlación lineal y r el valor de la prueba de Pears= on.

 

Figura 4. Análisis de correlación lin= eal entre la concentración de Cd en el atún del mercado de Caraguay (Thunnus albacares y Kwatsuvonus pelamis) y el peso d= e los peces. R2 representa la correlación lineal y r el valor de la prueba de Pearson.

 

La presencia de valores, por encima del límite permisible, de contenido de Cd,= nos manifiesta cómo perturban los contaminantes al ecosistema marino y a sus organismos acuáticos. Por lo expuesto, las entidades gubernamentales involucradas deberían realizar monitoreos periódicos en muestras de atún pa= ra evitar que la población se contamine con Cd. En la costa ecuatoriana, el or= igen de la contaminación por Cd es principalmente de tipo geogénico, por la meteorización de la roca parental procedente de la Cordillera de los Andes y por aporte atmosférico (Pozo, Sanfeliu, & Carrera, 2011; Senior et al., 2016). También se debe a la actividad antropogénica, entre estos: por acumulación de residuos industria= les, actividad minera, quema de basura y residuos agrícolas, explotación de petróleo, uso indiscriminado de insumos químicos en la agricultura, vertido= s de aguas domésticas e industriales sin tratamiento en la zona costera y a la escorrentía proveniente de las zonas de cultivos (Senior et al., 2016). Sumado a ello, en zonas aledańas a los ríos que desembocan en la costa ecuatoriana se ha registrado la presencia de fábrica= s de plástico, pintura, baterías y metalmecánicas, reportadas como potenciales fuentes antropogénicas de Cd (Pernía, Mero, Cornejo, Ramírez, & Ramírez, 2018).

En base a los presentes resultados, son necesarios estudios actualizados sobre= la presencia de metales pesados en la costa ecuatoriana. Más información sobre este tema permitirá dilucidar, por ejemplo, el comportamiento de los metales que están siendo biomagnificados en la cadena trófica. A nivel nacional, es escaso el conocimiento de esta problemática, generada por el vertido de cad= mio y otros metales, en cuerpos de agua que tienen impacto sobre el recurso pesquero, el deterioro de los ecosistemas y la salud humana.

 

4.&n= bsp;          = CONCLUSIONES<= /b>

Se comprobó la hipótesis de que existe contaminación por cadmio en atún fresco= y enlatado para consumo humano comercializado en la ciudad de Guayaquil y el Puerto Pesquero Santa Rosa. El 66% de las muestras analizadas de atún super= aron límites permisibles establecidos en las Normas INEN y en el Reglamento 488/= 2014 de la Unión Europea. No se observaron diferencias significativas entre los niveles de Cd en el atún enlatado y el atún fresco, ni entre las especies <= /span>Katsuwonus pelamis y Thunnus albacares, lo q= ue implica que el consumidor de atún está expuesto a ingerir este metal pesado a través del consumo de atún, independientemente de su presentación. Sin embargo, la procedencia del atún si influye sobre las concentraciones del metal pesado, siendo mayores las concentraciones en peces provenientes del mercado Caragu= ay. = Se efectuó un análisis comparativo de los resultados de las muestras de atún fresco y enlatado con estudios similares realizados en el Instituto Naciona= l de Pesca, demostrando que en el presente estudio realizado existe un increment= o en la contaminación de Cd.

 

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MASKANA, Vol. 9, No. 2, 2018

Revista semestral de la DIUC    =                                                                            =                                               81<= /span>=

https://doi= .org/10.18537/mskn.09.02.09

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