1. Introduction
Metals follow different pathways and cycles in the environment, some of them undergo transformations and are distributed in trace concentrations not harmful for most forms of life [1]. Furthermore, the accumulation of some of these metals in tissues of aquatic organisms is mainly influenced by the concentrations of such elements in their environment, both in water and sediments [2].
Metals are naturally present in soil and rocks as trace elements. Due to various anthropogenic impacts, these elements increase in concentration when they enter aquatic ecosystems by leaching. They directly or indirectly contaminate water supplies and thus become part of food chains posing a potential risk to public health through the consumption of organisms such as fish [3,4].
Monitoring studies of aquatic organisms in Mexico have been used to determine the concentration of metals that generally focus on benthic organisms and habitats, including bivalves such as oysters, mussels [4,5,6,7,8], and crustaceans [4,9,10]. However, the use of other free-living aquatic organisms such as fish can also be an effective monitoring tool. As these organisms are long-lived and mobile, they are good indicators for assessing water quality [11,12].
Different native fish species help define the biological integrity of a site as a measure of ecosystem health [13]. In contrast, invasive fish are a threat to native biodiversity through competition for food, nesting sites, predation, introduction of infectious agents, and displacement of native species. However, their presence is not considered in the management plans generated by headquarters of governmental institutions in Mexico City (INAPESCA, CONANP, PROFEPA, SEMARNAT, IMTA and SENASICA of SAGARPA) for the protected areas of southeastern Mexico [14,15]. The deltaic lagoon system of the Palizada River, located in the Laguna de Términos in the Flora and Fauna Protection Area in the state of Campeche, is one of the ecosystems most affected by the presence of the invasive Amazon sailfin catfish, Pterygoplichthys pardalis. The presence of this invasive fish causes an environmental and socio-economic impact on both fisheries and biodiversity loss, as well as on fishing as a source of employment and economic income [16]. Other impacts present in the Palizada River system are due to the fact that it is a tributary of the Usumacinta River, which receives polluted water discharged by industrial and oil activities along its entire course through southeastern Mexico.
Species such as the Amazon sailfin catfish have been reported by Mendoza et al. [17,18] to be one of the greatest threats to biodiversity, competing with and preying on native fish species in Mexico’s inland aquatic ecosystems. Exploitation of the Amazon sailfin catfish is one of the measures implemented to reduce the effect of invasive species and the problems it generates. For this reason, the Mexican National Commission for Aquaculture and Fisheries promotes its capture for human consumption and also its commercial exploitation in various productive sectors of the country [19]. Commercial fishing also promotes the use of introduced species of the family Cichlidae and some species of the family Cyprinidae [20].
In Mexico, the consumption of Amazon sailfin catfish is promoted, mainly among the inhabitants of the states of Chiapas and Tabasco [21]. The use of control strategies for this species has been incorporated into various agricultural activities such as agriculture, livestock, and aquaculture [19,21]. The presence of pollutants, such as metals in aquatic ecosystems, causes both native and invasive species to be exposed to these elements, which are incorporated into different aquatic ecosystems, such as rivers, lakes, and coastal lagoons in Mexico. This work is the first study on the determination of metals in native and invasive species in the Palizada River lagoon system, since many studies have focused on the analysis of pollutants in the Laguna de Términos, adjacent to this lagoon river system. The objective of this research was to evaluate the concentration and variation of Pb and Cd levels in muscle tissue among native and invasive fish species in the fluvial-lagoon-deltaic system of the Palizada River, Campeche.
2. Materials and Methods
2.1. Study Area
The Palizada River is located at the western end of the Laguna de Términos, between 18°29′13″ and 18°29′04″ N and 91°44′36″ and 91°51′31″ W; where most of the year the discharge of water from the mouth of this river flows almost directly into the Campeche shelf [22]. This river is the largest and narrowest branch, east of the Usumacinta River. This tributary also belongs to the larger basin of the Grijalva-Usumacinta system, from which it is derived to form the fluvial-lagoon-deltaic system of the Palizada River [22,23]. The system also forms part of the hydrological network of the Mexcalapa and Grijalva-Usumacinta rivers, which has an average annual contribution to the Laguna de Términos of 9.6 × 10 m3, accounting for almost 70% of the total water input to the lagoon [24].
The water inputs to the Palizada system are the Blanco stream, until it joins the Viejo River and flows into the Laguna del Este, as well as small streams from the Piñas and Marentes rivers in the east, which finally flow into the Barra de Boca Chica towards the Laguna de Términos [22]. The Palizada system has several meanders that run through a low, swampy alluvial plain covered with vegetation [22,23].
2.2. Sampling Sites and Collection of Specimens
Sampling sites were selected on the basis of a prospective visit to the study area. Subsequently, 19 final sampling sites were selected and georeferenced to cover a homogeneous distribution in the study area. The selection of sampling sites tried to cover river and lake areas (Figure 1). Samples were collected during three climatic seasons of the region, identified as: dry, March-May; rainy, June-September; and north winds, October-February [23,24].
Specimens of seven native and invasive fish species were collected in the study area, the invasive species were: Amazon sailfin catfish Pterygoplichthus pardalis, Common carp Cyprinus carpio, Grass carp Ctenopharyngodon idealla, and Nile tilapia Oreochromis niloticus. Native species include: Mayan cichlid Mayaheros urophthalmus, Twoband cichlid Vieja bifasciata, Bay snook Petenia splendida. For the capture of introduced and native species of the family Cichlidae (tilapia and mojarra), trawls with a minimum mesh size of 76.2 millimetres (3 inches) were used as fishing gear. For the rest of the native and some introduced species of the Cyprinidae family, a minimum mesh size of 127.0 millimetres (5 inches) was used [20]. Approximately five fish were captured at each sampling site during each season, all of which were approximately 15–20 cm and 230–300 g in commercial size. Species identification of collected specimens was carried out following the criteria of Miller et al. [25] and Wakida-Kusunoki and Amador del Angel [26]. The collected organisms were placed in hermetically sealed and pre-labelled polyethylene bags. They were then stored under refrigeration at a maximum temperature of approximately 4 °C and kept under these conditions until processing in the laboratory.
2.3. Ethics and Animal Use
The handling of specimens in this research was conducted in accordance with the Code of Practice for the Housing and Care of Animals used in scientific procedures. This document was issued on 14 April 2016 and under Section 1 of the Animals (Scientific Procedures) Act. Fish were killed by a severe blow to the head followed by the destruction of the brain. Furthermore, taking into account the above guidelines, this research, the planning and execution of this work complied with the commonly accepted ‘3Rs’ guidelines: Replacement of animals with alternatives wherever possible; Reduction of the number of animals used; and Refinement of experimental conditions and procedures to minimise harm to the animals.
2.4. Sample Processing
Processing of samples obtained in the field was carried out at the Laboratorio de Investigación de Recursos Acuáticos (LIRA) of the Instituto Tecnológico de Boca del Río (ITBOCA), where fish were dissected to extract muscle tissue from each organism. Once the samples were extracted, they were stored in airtight polyethylene bags and then frozen at −14 °C. They were then subjected to a freeze-drying dehydration process using the Thermo Savant Modulyo D-115 for 72 h at −49 °C and a vacuum pressure of 36 × 10−3 mbar. After this process, the samples were stored in sealed bags and finally ground in a blender to a fine particle size. Subsequently, the samples were stored in a desiccator until further processing.
2.5. Analytical Preparation and Microwave Acid Digestion
The material used in the development of the metal analysis was prepared according to the specifications for metal analysis NOM-117-SSA1-1994 [27]. The laboratory material was washed with phosphate-free neutral Extran® soap for 24 h and then rinsed with tap water. The material was then placed in a solution of distilled water with 20% nitric acid HNO3 (J.T.Baker®) for 24 h. After this period, the material was rinsed again with tap water. At the end, the material was washed with deionised water (Milli-Q) for 24 h, and finally dried and stored until use.
Sample digestion was carried out with a CEM Mars 5 microwave oven (CEM Corporation, Mathews, NC, USA) using 0.5 g of previously freeze-dried and ground sample. To this sample, 9 mL of reagent grade HNO3 was added, and a pressure of 120 and 100 PSI was used for the microwave digestion, with a temperature of 150 and 190 °C for 5 and 10 min, respectively. A blank sample and a positive control were run throughout the sample analysis. After completion of the microwave digestion, 0.45 µm Millipore® nitrocellulose filters were used and the filtrate was made up to 25 mL with deionised water (Milli-Q), the final extract was placed in an amber polyethylene vial and stored at 4 °C.
2.6. Quantification of Metals
A Thermo Scientific Ice 3500 AA atomic absorption apparatus (Thermo Scientific®, Beijing, China) was used to identify and quantify the concentration of metals by flame spectrophotometry. The procedure was performed according to the operating specifications established by the manufacturer and NOM-117-SSA1-1994 [27].
A calibration curve was prepared for each of the metals using certified high-purity standards (High-Purity Standards, Charleston, SC, USA), to quantify the metals in µg g−1 (dry weight). This curve presented an adequate fit, obtaining a correlation coefficient higher than 0.99.
2.7. Statistical Analysis
Metal concentrations in muscle tissue of native and invasive fish were analysed by site, season and species with TIBCO Statistica 14.0.0.15 software (TIBCO Software Inc., Palo Alto, CA, USA), using a one-way ANOVA. Metal data from invasive fish species samples were transformed using natural logarithms to meet the ANOVA assumptions. A multiple comparison of means was then performed using the Tukey’s test to determine the statistical differences (p < 0.05) between metal concentration at the sampling sites, season, and different native and invasive fish species.
3. Results
3.1. Metal Concentrations in Invasive Species
The Cd concentrations obtained in muscle tissue of the invasive species were higher than those obtained for the metal Pb in these species. The LCAR and LLAR sites had the highest Cd concentrations in the tissue of the four invasive fish species analysed: Amazon sailfin catfish (AS); grass carp (GC); common carp (CC); and Nile tilapia (NT) (Table 1). The lowest Cd concentration was detected in S9, located in the middle part of the fluvial-lagoon-deltaic system of the Palizada River. Cd concentrations in muscle tissue of the invasive species did not show statistically significant differences between the sampling sites analysed individually (p > 0.05) (Figure 2).
Pb concentrations showed statistically significant differences (p < 0.05) between the LLAR and LCAR sampling sites, while the rest of the sites analysed showed a similar pattern in the detected concentrations (Figure 2). LCAR showed the highest concentration of Cd, but the lowest concentration of Pb was also detected at this site (Table 1).
The concentrations for Cd and Pb did not show statistically significant differences between seasons (p > 0.05). Cd registered the highest concentration during the rainy season with 6.551 ± 1.014, followed by the dry season with 6.538 ± 0.639, while the lowest concentration was found during the north winds season with 5.998 ± 1.003 µg g−1 (dry weight). Cd presented the highest concentration in the invasive species analysed with respect to Pb concentrations, being the highest concentration in the dry season with 5.864 ± 0.547 followed by the north winds season with 5.504 ± 0.764 contrasting with the rainy season which presented the lowest concentration with 5.226 ± 1.421 µg g−1 dry weight.
The invasive fish species common carp (CC) and Amazon sailfin catfish (AS) showed the highest concentrations of Cd and Pb (Figure 3), the latter being lower than those obtained for Cd in the same species. However, statistically significant differences in Cd (p < 0.05) were detected between Amazon sailfin catfish (AS) and Nile tilapia (NT), the latter species having the lowest Cd and Pb concentrations in relation to the rest of the invasive fish species (Table 2). There were no statistically significant differences (p > 0.05) between Pb concentrations in the four invasive fish species analysed.
3.2. Metal Concentration in Native Species
The collection of native fish species in the fluvial-lagoon-deltaic system of the Palizada River was a small number compared to the number of invasive fish collected at the sampling sites. These fish were collected during the three seasons and only a total of seven fish were obtained at some of the sampling sites.
LCAR showed the highest concentrations of Cd and Pb, followed by LDUL which showed the same pattern for both metals. Pb presented a higher concentration than Cd only at LFRE, in the rest of the sampling sites analysed the mean concentrations of Cd were higher than those obtained for Pb (Table 1).
The rainy season presented the highest concentration of Cd with 5.920 and Pb with 5.820, followed by the dry season with 5.360 ± 0.470 for Cd and Pb with 4.886 ± 0.565 µg g−1 (dry weight). The lowest concentration was detected in northeast with 4.700 ± 1.086 for Cd and 4.403 ± 0.212 µg g−1 (dry weight) for Pb. Bay snook (BS) had the highest concentration of Cd, followed by Mayan cichlid (MC). While the Twoband cichlid (TC) species showed the highest mean Pb concentration and the lowest Cd concentration (Table 2).
4. Discussion
4.1. Concentration of Metals in Invasive Species
The accumulation of Cd and Pb in the four invasive fish species, at all sampling sites and seasons, indicates the capacity of these species to bioaccumulate these elements in their muscle tissue. The bioaccumulation of metals in tissues and fatty organs of aquatic organisms is influenced by their diet, making fish more exposed to chronic risk than other benthic aquatic species, such as crustaceans or mollusks [28,29].
The differences detected in Cd and Pb concentrations at sampling sites such as LCAR may be associated with its location at the end position, where it receives the pollutant transport from the discharge area of the fluvial-lagoon system, which flows into the coastal Laguna de Términos and this, in turn, into the Gulf of Mexico. The resuspension of sediments in the water column and the contribution of pollutants through the tributaries to the fluvial-lagoon-deltaic system of the Palizada River are other causes that contribute metals to this system, such as the Grijalva-Usumacinta basin, which is impacted by different anthropogenic sources. The Palizada River system receives wastewater discharges from urban settlements and thus pollutants along its course, which are discharged into this system without any treatment [24,28,29].
Analysis of fish muscle tissue is a monitoring tool that helps to determine whether there is a transfer of metals and other pollutants from the habitat to the tissue of the organisms. Consumption of impacted organisms can have a potential harmful effect on public health through the consumption of fish in its traditional forms, whether fried, processed as protein concentrate, silage, and/or processed as fishmeal [26,30]. The accumulation of metals varies according to different factors such as the type of species, size, type of feed, environmental conditions, level of contamination at the fishing site, physiological characteristics of the fish [30], and the period of exposure to which an organism is subjected in polluted waters [28,31].
This is the first study to analyse the concentrations of metals such as Cd and Pb in native and invasive fish species in the Palizada River. Previous research has been related to biological aspects and socio-economic impact caused by invasive species in this area [16,23,24], in addition to the determination of metals in meadow grasses [29]. For this reason, we mainly used the comparison between research generated with native and invasive fish species in other regions of the world, taking into account that this information helps to explain the pattern of metals in the species analysed in the context of the study area.
The maximum accumulation of Cd in the muscle tissue of the invasive fish in this study occurred during the rainy and dry seasons. These results may be related to the fact that, during the rainy season, the mobilisation of sediments according to climatic conditions and fertilisers derived from agricultural activity in the basin is the main source of this element [28,29,30]. On the other hand, during the the dry season, the reduction of the water column level is very marked, which concentrates pollutants in the sediments, making them the pathway that transfers of metals to the aquatic biota [30,31,32].
The maximum concentration of Cd and Pb was obtained in muscle tissue of common carp (CC) and Amazon sailfin catfish (AS). The influence of fish feeding habits is noteworthy, whereby diet is considered to be the main pathway of metal bioaccumulation [31,33]. This may reveal that the maximum concentrations detected in common carp (CC) and Amazon sailfin catfish (AS) show a similar trend, as both belong to the omnivore group and only the former can also feed on plankton and algae [31]. The similarity in feeding habits explain in part the tendency to accumulate metals in their muscle tissue. The concentrations of metals obtained in Amazon sailfin catfish (AS) in this research were higher than those obtained in other areas of the Grijalva and Usumacinta River basin [21,34], as well as those reported in other regions of the world, in different invasive species such of the genus Pterygoplichthys such as P. pardalis and P. multiradiatus [35,36,37,38]. It should be noted that there is a need to establish an international standard of permissible limit for metals in order to regulate exposure from consumption of these species.
The Nile tilapia O. niloticus is also of economic importance throughout Mexico, although its presence in ecosystems such as the fluvial-lagoon-deltaic system of the Palizada River is an indicator of ecological disturbance. This is due to the predatory capacity of this species [31] with the bioaccumulation of metals in its muscle tissue showing its capacity to accumulate environmental pollutants [35,36,37,38,39]. The concentrations obtained in this research in O. niloticus muscle were higher than those reported in other research works on species such as O. mossambicus [39] and O. niloticus [40]. Exploitation of these species should consider their capacity to bioaccumulate pollutants such as metals, as they could pose a risk to public health. The main strategy to control invasive species is through regional harvesting programmes. By integrating them as part of the diet, their consumption is intended to achieve control of invasive species and protection of native species in the areas of entry of these species.
Both Cd and Pb, analysed in this research in fish muscle tissue, have an impact on public health. Since Pb is a non-essential element, its exposure is widely documented to cause neurotoxic and nephrotoxic effects, while inorganic Pb is considered a possible carcinogen in humans [33,40]. Furthermore, Cd has important health effects as an endocrine disruptor, which can cause prostate damage [41]. Exposure to Cd in humans and wildlife can cause damage to the kidneys, intestinal tract, reproductive system and cardiovascular system. It is also classified as a carcinogen by the International Agency for Research on Cancer (IARC) [39,41,42]. The negative effects of Cd and Pb on public health and aquatic fauna highlight the importance of assessing these heavy metals as indicators of environmental quality in aquatic ecosystems.
The concentrations of Cd and Pb in invasive fish in the fluvial-lagoon system of the Palizada river exceeded the maximum tolerable limit (MTL) for fishery products. The maximum levels of Cd and Pb established by European Union (EU) are 0.05 and 0.3 μg g−1, respectively [43]. On the other hand, the maximum limits in Mexico, according to the Diario Oficial (2009), are 0.5 µg g−1 for Cd and Pb in the edible part of the muscle, in fresh, chilled and frozen products such as fish [44]. The United States Food and Drug Administration (USFDA) concurred on the latter permissible limit set for Cd [45]. Meanwhile, the European Union, the USFDA and the Standardisasi Nasional Indonesia (SNI) set a standard permissible limit for Pb of 0.3 µg g−1 [43,46,47]. On the other hand, the World Health Organization (WHO) considered a maximum permissible limit of 2.00 µg g−1 for Pb [48].
Discrepancies between the permissible limits set by international bodies may underestimate or overestimate the risk of dietary exposure to heavy metals for populations living in southeastern Mexico. The provisional tolerable daily intake (PTDI) for Cd has a value of 58.3 μg per person−1 [49]; while the individual tolerable daily intake (ITDI) in fish muscle ranges from 0.27–0.41 kg (wet weight) [33]. For Pb, the EU, in 2006, considered a limit value of 1.50 µg g−1 per week [43]. The concentrations obtained in the invasive fish of the Palizada River system in this research exceeded the national and international permitted limits. It should be noted that the maximum concentrations of Cd and Pb were detected in invasive species of major consumption and commercial importance such as common carp (CC) and Amazon sailfish (AS), which increases the potential risk of exposure of consumers of these species to pollutants such as metals.
4.2. Concentration of Metals in Native Species
Native fish species showed lower concentrations of Cd and Pb compared to the maximum values obtained for invasive fish species (Table 2). These results indicate the availability of these elements in the environment, but also that native species are well adapted to their environment, as they have metabolic pathways [31,40], which allow them to accumulate a lower concentration of Cd and Pb, compared to invasive species that have recently entered the ecosystem. Maximum Cd and Pb concentrations per sampling site showed similar trends to those obtained for invasive fish species. This indicates that both species are exposed throughout the year to these metals.
Due to the lack of scientific information on the concentration of metals such as Pb and Cd in fish species native to the study area, reference is made to the reported concentration of these metals in the Mugil cephalus, an economically important and commonly consumed species [33]. Furthermore, this species inhabits ecosystems similar to the study area analysed in this research. The levels of metals detected in M. cephalus were lower than those obtained in the native species of the Palizada River system, indicating a greater availability in the study area and a greater capacity for accumulation in the species studied.
The native fish species, Bay snook (BS) and Mayan cichlid (MC), showed the same pattern as the invasive species of bioaccumulating a higher concentration of Cd compared to Pb. Only the Twoband cichlid (TC) species did not show the same pattern, with Pb showing a higher mean concentration with respect to Cd. The concentrations obtained for Cd and Pb in native fish species in the fluvial-lagoon system of the Palizada River provide a scientific contribution on the concentration of metals in native species, particularly because the concentrations exceed the permissible limits. The results obtained for Cd and Pb suggest a potential chronic effect on the population that consumes these native and invasive fish species in the study area, representing a potential risk to public health and the environment.
5. Conclusions
The presence of Cd and Pb in the muscle tissue of native and invasive fish is an indicator of the environmental exposure of the ecosystem in which these fish develop. The concentrations identified in this study are associated with the physiological characteristics of the fish analysed.
The concentrations obtained in the fish species with respect to the sampling sites are related to sediment entrainment and to the hydrodynamics of the ecosystem, which allows for an increased exchange of currents, and in doing so, modifies the fish habitat in the study area. These concentrations may indicate the bioavailability of these metals by terrigenous and anthropogenic inputs, which has a negative impact on native and invasive fish living in the lagoon-deltaic system of the Palizada River.
In this study, the highest Cd concentration is reported for the common carp, an invasive species of high consumption. It is important to mention that there are governmental programmes that promote its consumption as a control and eradication strategy, in order to protect native species in the Gulf of Mexico ecosystems.
There is no record of studies demonstrating the food safety of fish in this area, however, there are studies that report that consumption of fishery resources contaminated by metals can influence androgenic activities and cause possible chronic effects on public health.
Specific national legislation on permissible limits for metals in invasive species is required, which would undoubtedly imply the need to strengthen scientific knowledge through research, disseminate the results and raise public awareness of the risks of consumption. Therefore, supervision and control of compliance with environmental legislation must be generated in order to act in the control of anthropogenic sources for the improvement and quality of the ecosystem.
Conceptualization, M.d.R.C.-C. and A.T.W.-K.; methodology, G.N.-R.; validation, M.d.R.C.-C. and A.T.W.-K.; investigation, M.d.R.C.-C. and F.L.-R.; resources, M.d.R.C.-C. and F.L.-R.; writing—original draft preparation, M.d.R.C.-C., A.T.W.-K. and G.N.-R.; writing—review and editing, M.d.R.C.-C., G.N.-R., A.T.W.-K.; supervision, F.L.-R., A.T.W.-K.; project administration, M.d.R.C.-C. and F.L.-R. All authors have read and agreed to the published version of the manuscript.
To the Tecnológico Nacional de México/Instituto Tecnológico de Boca del Río (TecnM/ITBOCA), and CONACYT (Consejo Nacional de Ciencia y Tecnología) for the support granted to execute this work to Scholarship No. 740232, through Postdoctoral Stays linked to the Strengthening of the Quality of the National Postgraduate, CALL 2018 (1).
The handling of specimens in this research was conducted in accordance with the Code of Practice for the Housing and Care of Animals used in scientific procedures. This document was issued on 14 April 2016 and under Section 1 of the Animals (Scientific Procedures) Act. The project identification code 5290.19-P for this paper, approval date from January 2018 to the current date by the Institutional Postgraduate and Research Committee, Instituto Tecnológico de Boca del Río (ITBOCA).
We choose to exclude this statement.
To the Tecnológico Nacional de México/Instituto Tecnológico de Boca del Río (TecnM/ITBOCA) for facilitating the development of this project. Also, to the Instituto Nacional de Pesca y Acuacultura for the partial funding through the research project “Aspectos biológicos pesqueros del pez diablo Pterygoplychthys pardalis en el Rio Palizada” (Biological aspects of the Amazon sailfin catfish Pterygoplychthys pardalis in the Palizada River).
The authors declare no conflict of interest.
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Enlarge this image.Figure 1. Sampling sites of fish species in the fluvial-lagoon-deltaic system of the Palizada River, Campeche.
Enlarge this image.Figure 2. Metal concentration in muscle tissue (µg g−1 dry weight) of invasive fish species by sampling site in the fluvial-lagoon-deltaic system of the Palizada River, Campeche. * indicate statistically significant differences (p < 0.05) of metals between sampling sites. Abbreviations: LCOR: Laguna Corcho; LDUL: Laguna Dulce; LDUL2: Laguna Dulce 2; LCAR: Laguna Carmen; LLAR: Laguna Larga; LCOL: Laguna Colorada; LCRU: Laguna de las Cruces; LFRE: Laguna Frente.
Enlarge this image.Figure 3. Metal concentration in muscle tissue (µg g−1, dry weight) of invasive fish species in the fluvial-lagoon-deltaic system of the Palizada River, Campeche. Abbreviations: AS: Amazon sailfin catfish; GC: grass carp; CC: common carp; NT: Nile tilapia. * indicate statistically significant differences (p < 0.05) between fish species.
Metal concentration (mean ± standard deviation) in fish muscle tissue (µg g−1 dry weight) of invasive and native fish species by sampling site in the fluvial-lagoon-deltaic system of the Palizada River, Campeche.
| Invasive fish species | |||
| Sampling site | N | Cd | Pb |
| S1 | 3 | 5.593 ± 1.245 | 4.670 ± 0.603 |
| S2 | 5 | 5.682 ± 0.880 | 5.290 ± 0.803 |
| S3 | 2 | 6.065 ± 0.403 | 5.340 ± 0.000 |
| S4 | 3 | 6.960 ± 0.533 | 6.080 ± 0.640 |
| S5 | 2 | 6.820 ± 0.098 | 5.510 ± 0.226 |
| S6 | 3 | 5.993 ± 0.340 | 5.480 ± 0.370 |
| S7 | 2 | 6.500 ± 0.070 | 6.160 ± 0.410 |
| LCOR | 5 | 6.328 ± 1.027 | 5.374 ± 0.725 |
| S8 | 3 | 7.210 ± 0.704 | 6.680 ± 0.302 |
| S9 | 3 | 5.403 ± 0.370 | 5.070 ± 0.480 |
| LCOL | 2 | 5.975 ± 1.053 | 5.590 ± 1.456 |
| S10 | 3 | 6.053 ± 1.317 | 5.243 ± 0.998 |
| LDUL2 | 3 | 6.693 ± 0.821 | 5.516 ± 0.858 |
| LCAR | 1 | 7.870 | 2.320 |
| S11 | 2 | 7.155 ± 0.261 | 6.355 ± 0.601 |
| LLAR | 1 | 7.660 | 7.760 |
| LCRU | 1 | 6.890 | 6.450 |
| TOTAL | 44 | 6.345 ± 0.917 | 5.545 ± 0.965 |
| Native fish species | |||
| Sampling site | N | Cd | Pb |
| S2 | 1 | 5.340 | 4.560 |
| LFRE | 1 | 3.450 | 4.340 |
| LDUL | 3 | 5.523 ± 0.356 | 4.896 ± 0.825 |
| LCOL | 1 | 4.900 | 4.560 |
| LCAR | 1 | 5.840 | 5.540 |
| Total | 7 | 5.157 ± 0.830 | 4.812 ± 0.614 |
Abbreviations: LCOR: Laguna Corcho; LDUL: Laguna Dulce; LDUL2: Laguna Dulce 2; LCAR: Laguna Carmen; LLAR: Laguna Larga; LCOL: Laguna Colorada; LCRU: Laguna de las Cruces; LFRE: Laguna Frente.
Metal concentration in muscle tissue (µg g−1, dry weight) of native and invasive fish species in the fluvial-lagoon-deltaic system of the Palizada River, Campeche.
| Invasive Species | Native Species | ||||||
|---|---|---|---|---|---|---|---|
| Species Code | N | Pb | Cd | Species Code | N | Pb | Cd |
| AS | 33 | 5.645 ± 1.047 | 6.547 ± 0.873 | TC | 2 | 5.080 ± 1.046 | 4.685 ± 1.746 |
| GC | 3 | 5.376 ± 0.063 | 6.283 ± 0.453 | BS | 2 | 4.885 ± 0.926 | 5.535 ± 0.431 |
| CC | 2 | 5.980 ± 0.905 | 6.630 ± 0.127 | MC | 3 | 4.586 ± 0.046 | 5.220 ± 0.280 |
| NT | 6 | 4.930 ± 0.464 | 5.173 ± 0.565 | ||||
| Total | 44 | 5.545 ± 0.965 | 6.345 ± 0.917 | Total | 7 | 4.812 ± 0.614 | 5.157 ± 0.830 |
Abbreviations: N: number of organisms; Invasive species of fish: AS: Amazon sailfin catfish Pterygoplichthys pardalis; GC: Grass carp Ctenopharyngodon idealla; CC: Common carp Cyprinus carpio; NT: Nile tilapia Oreochromis niloticus; Native species of fish: TC: Twoband cichlid Vieja bifasciata; MC: Mayan cichlid Mayaheros urophthalmus; BS: Bay snook Petenia splendida.
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; Lango-Reynoso, Fabiola 1 ; Navarrete-Rodríguez, Gabycarmen 1
; Wakida-Kusunoki, Armando Toyokazu 2 1 Tecnológico Nacional de México, Instituto Tecnológico de Boca del Río, Carretera Veracruz, Boca del Río CP 94290, Mexico;
2 Instituto Nacional de Pesca y Acuacultura, Centro Regional de Investigación Pesquera de Yucalpetén, Boulevard del Pescador s/n Esquina Antigua Carretera a Chelem, Mérida CP 97320, Mexico;