Hellgrammite as a Non-Conventional Biomonitor for Surface Water and Environmental Health Assessment

Axel  Eduardo Rico-S&#225;nchez; J. Evaristo Buend&#237;a-Chavarr&#237;a; Jacinto El&#237;as Sede&#241;o-D&#237;az; Eugenia L&#243;pez-L&#243;pez

doi:10.3791/66911

JoVE Journal > Environment

环境科学

Hellgrammite as a Non-Conventional Biomonitor for Surface Water and Environmental Health Assessment

Published: July 26, 2024

doi:

10.3791/66911

Axel Eduardo Rico-Sánchez¹, J. Evaristo Buendía-Chavarría², Jacinto Elías Sedeño-Díaz³, Eugenia López-López²

¹Posgrado en Hidrociencias,Colegio de Postgraduados, ²Instituto Politécnico Nacional, Laboratorio de Evaluación de la Salud de los Ecosistemas Acuáticos,Escuela Nacional de Ciencias Biológicas, ³Instituto Politécnico Nacional,Coordinación Politécnica para la Sustentabilidad

Summary

This protocol describes the use of biomarkers for the early detection of deleterious impacts in aquatic ecosystems. The biomarkers are closely related to sentinel traits, and their changes aid in detecting early-warning damages.

Abstract

The larvae of dobsonflies from the genus Corydalus, commonly known as Hellgrammites, are characterized by their notable size, extensive range of occurrence, and extended period of immaturity, which can last up to one year. Hellgrammites are clearly known to exhibit sensitivity to pollution and habitat structure impacts. Given these unique features, using Corydalus texanus larvae is highly suitable as reliable biomonitoring agents to assess the ecological integrity of aquatic ecosystems. This protocol aims to provide the necessary tools for C. texanus assessment and demonstrate their efficacy through a case study. Research findings have practical implications, indicating that C. texanus larvae exhibit early-warning responses to mining pollution, bioaccumulating high amounts of heavy metals such as Zn, Fe, and Al. The presence or absence of C. texanus populations may serve as a helpful indicator for identifying potential issues related to ecosystem health. The unconventional approach has shown early warnings of pollution in mining-impacted sites, highlighting the need for timely action to protect the environment. Given their unique traits, the use of C. texanus larvae is highly suggested as a reliable non-conventional bioindicator.

Introduction

Hellgramites are insect larvae from the order Megaloptera (Latreille, 1802), named dobsonflies or fishflies in their adult stage. A low diversity but widespread characterizes this group of top predator insect larvae from aquatic ecosystems¹. Hellgramite species occur in well-defined biogeographic regions; therefore, it is relatively easy to identify species without a high taxonomic knowledge. Notably, the Corydalidae larvae possess the most prominent species from the Megaloptera order (20-90 mm body length)², making hellgramite visible to the naked eye.

Hellgrammites play a crucial role in aquatic ecosystems as predators, with a powerful presence due to large chews denoting their impressive predatory shape. A dorsoventrally flattened body also joins with 7-8 pairs of filament gills along the body, and a head capsule with six stemmata per side makes hellgrammites fascinating organisms for entomologists and fans³. Adults of Corydalidae surprise and create an impression image to people due to their prominent size; however, they are entirely harmless. It is noteworthy that hellgrammites have the ability to persist in aquatic environments in their larval stage for a significant duration.

The phenotypical features of hellgrammites allow a particular chance to highlight their role in aquatic ecosystems; nevertheless, their indicator potential is the most wanted feature for aquatic ecologists. Vast knowledge of their bioindicator potential is highlighted in aquatic ecosystems because their occurrence relates to good health conditions in their habitats due to their intolerance to organic pollution in surface waters⁴^,⁵^,⁶^,⁷^,⁸.

Most Corydalidae megalopterans live in high-speed running waters as riffles and substrates predominated by cobble and pebbles, but hellgrammites also occur in low-gradient streams with snags and sand substrates, as well as in lentic habitats such as lakes³^,⁹^,¹⁰. Their wide range of occurrence mirrors the critical traits of a top predator and their ability to colonize several habitats aimed by their effective life history strategies¹¹. Hellgramites linked their traits with the dynamics of aquatic ecosystems; thus, strategies such as adaptation to aerial respiration by spiracles (in addition to their ventral tufts of tracheal gills) are proper of the Corydalidae strategies¹⁰.

Hellgrammites inhabit particular ecosystems and exhibit rapid responses to deviations from established patterns, thereby serving as an early-warning system⁷. The reactions of these wildlife organisms can be employed as a valuable tool to assess the impact of pollution on aquatic ecosystems, particularly in the case of non-target pollutant mixtures. Some deleterious effects on living organisms have been recognized in ecosystems because of individual toxicity of chemicals, but the effect of pollutant mixtures shall be identified. The early-warning responses from hellgrammites may make it possible to identify deleterious effects by giving a reference to the impacts of a mixture of pollutants or even when individual effects of pollutants recognize No Observable Effect Concentration (NOEC)¹².

Several model organisms have been used for experimental acute and chronic tests; however, they are cultured and maintained under controlled conditions¹³. Controlled conditions make them unable to identify the non-target effects of several pollutants they are exposed to. Also, NOEC is frequently recognized due to the complexity of the pollutant's mixture. For that reason, in the last decades, non-model native species with non-target effects were recognized to screen systems, which are essential to carrying out ecotoxicological research¹⁴. Consequently, hellgrammites seem able to assess the deleterious effects of pollution in aquatic ecosystems. Traits such as their biology, genetics, and physiology, among others, make non-model organisms suitable for impact assessment in ecosystems¹⁴.

This protocol aims to establish a novel biomonitoring tool using a non-model organism that can detect early-warning signals in response to non-target pollution mixtures. To achieve the best results, the traits exhibited by the larvae of the model species, C. texanus, have been comprehensively considered and integrated into the analysis¹⁵.

Protocol

Figure 1: Quick step-by-step guide on how to use the non-conventional biomonitor Corydalus texanus for implementation in aquatic ecosystems. Please click here to view a larger version of this figure.

1. Fieldwork

Identify study sites located upstream and downstream of the pollution source where suspected or evident impacts are recognized (i.e., punctual or diffuse emissions).
NOTE: The present protocol included 15 study sites in four main rivers: 1) Extoraz River (sites PB, EZ, RQ, BC); 2) Escanela-Jalpan River (ES, EN, AH, JL, PI, PA); 3) Ayutla River (AY); and 4) Santa María River (SM, AT).
Search and locate at least one reference site (a place under minor or absence of impacts) and define it as a study site.
NOTE: For the current study sites BC, ES, SM, AY and AT were considered as reference sites.
Recognize certain attributes of habitats that increase the likelihood of finding individuals of C. texanus. These include gravel substrate, rocky habitats with steeper gradients, high-speed flows, well-oxygenated waters, high canopy density, and habitats in highlands and lowlands.
Enclose a 100 m section of the stream to identify appropriate habitats for biomonitoring¹⁶.
Get inside the stream to collect samples.
Sample at least six individuals of C. texanus in habitats such as riffles, pebbles, clear waters, and debris using a kick net with a mesh size of 500 µm.
Remove rocks in the direction of the water flow and transfer the larvae into the net.
Handle the kick net with sampled larvae and transfer them to designated bottles for temporary housing. Handle the net with caution and fold the edges towards the interior to prevent any loss of larvae.
Measure the head width of sampled larvae using a caliper to identify instars IX to XI (within the range of 6 mm to 10 mm).
Purge larvae by immersing them in a bottle containing stream water for 30 min.
Place samples in plastic bottles with clear labeling and then euthanize them by immersion in liquid nitrogen (-75 °C) in a cryogenic tank.
Transport and store the samples securely at -45 °C in the ultra-freezer at the laboratory.
Using a polyethylene bottle, take a stream water sample of 200 mL, add 1 mL of nitric acid, and store the sample at 4 °C for subsequent heavy metal quantification in the laboratory.

2. Dissection of the sampled larvae and tissue separation

Put the plastic dissection tray on ice and wait until it reaches 4 °C, using a thermometer to check.
Take samples from the ultra-freezer and put them on the dissection tray to start dissecting.
Select target tissues: muscle, branches, neural tube, and exoskeleton.
Use a ceramic knife to remove the head and separate the tissues carefully. Open the body longitudinally and remove the gills on each side.
Separate the exoskeletons using a smaller ceramic knife and clean the excess tissue. Place the exoskeletons in an oven and dry them at 80 °C for 48 h.
After time is due, store dry exoskeletons for further analysis.
Keep cleaning soft tissues under cold conditions for further analysis by microassays.
Use a small ceramic knife to extract soft tissues from fat. Separate and pool each target tissue from individuals from the same sampling point.
Store each tissue type in a 2 mL microtube, maintaining cold conditions throughout the process.
To prepare each target tissue, weigh 100 mg of the tissue and add 1 mL of PBS solution with a pH of 7.4. Use a one-handed tissue tearor to homogenize each tissue. Typically, soft tissues require three cycles of 10 s each.
Centrifuge sample at 1,000 x g for 5 min at 4 °C. Transfer the supernatant to a 1 mL microtube.
Perform biomarker microassays.

3. Heavy metal quantification

Weigh 250 mg of dried exoskeletons from at least six specimens in the specified developmental stage using an analytical balance.
Grind exoskeletons in a glass mortar until they become finely powdered. Add 250 mL of ultrapure nitric acid to the powder reaction vessels.
To digest the samples, transfer them to a digestion microwave at 180 °C for 30-45 min.
NOTE: Use the right microwave-safe container for the microwave brand to heat samples safely and effectively. Digestion time for tissue samples varies by microwave brand, taking 30-45 min. Some brands offer standardized methods.
Perform a microwave digestion method for water samples following the EPA3015A method, using 45 mL of the water sample and adding 5 mL of nitric acid.
Measure heavy metals and metalloids in digested samples (water and tissues) using inductively coupled plasma optical emission spectroscopy (ICP-OES), including Hg, Cu, Pb, Zn, Fe, Cr, Cd, Mn, Ba, and As.
NOTE: Use argon grade 5 and standard solutions of each metal and metalloid to construct a calibration curve.

4. Microassays for the assessment of oxidative stress and biomarkers

Preparing reagents
1. Mix 6 g of NaH₂PO₄ with 1000 mL of ultrapure water to make a 50 mM Monobasic Phosphate Buffer. Store in a flask at 2-8 °C indefinitely.
2. To make 8.1% SDS, dissolve 450 mg of sodium dodecyl sulfate (SDS) in 5 mL ultrapure water. Prepare just before use.
3. Dilute 2 mL of trichloroethanoic acid (TCA) in 8 mL of ultrapure water (prepare fresh reagent when required).
4. Dissolve 100 mg of tetrabutylammonium (TBA) in 10 mL of ultrapure water (prepare fresh reagent when required).
5. To make 50 mM PBS pH 7.8, dissolve 97 mg of Na₂HPO₄ and 59 mg of NaH₂PO₄ in 10 mL of ultrapure water. Then, adjust the pH to 7.8 using NaOH to increase or HCl to decrease.
6. Make a 200 µg/mL solution of bovine catalase by dissolving 8 mg of it in 40 µL of ultrapure water (prepare fresh reagent when required).
7. To make a 50 mM TRIS/5 mM ethylenediaminetetraacetic acid (EDTA) solution, add 6.05 g of tris (hydroxymethyl)aminomethane (TRIS) and 0.073 g of EDTA to 45 mL of ultrapure water. Adjust pH to 7.6 with HCl and store at 4 °C until use.
8. For 0.1 M glutathione reduced (GSH) (for 45 duplicated samples), weigh 0.0184 g of GSH and dissolve it in 600 µL of 10 mM HCl.
9. To prepare 10 mM HCl, add 0.5 µL of concentrated HCl to 599.5 µL of ultrapure water.
10. Add 28.5 µL of glutathione reductase to 1.4 mL of 0.1 M TRIS/HCl 0.5 mM EDTA pH 8.0.
11. Mix 1.211 g of TRIS and 0.0146 g of EDTA with 90 mL of ultrapure water to prepare a 0.1 M TRIS/HCl and 0.5 mM EDTA solution at pH 8.0. Add HCl to adjust the pH if needed. The solution can be stored indefinitely at 2-8 °C.
12. Weight 0.075 g of NADPH and add it to 2.25 mL of 1% NaHCO₃ 1 mM EDTA.
13. Mix 1 g of NaHCO₃ and 0.0282 g of EDTA in 100 mL of ultrapure water to prepare a 1% NaHCO3 and 1 mM EDTA solution. Store the solution at 4-8 °C for an undetermined time.
14. Mix 2 µL of t-butyl hydroperoxide with 2 mL of ultrapure water to make a 7 mM solution. Mix immediately before use.
15. Mix 1 g of bovine serum albumin (BSA) with 1 mL of ultrapure water to create a 1 µg/µL stock solution.
Thiobarbituric acid reactive substances (TBARS) (lipid peroxidation, LPO)¹⁷
1. Add 5 µL of tissue supernatant to a 1 mL microtube. Add 45 µL of 50 mM PBS (fresh and stock solution).
2. Add 12.5 µL of 8.1% SDS (freshly prepared). Add 93.5 µL of 20% TCA pH 3.5 (freshly prepared).
3. Add 93.5 µL of 1% TBA (freshly prepared). Complete the volume by adding 50.5 µL of ultrapure water. Close the tube's lid and vortex it for 30 s.
4. Puncture the microtube lid with a needle and incubate in boiling water for 10 min.
5. Cool the tube at room temperature (RT), and then centrifuge it at 1000 x g for 10 min.
6. Add 150 µL of supernatant to a well in a 96-well microplate and measure absorbance at 530 nm using a microplate spectrophotometer.
7. To quantify lipid peroxides, create an 8-point TBARS calibration curve (0-160 µM) using malondialdehyde bis (dimethyl acetal) as described in Table 1. Adjust the malondialdehyde (MDA) curve according to tissue type or suspected damage level.
8. Express the results as nmol MDA eq·mg⁻¹ protein.
Superoxide dismutase antioxidant enzyme microassay (SOD)¹⁸
1. Use a 96-well plate. Add 147 µL of 1 M TRIS/5 mM HCl EDTA pH 8 into two wells as blanks. Add 144 µL of 1 M TRIS/5 mM HCl EDTA pH 8 into other wells by duplicate.
2. Take 3 µL from the supernatant and add it to the sample wells. Gently mix the contents on the plate several times.
3. Add 3 µL of 10 mM pyrogallic acid to each well within 30 s. Mix gently immediately.
4. Measure the absorbance at T0 (time = 0 s) and T10 (time = 10 s), at 420 nm and 25 °C.
5. Determine SOD by calculating the percentage of pyrogallol inhibition in the sample using the following equation:
  
  Where
  x% = percentage of oxidation of pyrogallol by SOD in the sample; therefore, oxidation of pyrogallol is equal to 100 – x%
  NOTE: Calculation of the SOD activity considering 1 IU is the volume that inhibits 50% of the pyrogallol oxidation as described below:
  
  Where
  y = sample volume on milliliter (inhibits 50% of pyrogallon)
  50% = percentage of inhibition of pyrogallol equals 1U of SOD
  0.003 = volume in milliliter of the sample
  100 – x% = inhibition of pyrogallol in percentage by the sample
6. Finally, determine SOD activity with the equation:
  
  SOD = activity of SOD in international units per microgram of protein
  Y = sample volume in that inhibits 50% of pyrogallol
  100 = factor of conversion from deciliter to milliliter.
  protein = protein concentration obtained from Bradford's quantification is expressed as micrograms per milliliter; it is necessary to divide by 10 to convert to grams per deciliter
Catalase antioxidant enzyme microassay (CAT)¹⁹^,²⁰
1. Use a 96-well microplate. Add 20 µL of sample supernatant into wells (by duplicate).
2. Add 20 µL of fresh catalase (200 µg/mL) into wells as a standard (by duplicate). Add 100 µL of 50 mM PBS pH 7.8 to the sample and blank wells.
3. Add 100 µL of 90 mM (30%) H₂O₂ into wells to start the reaction. After adding H₂O₂, read absorbance each 15 s for 2.5 min at 240 nm.
4. Calculate activity using the equation:
Glutathione peroxidase enzyme microassay (GPx)²¹
1. Use a 96-well microplate.
2. Mix 240 µL of 0.1 M GSH solution, 1 200 µL of 10 U/mL GSH-Rd solution, and 1 200 µL of 4 mM NADPH. Keep the solution on ice.
3. Add into wells 100 µL of 50 mM TRIS/HCl 5 mM EDTA pH 7.6. Add 1 µL of supernatant sample in duplicate. Tap the microplate and gently mix.
4. Add 50 µL of the mix solution (step 4.5.2) and mix gently.
5. Add 20 µL of the 7 mM t-butyl hydroperoxide solution into wells to start the reaction (it takes approximately 15 s to start the reaction in 16 duplicated samples). Quickly mix the microplate.
6. Monitor absorbance at every 1 min interval for 5 min at 25 °C at 340 nm.
7. Calculate GPx activity with the equation:
  
  Where
  GPx = activity in millimolar per minute per microgram of protein
  ΔAbs_340/min= Mean absorbance in delta
  10³ = molar to millimolar conversion
mg prot = protein concentration from Bradford's determination expressed in microgram per microliter
1. Protein quantification by Bradford's analysis²²
2. Perform a standard curve from bovine serum albumin (BSA) solutions, set from stock solution 1 µg/µL as shown in Table 2.
3. Use a 96-well microplate. Add 190 µL of Bradford's reagent in the sample and standard wells.
4. Add 10 µL of BSA in standard wells by duplicate. Add 10 µL of supernatant into the sample wells by duplicate.
5. Gentle mix with the pipette tip.
6. Read absorbance at 595 nm. Quantify the protein concentration with the standard curve.

Representative Results

The results of the study reveal that heavy metals, specifically Aluminum (Al), Iron (Fe), and Zinc (Zn), have a detrimental impact on the environment, as evidenced by Figure 2. The detection of high levels of heavy metals in both tissue and water samples collected from all sites has led to an unfavorable outcome. Outliers were detected, with a Bioaccumulation Factor (BAF) of 600, notably in mining-intensive areas such as the Extoraz River (sites PB, EP, RQ, and BC shown in Figure 3). Remarkably, in some study sites where zinc concentrations in the water were abnormally high (PB), it was not possible to find specimens of C. texanus. This indicates that the bioaccumulation threshold has probably been surpassed.

Figure 2: Boxplot of Bioaccumulation Factor (BAF) assessed in Corydalus texanus individuals sampled along 15 study sites. Bioaccumulation factor (BAF) was calculated for Al, Fe, and Zn metals according to analyzing water samples and exoskeletons of C. texanus individuals. Please click here to view a larger version of this figure.

Since SGBR is a protected natural area, it is essential to ensure that no environmental changes occur that could impact the sentinel organism. However, gradients in the responses of oxidative stress biomarkers were observed (Figure 3). According to the assessment, the sites with the lowest levels of cell membrane damage, as evidenced by LPO levels, were EN, SM, and CN. These same sites displayed a low level of SOD activity, which serves as the primary enzyme in the body's defense against oxidative stress. This suggests that there is minimal oxidative stress occurring in these locations, and therefore, interventions that do not affect sentinel organisms could be considered. In contrast, the activity of GPx was observed to be significantly lower in various sites, namely EP, RQ, BC, and ES, where high levels of LPO were recorded. This observation suggests that the organism is responding to the stressful conditions mainly caused by mining. Upon evaluating the early-warning markers within this particular organism, it has been discovered that certain sites hold low and high levels of impact. These findings effectively showcase the utility of utilizing this species as an unconventional sentinel.

Figure 3: Boxplot of the assessed biomarker responses in specimens of Corydalus texanus across 15 sampling sites in three main rivers flowing into a basin in Mexico (Sierra Gorda Biosphere Reserve) during the dry and wet seasons. The responses were measured using three biomarkers: (A) lipid peroxidation level (LPO) reflecting cellular early damage, (B) antioxidant response of first-line cellular defense superoxide dismutase (SOD), and (C) antioxidant response of cellular defense by glutathione peroxidase (GPx). Red arrows indicate the absence of biomonitor individuals or a very limited number of specimens, which occurred only once. Please click here to view a larger version of this figure.

Tube	200 µM of MDA bis (µL)	Ultrapure water (µL)	MDA bis concentration (µM)
1	0	1000	0
2	12.5	987.5	2.5
3	25	975	5
4	50	950	10
5	100	900	20
6	200	800	40
7	400	600	80
8	800	200	160

Table 1: MDA concentration needed to construct the MDA concentration curve.

Concentration (µg/µL)	Stock solution (µL)	Ultrapure water (µL)
0	0	50
0.1	5	45
0.2	10	40
0.4	20	30
0.8	40	10
1	50	0

Table 2: BSA concentration for protein quantification curve.

Discussion

Although the use of C. texanus is optimal for evaluation, it is necessary to consider several aspects of its use and collection. Chosen study sites prove challenging, owing to several factors such as unfavorable weather conditions, geographical inaccessibility, high aridity levels, or insufficient security protocols in selected regions. Stated constraints and limitations can often present challenges when conducting fieldwork. When evaluating specific regions, particularly those in tropical streams, obtaining samples can be challenging. Although Barbour²³ guidelines were adhered to for this purpose, there may be obstacles to adapting protocols in some ecosystems due to their particular traits. As previously stated, collecting samples in tropical lotic environments presents a variety of challenges due to regional and local factors. These factors encompass the high levels of environmental heterogeneity, substrates with high variation, catchment, width, depth, flow, riparian vegetation, and the broad range of physical-chemical conditions²⁴. Consequently, obtaining a uniform size for specimens can prove challenging, as they are naturally influenced by a stated factor range, particularly in response to seasonal changes. Consequently, standardizing their size can be a complex undertaking. Upon successful completion of the fieldwork, the subsequent laboratory procedures are facilitated, allowing further analysis.

The implementation of an early-warning assessment in C. texanus has demonstrated its viability in mirroring impacts in the context of aquatic ecosystems. In this regard, identifying aquatic macroinvertebrates as reliable indicators of human impact has proven to be a practical approach²⁵^,²⁶. The current research has shown that C. texanus serves as a highly effective non-traditional model for rapidly assessing environmental conditions. In the case of the current study, it demonstrated that C. texanus showed variation in responses to face heavy metal pollution derived from mining. Added effects of habitat alterations allow recognition of a high sensitivity grade in C. texanus. While evidence of mining activity was present in the area, traditional pollution indicators, such as the diversity index calculated in Rico-Sanchez et al.²⁷, failed to recognize the impact of heavy metal pollution in core zones or conservation sites. However, changes were observed in areas such as BC or SM, which are situated in core zones. Although natural protected areas are effective for conservation, the findings regarding C. texanus indicate that early warning signals of damage are already occurring unnoticed. The inclusion of non-conventional and indigenous fauna must be advocated to research protocols and prospective regulations within their respective nations, particularly in tropical regions where river ecosystems differ significantly from those in temperate areas²⁸. The use of a non-conventional biomonitor such as C. texanus may help improve the accuracy and relevance of research findings and enhance conservation efforts for these important species and their habitat.

The use of Corydalus sp. showed, as well, high sensitivity to diverse impacts from human activities (i.e., agriculture impacts such as land use change and use of agrochemicals), as observed in Filobobos River (a place towards the Gulf of Mexico basin)⁷. The study in question highlights the significant role of calcium in inducing stress on Corydalus sp. due to the heightened increase in LPO levels under abnormally hardened waters in the Filobobos River. These findings, together with the present, evidenced the usefulness of the Corydalus genus in assessing aquatic ecosystems at intertropical latitudes. However, before assessing a specific aquatic ecosystem, it is necessary to have prior knowledge of the study area. By conducting a thorough analysis, the optimal research locations must be determined to gather the most extensive and complete data.

The effectiveness of laboratory work is heavily dependent on the use of appropriate collection techniques. Collecting larger specimens can prove beneficial when conducting dissection due to the increased amount of soft tissue and exoskeleton available for analysis. However, it is important to note that seasonal variations may affect fatty tissue accumulation, making it challenging to separate the soft tissues and exoskeletons during temporal studies. In such cases, focusing on each individual's gills and available muscles may be advisable. Obtaining a significant number of individuals may represent a critical challenge. Due to the previously stated variations, getting enough tissue to assess the heavy metal content and biomarkers' response could be more challenging. The present study showed an example of this case because it was not possible to assess catalase in samples from the SGBR. Previous to the present protocol, the assessment of catalase demanded a high amount of tissue; nevertheless, the current proposal for catalase determination offers a minimum tissue amount for their assessment.

The current protocol proposal offers a suitable chance to take a feasible approximation of the ecological integrity using common hellgrammites in aquatic ecosystems. It provides crucial information for identifying punctual pollution or indirect deleterious effects of human impacts, allowing opportune information to stakeholders, ecologists, and aquatic scientists. Although the cost of the current protocol has been significantly reduced, it still remains relatively expensive due to the necessity of several reagents and the use of specialized equipment. Furthermore, the requirement of specialized equipment limits the number of locations where the complete assay can be performed.

Disclosures

The authors have nothing to disclose.

Acknowledgements

The authors would like to express their sincere gratitude to CONAHCyT for providing the FONINS P 1931 grant, which greatly facilitated their research efforts. They would also thank the Secretaría de Investigación y Posgrado at Instituto Politécnico Nacional for the invaluable support provided through the SIP project grant (20200577). In addition, the first author wishes to acknowledge the generous post-graduate scholarship awarded by CONAHCyT, which enabled the team to conduct field trips and gather essential data. Finally, the authors would like to express their appreciation for the invaluable assistance of María Teresa García Camacho in the laboratory, without whom this project would not have been possible.

Materials

Analytical balance of 220 g	Ohaus	PR224/E	This balance is useful for weighing the extracted tissue from specimens.
Chest waders	LaCrosse	700152M	We recommend using waders for sample collection. Alternatively, you can also use boots with rubber hip boots for sampling.
Cutting board	True	TRUE915121	It is recommended to use white and plastic boards.
Forceps	DR Instruments	112	It is recommended to use a 12 pul forceps made of stainless steel.
Inductively Coupled Plasma-Optical Emission Spectroscopy System	Perkin Elmer	7300 DV	A device for quantifying heavy metals using spectroscopy.
Kick net	LaMotte	0021-P	An alternative method for making a kick net involves manually crafting one using a mesh with a thickness of 500 micrometers.
Liquid Nitrogen	NA	NA	NA
Liquid Nitrogen Dewar Static Cryogenic Container	BestEquip	DF0504	It is recommended to use an aluminum tank with canisters.
Mortar and Pestle Set	Cole-Parmer	EW-63100-54	This is a porcelain mortar and pestle used for grinding dry tissues.
Multiwave GO Plus	Anton Paar	C93IP001EN-E	Multiwave is a useful tool for digesting multiple samples.
Oven for drying	Fisher scientific	506G	An incubator oven, also known as a dry tissue oven, is essential for drying tissues at temperatures of at least 80°C.
Precision scalpel	Xcelite by Weller	037103-48768	It is recommended to use a scalpel made of aluminum.
Tissue Homogenizer (tearer)	Kopro	K110000	It is recommended to use a tissue tearer with a base. Some companies offer ultrasonic tearers, which may be the optimal choice.
Ultra-Low Temperature Chest Freezer	REVCO	CA89200-384	Many companies provide freezers, but it is recommended to choose one with a storage temperature of at least -40°C.
Wide mouth plastic bottles	United Scientific	81900	Using polypropylene bottles with wide caps and mouths is strongly recommended.

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