Revista de Biología Tropical, ISSN: 2215-2075, Vol. 72: e56670, enero-diciembre 2024 (Publicado May. 21, 2024)

Aquatic macroinvertebrate community and water quality

in the Tambo River, Arequipa, Perú

Pastor Coayla-Peñaloza1; https://orcid.org/0000-0002-2317-9416

André Alexander Cheneaux-Diaz1; https://orcid.org/0000-0002-7148-0174

Claudia Viviana Moreno.Salazar1; https://orcid.org/0000-0001-5124-5663

Cynthia Elizabeth Cruz-Remache1; https://orcid.org/0000-0001-6178-5129

Cristina Damborenea2, 3*; https://orcid.org/0000-0002-6411-1282

1 Universidad Nacional de San Agustín, Arequipa, Perú; pcoaylap@unsa.edu.pe, acheneaux@unsa.edu.pe,

claudiavivianamore@gmail.com, ccruz.rem@gmail.com.

2 División Zoología de Invertebrados, Facultad de Ciencias Naturales y Museo, Universidad Nacional de La Plata,

Argentina; cdambor@fcnym.unlp.edu.ar (*Correspondence).

3 Consejo Nacional de Investigaciones Científicas y Técnicas, Argentina.

Received 27-IX-2023. Corrected 14-III-2024. Accepted 02-V-2024.

ABSTRACT

Introduction: The River Tambo basin is one of the main hydrographic systems of the Peruvian western water-

shed, being a source of development for agriculture, agroindustry, livestock, and domestic use in the Tambo

Valley and Arequipa City.

Objective: To analyze the structure of macroinvertebrates in River Tambo, Perú and assess the water quality

through this community.

Methods: Five sampling events were conducted between December 2018 and November 2019 in 12 stations,

using a Surber net (500 μm). Macroinvertebrates were identified at a family level. To assess community structure,

richness, Simpson’s dominance index (D), Pielou’s evenness (J’), and true diversity of order 1 were determined. A

nMDS based on the Bray-Curtis index was used to evaluate dissimilarity. To check for differences in community

structure, ANOSIM and two-way MANOVA were used. SIMPER was used to establish family contribution to

sample similarity. Relations between physicochemical and biological variables were determined by CCA. ABI

index was applied to assess ecological quality.

Results: 32 families were recognized, being the most abundant: Baetidae, Chironomidae, Leptohyphidae,

Simuliidae, Hydroptilidae, and Elmidae. The middle and low zones of the basin showed the highest and lowest

diversity respectively. There were significant differences (P < 0.05) in the community structure indices among

the 12 stations differed. There was a higher similarity among the 12 stations in December. ABI scores increased

from the low to the middle part of the river, which showed the highest ecological quality.

Conclusion: Macroinvertebrate communities from River Tambo reflect ecosystem conditions. Environments

impacted by human activities show lower diversity and ecological quality, due to the structure, habitat, and water

quality of the river being altered.

Key words: bioindicators; ecological quality; ABI index; desert; high-Andean.

https://doi.org/10.15517/rev.biol.trop..v72i1.56670

ACUATIC ECOLOGY

2Revista de Biología Tropical, ISSN: 2215-2075 Vol. 72: e56670, enero-diciembre 2024 (Publicado May. 21, 2024)

INTRODUCTION

Rivers are dynamic and multifunctional

systems characterized by the presence of drain-

age networks, with different courses and a high

degree of environmental heterogeneity (Custo-

dio & Chanamé, 2016), which contribute con-

siderably to the economic growth of a country

and can be used for different purposes such as

fishing, irrigation, transport, power generation,

tourism, and recreation (Galarza et al., 2021).

Therefore, anthropic pressures on these systems

alter their water quality, producing high levels

of pollution (Liévano-León & Ospina-Torres,

2013; Meneses-Campo et al., 2019), which

affect public health and ecosystem services.

Perú has not been an exception to this

problem, which has led to alterations in the

natural dynamics of hydrographic basins, and

therefore to losses or modifications in the

aquatic diversity of these systems (Gamarra et

al., 2018). Based on these diversity changes,

different methodologies have been developed

using a wide variety of organisms, from bacteria

to fish (Barbour et al., 1999; Oscoz et al., 2006),

among which macroinvertebrate monitoring

stands out, for the purpose of reflecting the

disturbances occurred in water bodies (López-

Mendoza et al., 2019).

Aquatic macroinvertebrates are in close

relation with the environment they inhabit.

Any change in the environmental conditions is

manifested in the structure and composition of

the aquatic invertebrate community that inhab-

its it (Terneus et al., 2012). They reflect envi-

ronmental changes in relatively short periods,

contributing to environmental and ecological

analyses of the state of the aquatic system, and

are therefore used in environmental assessment

studies (Hauer & Lamberti, 2011).

The hydrographic basins of the Peruvian

Pacific watersheds are characterized by dry

land conditions, which entails water shortage

problems for human consumption. These arid

and semi-arid ecosystems are of great economic

importance for Perú since they are used for

many anthropogenic activities (Arana-Maestre

et al., 2021). In the last 35 years there have

RESUMEN

Comunidad de macroinvertebrados acuáticos y calidad del agua en el río Tambo, Arequipa, Perú

Introducción: La cuenca del rio Tambo es uno de los principales sistemas hidrográficos de la vertiente occidental

del Perú y fuente de desarrollo para la agricultura, agroindustria, ganadería y consumo doméstico en el valle de

Tambo y la ciudad de Arequipa.

Objetivo: Analizar la estructura de macroinvertebrados en el río Tambo, Perú y evaluar la calidad del agua a

través de esta comunidad.

Métodos: Entre diciembre del 2018 y noviembre del 2019 se realizaron cinco muestreos en 12 estaciones,

empleando una red Surber (500 μm). Los macroinvertebrados se identificaron a nivel de familia. Se registró la

riqueza, dominancia de Simpson, equidad de Pielou, y diversidad verdadera de orden 1, para evaluar la estruc-

tura de la comunidad. Para estimar la similitud, se utilizó nMDS (índice de Bray-Curtis). Para verificar si existen

diferencias en la estructura comunitaria, se empleó MANOVA de dos vías y ANOSIM. Para establecer la contri-

bución de las familias a la similitud entre muestras, se utilizó SIMPER. La relación entre variables fisicoquímicas

y biológicas se determinó con ACC. Se aplicó el índice ABI para evaluar la calidad ecológica.

Resultados: se reconocieron 32 familias, siendo las más abundantes: Baetidae, Chironomidae, Leptohyphidae,

Simuliidae, Hydroptilidae y Elmidae. La mayor y menor diversidad se presentó en la parte media y baja de la

cuenca respectivamente. Existieron diferencias significativas (P < 0.05) de los índices de estructura comunitaria

entre las 12 estaciones. Se evidenció mayor similitud entre las 12 estaciones en diciembre. Los puntajes del índice

ABI se incrementan de la parte baja del río a la media, que se presentó la mejor calidad ecológica.

Conclusión: Las comunidades de macroinvertebrados del río Tambo reflejan el estado del ecosistema. Los

ambientes con impacto por actividad humana registran menor diversidad y calidad ecológica, ya que se altera la

estructura, hábitat y calidad de agua del río.

Palabras clave: bioindicadores; calidad ecológica; índice ABI; desierto; alto andino.

Revista de Biología Tropical, ISSN: 2215-2075, Vol. 72: e56670, enero-diciembre 2024 (Publicado May. 21, 2024)

been modifications in minimum runoff in sev-

eral Pacific basins that are attributed to human

activity (Lavado et al., 2012). One of them is

River Tambo, located on the Southwestern

flank of the Andean Mountain range, which

varies between 0-5 800 m above sea level in alti-

tude. It forms at the confluence of the Ichuña

and Paltiture Rivers. It flows through the locali-

ties of Yunga, Lloque, Quinistaquillas, El Fiscal,

Cocachacra, and Deán Valdivia. The lower

basin is exclusively used for agriculture. On

the high zone of the basin is situated the auric

project Chucapaca; in the middle zone, Pampa

Minera Cobre, and in the low zone, the cuprif-

erous project Tía María (Carpio-Fernández &

Peña, 2020; SENAMHI, 2009); and between

Moquegua and Puno, is located the auric mine

Florencia-Tucari. Water pollution from min-

ing waste in the Moquegua department and

the ecological debt generated by hydrological

pollution in River Tambo put the population

and agricultural, livestock, and hydrobiological

resources settled on the lower part of the basin

at risk of contamination (INDECI, 2021).

In view of this situation, the identification

and use of macroinvertebrates as bioindica-

tors that reflect the current ecological state

and water quality of River Tambo is proposed,

and thus generate a useful tool for integrated

management of hydric resources by compe-

tent authorities such as Autoridad Nacional

del Agua (ANA, 2019), municipalities, water

commissions, agricultural councils, etc., to be

able to detect water quality issues early, provid-

ing potentially impacted areas with alternative

solutions. The aim of this research is to analyze

the structure of aquatic macroinvertebrates in

River Tambo, Perú and assess the water quality.

MATERIALS AND METHODS

Study area: The study was carried out on

the main course of River Tambo (Fig. 1). The

main contributors to its hydrographic network

Fig. 1. Sampling stations in the River Tambo basin, Arequipa, Perú.

4Revista de Biología Tropical, ISSN: 2215-2075 Vol. 72: e56670, enero-diciembre 2024 (Publicado May. 21, 2024)

are the rivers Carumas, Coralaque, Ichuña, and

Paltuture. The mean altitude of the basin is

3 302 m.a.s.l., with a 7.46 % mean slope, a 1.72 %

main course slope, and a 329.18 km length.

Sampling: Sampling took place between

December 2018 and November 2019 (five

events) in 12 stations on the main course of the

river (Table 1). Due to poor accessibility, it was

not possible to sample E1 in August. Stations

E1, E2, E3, E11, and E12 showed modifications

from their natural course. A 150 m sampling

zone was delimited on the river margin, within

which sampling spots were selected. Three

samples were taken per station, using a 500 µm

mesh diameter Surber sampler net. Samples

were stored in 500 ml containers and fixed in

4 % formalin.

Identification: In the laboratory, the sam-

ples were rinsed with water through a 500

µm sieve and preserved in 70 % alcohol for

identification (Domínguez & Fernández, 2009;

Roldán-Pérez, 2003). Taxonomic identification

was done to family level following the keys by

Merritt et al. (2008), Domínguez and Fernán-

dez (2009), Prat et al. (2011), and Thorp and

Lovell (2015).

Physicochemical variables: The following

physicochemical variables were measured in

each sampling station directly with a Hanna

HI9829 multiparameter probe: dissolved oxy-

gen, pH, conductivity, and temperature.

Data analysis: The structure of the mac-

roinvertebrate community was assessed using

richness (number of families) (S), abundance

(number of individuals of a family/m2), Simp-

son’s dominance index (D), Pielou’s evenness

(J’), and true diversity (D1) (Moreno, 2001).

A multivariate analysis of variance (MANO-

VA) was used to compare community indices

between sampling sites, and Tukey’s test was

used for multiple post hoc comparisons. A

canonical correspondence analysis (CCA) was

performed to assess the relation between mac-

roinvertebrates and physicochemical variables.

An analysis of similarities (ANOSIM) (with

9 999 permutations) was used to test for dif-

ferences in community composition between

sampling zones and the statistical significance

of the groupings. Similarity percentage analysis

(SIMPER) and non-metric multidimensional

scaling (nMDS) based on the Bray-Curtis index

were used to explore variations in macro-

invertebrate taxa composition among the 12

Table 1

Location of sampling stations in the River Tambo basin, Arequipa, Perú.

Station Basin

Zone

Coordinates Altitude

(m.a.s.l.)

Characteristics

(Substrate)

Latitude Longitude

E1 Lower 17°07’51’’ S 71°46’08’’ W 43 Sand

E2 Lower 17°04’03’’ S 71°44’00’’ W 103 Sand

E3 Lower 17°01’30’’ S 71°41’23’’ W 156 Sand

E4 Lower 16°59’23’’ S 71°38’03’’ W 227 Pebbles

E5 Lower 16°5’940’’ S 71°34’39’’ W 282 Pebbles

E6 Lower 17°01’57’’ S 71°31’14’’ W 378 Pebbles

E7 Middle 16°46’09’’ S 70°58’43’’ W 1332 Pebbles

E8 Middle 16°46’40’’ S 70°55’06’’ W 1452 Rock

E9 Middle 16°46’15’’ S 70°51’38’’ W 1587 Rock

E10 Middle 16°45’39’’ S 70°49’32’’ W 1663 Pebbles

E11 Higher 16°28’02’’ S 70°40’10’’ W 2487 Rock

E12 Higher 16°26’29’’ S 70°48’43’’ W 2594 Rock

Revista de Biología Tropical, ISSN: 2215-2075, Vol. 72: e56670, enero-diciembre 2024 (Publicado May. 21, 2024)

sampling stations. The analyses were carried

out on EXCEL® and PAST version 4.13 (Ham-

mer et al., 2001).

River ecological quality: The ecological

quality of the river was determined using the

ABI index (Andean Biotic Index) (Medina-

Tafur et al., 2010). In this index, families of

aquatic macroinvertebrates are ordered from

least to greatest tolerance to environmental

disturbances in 10 groups, with scores that vary

between 10 and 1. The score 10 corresponds

to the most sensitive families and the score 1

to the most tolerant families. The sum of the

scores for all families provides the total ABI

index score.

RESULTS

Physicochemical parameters: Superficial

water temperature varied between 15.48 ºC

(E12) and 24.04 ºC (E4). Values for pH ranged

from 7.96 (E6) to 8.61 (E5). Electric conductiv-

ity (EC) varied between 2 239.67 and 3 645.11

μS/cm recorded at E7 and E4 respectively.

Dissolved oxygen concentration (DO) varied

between 5.5 mg/L at E1 and 9.7 mg/L at E8.

Finally, total dissolved solids (TDS) ranged

between 970.33 ppm (E10) and 2 632.08 ppm

(E6) (Table 2).

Macroinvertebrates diversity: The three

families with the highest presence and total

abundance were Chironomidae (8 326 ind/m2),

Baetidae (6 209 ind/m2), and Leptohyphidae

(4 684 ind/m2). Other families stood out also

occurring at every station, but with a lower

density, standing out Simuliidae (3 292 ind/

m2), Hydroptilidae (2 103 ind/m2), and Elmi-

dae (1 429 ind/m2) (Table 3).

The highest richness was registered at sta-

tions E9 (December 2018 and November 2019)

and E10 (June and August 2019) with 15 fami-

lies recorded. Stations E1 (May 2019) and E2

(December 2018) showed the lowest richness,

with three and six families respectively. The

highest dominance values were recorded at

station E1 (May and June 2019): 0.93 and 0.84

respectively. Stations from the middle (E7, E8,

E9, and E10) and high (E11 and E12) zones

of the river showed low dominance values.

High evenness values (> 0.5) were recorded at

stations E4, E5, E6, and E12 in every month.

The highest true diversity was recorded at

E3 (December 2018), E6, and E7 (November

2019) with 7.79, 7.68, and 7.98 effective species

respectively. Station E1 (May and June 2019)

showed the lowest true diversity, with 1.20 and

1.54 effective species respectively (Fig. 2).

The two-way MANOVA test showed sig-

nificant differences (P < 0.05) in the values of

Table 2

Mean monthly values for physicochemical parameters in River Tambo, Arequipa Region, Perú.

Station Temp.[°C] pH EC[µS/cm] DO(mg/L) TDS [ppm]

E1 21.65 ± 2.19 8.38 ± 0.20 2 230.71 ± 743.93 7.44 ± 2.76 1 110.71 ± 375.00

E2 21.61 ± 2.98 8.38 ± 0.13 2 797.92 ± 1 498.04 7.43 ± 2.85 1 398.83 ± 748.79

E3 22.83 ± 2.84 8.52 ± 0.10 2 141.96 ± 1 858.80 7.44 ± 3.06 1 345.92 ± 686.58

E4 24.02 ± 3.58 8.40 ± 0.30 2 943.17 ± 1 573.15 8.89 ± 1.36 1 471.67 ± 786.70

E5 22.87 ± 3.03 8.55 ± 0.12 2 238.93 ± 755.24 9.09 ± 0.75 1 115.73 ± 380.24

E6 21.88 ± 3.28 8.07 ± 0.80 2 442.07 ± 1 497.50 9.27 ± 1.05 2 431.73 ± 2 327.94

E7 19.99 ± 2.61 8.56 ± 0.08 2 101.20 ± 766.35 7.18 ± 2.93 1 050.60 ± 383.16

E8 19.76 ± 2.48 8.46 ± 0.08 2 089.47 ± 801.99 6.74 ± 2.68 1 044.53 ± 401.06

E9 19.31 ± 2.16 8.43 ± 0.11 2 035.87 ± 935.76 7.02 ± 2.96 1 018.20 ± 467.68

E10 18.70 ± 2.14 8.37 ± 0.12 1 964.80 ± 832.06 6.62 ± 2.60 862.87 ± 532.31

E11 16.33 ± 6.32 8.61 ± 0.37 2 641.27 ± 1 203.69 7.20 ± 1.26 1 334.33 ± 577.81

E12 16.08 ± 4.26 8.57 ± 0.32 2 609.93 ± 1 433.80 7.62 ± 1.64 1 349.53 ± 648.48

6Revista de Biología Tropical, ISSN: 2215-2075 Vol. 72: e56670, enero-diciembre 2024 (Publicado May. 21, 2024)

community structure indices, regarding sta-

tion, month, and the interaction between them

(Table 4). According to Tukey’s test, in Novem-

ber 2019 there were significant differences (P <

0.05) in dominance, evenness and true diversity

in relation to the other four months; December

2019 and May 2018 recorded a significant dif-

ference (P < 0.05) in richness in comparison

to the other months. Station E1 differed sig-

nificantly (P < 0.05) from the other 11 stations

Table 3

Mean abundance of aquatic macroinvertebrates (ind/m2) during the sampled period in

River Tambo, Arequipa Region, Perú.

E1 E2 E3 E4 E5 E6 E7 E8 E9 E10 E11 E12

Platyhelminthes

Dugesiidae 000110000000

Nematoda 101101010110

Annelida

Glossiphoniidae 000100000000

Lumbriculidae 2 9 12 56 19 10 0 0 1 0 3 0

Mollusca

Physidae 0 0 3 7 0 64 22 4 7 45 0 0

Arthropoda Malacostraca

Palaemonidae 971200000100

Arthropoda Copepoda

Centropagidae 000000400001

Cyclopidae 010100000000

Arthropoda Ostracoda 0 16 58 44 24 20 11 38 64 24 13 7

Arthropoda Acari

Limnesiidae 002130335272

Limnozetidae 0001127000000

Arthropoda Hexapoda

Baetidae 17 44 94 96 343 382 613 1 003 1 425 1 427 304 461

Blephariceridae 0 0 0 0 0 4 49 164 351 412 38 13

Ceratopogonidae 6 29 1 2 7 2 9 8 7 9 26 7

Chironomidae 867 427 1 126 1 499 644 686 354 414 376 705 946 282

Coenagrionidae 011111000100

Dytiscidae 0 0 0 1 1 1 4 3 7 0 1 0

Elmidae 41 96 156 287 378 190 50 41 76 99 8 7

Gomphidae 000000211100

Gripopterygidae 000000000400

Hydrobiosidae 0000000000337

Hydrophilidae 6 28 23 42 68 98 64 64 222 113 0 2

Hydroptilidae 10 24 105 279 546 193 143 240 210 194 135 24

Leptohyphidae 55 30 138 131 607 339 1 085 680 1 383 230 1 5

Libellulidae 000000000200

Limnephilidae 1 1 6 39 100 102 83 55 215 52 19 79

Mesovelidae 2712721530110

Muscidae 2 2 14 12 7 10 53 51 26 40 83 12

Psychodidae 000100051021

Simuliidae 22 25 39 221 119 330 118 352 1 224 751 47 44

Stratiomyidae 000010000000

Tabanidae 010060000040

Revista de Biología Tropical, ISSN: 2215-2075, Vol. 72: e56670, enero-diciembre 2024 (Publicado May. 21, 2024)

in dominance and true diversity values. Even-

ness was also significantly different (P < 0.05)

between E1 and E2 and between them and the

rest of the stations. Considering richness val-

ues, stations from the middle zone of the river

(E7, E8, E9, and E10) are significantly different

(P < 0.05) from some of the stations of the

lower (E1, E2 and E3) and higher zone of the

river (E11 and E12).

Fig. 3 shows the temporal heterogeneity

of the aquatic macroinvertebrate community

in River Tambo. There were significant differ-

ences (R = 0.16, P < 0.05) between the lower

and middle, and middle and higher zones. At

a temporal level, nMDS showed similar group-

ings between the 12 stations for May and June

2019, while the distance between points widens

in August and November 2019. In December,

the difference among the 12 stations was evi-

dent, and the polygon formed by their distances

was the largest.

The nMDS analysis, at a temporal and

spatial level, showed some grouping in the sta-

tions from the lower, middle, and higher zones

of the river. Spatially, lower zone stations (E1,

E2, E3, E4, E5, and E6) showed heterogene-

ity between them, while in the higher zone

(E11 and E12) there was a lower heterogeneity

(Fig. 4). The similarity test (ANOSIM) shows

Fig. 2. Community structure indices in River Tambo, Arequipa, Perú. A. Richness (N); B. Dominance (D); C. Pielou’s

evenness (J); D. True diversity (D1).

Tabl e 4

Two-way MANOVA test for community structure indices

in River Tambo, Arequipa Region, Perú.

DF F P

Month Richness 4 9.52 < 0.001

Dominance 4 9.78 < 0.001

Evenness 4 5.57 < 0.001

True Diversity 4 19.02 < 0.001

Station Richness 11 11.02 < 0.001

Dominance 11 7.03 < 0.001

Evenness 11 4.04 < 0.001

True Diversity 11 5.71 < 0.001

Month * Station Richness 43 3.01 < 0.001

Dominance 43 2.28 < 0.001

Evenness 43 2.53 < 0.001

True Diversity 43 2.18 0.001

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Fig. 3. Non-parametric Multidimensional Scaling analysis (nMDS) by month in River Tambo, Arequipa, Perú. December 2018

(light blue), May 2019 (orange), June 2019 (black), August 2019 (yellow), and November 2019 (blue). Stress value = 0.215.

Fig. 4. Non-parametric Multidimensional Scaling Analysis (nMDS) by sampling station in River Tambo, Arequipa, Perú.

Lower zone (red), middle zone (blue), and higher zone (green). December, X; May, *; June, +; August O; November #. Stress

value = 0.215.

Revista de Biología Tropical, ISSN: 2215-2075, Vol. 72: e56670, enero-diciembre 2024 (Publicado May. 21, 2024)

that the macroinvertebrate composition does

not differ significantly (R = 0.16, P > 0.05)

between stations from the lower (E1, E2, E3,

E4, E5, and E6), middle (E7, E8, E9, and E10)

and higher (E11 and E12) River Tambo basin,

except between E1 and E6 where there were

significant differences (P < 0.05). Every month

showed significant differences (R = 0.18, P <

0.05), except for August and November.

CCA showed that stations E11 and E12

are related to low temperatures, and stations

E1, E2, E3 and E4 to high temperatures, pH,

and conductivity values. Stations E7, E8, and

E9 associated with low conductivity and high

dissolved oxygen values. Whereas Elmidae was

related to high temperatures and dissolved oxy-

gen; Leptohyphidae, Simuliidae and Baetidae

were related to low conductivity values; Chi-

ronomidae and Baetidae to high and low tem-

peratures respectively; and to a lesser extent,

Hydroptilidae to temperature and Chironomi-

dae to conductivity (Fig. 5).

Regarding family composition between the

three zones of the basin, 85 % of total dissimi-

larity was determined. Generally, Baetidae and

Chironomidae contributed individually more

than 20 % of this dissimilarity, except in the

middle zone, where Leptohyphidae had the

highest individual contribution (> 25 %), and

in the lower zone, where Baetidae had less than

10 % of individual contribution (Table 5).

The lowest scores of the ABI index were

recorded at station E1 (May 2019, the value

was 9) with a poor quality average value (Table

6). The highest index scores were recorded in

November at stations E7, E8, E9, and E10, the

latter having the highest score recorded and

good quality (June 2019, value 76). Stations

E11 and E12 showed a good and moderate

average quality respectively. The results show

Fig. 5. Canonical correspondence analysis (CCA) by sampling stations on River Tambo Arequipa, Perú. Lower zone (red),

middle zone (blue) and higher zone (green). EC, electric conductivity; DO, dissolved oxygen concentration; TDS, total

dissolved solids.

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an increase in the ABI index upriver from E1

to E10. At station E12, on the high zone of the

river, these indices decrease (up to 18 in June

2019) and remain at a moderate quality most of

the time (between 20 and 55) (Table 6).

DISCUSSION

The results of this study show the great-

est diversity in the upper and middle parts of

the River Tambo. The lower parts have less

diversity and richness of taxa due to physical-

chemical conditions, anthropic intervention,

and type of substrate. The ABI index shows an

increase upriver, from E1 to E10, indicating a

quality improvement upstream.

Physicochemical parameters in River

Tambo showed that dissolved oxygen, tempera-

ture, and conductivity are within category 3

standards for water environmental quality, used

for irrigation and animal watering (MINAM,

2017). According to our observations, dissolved

oxygen is within normal levels at stations E6,

E7, E8, and E9 as stipulated in D. S. N°004-

2017 (MINAM, 2017). All twelve stations in

this study showed high conductivity values.

Tabl e 5

SIMPER analysis per basin and basin zones of River Tambo Arequipa Region, Perú.

Family Contribution %

Basin Lower zone Middle zone Higher zone

Baetidae 26.44 9.14 22.99 27.59

Chironomidae 21.67 39.51 9.90 39.09

Leptohyphidae 15.35 11.13 27.37

Simuliidae 11.19 6.86 15.74 4.34

Hydroptilidae 15.58 8.08 5.80 6.13

Elmidae 5.23 12.53 - -

Blephariceridae - - 6.72 -

Limnephilidae - - - 6.41

Muscidae - - - 4.01

Total 85.46 87.25 88.53 87.57

Tabl e 6

Scores of ABI index for the biotic quality of River Tambo, Arequipa Region, Perú.

Station DEC-2018 MAY-2019 JUN-2019 AUG-2019 NOV-2019 Average QUALITY

E1 19 ll9 ll28 llSI ll37 ll23 llPoor

E2 16 ll25 ll42 ll41 ll40 ll33 llModerate

E3 35 ll36 ll51 ll42 ll43 ll41 llModerate

E4 51 ll27 ll57 ll35 ll36 ll41 llModerate

E5 53 ll41 ll49 ll61 ll43 ll49 llGood

E6 43 ll41 ll51 ll55 ll45 ll47 llGood

E7 47 ll48 ll63 ll58 ll64 ll56 llGood

E8 55 ll58 ll36 ll64 ll66 ll56 llGood

E9 64 ll48 ll44 ll56 ll72 ll57 llGood

E10 52 ll51 ll76 ll64 ll72 ll63 llGood

E11 60 ll35 ll43 ll74 ll48 ll52 llGood

E12 52 ll30 ll28 ll42 ll55 ll41 llModerate

l l Very good ll Good ll Moderate

ll Poor ll Very bad ll NI= No information

Revista de Biología Tropical, ISSN: 2215-2075, Vol. 72: e56670, enero-diciembre 2024 (Publicado May. 21, 2024)

Sediment ingress because of the lack of river-

side vegetation at all stations could be an expla-

nation for these high values (Reis-Oliveira et al.,

2014; Ternus et al., 2011). According to Rodier

(1998) and Meneses-Campo et al. (2019), the

River Tambo have high mineralization, since

the conductivity is higher than 1 000 µS/cm

and these values rise progressively downriver,

such as on stations E9, E8, E7, and E6 in this

study, located in the middle to low zone of the

river. Another possible cause of these high con-

ductivity values may be the ionic concentration

result of human activities (Castro et al., 1996).

On the other hand, temperature is one of the

factors that determine the physical properties

and the richness and distribution of macro-

invertebrate families (Bustamante-Toro et al.,

2008; Custodio & Chanamé, 2016).

Stations E1 and E2, showed the lowest

richness and diversity in the whole basin, prob-

ably due to the impact caused by the observed

destruction of habitats for community settle-

ment and the predominance of sandy substrates

(Burdet & Watts, 2009). Regarding stations E11

and E12 on the higher zone, where there was

also evidence of course modification, diversity

also showed low values, however, the dominant

substrate here was rocky. Generally, rivers with

sandy substrate harbor few species, with few

individuals per species (Arocena, 1998; Boc-

cardi, 2004; Chalar, 1994; Pintos et al., 1992),

given that it’s a specialized substrate, unstable

in water currents. By contrast, rocky substrates

tend to be richer than sandy ones, since they

provide more surface for the growth of the bio-

film on which various primary consumers feed

(Meza-Salazar et al., 2012).

At the stations located in the lower zone of

the river, Chironomidae was the most abundant

taxon. According to Butakka et al. (2016), this

family can inhabit a variety of habitats, from

pristine to highly polluted, and from freshwater

to hypersaline environments. Likewise, Pinder

(1995) and Oviedo-Machado and Reinoso-

Flores (2018) state that chironomids can colo-

nize a wide range of macro and microhabitats,

such as rapids, pools, submerged wood, sand,

gravel, pebbles, and roots, as well as utilize

fine sediments to produce tubular refuges.

According to Giraldo et al. (2014), at stations

with anthropic intervention by agriculture and

livestock raising, there is a greater abundance

of Diptera families, matching the observations

made in this study at stations from the lower

zone of the river.

The absence of riverside cover and in

some stations the presence of sandy substrates

could be responsible for the low representa-

tion of Trichoptera and Ephemeroptera in the

basin (Principe et al., 2019). Allan et al. (1997)

mention that sites deteriorated by deforesta-

tion and the change in soil use for productive

activities are related to the rise in sedimenta-

tion, reduction in the ingress of allochthonous

material, and consequently, the loss of habitat

heterogeneity. However, at stations located in

the middle zone there was a high abundance of

Leptohyphidae, Baetidae, Limnephilidae, and

Hydroptilidae. Regarding Leptohyphidae and

Baetidae (Ephemeroptera), Bücker et al. (2010)

and Lorion and Kennedy (2009) found that

they may abound in streams in deforested

areas subject to agricultural and livestock pres-

sure, in addition to their larvae remaining on

rocky substrates, characteristic of this part of

the river. For Trichoptera (Limnephilidae and

Hydroptilidae), Serna et al. (2015) and Springer

(2010) mention that they can construct shelters

on substrates such as stones, rocks, gravel, and

macrophytes, which allow them to survive in a

wider variety of habitats.

The CCA remarked the importance of

dissolved oxygen, temperature, and conductiv-

ity in the distribution of aquatic macroinver-

tebrates in River Tambo. In similar studies it’s

noted that the physicochemical properties pre-

viously mentioned, as well as pH and dissolved

solids may explain the dynamics of neotropi-

cal lotic systems (Carvacho-Aránguiz, 2012;

Mancilla et al., 2009; Morelli & Verdi, 2014),

given that most aquatic organisms are sensi-

tive to these factors (Carvacho-Aránguiz, 2012;

Domínguez & Fernández, 2009; Meza-Salazar

et al., 2012; Quinn & Hickey, 1990; Roldán-

Perez, 1996; Toro et al., 2002;). Some families

are more sensitive to increases in conductivity,

12 Revista de Biología Tropical, ISSN: 2215-2075 Vol. 72: e56670, enero-diciembre 2024 (Publicado May. 21, 2024)

like Leptohyphidae, Simuliidae, and Baetidae

(Meneses-Campo et al., 2019), while others are

more resistant, like Elmidae and Chironomidae,

that showed a positive relation to an increase in

temperature. Elmidae is characterized by car-

rying out gas exchange through the plastron,

taking atmospheric oxygen, submerging, and

exchanging the gas with the oxygen dissolved

in the water, which makes them sensitive to

low availability of dissolved oxygen (Arias-Diaz

et al., 2007; Brown, 1987). Chironomidae is

widely distributed and adapts to different envi-

ronmental conditions, besides being present in

polluted waters (Gutiérrez-Garaviz et al., 2014).

Hydroptilidae lacks any relation with the physi-

cochemical parameters considered.

In many neotropical rivers, there is a pro-

gressive succession of sensitive taxa by others

more tolerant to pollution (Medina-Tafur et

al., 2007). According to the results of the ABI

index, the high and middle zones of the River

Tambo showed a good to moderate quality dur-

ing the sampled period, which probably allowed

for the establishment of an aquatic community

similar to what would be found under natural

conditions (Domínguez et al., 2020). In the

case of the lower part of the river, the water

quality is poor according to the index values.

This is probably due to the presence of a higher

concentration of contaminants as a result of the

intense agricultural activity carried out in this

part of the river (ANA, 2019), as well as from

the discharge of residual effluents from human

settlements in the area, which limit the estab-

lishment of little tolerant macroinvertebrates,

and therefore there is a predominance of those

with a high tolerance to organic contamination,

like Chironomidae (Liévano-León & Ospina-

Torres, 2007; Tobias-Loaiza & Guzmán-Soto,

2022), which has been linked to contamination

and eutrophication of freshwater ecosystems

(González del Tanago & García-Jalón, 1984).

The biological and physicochemical

parameters of a body of water determine the

establishment of the macroinvertebrate com-

munity (Vannote et al., 1980). It has been

reported that, when ecological conditions

are good, Plecoptera, Ephemeroptera, and

Trichoptera are present (Norris & Hawkins,

2000). However, some Ephemeroptera such as

Baetidae and Leptohyphidae, and some Trichop-

tera such as Hydroptilidae and Hydropsychidae,

may be more tolerant (Ríos-Touma et al., 2014).

During the present study, in the high and middle

zone of the river, the presence of Blephariceridae,

Gripopterygidae, Gomphidae, and Hydrobio-

sidae was recorded. The establishment of these

families that are sensitive to organic pollution

(with scores higher than 8 in the ABI index)

(Leaño-Sanabria & Pérez-Barriga, 2020; Roldán-

Pérez, 2016) indicates that the ecological condi-

tions are better upriver. On the contrary, a high

abundance of Chironomidae is typical of zones

where ecological conditions are not suitable to

support an aquatic community similar to that

which would be found in natural conditions

(Medina-Tafur et al., 2010). This family showed

higher abundance at stations E1 and E2, located

in the lower zone of the river, close to its mouth

in the Pacific Ocean, where the greatest environ-

mental impact on the river is evident.

This study is the first one on aquatic mac-

roinvertebrate communities in the River Tambo

and in Arequipa region. The structure and

diversity of macroinvertebrates constitute the

base information for future monitoring in this

basin and the water quality indices obtained

are indicative of the health of the ecosystem

and valuable tools to evaluate and manage

this resource.

Ethical statement: the authors declare

that they all agree with this publication and

made significant contributions; that there is

no conflict of interest of any kind; and that we

followed all pertinent ethical and legal proce-

dures and requirements. All financial sources

are fully and clearly stated in the acknowled-

gments section. A signed document has been

filed in the journal archives.

ACKNOWLEDGMENTS

To Universidad Nacional de San Agustín for

financing this research through FUNDS UNSA

- INVESTIGA. Contrato IAI-006-2018-UNSA.

Revista de Biología Tropical, ISSN: 2215-2075, Vol. 72: e56670, enero-diciembre 2024 (Publicado May. 21, 2024)

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